Endangered and Threatened Wildlife and Plants; 12-Month Finding on a Petition To Downlist Three San Clemente Island Plant Species; Proposed Rule To Reclassify Two San Clemente Island Plant Species; Taxonomic Correction, 29078-29128 [2012-11339]
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Federal Register / Vol. 77, No. 95 / Wednesday, May 16, 2012 / Proposed Rules
DEPARTMENT OF THE INTERIOR
Fish and Wildlife Service
50 CFR Part 17
[Docket No. FWS–R8–ES–2012–0007;
FXES11130900000C5–123–FF09E32000]
RIN 1018–AY04
Endangered and Threatened Wildlife
and Plants; 12-Month Finding on a
Petition To Downlist Three San
Clemente Island Plant Species;
Proposed Rule To Reclassify Two San
Clemente Island Plant Species;
Taxonomic Correction
Fish and Wildlife Service,
Interior.
ACTION: Notice of 12-month petition
finding and proposed rule.
AGENCY:
We, the U.S. Fish and
Wildlife Service, announce our 12month findings on a petition to
reclassify San Clemente Island lotus,
and San Clemente Island paintbrush
under the Endangered Species Act are
warranted and we propose to change the
status of these two species from
endangered to threatened. We also
propose to correct the scientific and
common names of San Clement Island
lotus. We are also announcing our 12month finding on a petition to reclassify
San Clemente Island bush mallow is not
warranted at this time, and therefore we
are not proposing to change the status
of this species. We are taking these
actions as a result of a petition to
reclassify these three species.
DATES: The finding announced in this
document was made on May 16, 2012
Regarding the proposed rule to
reclassify Acmispon dendroideus var.
traskiae and Castilleja grisea, we will
accept comments received or
postmarked on or before July 16, 2012.
We must receive requests for public
hearings, in writing, at the address
shown in the FOR FURTHER INFORMATION
CONTACT section by July 2, 2012.
ADDRESSES: This finding is available on
the Internet at https://
www.regulations.gov at Docket Number
[FWS–R8–ES–2012–0007]. Supporting
documentation we used in preparing
this finding is available for public
inspection, by appointment, during
normal business hours at the U.S. Fish
and Wildlife Service, Carlsbad Fish and
Wildlife Office, 6010 Hidden Valley
Road, Suite 101, Carlsbad, CA, 92011.
Please submit any new information,
materials, comments, or questions
concerning this finding to the above
address. Regarding the proposed rule to
reclassify Acmispon dendroideus var.
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SUMMARY:
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traskiae and Castilleja grisea, you may
submit comments by one of the
following methods:
Federal eRulemaking Portal: https://
www.regulations.gov. Follow the
instructions for submitting comments
for Docket No. [FWS–R8–ES–2012–
0007].
U.S. mail or hand delivery: Public
Comments Processing, Attn: Docket No.
[FWS–R8–ES–2012–0007]; Division of
Policy and Directives Management; U.S.
Fish and Wildlife Service; 4401 N.
Fairfax Drive, Suite 222; Arlington, VA
22203.
We will not accept email or faxes. We
will post all comments on https://
www.regulations.gov. This generally
means that we will post any personal
information you provide us (see the
Public Comments Solicited section
below for more information).
FOR FURTHER INFORMATION CONTACT: Jim
Bartel, Field Supervisor, Carlsbad Fish
and Wildlife Office (see ADDRESSES); by
telephone at 760–431–9440; or by
facsimile (fax) at 760–431–9624. If you
use a telecommunications device for the
deaf (TDD), please call the Federal
Information Relay Service (FIRS) at
800–877–8339.
SUPPLEMENTARY INFORMATION:
Executive Summary
This document contains: (1) 12-month
findings in response to a petition to
reclassify Malacothamnus clementinus,
Acmispon dendroideus var. traskiae,
and Castilleja grisea as threatened; and
(2) a proposed rule to reclassify A. d.
var. traskiae and C. grisea as threatened
under the Act.
Species addressed. Malacothamnus
clementinus (San Clemente Island bush
mallow), Acmispon (previously listed as
Lotus) dendroideus var. traskiae
(previously San Clemente Island broom
and currently known as San Clemente
Island lotus), and Castilleja grisea (San
Clemente Island paintbrush) are
endemic to San Clemente Island, which
is located 64 miles (mi) (103 kilometers
(km)) west of San Diego, California.
Current habitat conditions for M.
clementinus, A. d. var. traskiae, and C.
grisea on San Clemente Island are the
result of present and historical land use
practices. San Clemente Island is owned
by the U.S. Department of the Navy and,
with its associated offshore range
complex, is the primary maritime
training area for the Navy Pacific Fleet
and Navy Sea, Air and Land teams
(SEALs). The island also supports
training by the U.S. Marine Corps, the
U.S. Air Force, and other military
organizations.
Purpose of the Regulatory Action.
Under the Endangered Species Act, we
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may be petitioned to list, delist or
reclassify a species. In 2010, we
received a petition from the Pacific
Legal Foundation requesting that the
Service reclassify Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea from
endangered to threatened. These species
are currently listed as endangered under
the Act. In 2011, we published our 90day finding on the petition which
concluded that the petition contained
substantial information indicating
reclassification of the three San
Clemente Island plants may be
warranted. We therefore also announced
that we were initiating status reviews
for these taxa as required under the Act.
A change in listing status can only be
done by issuing a rule.
Basis for the Regulatory Action.
Under the Endangered Species Act, a
species may be determined to be
endangered or threatened based on any
of five factors: (A) The present or
threatened destruction, modification, or
curtailment of its habitat or range; (B)
Overutilization for commercial,
recreational, scientific, or educational
purposes; (C) Disease or predation; (D)
The inadequacy of existing regulatory
mechanisms; or (E) Other natural or
manmade factors affecting its continued
existence.
We reviewed all available scientific
and commercial information pertaining
to the five threat factors in our status
review of each species.
We summarize the results of our
status review for each species below.
Malacothamnus clementinus (San
Clemente Island Bush Mallow)
• Our review does not support a
conclusion that the threats have been
sufficiently removed, or that their
imminence, intensity, or magnitude
have been reduced to the extent that the
species no longer meets the definition of
an endangered species. Threats
associated with military activities,
erosion, nonnatives, fire, climate
change, and low genetic diversity
continue to impact Malacothamnus
clementinus at all of the 11 occurrences
on San Clemente Island. M. clementinus
continues to be impacted throughout its
range because of the change in intensity
of training and associated impacts
enacted in the 2008 San Clemente
Island Military Operations and Fire
Management Plan (MOFMP).
Additionally, closure of areas on San
Clemente Island to natural resource
personnel creates uncertainty regarding
the status of 4 of 11 occurrences,
including the largest and most
genetically diverse, and whether those
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occurrences will benefit from
conservation measures.
• We find that reclassifying
Malacothamnus clementinus is not
warranted at this time.
• Although we recommended
downlisting in our 2007 status review,
at this time we believe that
Malacothamnus clementinus continues
to be in danger of extinction throughout
its range.
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Acmispon dendroideus var. traskiae
(San Clemente Island Lotus)
• We find that the ongoing threats are
not of sufficient imminence, intensity,
or magnitude to indicate that Acmispon
dendroideus var. traskiae is presently in
danger of extinction throughout its
range and does not, therefore, meet the
definition of an endangered species.
• Since listing and the removal of
feral goats and pigs on San Clemente
Island, the distribution of Acmispon
dendroideus var. traskiae has expanded
from 6 to 29 occurrences. Significant
gains in distribution demonstrate that
the species is persisting despite existing
threats across the landscape.
• The Navy is implementing an
Island Integrated Natural Resources
Management Plan (INRMP) to
coordinate the management of natural
resources and provide for long-term
conservation planning within the scope
of military readiness.
• While it is anticipated that military
training activities, erosion, nonnatives,
and fire will have ongoing impacts to A.
d. var. traskiae habitat, impacts from
these threats are reduced and
minimized based on its distribution and
current and anticipated conservation
efforts for the taxon.
• We find that reclassifying
Acmispon dendroideus var. traskiae as
threatened is warranted.
Castilleja grisea (San Clemente Island
Paintbrush)
• We find the ongoing threats are not
of sufficient imminence, intensity, or
magnitude to indicate that Castilleja
grisea is presently in danger of
extinction across its range and does not,
therefore, meet the definition of an
endangered species.
• Since listing and the removal of
feral goats and pigs on San Clemente
Island, the distribution of Castilleja
grisea has expanded from 19 to 29
known occurrences. This significant
increase in occurrences shows that the
species is persisting despite existing
threats across the landscape.
• The Navy is implementing an
Island Integrated Natural Resources
Management Plan (INRMP) to
coordinate the management of natural
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resources and provide for long-term
conservation planning within the scope
of military readiness.
• While it is anticipated that military
training activities, erosion, nonnatives,
and fire will have ongoing impacts to
Castilleja grisea habitat, impacts from
these threats are reduced and
minimized based on its distribution and
current and anticipated conservation
efforts for the taxon.
• We find that reclassifying Castilleja
grisea as threatened is warranted.
We are proposing the following
changes to the List of Threatened and
Endangered Plants:
• Correct the scientific and common
names of Acmispon dendroideus var.
traskiae, formerly known as Lotus
dendroideus var. traskiae (San Clemente
broom).
• Change the status of Acmispon
dendroideus var. traskiae from
endangered to threatened.
• Change the status of Castilleja
grisea from endangered to threatened.
Acronyms Used
We use several acronyms throughout
the preamble to this proposed rule. To
assist the reader, we set them forth here:
AFP = Artillery Firing Point
AVMA = Assault Vehicle Maneuver Area
BMP = Best Management Practices
CERCLA = Comprehensive Environmental
Response, Compensation and Liability Act
CESA = California Endangered Species Act
CDFG = California Department of Fish and
Game
CNDDB = California Natural Diversity
Database
CNPS = California Native Plant Society
DPS = Distinct Population Segment
EO = California Natural Diversity Database
element occurrence
GIS = Geographic Information System
INRMP = Integrated Natural Resources
Management Plan
IOA = Infantry Operations Areas
IPCC = Intergovernmental Panel on Climate
Change
MOFMP = Military Operations and Fire
Management Plan
Navy = United States Department of the Navy
NEPA = National Environmental Policy Act
NPPA = Native Plant Protection Act
OHV = Off Highway Vehicle
OMB = Office of Management and Budget
PL = Point Location
RCRA = Resource Conservation and Recovery
Act
SEALs = Navy Sea, Air, and Land teams
SERG = San Diego State University Soil
Ecology and Restoration Group
SHOBA = Shore Bombardment Area
SPR = Significant Portion of the Range
SWAT = Special Warfare Training Areas
TAR = Training Area Ranges
USFWS = United States Fish and Wildlife
Service
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Public Comments Solicited
Our intent is to use the best available
commercial and scientific data as the
foundation for all endangered and
threatened species classification
decisions. Therefore, we request
comments or information from the
public, other concerned governmental
agencies, Native American tribes, the
scientific community, industry, or any
other interested parties concerning this
proposed rule to downlist Acmispon
dendroideus var. traskiae and Castilleja
grisea. We particularly seek comments
concerning:
(1) Reasons why we should or should
not reclassify Acmispon dendroideus
var. traskiae and Castilleja grisea under
the Act.
(2) New biological, trade, or other
relevant information and data
concerning any threat (or lack thereof)
to A. d. var. traskiae and C. grisea.
(3) New information and data on the
projected and reasonably likely impacts
to A. d. var. traskiae and C. grisea
associated with climate change.
(4) The location of, and status, trends,
and threats to, any additional
occurrences of A. d. var. traskiae and C.
grisea.
(5) New information and data
concerning the range, distribution,
occurrence size, and occurrence trends
of A. d. var. traskiae and C. grisea.
(6) New information and data on the
current or planned activities within the
geographic range of A. d. var. traskiae
and C. grisea that may adversely affect
or benefit the species.
(7) New information on the host
plants of C. grisea.
(8) Information and data on the
hybridization of A. d. var. traskiae, and
the impacts of this hybridization on the
species.
We will also continue to accept new
information that becomes available
concerning the status or threats to the
Malacothamnus clementinus or its
habitat at any time.
We will post your entire comment on
https://www.regulations.gov. Before
including your address, phone number,
email address, or other personal
identifying information in your
comment, you should be aware that
your entire comment—including your
personal identifying information—may
be made publicly available at any time.
While you can ask us in your comment
to withhold your personal identifying
information from public review, we
cannot guarantee that we will be able to
do so.
Comments and materials we receive,
as well as supporting documentation we
used in preparing this proposed rule,
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will be available for public inspection
on https://www.regulations.gov, or by
appointment during normal business
hours at the Carlsbad Fish and Wildlife
Office (see ADDRESSES).
Public Hearing
The Act provides for one or more
public hearings on this proposal, if
requested. Requests must be received by
the date specified in DATES. Such
requests must be made in writing and
addressed to the Field Supervisor (see
FOR FURTHER INFORMATION CONTACT
section above).
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Background
Section 4(b)(3)(B) of the Endangered
Species Act of 1973, as amended (Act;
16 U.S.C. 1531 et seq.), requires that, for
any petition to revise the Federal Lists
of Endangered and Threatened Wildlife
and Plants that contains substantial
scientific or commercial information
that reclassifying the species may be
warranted, we make a finding within 12
months of the date of receipt of the
petition. In this finding, we will
determine whether the petitioned action
is: (a) Not warranted, (b) warranted, or
(c) warranted, but the immediate
proposal of a regulation implementing
the petitioned action is precluded by
other pending proposals to determine
whether species are endangered or
threatened, and expeditious progress is
being made to add or remove qualified
species from the Federal Lists of
Endangered and Threatened Wildlife
and Plants. We must publish these 12month findings in the Federal Register.
Previous Federal Actions
Malacothamnus clementinus,
Acmispon dendroideus var. traskiae,
and Castilleja grisea were listed as
endangered under the Act on August 11,
1977 (42 FR 40682). Subsequently, a
Recovery Plan for Channel Island
species, including M. clementinus, A. d.
var. traskiae, and C. grisea, was
finalized in 1984 (USFWS 1984, pp. 1–
165), and 5-year status reviews were
completed for each of these taxa in 2007
(USFWS 2007a, pp. 1–28; USFWS
2007b, pp. 1–22; USFWS 2007c, pp. 1–
19). These status reviews recommended
reclassification of M. clementinus, A. d.
var. traskiae, and C. grisea from
endangered to threatened status.
On May 18, 2010, we received a
petition dated May 13, 2010, from the
Pacific Legal Foundation requesting that
the Service delist Oenothera californica
(avita) subsp. eurekensis (Eureka Valley
evening-primrose) and Swallenia
alexandrae (Eureka Valley dunegrass),
and downlist tidewater goby
(Eucyclogobius newberryi), Acmispon
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dendroideus (Lotus scoparius subsp.)
var. traskiae, Malacothamnus
clementinus, and Castilleja grisea from
endangered to threatened under the Act.
The petition was based on the analysis
and recommendations contained in the
2007 5-year reviews for these taxa. In a
letter to the petitioner dated September
10, 2010, we acknowledged receipt of
the petition and initiated a review of the
petition under a provision of section 4
of the Act. We stated that we anticipated
making an initial 90-day finding in
Fiscal Year 2011 (based on available
staffing and funding) as to whether or
not the petition presented substantial
information indicating that the
requested action may be warranted.
On January 19, 2011, we published a
90-day finding (76 FR 3069) in which
we concluded that the petition and
information in our files provided
substantial information that the
reclassification of these species may be
warranted, and announced that we were
initiating status reviews for these
species. Five-year reviews pursuant to
section 4(c)(2)(A) of the Act for
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea were previously initiated on May
21, 2010 (75 FR 28636). We will base
our 5-year review recommendations on
the information and conclusions
provided in this finding, and we expect
to finalize those reviews following
publication of this finding. To ensure
that the status reviews are
comprehensive, we requested in the 90day finding any scientific or commercial
data and other information regarding
these taxa be submitted by March 21,
2011. This document includes: (1) A
notice that constitutes the 12-month
finding in response to the petition to
reclassify M. clementinus, A. d. var.
traskiae, and C. grisea as threatened (the
12-month findings for O. californica
(avita) subsp. eurekensis, S. alexandrae,
and tidewater goby will be addressed in
separate documents); and (2) a proposed
rule to reclassify A. d. var. traskiae and
C. grisea from endangered to threatened
under the Act.
Species Information
For purposes of this finding, we
present the species description and
taxonomy for each individual plant
species below. However, the remaining
species information, where possible, is
combined for all three taxa to avoid
redundancy, followed by applicable
species-specific information by taxon.
Species Description and Taxonomy—
Malacothamnus clementinus
Malacothamnus clementinus is a
rounded subshrub (stems woody only at
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the base) in the Malvaceae (mallow
family). Plants are 2.3 to 3.3 feet (ft) (0.7
to 1 meters (m)) tall with numerous
hairy branched stems arising from the
base of the plant (Munz and Johnston
1924, p. 296; Munz 1959, pp. 122–125;
Bates 1993, p. 752; Junak 2006a, pers.
comm.). Plants have the ability to
spread vegetatively by underground
rhizomes, resulting in patches of
spatially separate, but genetically
identical, individuals (Evans and Bohn
1987, p. 538). The leaves are 1.2 to 2
inches (in) (3 to 5 centimeters (cm))
wide and conspicuously bicolored, with
green upper surfaces covered in short
fine hairs and veiny, white
undersurfaces that are densely matted
with hairs (Munz and Johnston 1924, p.
296). Flowers are clustered in the
uppermost leaf axils, forming
interrupted spikes 3.9 to 7.9 in (10 to 20
cm) long (Munz 1959, p. 125). Flowers
are bisexual and variously described as
having pink or white and fading
lavender petals (Munz and Johnston
1924, p. 296; Bates 1993, p. 752). Each
flower can produce about 10 seeds that
are 0.08 in (2 millimeters (mm)) long
(Munz 1959, p. 122; Navy 2002, p. C–
43). The fruits mature and open slowly
and irregularly on the plant (Navy 2002,
p. C–43). The genus Malacothamnus
includes 20 species found in the
southwestern region of the United States
(Junak and Wilken 1998, p. 290).
Malacothamnus clementinus is endemic
to San Clemente Island and is the only
species within the genus that occurs
there (Bates 1993, p. 752; Tierra Data
Inc. 2005, p. C–8).
No taxonomic classifications or
nomenclature changes affecting this
taxon have been published since it was
listed as endangered in 1977. The
Jepson Manual, the standard reference
flora for the State, continued to treat this
species under the same name,
Malacothamnus clementinus, in the
recent edition (Bates 2012, pp. 1–2).
Species Description and Taxonomy—
Acmispon dendroideus var. traskiae
Acmispon dendroideus var. traskiae
is a suffrutescent (semi-woody), shortlived (less than 5 years), floriferous
(flower bearing) subshrub in the legume
family Fabacaeae (pea family). It is
endemic to San Clemente Island (Isely
1993, p. 619), and is one of five taxa in
the genus Acmispon found on the island
(Tierra Data Inc. 2005, p. C–8; Brouillet
2008, pp. 388–392). There are no other
varieties of A. dendroideus found on the
island. This variety can be distinguished
from other varieties of A. dendroideus
by its bushy habit and elongated fruits
(Allan 1999, p. 88). Acmispon
dendroideus var. traskiae is typically
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less than 4 ft (1.2 m) tall with slender
erect green branches (Munz 1974, pp.
449–450; USFWS 1984, p. 59; Allan
1999, p. 82). Each leaf has three to five
leaflets, each approximately 0.2 to 0.3 in
(5 to 9 mm) long and uniformly glabrous
(surface without hair) to finely hairy
(USFWS 1984, p. 59; Allan 1999, p. 82).
Acmispon dendroideus var. traskiae has
small yellow flowers that are bisexual
and arranged in one to five flowered
clusters on stalks that arise from axils
between the stem and leaf of terminal
shoots (Junak and Wilken 1998, p. 256).
Pistils are initially yellow, turning
orange then red as the fruit matures
(USFWS 1984, p. 59; California Native
Plant Society (CNPS) 2001, p. 208).
Acmispon dendroideus var. traskiae
has undergone taxonomic realignments
since the 1977 listing. We accept the
change of scientific name to Acmispon
dendroideus (Greene) Brouillet var.
traskiae (Noddin) Brouillet from Lotus
dendroideus (Nutt.) Ottley subsp.
traskiae. This change is supported by
morphological and molecular data
(Allan and Porter 2000, p. 1876;
Sokoloff 2000, p. 128; Brouillet 2008, p.
389).
The name used for this taxon when it
was listed in 1977 (42 FR 40682) was
Lotus scoparius (Nutt.) Ottley subsp.
traskiae (Abrams) Raven. Subsequently,
Isely (1978, p. 467) separated this and
two other Channel Islands endemic taxa
(L. scoparius var. veatchi Ottley and L.
scoparius var. dendroideus (Greene)
Ottley) from mainland Lotus scoparius.
He recognized them as varieties
(considered equivalent to subspecies in
plants) of a single species, Lotus
dendroideus, which was the oldest
name among the three taxa. The name,
Lotus dendroideus var. traskiae, was
published by Isely in 1978 (p. 467), and
recognized in floristic (Isely 1993, p.
619) and systematic treatments (Isely
1998, p. 646). Following Isely’s
taxonomic revision, we amended the list
of endangered and threatened plants (50
CFR 17.12), but incorrectly transcribed
the name as Lotus dendroideus subsp.
traskiae (USFWS 1980, 45 FR 82483).
This combination, as a subspecies and
not a variety, was never validly
published and thus cannot be used.
Recent morphological (Sokoloff 2000,
p. 128) and molecular (Allan and Porter
2000, p. 1876) data support recognition
of a separate genus, Acmispon, from
Lotus. The required nomenclatural
combination Acmispon dendroideus
(Greene) Brouillet var. traskiae (Noddin)
Brouillet was made in 2008 (Brouillet
2008, p. 389). This name is recognized
and accepted by the scientific
community in floristic works, the
Jepson Manual revision for California
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(Brouillet 2012), and the continental
Flora of North America, as well as by
the California Native Plant Society
(CNPS 2011). We concur with the
scientific evidence and acceptance by
the scientific community and likewise
accept the name Acmispon dendroideus
var. traskiae. Based upon this
acceptance, we will make appropriate
corrections to this taxon’s references in
our regulations (50 C.F.R. 17.12) and
will use this nomenclature in future
notices regarding this taxon. Moreover,
in previous documents, this taxon has
been referred to by other common
names (such as Trask’s Island lotus, San
Clemente Island broom, and San
Clemente Island lotus) (Isely 1993, p.
619; 76 FR 3069, January 19, 2011; 42
FR 40682, August 11, 1977). In this
document, we use San Clemente Island
lotus to represent A. d. var. traskiae.
The taxonomic and nomenclatural
changes described here do not alter the
description, distribution, or listing
status of the taxon.
Species Description and Taxonomy—
Castilleja grisea
Castilleja grisea is a highly branched
hemiparasitic (plant that can be either
free-living or parasitic) perennial herb to
subshrub in the Orobanchaceae
(broomrape family) (Chuang and
Heckard 1993, p. 1016; Young et al.
1999, p. 890; Olmstead et al. 2001, p.
352). Castilleja grisea is endemic to San
Clemente Island and the only species of
the genus found there (Chuang and
Heckard 1993, p. 1021; Helenurm et al.
2005, p. 1222; Tierra Data Inc. 2005, p.
A–7). Castilleja grisea plants are 1.3 to
2 ft (0.4 to 0.6 m) tall and ash-gray in
color with densely hairy leaves (Chuang
and Heckard 1993, p. 1021). The leaves
are alternate and linear, and 0.4 to 2 in
(1 to 5 cm) long with 0 to 3 lobes
(Chuang and Heckard 1993, p. 1021).
The yellow bisexual flowers are borne
in terminal spikes. The fruit is a semiwoody capsule, 0.4 to 0.5 in (10 to 12
mm) long, bearing many small seeds
(Chuang and Heckard 1993, p. 1021;
Junak and Wilken 1998, p. 83). Seeds
have a deeply netted seedcoat, and are
0.4 to 0.6 in (1 to 1.5 mm) in diameter
(Muller and Junak 2011, p. 12).
Castilleja grisea was described by
Dunkle (p. 31) in 1943. The name has
not changed since the species was
listed, although the family affiliation
has been changed to the Orobanchaceae
(broomrape family) from the
Scrophulariaceae (figwort family;
Olmstead et al. 2001, p. 352). We will
revise our regulations at 50 C.F.R. 17.12
to reflect this change in family
affiliation. This taxonomic change
remains consistent in the upcoming
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Sfmt 4702
29081
edition of the Jepson Manual (Chuang
and Heckard, Weatherwax, rev. 2012).
Species Location
Description and Land Use of San
Clemente Island
Malacothamnus clementinus,
Acmispon dendroideus var. traskiae,
and Castilleja grisea are endemic to San
Clemente Island (Raven 1965, p. 60),
which is located 64 miles (mi) (103
kilometers (km)) west of San Diego,
California (USFWS 1984, p. 5). The
island is approximately 56 square mi
(145 square km) (Junak and Wilken
1998, p. 2) and is long and narrow: 21
mi (34 km) long by 1.5 mi (2.4 km) wide
at the north end and 4 mi (6.4 km) wide
at the south end (USFWS 1984, p. 5).
The historical ranges and
distributions of Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea on
San Clemente Island are unknown
because botanical studies were not
conducted on the island prior to
grazing, which began in the 1800s
(Kellogg and Kellogg 1994, p. 4). The
first herbarium specimens were
collected in 1894 for M. clementinus
and C. grisea, and in 1905 for A. d. var.
traskiae. Although herbarium
specimens were collected from time to
time, the first surveys for these species
did not occur until the 1970s (USFWS
2007b, p. 4).
San Clemente Island is owned by the
U.S. Department of the Navy (Navy)
and, with its associated offshore range
complex, is the primary maritime
training area for the Pacific Fleet and
SEALs. The island also supports
training by the U.S. Marine Corps, the
U.S. Air Force, and other military
organizations. As the western most
training range in the eastern Pacific
Basin where training operations are
performed prior to troop deployments,
portions of the island receive intensive
use by the military (Navy 2008b, p. 2–
2). Various training activities occur
within particular land use designations
and training areas on the island, which
are coincidentally concentrated in
habitat that supports Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. In
2008, the Navy adopted the MOFMP to
increase the amount and intensity of
training on San Clemente Island (Navy
2008b, pp. 2–1 to 2–52). The impact to
habitat from military activities is
increasing under this plan (USFWS
2008, pp. 1–237).
Military training activities within
Naval Special Warfare Training Areas
(SWAT), Training Area Ranges (TAR),
Impact Areas, and the Infantry
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srobinson on DSK4SPTVN1PROD with PROPOSALS2
Operations Areas (IOA) involve the
movement of vehicles and troops over
the landscape, and can include live
munitions fire, incendiaries,
demolitions, and bombardment. These
activities have multiple impacts,
including disturbances to soil and
vegetation, spread of nonnative plant
species, creation of road ruts and trails,
and compaction of soils (USFWS 2008,
pp. 83–87). TARs cover a total of 1,840
acres (ac) (744 hectares (ha)), or 5.4
percent of the island, while IOAs
encompass 8,815 ac (3,567 ha) or
approximately 25 percent of the island,
SWATs cover a total of 10,897 ac (4410
ha) or approximately 30 percent of the
island, and Impact Areas cover 3,459 ac
(1,400 ha) or approximately 10 percent
of the island (Navy 2008a, pp. 2–17, 2–
45; Navy 2008b, p. 3.11–52).
The Navy has delineated areas of
military use to define where specific
activities will take place. These
delineated areas include the Shore
Bombardment Area (SHOBA),
constituting the southern one third of
the island. Please note that while the
SHOBA boundary is illustrated in
Figures 1 to 3, no other boundaries are
shown for security reasons, although
other training areas will be discussed in
the text of this document. SHOBA,
which covers approximately 10,061 ac
(4071 ha) (Navy 2009, p. 2–4), serves as
a buffer around Impact Areas I and II
and supports a variety of training
operations. Parts of SHOBA are not
subject to training activities and serve
only as a buffer, while other areas
support military activities, including
movement of troops and vehicles or
bombing exercises (Navy 2002, p. 2–4).
The Impact Areas sustain heavy live fire
and are a recurrent source of wildfires.
Fuel breaks are applied each year prior
to fire season to help prevent spread of
fire to areas outside of the Impact Areas.
Because parts of SHOBA are used for
ship-to-shore bombardment, access to
this area is restricted for nonmilitary
personnel on days when bombing is
occurring. Individuals conducting
surveys or working on invasive species
control projects are granted access to
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areas outside of the Impact Areas within
SHOBA when military activities
requiring exclusive use are not
occurring. Because of the frequency of
training, access to SHOBA can be
restricted for long periods of time.
Range operators are aware of the natural
resource obligations within SHOBA,
and at least 1 day a week is usually
allowed for natural resource programs to
conduct their activities. Weeks with
reduced natural resource access,
including infrequent events that exclude
natural resource personnel from SHOBA
for 10 to 20 days, are announced in
advance and provide natural resource
managers the opportunity to plan
accordingly.
Safety concerns relative to the
presence of unexploded ordnance
within SHOBA have recently prompted
the Navy to review access policies
(O’Connor 2006, pers. comm.; USFWS
2008, p. 50; Munson 2011c, pers.
comm.). In the Navy’s MOFMP (Navy
2008a; pp. 2–38 to 2–44), Impact Areas
I and II were indefinitely closed ‘‘for
any purpose, including monitoring and
management of endangered and
sensitive species and their habitat’’ for
safety reasons (Navy 2008a, p. 2–45).
Impact Areas I and II cover
approximately 3,459 ac (1,400 ha), or
approximately 10 percent of the island’s
36,000 ac (14,568 ha; Navy 2008a, p. 2–
45. The Navy is revising its INRMP to
develop solutions to monitor species
and their threats in these areas
potentially through unmanned vehicles,
aircraft, or with the assistance of range
maintenance personnel that regularly
access the areas. In the meantime, there
are no monitoring or management
actions occurring in these areas.
Access to additional areas on the
island where unexploded ordnance has
been found is now also restricted for
natural resource personnel (such as
areas in the eastern escarpment within
SHOBA, Eel Point, Pyramid Head, and
Lemon Tank Canyon) (Munson 2011c,
pers. comm.). Restricted access to these
sites limits the opportunities to acquire
information on the status of
Malacothamnus clementinus, Acmispon
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Fmt 4701
Sfmt 4702
dendroideus var. traskiae, and
Castilleja grisea occurrences, and
inhibits the ability to manage threats in
those areas. The Navy is developing
plans to trim the vegetation in these
areas so that sweeps by specially trained
technicians can clear the areas of
unexploded ordnance to allow access by
nonmilitary personnel (Munson 2011c,
pers. comm.).
As part of its monitoring and recovery
efforts for listed species, the Navy
initiated several rare plant surveys on
San Clemente Island (Junak and Wilken
1998, pp. 1–416, GIS data; Junak 2006,
pp. 1–176, GIS data; Tierra Data Inc.
2008, pp. 1–24, appendices and GIS
data; SERG 2009–2011, GIS data). These
surveys involved the collection of point
locations that represent discrete
localities of plants detected during field
surveys. Temporal and spatial variation
among data points from these surveys is
likely due to differences between
individual researchers’ survey
techniques or accuracy of data records.
Groups of plants were described in the
past using many different terms
including: Point localities, populations,
occurrences, and element occurrences.
Unless referring to a specific author’s
research and language, we refer to
identifiable and separable groups of
plants as ‘‘occurrences’’ in this finding
and proposed rule. We defined these
occurrences by mapping smaller
groupings of plants (point locations) and
combining point locations that fall
within 0.25 mi (402 m) of one another
with any corresponding California
Natural Diversity Database (CNDDB)
polygons. These combined points meet
the broader California Department of
Fish and Game (CDFG) definition of an
element occurrence, which is a record of
an observation or series of observations.
Discussion of occurrences throughout
this 12-month finding includes
groupings of CNDDB element
occurrences and point localities within
a 0.25-mi (402 m) radius of a given
occurrence. Information for each
occurrence of these three taxa is
described in Table 1.
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Federal Register / Vol. 77, No. 95 / Wednesday, May 16, 2012 / Proposed Rules
29083
TABLE 1—DISTRIBUTION AND STATUS OF OCCURRENCES OF Malacothamnus clementinus (SAN CLEMENTE ISLAND BUSH
MALLOW), Acmispon dendroideus VAR. traskiae (SAN CLEMENTE ISLAND LOTUS), AND Castilleja grisea (SAN
CLEMENTE ISLAND PAINTBRUSH)
Location
description
Element
occurrence (EO) #
and point location
(PL) 1
Status 2 at listing;
year of first record
Current
status
(reference)
Current threats 3
Military use 4
Malacothamnus clementinus
Canchalagua Canyon
No EO; 1 PL .............
Unknown ...................
Presumed Extant
(SERG 2011).
Horse Beach Canyon
EO 3; 48 PLs ............
Unknown ...................
Presumed Extant
(Junak 2005).
Lower China Canyon ..
EO 1; 9 PLs ..............
Extant; 1975 herbarium record.
Presumed Extant
(Junak 1997,
SERG 2009).
Upper China Canyon
(including Upper
Horse Beach Canyon).
No EO; 4 PLs ...........
Extant; 1975 herbarium record.
Extant (SERG 2010)
Cave Canyon (including Kinkipar Canyon).
Chukit Canyon ............
No EO; 27 PLs .........
Unknown ...................
Extant (SERG 2010)
2 PLs .........................
Unknown ...................
Extant (Junak 2004)
Lemon Tank Canyon ..
EO 2 ..........................
Extant; 1923 herbarium record.
Presumed Extant
(CNDDB 1996).
Box Canyon ................
EO 4; 9 PLs ..............
Unknown ...................
Extant (SERG 2009)
Norton Canyon ...........
EO 7; 27 PLs ............
Unknown ...................
Extant—(SERG 2011)
Middle Ranch Canyon
EO 5; 5 PLs ..............
Unknown ...................
Extant (SERG 2008)
Waymuck Canyon ......
EO 6; 1 PL ................
Unknown ...................
Presumed Extant
(CNDDB 1985).
A: Nonnative, Fire; E:
Fire, Climate, Genetic.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate, Genetic.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate, Genetic.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate, Genetic.
A: Nonnative, Fire; E:
Fire, Climate, Genetic.
A: Nonnative, Fire; E:
Fire, Climate, Genetic.
A: Land Use, Erosion,
Nonnative; E:
Movement, Climate, Genetic.
A: Nonnative; E: Climate, Genetic.
A: Nonnative; E: Climate, Genetic.
A: Erosion, Nonnative; E: Climate,
Genetic.
A: Erosion, Nonnative; E: Climate,
Genetic.
Low Military Value;
Area Recently
Closed.
High Military Value;
Area Closed.
High Military Value;
Area Closed.
Low Military Value.
Medium Military
Value.
Low Military Value.
Low Military Value;
Area Closed.
Low Military Value.
Low Military Value.
Low Military Value.
High Military Value.
Acmispon dendroideus var. traskiae
EO 1, 9 PLs ..............
Extant; 1980 CNDDB
Extant (Junak 2006,
SERG 2008).
Bryce Canyon .............
No EO, 14 PLs .........
Unknown ...................
Extant (SERG 2009)
North Mosquito Cove
srobinson on DSK4SPTVN1PROD with PROPOSALS2
Eagle Canyon .............
EO 8, 14 PLs ............
Extant; 1939 herbarium record.
Extant (SERG 2010)
Canchalagua Canyon
(including south
Mosquito Cove).
EO 4, 21 PLs ............
Unknown ...................
Extant (SERG 2011)
Thirst Canyon (including Vista Canyon).
Cave Canyon .............
No EO, 8 PLs ...........
Unknown ...................
Extant (SERG 2009)
No EO, 3 PLs ...........
Unknown ...................
Horse Canyon ............
No EO, 2 PLs ...........
Unknown ...................
Pyramid Head ............
EO 5, 1 PL ................
Extant; 1979 CNDDB
Presumed Extant
(Junak 1997).
Presumed Extant
(Junak 1997).
Presumed Extant
(Junak 1997).
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Sfmt 4702
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative, Fire; :
Fire, Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative, Fire; E:
Fire, Climate.
A: Nonnative, Fire; E:
Fire, Climate.
A: Nonnative, Fire; E:
Fire, Climate.
A: Nonnative, Fire; E:
Fire, Climate.
E:\FR\FM\16MYP2.SGM
16MYP2
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
Medium Military
Value.
Medium Military
Value.
Medium Military
Value.
High Military Value;
Area Closed.
29084
Federal Register / Vol. 77, No. 95 / Wednesday, May 16, 2012 / Proposed Rules
TABLE 1—DISTRIBUTION AND STATUS OF OCCURRENCES OF Malacothamnus clementinus (SAN CLEMENTE ISLAND BUSH
MALLOW), Acmispon dendroideus VAR. traskiae (SAN CLEMENTE ISLAND LOTUS), AND Castilleja grisea (SAN
CLEMENTE ISLAND PAINTBRUSH)—Continued
Element
occurrence (EO) #
and point location
(PL) 1
Status 2 at listing;
year of first record
SHOBA Boundary
(north to Twin Dams
Canyon).
Twin Dams Canyon ....
No EO, 8 PLs ...........
Unknown ...................
Presumed Extant
(Junak 1996).
A: Nonnative; E: Climate.
Medium Military
Value.
No EO, 2 PLs ...........
Unknown ...................
Extant (Junak 2006)
Horton Canyon (including Stone,
Burn’s, and Horton
Canyons).
Tota Canyon ...............
EO 13, 27 PLs ..........
Unknown ...................
Extant (SERG 2010)
A: Nonnative; E: Climate.
A: Erosion, Nonnative; E: Climate.
Medium Military
Value.
Medium Military
Value.
No EO, 7 PLs ...........
Unknown ...................
No EO, 19 PLs .........
Unknown ...................
EO 16, 2 PLs ............
Unknown ...................
Extant (SERG 2011)
Chamish Canyon ........
EO 3, 1 PL ................
Extant; 1980 CNDDB
Presumed Extant
(Junak 1997).
Box Canyon ................
No EO, 2 PLs ...........
Unknown ...................
Norton Canyon ...........
No EO, 1 PL .............
Unknown ...................
Presumed Extant
(Junak 1997).
Extant (Junak 2004)
Upper Middle Ranch
Canyon.
Lower Middle Ranch
Canyon.
Waymuck Canyon ......
EO 10, 5 PLs ............
Unknown ...................
Extant (Junak 2004)
No EO, 3 PLs ...........
Unknown ...................
Extant (SERG 2008)
No EO, 4 PLs ...........
Unknown ...................
Extant (SERG 2011)
Warren Canyon ..........
EO 12, 20 PLs ..........
Unknown ...................
Extant (SERG 2011)
Middle Wallrock Canyon.
Upper Wallrock Canyon.
Seal Cove Terraces ...
No EO, 10 PLs .........
Unknown ...................
Extant (Junak 2004)
No EO, 3 PLs ...........
Unknown ...................
Extant (Junak 2006)
No EO, 3 PLs ...........
Unknown ...................
Extant (Junak 2004)
Eel Cove Canyon (including terraces).
EO 14, 6 PLs ............
Unknown ...................
Extant (SERG 2010)
Middle Island Plateau
EO 7, 6 PLs ..............
Unknown ...................
Extant (Tierra Data
2007).
Wilson Cove ...............
EO 11, 52 PLs ..........
Extant; 1981 CNDDB
Extant (SERG 2010)
North Wilson Cove .....
EO 9, no PLs ............
Unknown ...................
North Island Terraces
EO 15, no PLs ..........
Extant; 1959 herbarium record.
Unknown ...................
A: Erosion, Nonnative; E: Climate.
A: Erosion, Nonnative; E: Movement, Climate.
A: Erosion, Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Erosion, Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative; E: Climate.
A: Nonnative; E: Climate, Hybridization.
A: Erosion, Nonnative; E: Climate.
A: Nonnative; E: Climate.
A: Nonnative; E: Climate.
A: Erosion, Nonnative; E: Movement, Climate.
A: Nonnative; E:
Movement, Climate.
A: Erosion, Nonnative; E: Climate.
A: Erosion, Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Erosion, Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate, Hybridization.
A: Erosion, Nonnative; E: Climate.
A: Erosion, Nonnative; E: Movement, Climate.
Low Military Value.
Lemon Tank Canyon
(including Nanny
Canyon).
Larkspur Canyon ........
Presumed Extant
(SERG 2010).
Extant (Junak 2004)
srobinson on DSK4SPTVN1PROD with PROPOSALS2
Location
description
Current
status
(reference)
Presumed Extant
(CNDDB 1996).
Current threats 3
Military use 4
Low Military Value;
Area Partially
Closed.
Low Military Value.
Low Military Value.
Low Military Value.
Low Military Value.
Low Military Value.
Low Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
High Military Value.
Medium Military
Value.
Castilleja grisea
Thirst Canyon (including Vista Canyon).
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PLs.
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Extant; 1980 CNDDB
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Extant (SERG 2010)
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A: Nonnative, Fire; E:
Climate.
E:\FR\FM\16MYP2.SGM
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Medium Military
Value.
Federal Register / Vol. 77, No. 95 / Wednesday, May 16, 2012 / Proposed Rules
29085
TABLE 1—DISTRIBUTION AND STATUS OF OCCURRENCES OF Malacothamnus clementinus (SAN CLEMENTE ISLAND BUSH
MALLOW), Acmispon dendroideus VAR. traskiae (SAN CLEMENTE ISLAND LOTUS), AND Castilleja grisea (SAN
CLEMENTE ISLAND PAINTBRUSH)—Continued
Element
occurrence (EO) #
and point location
(PL) 1
Eagle Canyon (including Grove Canyon).
EO 7 & 30; 50 PLs ...
Extant; 1979 herbarium record.
Extant (Tierra Data
2006).
Bryce Canyon .............
EO 3, 8 & 47; 43 PLs
Extant; 1979 GIS
data.
Extant (SERG 2010)
Canchalagua Canyon
(including south
Mosquito Cove and
Matriarch Canyon).
EO 4 & 27; 56 PLs ...
Extant; 1963 herbarium record.
Extant (SERG 2011)
Knob Canyon .............
EO 2 & 49; 21 PLs ...
Extant; 1979 CNDDB
Extant (Tierra Data
2006, SERG 2008).
Pyramid Head ............
EO 1 & 15; 25 PLs ...
Extant; 1965 herbarium record.
Extant (SERG 2011)
Snake Canyon (including Sun Point).
Upper Chenetti Canyon.
EO 23; 4 PLs ............
Extant; 1939 CNDDB
EO 34; 1 PL ..............
Unknown ...................
Presumed Extant
(Junak 1997).
Extant (Junak 2004)
Horse Beach Canyon
EO 33 & 35; 49 PLs
Extant; 1939 herbarium record.
Presumed Extant
(Junak 2005).
China Canyon ............
EO 25, 37 & 46; 6
PLs.
Extant; 1939 herbarium record.
Presumed Extant
(Junak 1997;
SERG 2009).
Red Canyon ...............
EO 36; no PLs ..........
Extant; 1975 herbarium record.
Presumed Extant
(CNDDB 1986).
Kinkipar Canyon .........
No EO; 2 PLs ...........
Unknown ...................
Extant (SERG 2006)
Cave Canyon .............
EO 17, 18 & 45; 9
PLs.
No EO; 6 PLs ...........
Extant; 1980 CNDDB
Extant (SERG 2009)
Horse Canyon ............
Unknown ...................
Extant (SERG 2010)
Upper Horse Canyon
srobinson on DSK4SPTVN1PROD with PROPOSALS2
Location
description
EO 19 & 39; 1 PL .....
Extant; 1979 CNDDB
Extant (Junak 2004)
SHOBA Boundary
(north to and including Twin Dams Canyon).
Horton Canyon (including Stone and
Burn’s Canyons).
Lemon Tank Canyon
(including Tota Canyon).
EO 31; 55 PLs ..........
Extant; 1965 CNDDB
Extant (Junak 2006,
SERG 2011).
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Climate.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Climate.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Climate.
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Climate.
A: Nonnative, Fire; E:
Fire, Climate.
A: Nonnative, Erosion, Fire, Fire
Management; E:
Fire, Climate.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate.
A: Land Use, Erosion,
Nonnative, Fire,
Fire Management;
E: Movement, Fire,
Climate.
A: Nonnative, Fire; E:
Climate.
A: Nonnative, Fire; E:
Climate.
A: Nonnative, Fire; E:
Climate.
A: Erosion, Nonnative, Fire; E: Climate.
A: Nonnative; E: Climate.
EO 12 & 44; 24 PLs
Extant; 1981 CNDDB
Extant (Junak 2006,
SERG 2010).
A: Erosion, Nonnative; E: Climate.
Medium Military
Value.
No EO; 14 PLs .........
Unknown ...................
Extant (SERG 2010)
Low Military Value;
Area Closed.
Nanny Canyon ...........
EO 13; 3 PLs ............
Extant; 1979 CNDDB
Extant (Junak 2004)
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative; E:
Movement, Climate.
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Status 2 at listing;
year of first record
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Current
status
(reference)
Sfmt 4702
Current threats 3
E:\FR\FM\16MYP2.SGM
16MYP2
Military use 4
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
Low Military Value;
Area Recently
Closed.
High Military Value;
Partially Recently
Closed.
High Military Value;
Area Closed.
High Military Value;
Area Closed.
High Military Value;
Area Closed.
High Military Value;
Area Closed.
High Military Value;
Area Closed.
Medium Military
Value.
Medium Military
Value.
Medium Military
Value.
Medium Military
Value.
Medium Military
Value.
Low Military Value;
Area Partially
Closed.
29086
Federal Register / Vol. 77, No. 95 / Wednesday, May 16, 2012 / Proposed Rules
TABLE 1—DISTRIBUTION AND STATUS OF OCCURRENCES OF Malacothamnus clementinus (SAN CLEMENTE ISLAND BUSH
MALLOW), Acmispon dendroideus VAR. traskiae (SAN CLEMENTE ISLAND LOTUS), AND Castilleja grisea (SAN
CLEMENTE ISLAND PAINTBRUSH)—Continued
Location
description
Element
occurrence (EO) #
and point location
(PL) 1
Status 2 at listing;
year of first record
Current
status
(reference)
Larkspur Canyon (including Chamish
Canyon).
EO 14 & 48; 15 PLs
Extant; 1981 CNDDB
Extant (SERG 2006—
2011).
Box Canyon ................
EO 20 & 41; 22 PLs
Extant; 1979 CNDDB
Extant (SERG 2011)
Upper Norton Canyon
EO 21; 6 PLs ............
Extant; 1979 CNDDB
Extant (SERG 2011)
Middle Ranch Canyon
EO 24; 8 PLs ............
Extant; 1981 CNDDB
Extant (SERG 2008)
Waymuck Canyon ......
EO 22; 1 PL ..............
Unknown ...................
Extant (Junak 2004)
Plain northeast of
Warren Canyon.
No EO; 4 PLs ...........
Unknown ...................
Extant (Tierra Data
2007).
Seal Cove Terraces ...
EO 43; 2 PLs ............
Unknown ...................
Extant (CNDDB 1985,
SERG 2010).
Eel Cove Canyon (including terraces).
No EO; 3 PLs ...........
Unknown ...................
Extant (Junak 2004)
Terrace Canyon (south
to terraces around
Spray).
West Cove ..................
No EO; 6 PLs ...........
Unknown ...................
Presumed Extant
(SERG 2004).
No EO; 3 PLs ...........
Unknown ...................
Extant (Tierra Data
2006).
Current threats 3
A: Land Use, Erosion,
Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative; E: Climate.
A: Nonnative; E: Climate.
A: Nonnative; E: Climate.
A: Nonnative; E: Climate.
A: Land Use, Erosion,
Nonnative; E:
Movement, Climate.
A: Erosion, Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Nonnative, Fire; E:
Movement, Fire,
Climate.
A: Erosion, Nonnative; E: Movement, Climate.
A: Land Use, Erosion,
Nonnative; E:
Movement, Climate.
Military use 4
Low Military Value.
Low Military Value.
Low Military Value.
Low Military Value.
High Military Value.
Medium Military
Value.
High Military Value.
High Military Value.
High Military Value.
Medium Military
Value.
1 EO:
element occurrence, as defined and described according to the California Natural Diversity Database. PL: point locations of plants.
identified in the listing rule for these three taxa include: Factor A: habitat modification by feral animals; Factor C: grazing by animals;
Factor E: nonnative plants.
3 Current threats: Nonnative = Nonnative Plants; Movement = Movement of Vehicles and Troops; Climate = Climate Change; Genetic = Genetic Diversity.
4 Military value as defined in the Navy’s 2002 Integrated Natural Resources Management Plan (INRMP). Values defined according to the management emphasis, with high-value areas designated for maximum military use and low-value areas retaining the greatest flexibility for maintaining natural resource values.
2 Threats
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Species Distribution—Malacothamnus
clementinus
For many decades prior to its listing,
Malacothamnus clementinus was only
known from the type locality (the area
where the species is first identified and
described) at Lemon Tank Canyon, on
the eastern side of the middle of the
island (Kearney 1951, p. 128; USFWS
1984, p. 48). Dumping of scrap metal
actually protected this occurrence from
the ongoing threat of feral goat
herbivory by preventing the goats from
destroying the plants (USFWS 1984, p.
48). The historical range and
distribution of M. clementinus on San
Clemente Island is unknown because
surveys were not carried out before the
plant’s decline. In the Recovery Plan,
we noted that a public citizen
commented in the Listing Rule on the
discovery of two to three small plants
on the edge of an inaccessible ledge in
China Canyon (now described as two
occurrences—Lower China Canyon and
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Upper China Canyon; 42 FR at 40683;
USFWS 1984, p. 48). These two
occurrences, along with the occurrence
at Lemon Tank, were known at the time
of listing. Since listing, eight new
occurrences of M. clementinus have
been discovered among the generally
southwesterly facing coastal terraces
and their associated escarpments in the
southern and middle regions of San
Clemente Island (Junak and Wilken
1998, pp. 1–416, GIS data; Junak 2006,
pp. 1–176, GIS data; Tierra Data Inc.
2008, pp. 1–24, appendices and GIS
data; SERG 2009–2011, GIS data; Figure
1). Many of these new occurrences have
appeared since feral goats and pigs were
removed from the island in the early
1990s. This suggests the possibility that
the plants reemerged from underground
stems that survived grazing by feral
herbivores (Junak 2006a, pers. comm.).
Malacothamnus clementinus
occurrences are scattered below canyon
rims, at the base of terrace escarpments,
and in flat areas from approximately
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Middle Ranch Canyon in the north to
Horse Beach Canyon in the south. A
large, genetically diverse occurrence is
found within Horse Beach Canyon
(Helenurm 1999, pp. 39–40). Ten of the
11 known occurrences are located
throughout the southwestern region of
the island; in addition, the Lemon Tank
Canyon occurrence is located in the
northeastern region of the island (Figure
1). Six of the occurrences are within
SHOBA, and five are to the north
outside of SHOBA. The main southern
distribution of M. clementinus is
disconnected from the historical type
locality (the area where the species is
first identified and described) of the
species, which is the Lemon Tank
Canyon occurrence. Lemon Tank lies
about 3.6 mi (5.8 km) to the northeast
of the nearest occurrence (Waymuck
Canyon). The Lemon Tank Canyon
occurrence has not been resurveyed
since 1996, and its current status is
uncertain and presumed extant (CNDDB
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2011a, p. 2). Beyond the 11 known
occurrences, there is an additional
record of M. clementinus in the northern
plateau area of the island, near Ridge
Road, but this has not been confirmed
despite targeted searches for the plant
(SERG 2006, GIS data; Howe 2011a,
pers. comm.). We are not considering
this record as a known occurrence at
this time due to the possibility of error.
The known range of M. clementinus
has expanded to the south on San
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Clemente Island since its listing, with
the distance between the northernmost
and southernmost occurrence spanning
about 9.5 mi (15.3 km). Occurrences
within Impact Areas I and II in the
southwestern portion of the island
(within SHOBA) have not been
surveyed since 2006, largely due to area
closures implemented through the
recent MOFMP (Navy 2008a, pp. 2–38
to 2–44; Munson 2011a, pers. comm.).
Because of these closures, we were
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unable to evaluate the status of
occurrences in Horse Beach Canyon,
Lower China Canyon, and part of Upper
China Canyon for this review. While the
remaining eight occurrences fall outside
of these Impact Areas, one of the largest
and most genetically diverse of the 11
known occurrences, Horse Beach
Canyon, is within the restricted area.
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Aerial stems of Malacothamnus
clementinus can sprout from spreading
underground stems (rhizomes). This
makes it difficult to distinguish
individual plants among groups of
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stems. Consequently, the size of an
occurrence has been variously measured
by counting the number of stem
groupings or ‘‘clumps,’’ counting the
total number of stems within a clump,
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and measuring the approximate area
covered by plant groupings. These
inconsistent survey methods make it
difficult to document occurrence trends
beyond the appearance of new
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occurrences. There is no detailed
information about the abundance
(number or density of plants) of M.
clementinus at the time of its listing in
1977 (42 FR 40683). Occurrences
documented in 1996 to 1997 ranged in
size from 1 to 50 clumps (Junak and
Wilken 1998, p. 301). The Navy recently
estimated 1,516 individuals of M.
clementinus recorded since 2006
(Munson 2011d, pers. comm.). However,
given the challenge in distinguishing
individuals in a group of plants, and
variability in methods of estimating the
number of individuals, it is difficult to
accurately quantify the abundance of M.
clementinus on San Clemente Island
and, as such, numbers should be
interpreted cautiously.
Despite difficulties in determining
species abundance, extensive surveys
for Malacothamnus clementinus have
detected 8 new occurrences since
listing, for a total of 11 occurrences.
This suggests that the species is
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responding favorably to the elimination
of grazing pressure from feral herbivores
on San Clemente Island. It is unknown
to what extent this increase is
attributable to more intensive survey
efforts, detection of previously
undetected individuals, recruitment
from the seed bank, resprouting from
rhizomes, recolonization associated
with dispersal events, or management
efforts.
Species Distribution—Acmispon
dendroideus var. traskiae
Since the 1970s, the distribution of
Acmispon dendroideus var. traskiae has
been documented on north-facing slopes
over most of the eastern and western
sides of the island (USFWS 1984, p. 59;
Junak and Wilken 1998, p. 256; Navy
2002, p. D–9; Junak 2006, p. 125).
Twenty-nine occurrences of this taxon
have been identified, which span the
entire length of the island from Wilson
Cove to the southern tip east of Pyramid
Cove, a distance of approximately 19 mi
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(31 km) (Junak and Wilken 1998, p. 261;
Junak 2006, Map A–C) (Figure 2). The
majority of occurrences tend to be
clustered on north-facing slopes on the
eastern side of the island (Table 1). The
distribution of A. d. var. traskiae spans
the boundary of SHOBA at the southern
end of the island: 8 occurrences fall
within SHOBA and 21 are outside
(Junak and Wilken 1998, pp. 1–416, GIS
data; Junak 2006, pp. 1–176, GIS data;
Tierra Data Inc. 2008, pp. 1–24,
appendices and GIS data; SERG 2009–
2011, GIS data). Approximately 13 of 29
(45 percent) of the occurrences (Wilson
Cove, Canchalagua Canyon, Middle
Island Plateau, North Mosquito Cove,
Eagle Canyon, Larkspur Canyon,
Chamish Canyon, Lemon Tank Canyon,
Seal Cove Terraces, Eel Cove Canyon,
Middle Wallrock Canyon, Warren
Canyon, and North Island Terraces) are
partially or wholly within the
boundaries of a training area (IOA, TAR,
or SWAT).
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Acmispon dendroideus var. traskiae
tends to occur in small groups of 10 to
50 individuals (Allan 1999, p. 84).
There is no information about the
abundance of A. d. var. traskiae at the
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time of its listing in 1977. In the 1984
Recovery Plan (USFWS, p. 59), six
occurrences of A. d. var. traskiae were
recognized, all generally associated with
rocky areas. However, no other specific
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information regarding species location
or numbers of individuals at those six
sites was provided in the Recovery Plan,
except the statement that ‘‘the largest
number of plants grow in the vicinity of
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Wilson Cove’’ (USFWS 1984, p. 59).
Additionally, there are only a few
herbarium specimens of the taxon,
making historical distribution and
condition of the species difficult to
assess. For purposes of comparison to
the current status, we will use the
number of occurrences cited in the
recovery plan as the most conservative
estimate of species’ distribution around
the time of its listing (Table 1). Thus,
the historical range (based on herbarium
records, CNDDB records, and the
recovery plan) includes occurrences in
the northern part of the island (Wilson
Cove) down to the southern point
(Pyramid Head).
CNDDB currently lists 14 element
occurrences of Acmispon dendroideus
var. traskiae (as Lotus dendroideus
subsp. traskiae) (CNDDB 2011b) that are
presumed extant. These occurrences are
located on both the western and eastern
sides of the island and are distributed
across almost the entire length of the
island. Recently, survey efforts have
concentrated on discovering new plant
occurrences, rather than tracking the
status of historical occurrences (Junak
2006a, pers. comm.). New observations
were mainly concentrated on northfacing slopes in the middle of the
island, both on the eastern and western
sides. Analysis of these newer point
localities revealed proximity to
individuals detected during the 1996
and 1997 surveys. These element
occurrences and point localities
combined total 29 separate A. d. var.
traskiae occurrences (Table 1).
Abundance is difficult to determine
for this species because range-wide
surveys were not conducted each year.
Instead, monitoring took place over
multiple years with varying conditions.
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A recent estimate from the Navy
reported 3,525 individuals of Acmispon
dendroideus var. traskiae recorded since
2006 (Munson 2011d, pers. comm.).
Even though there is uncertainty in the
number of individuals, the number of
occurrences has increased from 6 to 29.
Thus, extensive survey findings suggest
that A. d. var. traskiae has increased
throughout most of its historical range,
and there are more occurrences now
than there were at the time of listing. It
is unknown to what extent this increase
is attributable to more intensive survey
efforts, detection of previously
undetected individuals, recruitment
from the seed bank, recolonization
associated with dispersal events, or
management efforts. The increase in
number of occurrences could indicate
an increase in the distribution of A. d.
var. traskiae on San Clemente Island.
Species Distribution—Castilleja grisea
Castilleja grisea was described as
relatively common on San Clemente
Island in the 1930s, and subsequently
declined as a result of unchecked
grazing by introduced feral herbivores
(Helenurm et al. 2005, p. 1222). The
historical range and distribution of C.
grisea on San Clemente Island is
unknown because botanical studies
were not completed before the plant’s
decline. Herbarium records documented
the species on the south and east sides
of the island before the time of listing
(California Consortium of Herbaria
2011, records for C. grisea). By 1963, C.
grisea was reported as rare or occasional
(Raven 1963, p. 337). Since the
complete removal of goats and pigs from
San Clemente Island in 1992, C. grisea
has been detected across much of the
island (Helenurm et al. 2005, pp. 1221,
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1226; Junak 2006, p. 47; USFWS 2007c,
p. 14). Plants have been recorded across
the southern two-thirds of the island,
and a single disjunct occurrence was
documented at the northern end in West
Cove (Junak and Wilken 1998, pp. 1–
416, GIS data; Junak 2006, pp. 1–176,
GIS data; Tierra Data Inc. 2008, pp. 1–
24, appendices and GIS data; SERG
2009–2011, GIS data) (Figure 3). The
distribution of any parasitic or
hemiparasitic plant is limited by the
distribution of its host or hosts.
However, host availability does not
appear to be limiting the abundance of
this species.
The linear distance between the
northernmost and southernmost
occurrences is 19.7 mi (32 km), with
plants primarily distributed across the
southern 15.5 mi (25 km) of the island.
Occurrences on the southern end of the
island on both the western and eastern
sides are reported in the CNDDB
(CNDDB 2011c). We combined CNDDB
element occurrences with adjacent point
localities from island surveys to identify
Castilleja grisea occurrences (Table 1).
The known distribution for C. grisea
documented since 1992 reflects a more
continuous and slightly expanded
distribution since the time of listing
(Tierra Data Inc. 2008, p. B–3). Survey
efforts have concentrated on discovering
new occurrences rather than tracking
the status of historical occurrences
(Junak, 2006a, pers. comm.). Using
available GIS and distribution data, we
have determined there are 29
occurrences of C. grisea currently on the
island; only 19 of these were known at
listing.
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(Table 1). The extant occurrences at
listing are derived from herbarium
records, CNDDB records, and
information in the Recovery Plan.
Distribution of C. grisea extends into
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SHOBA at the southern end of the
island; 15 occurrences fall within and
14 outside of SHOBA.
A number of surveys have found new
occurrences throughout the island
(Junak and Wilken 1998, GIS data; Junak
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2006, GIS data; Tierra Data Inc. 2008,
GIS data; SERG 2009–2011, GIS data;
CNDDB 2011c). Most new observations
were concentrated in steep canyons on
the western side of the island, although
a few were discovered near previously
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recorded individuals in the eastern
canyons. Recent counts, based on the
Navy’s data, estimate 11,733 individuals
of Castilleja grisea since 2006 (Munson
2011d, pers. comm.). Extensive survey
efforts since 1992 suggest C. grisea has
filled in its known historical range on
the island, and there are more
individuals now than at listing. Even
though there is uncertainty in the
number of individuals, the number of
occurrences of species has increased
from 19 to 29. It remains unknown how
much of this apparent increase in range
density can be attributed to more
intensive survey efforts, detection of
previously undetected individuals,
recruitment from the seed bank,
recolonization associated with dispersal
events, or management efforts. However,
the increase in the number of
occurrences suggests an expansion of
the species across the island.
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Habitat
General Habitat Conditions
Current habitat conditions for
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea on San Clemente Island are the
result of present and historical land use
practices. San Clemente Island has been
inhabited by humans for thousands of
years (Schoenherr et al. 1999, p. 317).
There is evidence that the Gabrielino
people used the island for harvesting
marine organisms before European
settlers arrived. The first lease for sheep
ranching was granted in 1848
(Schoenherr et al. 1999, p. 317). From
1850 until 1934, San Clemente Island
was used for sheep and cattle ranching,
goat grazing, and pig farming (Navy
2002, pp. 3–4). Some accounts even
report goats present on the island as
early as 1827 (Dunkle 1950, p. 261).
These nonnative herbivores greatly
changed the vegetative landscape of San
Clemente Island, and were cited in the
final listing rule (42 FR 40682; August
11, 1977) for M. clementinus, A. d. var.
traskiae, and C. grisea as the main cause
of these species’ decline. Sheep were
removed from the island in the 1930s,
but feral goats and pigs were not
completely eradicated until 1992. Since
the removal of goats and pigs, the
vegetation on San Clemente Island has
rebounded, and the condition of many
rare plants has improved (Junak 2006a,
pers. comm.). As a persistent historical
impact to the landscape, overgrazing
also led to the creation of bare trails,
denuded areas, and severe erosion.
Grazing animals also facilitated the
introduction and spread of nonnative
plants. Specifically, nonnative grasses
were spread through grazing and
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ranching on the island (Navy 2002,
p. 3–31).
Fire
Past and current fire regimes (pattern,
frequency, and intensity of fire in an
area) have influenced the distribution of
native and nonnative plants on San
Clemente Island (Navy 2002, p. 3–28).
Although the natural fire regime of the
island is unknown, there have only been
three documented lightning ignitions of
wildfires on the Channel Islands in 140
years (Carroll et al. 1993, p. 83). Natural
fire ignition was probably rare, as
lightning-caused fires tend to be less
frequent with proximity to the coastline,
due to higher fuel moisture levels and
a cooler climate (Keeley 1982, pp. 436–
437; Keeley 2002, p. 305). While the
island was used for ranching, fires were
set intermittently to increase the forb
and grass cover (Navy 2002, p. 3–29).
After purchase by the Navy in 1934, fire
ignited by military training activities
became a more common occurrence
throughout much of the island.
It was assumed in previous
descriptions that Malacothamnus
clementinus is adapted to, and tolerant
of, the periodic fires that probably
occurred in a prehistorical, lightningignition fire regime, although there is no
direct research to support this
assumption (USFWS 1984. p. 48; Navy
2002, D–20; USFWS 2007a, p. 3). Other
species in the same genus are fire
tolerant and able to adapt, such as
Malacothamnus fremontii (Fremont’s
bushmallow), a primary successional
species that can form the major shrub
cover after a fire (Rundel 1982, p. 86).
The seeds of M. fremontii are stimulated
by heat shock treatments, suggesting
that it is adapted to germinate after fires
(Keeley et al. 2005, p. 175). Another
related species, M. fasciculatus
(Mendocino bushmallow), germinates
after being stimulated by heat and is
known to flourish after fires (Swensen et
al. 1995, pp. 412–413; Beyers and
Wakeman 1997, p. 2). Malacothamnus
clementinus has underground stems,
and can resprout after disturbance to
reproduce vegetatively. The fire
tolerance of the genus and its ability to
resprout suggest that M. clementinus
may be adapted to fire. Although no
direct research has been done on the
effects of fire on M. clementinus, its
continued presence in areas that have
burned (such as SHOBA) indicates that
it is tolerant of at least occasional fire
(intervals of at least 5 years) (Navy
2008b, pp. 3.11–24, 3.11–81). However,
frequent fires could exceed its tolerance
of fire intensity and frequency.
The fire tolerance of Acmispon
dendroideus var. traskiae is unknown.
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Some studies have shown that the
related mainland species, Lotus
scoparius (deerweed), is fire tolerant
and becomes more abundant in years
after fire (Nilsen and Schlesinger 1981,
p. 217; Westman and O’Leary 1986, pp.
184–185). Other studies indicate that
intense or frequent burns (three times in
6 years) of L. scoparius lead to
establishment of fewer seedlings
(Westman and O’Leary 1986, p. 185;
Haidinger and Keeley 1993, p. 141). In
San Clemente Island species,
observations show that Acmispon
argophyllus var. adsurgens (San
Clemente Island bird’s-foot trefoil)
germination is slowed or depressed after
fire, but A. argophyllus var. argenteus
(silver bird’s-foot trefoil) flourishes in
burn areas (Allan 1999, pp. 90–91).
Observations of A. d. var. traskiae before
and several years following a fire in
Canchalagua Canyon found that adult
plants were usually killed by fire, but
were replaced with a similar number of
seedlings after the fire (Navy 2002, p. D–
10; Tierra Data Inc. 2005, p. 80). Based
on A. d. var. traskiae’s growth
characteristics and occurrence increases
in areas affected by fire, and the fire
adaptations of related species, A. d. var.
traskiae may be resilient to at least
occasional fire. Frequent fires could
exceed its tolerance of fire intensity and
frequency, and exhaust the seed bank in
repeatedly burned areas. Until studies
can be conducted specifically on A. d.
var. traskiae, it is prudent to avoid the
conclusion that the species benefits
from, or germinates with, fire.
The fire tolerance of Castilleja grisea
is unknown at this time. We do not
know of any studies conducted on the
fire tolerance of this species, and there
is very little information from related
species to infer fire tolerance for the
genus Castilleja. A related rare species,
C. levisecta (golden Indian paintbrush),
tolerates fire and performs better in
areas that have burned in the past
(Dunwiddie 2002, p. 1; Dunwiddie
2009, p. 5). Castilleja grisea has
survived and expanded its distribution
in areas that have burned. It is generally
assumed that the species has some
tolerance of infrequent fire (Navy 2002,
D–32) based on C. grisea occurrence
increases in areas affected by fire, and
the fire adaptations of other plants in
the genus. However, until speciesspecific research is conducted, we
cannot conclude with certainty that C.
grisea is adapted to fire. Additionally,
research is needed on the fire tolerance
of potential host plants and their
impacts on establishment of C. grisea.
Although the three species share the
same island habitat, they inhabit
different niches. The habitat
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Habitat—Malacothamnus clementinus
Malacothamnus clementinus occurs
in a variety of habitats on San Clemente
Island. Historically, it was observed on
rocky canyon walls and ridges,
presumably because foraging goats did
not graze those areas. More recently, M.
clementinus has been found at the base
of escarpments between coastal terraces
on the western side of the island within
maritime cactus scrub (Navy 2002, pp.
D–19, D–20). It can also occur on low
canyon benches and in rocky
grasslands. Malacothamnus clementinus
is found at approximately 30 to 900 ft
(10 to 275 m) elevation (CNPS 2001, p.
215). Moisture that collects in rock
crevices and at the base of canyon walls
and escarpments may provide favorable
conditions for this species (Junak 2006a,
pers. comm.). Based on its habitat range
on the island and the ease of cultivating
the plant, M. clementinus appears to
tolerate a broad range of soil types
(USFWS 1984, p. 50). It is often
associated with maritime cactus scrub
vegetation on coastal flats at the
southwestern end of the island (Junak
and Wilken 1998, p. 256). In the INRMP,
M. clementinus is listed as associated
with canyon woodlands (approximately
696 ac (282 ha)), maritime desert scrubprickly pear vegetation community
(approximately 8,921 ac (3,610 ha)), and
maritime sage scrub (approximately 369
ac (149 ha)) (Navy 2002, pp. 3–57, 3–63,
3–66). According to Junak and Wilken
(1998, p. 290), it is associated with
numerous plant species, including:
Artemisia californica (California sage
brush), Avena fatua (wild oat), Bromus
spp. (brome grass), Calystegia
macrostegia subsp. amplissima (island
morning glory), Encelia californica
(California brittlebush), Nassella cernua
(nodding needlegrass), Nassella lepida
(foothill stipa), Opuntia littoralis
(western prickly pear), Opuntia oricola
(chaparral prickly pear), Opuntia
prolifera (cholla), and Rhus intergrifolia
(lemonade sumac).
Habitat—Acmispon dendroideus var.
traskiae
Acmispon dendroideus var. traskiae
occurs on north-facing slopes, canyon
bottoms, or ridgelines (Junak 2006, p.
125). Plants grow somewhat colonially
around rock outcrops and boulders in
grassy areas, and along the interface
between grassland and maritime sage
scrub (Allan 1999, p. 84; Navy 2002, p.
D–9). Acmispon dendroideus var.
traskiae occurs between 25 and 1,400 ft
(7.6 to 463 m) in elevation on welldrained soils where adequate soil
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moisture is available to the plant (Junak
and Wilken 1998, p. 256; Navy 2002, p.
D–9). Some plants have been found in
close proximity to buildings, roads, and
pipelines, indicating that A. d. var.
traskiae is capable of colonizing
disturbed areas (Allan 1999, p. 84; Navy
2002, p. D–9). A. d. var. traskiae is
associated with two habitat types on the
island: Canyon woodland supported on
approximately 696 ac (282 ha) and
maritime desert scrub along the
northeastern escarpment supported on
approximately 6,228 ac (2,520 ha) (Navy
2002, pp. 3–57, 3–58). According to
Junak and Wilken (1998, p. 256), A. d.
var. traskiae is associated with
numerous plant species including, but
not limited to: Artemisia californica,
Avena fatua, Bromus spp., Calystegia
macrostegia subsp. amplissima,
Dichelostemma capitatum (wild
hyacinth), Gnaphalium bicolor
(bicolored everlasting), Hemizonia
clementina (island tarplant), Opuntia
spp. (prickly pear), Nassella pulchra
(purple stipa), and Quercus tomentella
(island live oak).
Habitat—Castilleja grisea
Castilleja grisea is often associated
with coastal sage scrub found on
approximately 369 ac (149 ha) of the
island and maritime desert scrub plant
communities found on approximately
5,858 ac (2,371 ha), with scattered
concentrations of plants in canyon
woodland (approximately 696 ac (282
ha)) and grassland habitat
(approximately 8,921 ac (3,610 ha))
(Navy 2002, pp. 3–58, 3–63, 3–66).
Plants are located in steep, rocky
canyons on both the eastern escarpment
and western side of the island, although
some have been observed on coastal
bluffs, slopes, and terraces around the
island’s perimeter. Some of the largest
concentrations of plants are located in
bowl-shaped swales on coastal terraces
(Junak and Wilken 1998, p. 82).
Castilleja grisea grows between 32 and
2,000 ft (10 and 365 m) in elevation.
This hemiparasitic plant is known to
parasitize many different plants,
although a definitive understanding of
host-plant associations is currently
unknown. Potential host plants include
Calystegia macrostegia subsp.
amplissima (island morning glory),
Opuntia littoralis (prickly pear), and
Constancia nevinii (Nevin’s
eriophyllum). These may be important
habitat components for C. grisea. Junak
and Wilken (1998, p. 82) suggest that
habitat conditions must be of sufficient
quality to sustain potential host plants
and provide opportunities for C. grisea
establishment. Numerous plant species
are associated with C. grisea including,
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but not limited to: Artemisia californica,
Calystegia macrostegia subsp.
amplissima, Encelia californica,
Constancia nevinii (Nevin’s woolly
sunflower), Hemizonia clementina,
Isocoma menziesii (Menzies’
goldenbush), Lycium californicum
(California boxthorn), and Opuntia spp.
(Junak and Wilken 1998, p. 82).
Biology and Genetics
Biology—Malacothamnus clementinus
Malacothamnus clementinus is an
herbaceous clonal plant (descended
asexually from a single individual) that
may spread locally by underground
rhizomes that produce aerial stems. On
average there are 90 flowers per
inflorescence (a flower cluster) (Junak
and Wilken 1998, p. 291). The species
flowers in the spring, typically from
March to August (Kearney 1951, p. 115;
Navy 2002, D–19; California Native
Plant Society 2011). Junak and Wilken
(1998, p. 291) found that M. clementinus
is self-compatible (capable of selffertilization), but not self-pollinating.
The plant produced seed when hand
pollinated with pollen from the same
plant, but not when flowers were bagged
to prevent pollinator visitations (Junak
and Wilken 1998, p. 291). It is generally
thought that M. clementinus is
pollinated by insects, although no
specific pollinator for this species is
known. Other species in the family
Malvaceae are pollinated by specialist
bees in the genus Diadasia (Sipes and
Tepedino 2005, p. 487). Given the
evidence that suggests pollinators may
be necessary for successful seed
production, a decline in M. clementinus
may in part be due to a decline in
pollinators or an absence of pollinator
visitations (Junak and Wilken 1998, p.
291).
Each fertilized flower produces three
to four seeds on average (Junak and
Wilken 1998, p. 291). Seed production
in natural occurrences of
Malacothamnus clementinus is very low
(Helenurm 1997, p. 51; Helenurm 1999,
p. 39; Junak 2006a, pers. comm.), as is
germination, with low germination rates
of only 4 to 35 percent (Evans and Bohn
1987, p. 538; Junak and Wilken 1998, p.
291). Junak and Wilken (1998, p. 291)
hypothesized that the relatively low
number of seeds produced in situ could
be due to low pollinator visitation rates
or some other unknown factor. Seed
germination may be stimulated by heat
associated with fire in other Malvaceae
species, although this has not been
studied in M. clementinus (Keeley et al.
2005, p. 175). Junak and Wilken (1998,
p. 291) tried scarifying seeds (softening
the outer coat of a seed through
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mechanical or chemical means) to
promote germination, but this did not
significantly increase germination rates.
Based on these limited studies of seed
production and germination in M.
clementinus, it is difficult to determine
the cause of its low reproductive output.
In addition to sexual reproduction,
Malacothamnus clementinus can
reproduce vegetatively, or clonally, by
sprouting from rhizomes (Evans and
Bohn 1987, p. 538). Because M.
clementinus typically occurs in clusters
of stems, it is difficult to differentiate
between individuals, as rhizome sprouts
can also look like seedlings. Therefore,
it can be a challenge to determine in the
field if a small plant is a seedling or a
sprout without digging up the root
system (Junak 2006b, pers. comm.). The
life history of M. clementinus suggests
that many of the newly detected
occurrences have sprouted from
underground rhizomes (Junak 2006a,
pers. comm.).
Genetics—Malacothamnus clementinus
Genetic studies have provided
insights into the clonal nature of
Malacothamnus clementinus. Overall,
genetic diversity found in the M.
clementinus occurrences is very low
compared with other island endemic
plant taxa (Helenurm 1999, p. 40).
However, individuals in a patch do not
represent the same genetic individual,
and there is genetic diversity within
patches of M. clementinus (Helenurm
1999, p. 39). A substantial proportion of
the genetic diversity in M. clementinus
is found among different occurrences
rather than within a single occurrence.
This research indicates that each
occurrence may contain unique genetic
variation not found elsewhere, and that
there is not much cross pollination or
gene flow between occurrences or even
patches in the same area (Helenurm
1999, pp. 39–40); this underscores the
high conservation value of each of the
different occurrences to the long-term
survival and recovery of the species.
Malacothamnus clementinus may
have low genetic fitness due to small
occurrence numbers, low seed
production, and low genetic diversity.
Helenurm (1999, p. 40) found that most
of the species’ genetic variation is
within the Box Canyon and Horse Beach
Canyon occurrences, although other
occurrences may contain unique genetic
material not found elsewhere (Helenurm
1999, p. 40). Occurrences of M.
clementinus could be vulnerable to
inbreeding depression (loss of vigor and
general health) and reduced seed
production due to apparently limited
outcrossing (reproduction between
individuals of different strains) of the
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plant (Helenurm 1997, p. 50; Helenurm
1999, p. 40).
Biology—Acmispon dendroideus var.
traskiae
Acmispon dendroideus var. traskiae
flowers between February and August,
with halictid bees (a family of small
solitary bees that typically nest in the
ground), bumblebees, and small beetles
observed foraging on the flowers (Junak
and Wilken 1998, p. 257; Allan 1999,
pp. 64, 85). The taxon is self-compatible
(Allan 1999, pp. 85–86), but plants may
also rely on insects for more effective
pollination (Arroyo 1981, pp. 728–729).
Fertilized ovaries develop into a
slender, beak-like fruit 1 to 2 in (2.5 to
5 cm) long containing up to six seeds
(Isely 1993, p. 619; Junak and Wilken
1998, p. 257; Allan 1999, p. 82). The
fruits do not split open to release their
seeds at maturity (Isely 1993, p. 619), so
it is likely that they disperse close to the
parent plants, which may limit the
ability of A. d. var. traskiae to colonize
unoccupied suitable habitat. Junak and
Wilken (1998, p. 257) found that, on
average, a single A. d. var. traskiae
individual can produce approximately
36 to 64 flowering shoots, 118 to 144
flowers per shoot, and 4 to 6 seeds per
fruit. This suggests that, under ideal
conditions, an individual A. d. var.
traskiae can produce a high volume of
seeds (16,000 or more). Like most
legumes, A. d. var. traskiae seeds
require scarification or gradual seed coat
degradation to germinate (Wall 2011,
pers. comm.).
Genetics—Acmispon dendroideus var.
traskiae
Allan (1999, pp. 1–105) analyzed 10
California mainland and Channel Island
taxa of Lotus (all of which are now in
the genus Acmispon and referred to as
such here), including Acmispon
dendroideus var. traskiae. Of the 29
occurrences of A. d. var. traskiae on San
Clemente Island, Allan (1999, pp. 50–
53) sampled only the Wilson Cove
occurrence. The Acmispon island
populations, including A. d. var.
traskiae, tended to have lower genetic
variability than mainland populations
(Allan 1999, p. 63). There are several
possible explanations for this lower
genetic variation, including small
occurrence size, genetic bottlenecks
associated with the establishment of
new island occurrences, stochastic
events (a random incident such as local
extinctions), and genetic isolation
(Allan 1999, p. 63). Allan’s (1999, p. 61)
analysis of genetic diversity also found
that the majority (67 percent) of A. d.
var. traskiae’s variability is found
among, rather than within, occurrences.
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He postulated that the low genetic
variability within a given occurrence
may be due to endemism (native to or
confined to a certain region), partial
inbreeding, isolation, and stochastic
events in small occurrences (Allan 1999,
pp. 63–64).
Acmispon dendroideus var. traskiae
has been known to hybridize with A.
argophyllus var. argenteus in disturbed
areas in Wilson Cove (Liston et al. 1990,
pp. 239–240; Allan 1999, p. 86). Based
on intermediate characteristics, the
hybrid plants appear to be first
generation plants (F1 generation) from a
cross between the two varieties. It is not
known whether these plants are capable
of producing viable seeds by
backcrossing between the hybrids or
with the putative parent plants (Allan
1999, p. 86). Plants of intermediate
morphology were first observed by R.M.
Beauchamp in 1986 (Liston et al. 1990,
p. 239). In April 1989, Liston et al.
(1990, pp. 239–240) noted a small
number of suspected hybrids in the
same area as the largest known
occurrence of A. d. var. traskiae in
Wilson Cove. A smaller group of
nonhybrid A. argophyllus var. argenteus
was found approximately 80 ft (24.4 m)
upwind; the two taxa were separated by
a road. No documented evidence of
hybridization has been recorded
anywhere else on the island (Allan
1999, p. 86), although there are
unconfirmed reports in other areas (e.g.,
Warren Canyon; A. Braswell 2011, pers.
obs.).
Biology—Castilleja grisea
All taxa of Castilleja are considered
hemiparasitic. Plants are capable of
photosynthesis and can exist without a
host, but are able to derive water,
nutrients, or photosynthates from a host
plant if present (Heckard 1962, p. 25).
Castilleja roots have haustorial
attachments (specialized absorbing
structures) that penetrate the host
plant’s root tissue, forming an organic
bridge with the host (Heckard 1962, p.
27). In field settings, species of
Castilleja tend to establish haustorial
connections with one or more hosts
(Heckard 1962, p. 27; Atsatt and Strong
1970, p. 280). In greenhouse studies,
seedlings of C. grisea grown in the
absence of host plants did not perform
well and died shortly after germination,
suggesting that host plants are important
for this species (Junak and Wilken 1998,
p. 84). Greenhouse studies have also
shown that overall performance and
fecundity of parasitic plants are usually
higher with a host than without one
(Heckard 1962, p. 29; Atsatt and Strong
1970, p. 280).
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Castilleja grisea appears to be capable
of forming haustorial connections with
a range of plant species (Heckard 1962,
p. 28; Atsatt and Strong 1970, p. 280;
Marvier 1996, p. 1399; Adler 2002, p.
2704; Adler 2003, p. 2086). Nassella
pulchra, Calystegia macrostegia subsp.
amplissima, and Constancia nevinii are
considered potential hosts (Muller 2009,
pers. comm.). Twelve co-occurring plant
taxa have been found consistently in C.
grisea occurrences (Muller and Junak
2011, p. 5). However, further study is
needed to determine which of these
plants serve as hosts to C. grisea, and at
what frequency. Castilleja grisea may
rely on more than one host species for
growth and reproduction. Therefore,
recovery may depend on the
conservation of a community of host
species (Marvier and Smith 1997, p.
846).
Castilleja grisea flowers between
February and May, producing yellow
bisexual flowers (Chuang and Heckard
1993, pp. 1016–1024; Navy 2002, p. D–
31). Castilleja grisea is likely selfincompatible (unable to produce viable
seed through self-fertilization), as
observed in other species of the genus
(Carpenter 1983, p. 218; Junak and
Wilken 1998, p. 84). Among four
populations of C. grisea examined,
Junak and Wilken (1998, pp. 83–84)
found limited flower-to-fruit conversion
(67 to 71 percent of flowers produced
fruits) and large variation in the number
of seeds set per fruit. Castilleja grisea
appears to produce seed primarily
through outcrossing, and relies on
pollinators for sexual reproduction
(Junak and Wilken 1998, p. 84;
Helenurm et al. 2005, p. 1225).
Castilleja grisea is most closely
related to, and shares floral traits with,
other species in the genus primarily
adapted for bee pollination (Chuang and
Heckard 1991, p. 658). A single bee from
the family Andrenidae, covered in
pollen, was recently collected from a
flowering C. grisea plant in Canchalagua
Canyon on San Clemente Island (Howe
2009a, pers. comm.). The fruit of C.
grisea is an ovoid capsule, less than 0.5
in (1.27 cm) long, and contains
approximately 150 seeds (Junak and
Wilken 1998, pp. 82–83). The seed coats
are deeply netted, which indicates they
can float and may be able to disperse via
water (Muller and Junak 2011, pp. 12,
16). During attempts to propagate C.
grisea plants from seed, no significant
differences were found between seed
viability (79.5 to 85 percent) and
germination (68.3 to 76.7 percent),
suggesting that most viable seed are able
to germinate immediately without a
period of dormancy to induce
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germination (Junak and Wilken 1998,
pp. 83–84).
Genetics—Castilleja grisea
Genetic variation within Castilleja
grisea is moderately high for an insular
endemic plant, particularly given its
history of extreme rarity (Helenurm et
al. 2005, p. 1225). This suggests C.
grisea may have retained substantial
genetic variation through the period of
overgrazing. Consistent with an
outcrossing breeding system, most of the
genetic variation in C. grisea is within,
rather than among, occurrences
(Helenurm et al. 2005, p. 1225).
Historically, there were likely high rates
of gene flow between occurrences. The
transmittal of genes between
occurrences in the past influenced the
genetic similarity found between
occurrences by Helenurm et al. (2005, p.
1226). While all occurrences are
important for maintaining levels of gene
flow, the loss of any single occurrence
is unlikely to represent a significant loss
of genetic diversity to the species
(Helenurm et al. 2005, p. 1226). Overall,
this species likely does not have low
fitness due to limiting genetic factors
(Helenurm et al. 2005, p. 1226).
Recovery
Section 4(f) of the Act directs us to
develop and implement recovery plans
for the conservation and survival of
endangered and threatened species
unless we determine that such a plan
will not promote the conservation of the
species. The Act directs that, to the
maximum extent practicable, we
incorporate into each plan:
(1) Site-specific management actions
that may be necessary to achieve the
plan’s goals for conservation and
survival of the species;
(2) Objective, measurable criteria,
which when met would result in a
determination, in accordance with the
provisions of section 4 of the Act, that
the species be removed from the list;
and
(3) Estimates of the time required and
cost to carry out the plan.
However, revisions to the list (adding,
removing, or reclassifying a species)
must reflect determinations made in
accordance with sections 4(a)(1) and
4(b) of the Act. Section 4(a)(1) requires
that the Secretary determine whether a
species is endangered or threatened (or
not) because of one or more of five
threat factors. Therefore, recovery
criteria must indicate when a species is
no longer endangered or threatened by
any of the five factors. In other words,
objective, measurable criteria, or
recovery criteria contained in recovery
plans, must indicate when we would
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anticipate an analysis of the five threat
factors under section 4(a)(1) would
result in a determination that a species
is no longer endangered or threatened.
Section 4(b) of the Act requires that the
determination be made ‘‘solely on the
basis of the best scientific and
commercial data available.’’
Thus, while recovery plans are
intended to provide guidance to the
Service, States, and other partners on
methods of minimizing threats to listed
species and on criteria that may be used
to determine when recovery is achieved,
they are not regulatory documents and
cannot substitute for the determinations
and promulgation of regulations
required under section 4(a)(1) of the
Act. Determinations to remove a species
from the list made under section 4(a)(1)
of the Act must be based on the best
scientific and commercial data available
at the time of the determination,
regardless of whether that information
differs from the recovery plan.
In the course of implementing
conservation actions for a species, new
information is often gained that requires
recovery efforts to be modified
accordingly. There are many paths to
accomplishing recovery of a species,
and recovery may be achieved without
all criteria being fully met. For example,
one or more recovery criteria may have
been exceeded while other criteria may
not have been accomplished, yet the
Service may judge that, overall, the
threats have been minimized
sufficiently, and the species is robust
enough, that the Service may reclassify
the species from endangered to
threatened or perhaps delist the species.
In other cases, recovery opportunities
may have been recognized that were not
known at the time the recovery plan was
finalized. These opportunities may be
used instead of methods identified in
the recovery plan.
Likewise, information on the species
may be learned that was not known at
the time the recovery plan was
finalized. The new information may
change the extent that criteria need to be
met for recognizing recovery of the
species. Overall, recovery of species is
a dynamic process requiring adaptive
management, planning, implementing,
and evaluating the degree of recovery of
a species that may, or may not, fully
follow the guidance provided in a
recovery plan.
Thus, while the recovery plan
provides important guidance on the
direction and strategy for recovery, and
indicates when a rulemaking process
may be initiated, the determination to
remove a species from the Federal List
of Endangered and Threatened Plants
(50 CFR 17.12) is ultimately based on an
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analysis of whether a species is no
longer endangered or threatened. The
following discussion provides a brief
review of recovery planning for
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea, as well as an analysis of the
recovery criteria and goals as they relate
to evaluating the status of the taxa.
In 1984, the Service published the
Recovery Plan for the Endangered and
Threatened Species of the California
Channel Islands (Recovery Plan) that
addresses 10 plants (including
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea) and animals distributed among
three of the Channel Islands (USFWS
1984). Recovery plans are intended to
guide actions to recover listed species
and to provide measurable objectives
against which to measure progress
towards recovery. Following guidance
in effect at that time, the Recovery Plan
was not focused on criteria that
specifically addressed the point at
which threats identified for each species
in the listing rule would be removed or
sufficiently ameliorated. Given the
threats in common to the 10 species
addressed, the Recovery Plan is broad in
scope and focuses on restoration of
habitats and ecosystem function. Instead
of specific criteria, it included six
general objectives covering all 10 of the
plant and animal species:
Objective 1: Identify present adverse
impacts to biological resources and
strive to eliminate them.
Objective 2: Protect known resources
from further degradation by: (a)
Removal of feral herbivores, carnivores,
and selected exotic plant species; (b)
control of erosion in sensitive locations;
and (c) direct military operations and
adverse recreational uses away from
biologically sensitive areas.
Objective 3: Restore habitats by
revegetation of disturbed areas using
native species.
Objective 4: Identify areas of San
Clemente Island where habitat
restoration and population increase of
certain addressed taxa may be achieved
through a careful survey of the island
and research on habitat requirements of
each taxon.
Objective 5: Delist or upgrade the
listing status of those taxa that achieve
vigorous, self-sustaining population
levels as the result of habitat
stabilization, restoration, and preventing
or minimizing adverse human-related
impacts.
Objective 6: Monitor effectiveness of
recovery effort by undertaking baseline
quantitative studies and subsequent
follow-up work (USFWS 1984, pp. 106–
107).
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Progress has been made toward
achieving these objectives. Our review
of the Recovery Plan focuses on the
actions identified that promote the
recovery of Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. The
Recovery Plan adopts a generalized
strategy of eliminating or controlling
selected nonnative species and restoring
habitat conditions on the Channel
Islands to support viable, self-sustaining
occurrences of each of the addressed
taxa. The Recovery Plan states that
‘‘[o]nce the threats to these taxa have
been removed or minimized and the
habitats are restored, adequately
protected, and properly managed,
reclassification for some taxa may be
considered’’ (USFWS 1984, p. 108).
Actions specified in the Recovery Plan
that are pertinent to recovery of the
endangered San Clemente Island plant
taxa include:
(1) Removing feral animals;
(2) Removing or controlling selected
nonnative plants;
(3) Controlling erosion;
(4) Revegetating eroded and disturbed
areas;
(5) Reintroducing and reestablishing
listed plant species populations;
(6) Modifying existing management
plans to minimize habitat disturbance
and incorporate recovery actions into
natural resource management plans;
(7) Protecting habitat by minimizing
habitat loss and disturbance and by
preventing the introduction of
additional nonnative organisms;
(8) Determining the habitat and other
ecological requirements of the listed
plant taxa (such as reproductive biology
and fire tolerance);
(9) Evaluating the success of
management actions;
(10) Increasing public support for
recovery efforts; and,
(11) Using existing laws and
regulations to protect each taxon.
Recovery Plan Implementation
The primary objective of the Recovery
Plan is to restore endangered and
threatened species to nonlisted status.
Though specific size and number of
occurrences needed for self-sustaining
populations for each species was not
identified, habitat restoration and
protection that would result in
achieving self-sustaining populations
(see Objective 5) were discussed. The
Recovery Plan stated that
reclassification of these taxa may be
considered after threats have been
removed or sufficiently minimized and
the habitat is restored. Specific criteria
for determining when threats have been
removed or sufficiently minimized were
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not identified in the Recovery Plan, but
six objectives were described in general
to achieve recovery of the Channel
Island species. This section provides a
summary of actions and activities that
have been implemented according to the
1984 Recovery Plan (USFWS 1984, pp.
106–107) and contribute to achievement
of these objectives.
Objective 1: Identify Present Adverse
Impacts to Biological Resources and
Strive To Eliminate Them
The Navy has taken steps to eliminate
incidental impacts to the three species
by educating Navy personnel stationed
on San Clemente Island. To increase
support for recovery efforts, the Navy
has created the position of Island
Operations Manager. This individual’s
role is to act as a liaison between the
Navy’s natural resource branch and
other island users (Larson 2009, pers.
comm.). The Island Operations Manager
educates users of the island to the
uniqueness and fragility of the island’s
ecosystem, and briefs new operational
groups as they come onto the island
(Larson 2009, pers. comm.). These
briefings inform operational groups of
the Navy’s natural resource management
responsibilities under the law, and may
include additional information about
threats to, and locations of, listed taxa.
The Recovery Plan recommends that
existing laws and regulations be used to
protect Malacothamnus clementinus,
Acmispon dendroideus var. traskiae,
and Castilleja grisea from threats on San
Clemente Island. Based on the
occurrence of these taxa on federally
owned land, the primary laws with
potential to protect them include the
National Environmental Policy Act
(NEPA) and the Act. NEPA requires
Federal action agencies to integrate
environmental values into their decision
making processes by considering the
environmental impacts of their
proposed actions and reasonable
alternatives to those actions. The Navy
has implemented NEPA since its
enactment in 1970. Likewise, the Navy
has a history of consultation and
coordination with the Service under the
Act regarding the effects of various San
Clemente Island activities on federally
listed species since taxa on the island
were first listed in 1977. Finally,
pursuant to the Sikes Act Improvement
Act, the Navy adopted an INRMP for
San Clemente Island in 2002 that helps
guide the management and protection of
these taxa (Navy 2002, pp. 1.1–8.12). An
INRMP is a plan that is intended ‘‘* * *
to guide installation commanders in
managing their natural resources in a
manner that is consistent with the
sustainability of those resources while
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ensuring continued support of the
military mission’’ (Navy 2002, p. 1–1).
To achieve this, the INRMP identifies
goals and objectives for specified
management units and their natural
resources. The following objectives have
been incorporated as part of the INRMP
to address the Recovery Plan task of
incorporating recovery actions into
existing management plans:
(1) Protect, monitor, and restore
plants and cryptograms (soil crusts
composed of living cyanobacteria, algae,
fungi, or moss) in order to manage for
their long-term sustainability on the
island;
(2) Consider Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, or Castilleja grisea as
‘‘Management Focus Plants,’’ such that
they are considered independently from
their plant communities as special
management focuses (habitat protection
alone is not assumed to be sufficient for
their protection);
(3) Conduct status surveys for listed
plants;
(4) Ensure that Management Focus
Plants have a network of suitable sites;
(5) Perform studies to determine the
pollinators of Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, or Castilleja grisea; and
(6) Continue to apply genetic research
and management approaches to rare
plant management.
Through these mechanisms, the Navy
is required to identify and address all
threats to these species during the
INRMP planning process. If possible,
threats are ameliorated, eliminated, or
mitigated through this procedure. The
Navy has strived to fulfill this objective
through both internal planning (INRMP)
and through compliance with Federal
law (consultations with the Service
under the Act and preparing
environmental review documents under
NEPA). As discussed below under the
five factors, the actions taken by the
Navy under the INRMP have not
completely eliminated all adverse
impacts, but many threats have been
greatly reduced. These contributions to
the elimination of adverse impacts
partially fulfill, but do not fully achieve,
the objective for all three species.
Objective 2: Protect Known Resources
From Further Degradation By: (a)
Removal of Feral Herbivores,
Carnivores, and Selected Exotic Plant
Species; (b) Control of Unnatural
Erosion in Sensitive Locations; and (c)
Directing Military Operations and
Adverse Recreational Uses Away From
Biologically Sensitive Areas
In 1992, the Navy fulfilled a major
part of this objective by removing the
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last of the feral goats and pigs from San
Clemente Island (as described above in
the Habitat section). Nonnative plants
have also been targeted for removal from
San Clemente Island, and efforts to
control nonnatives have been
implemented on an annual basis since
approximately 1993 (O’Connor 2009a,
pers. comm.). The specific nonnative
plants targeted and amount of money
allocated to this program are adjusted
on an annual basis (O’Connor 2009b,
pers. comm.; Munson 2011a, pers.
comm.). The effectiveness of this
program was recently improved by
providing authorization to apply
herbicides (O’Connor 2009b, pers.
comm.). Priorities in the nonnative
plant program are currently focused on
new nonnatives to the island and
particularly destructive nonnative
species.
The Navy is also taking steps to
minimize the effects of erosion on the
island. Erosion control measures are
being incorporated into project designs
to minimize the potential to exacerbate
existing erosion (O’Connor 2009c, pers.
comm.). With the expansion of military
operational areas, the Navy committed
to prepare and implement an erosion
control plan that will minimize soil
erosion within and adjoining the
operational areas (Navy 2008b, pp. 5–
30; USFWS 2008 p. 62). However, this
plan has not been finalized nor yet
implemented, and it is unclear whether
erosion control measures will be
implemented consistently or at all in
areas that are operationally closed to
monitoring and access due to
unexploded ordnance. The proposed
erosion control plan includes
development and application of best
management practices (BMPs) such as:
Establishing setbacks and buffers from
steep slopes, drainages, and sensitive
resources; constructing site-specific
erosion control structures; conducting
revegetation and routine maintenance;
and monitoring and adjusting the BMPs
as appropriate. While the erosion
control plan is being prepared, the Navy
has postponed all major battalion
movements and training, and is using
BMPs when creating and approving
projects that might contribute to erosion
on the island. The Navy has taken steps
to reduce the threat of erosion on the
island and contribute to the
achievement of this objective.
The Navy is taking precautions to
avoid plants when possible to minimize
direct impacts to Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea
resulting from military activities. For
example, in the MOFMP, the Navy
proposed to develop a Training Area
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Range (TAR) that contained A. d. var.
traskiae within its boundaries. After
consultation with USFWS, the Navy
revised these boundaries to avoid most
of the A. d. var. traskiae and minimize
the impact of training on the species
(USFWS 2008, p. 118).
This objective has been largely met for
Acmispon dendroideus var. traskiae and
Castilleja grisea. Feral herbivores have
been removed, erosion control measures
are being implemented, and military
activities are avoiding direct impacts to
plants whenever possible. The Navy is
also developing an erosion control plan
for military activities. However, many
occurrences of Malacothamnus
clementinus are located in areas that
continue to be impacted, or their status
remains unknown due to closures.
Therefore, Objective 2 has not been
sufficiently satisfied for this taxon.
Objective 3: Restore Habitats by
Revegetation of Disturbed Areas Using
Native Species
Since 2001, the Navy has contracted
with the San Diego State University Soil
Ecology and Restoration Group (SERG)
to propagate and outplant (transplant
individuals from the greenhouse to
vegetative communities) native species
on the island (Howe 2009b, pers.
comm.). The SERG propagates and
outplants approximately 4,000 native
plants per year, and has initiated
restoration at approximately 28 sites
(O’Connor 2009b, pers. comm.). This
program has not included propagation
and outplanting of listed plant taxa,
except in one recent instance to replace
Acmispon dendroideus var. traskiae
plants that were extirpated during a
scrap metal removal project (Munson
2011a, pers. comm.). The outplanting of
native species is primarily focused on
restoring sensitive island habitats and
improving habitat conditions for
endangered animal taxa (such as the San
Clemente loggerhead shrike (Lanius
ludovicianus mearnsi)), with some
revegetation of eroded and disturbed
areas (O’Connor 2009, pers. comm.).
Although only one of the restoration
efforts was specifically designed for the
benefit of one of the three plant taxa
addressed in this finding, restoration of
the island’s vegetation communities
should help improve habitat suitability
for all three taxa by reducing the spread
of invasive nonnative plants and
restoring ecological processes. Although
progress has been made towards
restoring disturbed areas, there are still
areas (e.g., especially within SHOBA)
that need further restoration of native
species. Therefore, while restoration is
occurring, the objective has not been
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Objective 4: Identify Areas of San
Clemente Island Where Habitat
Restoration and Population Increase of
Certain Addressed Taxa May be
Achieved Through a Careful Survey of
the Island and Research on Habitat
Requirements of Each Taxon
Since they were listed, a number of
studies have addressed the ecology,
taxonomy, and genetics of the three
plant taxa. Evans and Bohn (1987, pp.
537–545) observed insects on plants,
collected seeds, and studied the
germination of Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. Junak
and Wilken (1998, pp. 1–426) studied
flowering and fruiting in natural
populations and performed germination
trials with collected seeds from all three
taxa. Allan (1999, pp. 46–105) observed
pollinators and germinated seeds
collected from A. d. var. traskiae. Liston
et al. (1990) confirmed suspected
hybridization between A. d. var.
traskiae and A. argophyllus var.
argenteus using genetic techniques.
Additionally, Allan (1999, pp. 46–105)
surveyed the genetics of a number of
taxa within the genus Lotus, including
a group that includes A. d. var. traskiae,
to compare genetic divergence between
California mainland and island taxa.
Helenurm et al. (2005, pp. 1221–1227)
studied patterns of genetic variation
among occurrences of C. grisea.
Helenurm (1997, pp. 41–51; 1999, pp.
29–40) studied the genetic variation and
clonal nature of M. clementinus. These
studies have helped to elucidate
potential plant pollinators and mating
systems, plant propagation techniques,
and to design management strategies
that take into consideration genetic
factors. There is a growing body of
knowledge on the habitat requirements
and life history of listed species on the
island. This research, encouraged and
supported by the Navy, has contributed
to achieving Objective 4 and to planning
successful restoration of habitat and
recovery of the three taxa. Additional
surveys and research necessary to
identify appropriate restoration,
management, and recovery actions
include: further genetic studies for M.
clementinus, research on the degree of
hybridization in A. d. var. traskiae and
study of the host plants of C. grisea.
Thus, this objective has not been fully
achieved at this time for the three
species.
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Objective 5: Delist or Upgrade the
Listing Status of Those Taxa That
Achieve Vigorous, Self-Sustaining
Population Levels as the Result of
Habitat Stabilization, Restoration, and
Preventing or Minimizing Adverse
Human-Related Impacts
The distributions of Acmispon
dendroideus var. traskiae and Castilleja
grisea have increased substantially over
much of the island since listing. There
are now vigorous, self-sustaining
occurrences of A. d. var. traskiae and C.
grisea on San Clemente Island, as
described above. Threats to these taxa
have also been reduced to levels such
that they are no longer in danger of
extinction throughout all of their range
(USFWS 2007b, pp. 1–22; USFWS
2007c, pp. 1–19). Although the goal of
delisting has not yet been met, the
objective to improve the status of A. d.
var. traskiae and C. grisea to the point
they can be reclassified has been met.
Because many occurrences of
Malacothamnus clementinus are located
in areas that continue to be impacted, or
their status remains unknown due to
closures, we have not yet met either
standard of this objective to reclassify or
delist this species.
Objective 6: Monitor Effectiveness of
Recovery Efforts by Undertaking
Baseline Quantitative Studies and
Subsequent Follow Up Work
To evaluate the success of
management actions undertaken to
benefit the three plant taxa, the Navy
implemented a long-term vegetation
monitoring study (Tierra Data Inc. 2005,
pp. i–96 and Appendices) and
commissioned sensitive plant surveys
(Junak and Wilken 1998, pp. 1–416;
Junak 2006, pp. 1–176). Overall,
vegetation trend monitoring reveals that
the cover of both native and nonnative
plant species has changed since the
removal of feral goats and pigs, but the
response of individual species and
vegetative communities has varied, with
some species and communities
exhibiting greater changes than others.
Discerning long-term vegetative
community trends is difficult because
the vegetative community study was
preceded by a wet year that likely had
a strong influence on the data collected
(Tierra Data Inc. 2005, p. 29). Within the
few monitoring plots that included the
three plant taxa, occurrence counts
varied among years and did not provide
a clear indication of trend (Tierra Data
Inc. 2005, pp. 79–80). The clearest
indication of the success of feral animal
removals for the three plant taxa was
obtained from rare plant survey data
(Junak and Wilken 1998, pp. 1–416, GIS
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data; Junak 2006, pp. 1–176, GIS data;
Tierra Data Inc. 2008, pp. 1–24,
appendices and GIS data; SERG 2009–
2011, GIS data). These surveys have
added substantially to the number of
documented occurrences of each of the
three taxa.
Rare plant surveys and island flora
studies have documented many more
locations occupied by Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea than
were known at the time of listing. Since
listing, 8 additional occurrences of M.
clementinus, 23 occurrences of A. d.
var. traskiae, and 10 occurrences of C.
grisea have been documented (Table 1).
It is unknown whether the higher
number of occurrences represents
detections due to increased survey
efforts, recruitment from the seed bank,
or recolonization by the plants as a
result of management actions
implemented by the Navy to conserve
listed species on the island (see
Distribution section for each taxon
above). However, this improvement in
the documented status of each of these
taxa suggests that feral goats and pigs
were a significant threat to each. Thus,
their improved status may largely be
due to the implementation of a single
action identified in the Recovery Plan.
Because portions of the island remain
closed, monitoring effectiveness of
recovery efforts is not being fully
implemented. Occurrences for each
species, as described above, are closed
to access for monitoring or any recovery
efforts. Thus, Objective 6 cannot be fully
met for the three taxa under current
operational closure directives.
Summary of Recovery Plan
Implementation
In summary, while the Recovery Plan
does not include taxon-specific
downlisting or delisting criteria for
measuring the recovery of
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea, many of the actions identified in
the Recovery Plan have been
implemented to benefit these taxa. Most
significantly, the Navy removed feral
goats and pigs from San Clemente Island
in 1992. The improvement in the
documented status of each of these
listed plant taxa suggests that the
removal of these animals was integral to
their ability to establish vigorous, selfsustaining occurrences. Though the
distribution of Malacothamnus
clementinus has continued to increase
on the island, the majority of its range
occurs within SHOBA. Since access to
Impact Areas within SHOBA is
restricted to military personnel, the
status of three M. clementinus
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occurrences is uncertain at this time. A
fourth occurrence, with a significant
amount of genetic diversity, outside of
the impact areas is also closed at this
time. Due to limited access to these
areas, there are insufficient data to
indicate that the objectives have been
successfully met. In addition, limited
access precludes natural resource
managers from implementing
management actions, such as nonnative
control and fire suppression.
In contrast, threats are reduced in
areas occupied by Acmispon
dendroideus var. traskiae and Castilleja
grisea, and many of the objectives have
been met in part or full. Complementing
the success of these conservation
measures, the ecology and genetics of
each of these taxa have been studied,
and a number of programs are now in
place to improve habitat suitability,
prevent introductions of nonnative
species, guide and track management
efforts, and protect occurrences of these
plant taxa. We investigated other
potential threats for these taxa and
concluded that they do not pose
significant impacts. Based on our review
of the Recovery Plan, we conclude that
the status of Acmispon dendroideus var.
traskiae and Castilleja grisea has
improved due to activities being
implemented by the Navy on San
Clemente Island. The effects of these
activities on the status of the three taxa
are discussed in further detail below.
Summary of Factors Affecting the
Species
Section 4 of the Act and its
implementing regulations (50 CFR part
424) set forth procedures for listing
species, reclassifying species, or
removing species from the Federal Lists
of Endangered and Threatened Wildlife
and Plants. ‘‘Species’’ is defined by the
Act as including any species or
subspecies of fish or wildlife or plants,
and any distinct vertebrate population
segment of fish or wildlife that
interbreeds when mature (16 U.S.C.
1532(16)). Once the ‘‘species’’ is
determined, we then evaluate whether
that species may be endangered or
threatened because of one or more of the
five factors described in section 4(a)(1)
of the Act. Those factors are:
(A) The present or threatened
destruction, modification, or
curtailment of its habitat or range;
(B) Overutilization for commercial,
recreational, scientific, or educational
purposes;
(C) Disease or predation;
(D) The inadequacy of existing
regulatory mechanisms; or
(E) Other natural or manmade factors
affecting its continued existence.
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We must consider these same five
factors in reclassifying or delisting a
species. Listing, reclassifying, or
delisting may be warranted based on
any of the above threat factors, either
singly or in combination. For species
that are already listed as threatened or
endangered, an analysis of threats is an
evaluation of both the threats currently
facing the species and the threats that
are reasonably likely to affect the
species in the foreseeable future
following the delisting or downlisting.
Under section 3 of the Act, a species
is ‘‘endangered’’ if it is in danger of
extinction throughout all or a significant
portion of its range, and is ‘‘threatened’’
if it is likely to become endangered in
the foreseeable future throughout all or
a significant portion of its range. The
word ‘‘range’’ refers to the range in
which the species currently exists, and
the word ‘‘significant’’ refers to the
value of that portion of the range being
considered to the conservation of the
species. The ‘‘foreseeable future’’ is the
period of time over which events or
effects reasonably can or should be
anticipated, or trends extrapolated.
We considered and evaluated the best
available scientific and commercial
information for this analysis.
Information pertaining to
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea in relation to the five factors
provided in section 4(a)(1) of the Act is
discussed below. For the purposes of
this analysis, we will first evaluate
whether the currently listed species
should be considered threatened or
endangered throughout all their ranges.
If we determine that the species are
threatened, then we will consider
whether there are any significant
portions of their ranges where they are
in danger of extinction or likely to
become endangered within the
foreseeable future. The five factors listed
under section 4(a)(1) of the Act and
their applications to M. clementinus, A.
d. var. traskiae, and C. grisea are
presented below.
Malacothamnus clementinus (San
Clemente Island Bush Mallow)
In the 2007 status review, we
acknowledged that the predominant
threat at listing (grazing from feral
herbivores) was ameliorated with the
removal of goats and pigs from the
island in 1992 (USFWS 2007a, pp. 1–
28). Threats to Malacothamnus
clementinus identified in 2007
included: (1) Land use, (2) fire, (3)
nonnative species, (4) erosion, (5)
natural factors, (6) fire management, and
(7) limited access to SHOBA. Land use,
fire, nonnatives, erosion, and fire
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management are discussed as habitat
threats below under Factor A. Natural
factors in the 2007 status review refer to
the low genetic diversity of this taxon
and are discussed in Factor E below. In
2007, access to SHOBA was described
as a threat because it ‘‘undermines the
effectiveness of surveys and
management efforts’’ (USFWS 2007a, p.
21). While lack of access to portions of
the island still limits our ability to
assess the status of the taxon, access to
SHOBA is not considered a threat.
Rather, the lack of access contributes to
uncertainty in assessing threats and the
species’ response to those threats and to
actions taken to ameliorate threats. In
this finding, we focus on threats
responsible for impacting the listed
entity or habitat where it occurs, not our
inability to access these areas.
Factor A. The Present or Threatened
Destruction, Modification, or
Curtailment of Its Habitat or Range
The final listing rule (42 FR 40682;
August 11, 1977) identified the
following threats to Malacothamnus
clementinus: Habitat alteration and
destruction, competition from nonnative
species, and direct predation by
nonnative herbivores (goats and pigs).
With the final removal of these
herbivores in 1992, the vegetation on
San Clemente Island has rebounded,
and the status of many rare plant
occurrences, including M. clementinus,
has improved (Tierra Data Inc. 2005, p.
8; Junak 2006a, pers. comm.). Although
the direct threat from predation to M.
clementinus identified in the final
listing rule has been eliminated, erosion
as a result of overgrazing and invasive
nonnative plants remain ongoing threats
to habitat of M. clementinus. The
Recovery Plan also identified habitat
alteration and disturbance from the
Navy’s use of the island for military
operational and training needs as
additional threats to the habitats
occupied by M. clementinus (USFWS
1984, pp. 58–63). Additional threats
identified since listing include
alteration of San Clemente Island
habitats by military training activities,
fire, and fire management. As outlined
below, we discuss in this section the
impacts of the following threats that
affect the habitat or range of M.
clementinus: (1) Land use, (2) erosion,
(3) nonnative plants, (4) fire, and (5) fire
management.
Land Use
In this section we describe threats
considered likely based on land use
designations. A total of 11
Malacothamnus clementinus
occurrences are distributed on San
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Clemente Island, including one midisland (Lemon Tank Canyon) and the
remaining 10 approximately 9.5 mi
(15.3 km) along the southwesterly facing
coastal terraces at the southern end of
the island. Historically, the island was
used for grazing and ranching. At the
time of listing, the Navy had acquired
the island, although military operations
were not intense and feral grazers were
still on the island. Since listing, training
activities and land use by the Navy have
increased significantly. Since it was first
listed in 1977, the Navy has consulted
and coordinated with us regarding the
effects of various activities on M.
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea
(USFWS 2002, pp. 1–21; USFWS 2003,
p. 1; USFWS 2004, pp. 1–2; USFWS
2008, pp. 1–237). These consultations
have addressed numerous activities
including training, fire management, the
installation of wind turbines, missile
tests, maintenance and construction of
Ridge Road and the assault vehicle
maneuver route, construction of
berthing buildings, and development
and use of training areas.
Most recently, training activities
approved in the MOFMP include
substantial increases in vehicle and foot
traffic in the IOA (Navy 2008b, pp. 2–
1 to 2–52). In November 2008, we
completed a biological opinion
describing the impact of the Navy’s
military training program proposed in
the MOFMP on 11 federally listed
species on San Clemente Island,
including the three taxa that are the
subject of this finding (USFWS 2008,
pp. 1–237). This consultation addressed
the proposed expansion of the
frequency and amount of military
training on the island, along with
enhanced training complex capabilities,
construction of new gates and buildings,
use of an IOA, change in fire
management strategies, and use of an
assault vehicle maneuver corridor.
Examples of projected increases in
training levels relative to a
representative year of training prior to
2008 include: 11 percent increase in
naval fire support exercises, 23 percent
increase in land bombing exercises, 150
percent increase in explosive ordnance
disposal, 60 percent increase in artillery
operations, 90 percent increase in land
demolitions, 19 percent increase in land
navigation exercises, and 96 percent
increase in SEAL platoon operations
(USFWS 2008, p. 11).
We considered the status and
distribution of Malacothamnus
clementinus, and the various
management, avoidance, and
minimization measures in place,
including those the Navy will
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implement with the new MOFMP in our
2008 biological opinion (we also
considered impacts to Acmispon
dendroideus var. traskiae and Castilleja
grisea). Additionally, the Service made
conservation recommendations within
the biological opinion, including: (1)
Considering recommended actions from
the 5-year review in the upcoming
revision of the INRMP, (2) propagation
and outplanting of narrowly distributed,
listed plant species, and (3) the
collection of M. clementinus cuttings
and seeds from Horse Beach Canyon for
the propagation and outplanting of
individuals in areas without military
training. We concluded that ongoing
and likely impacts from the proposed
increases in military training activities
would not jeopardize the continued
existence of M. clementinus, A. d. var.
traskiae, and C. grisea (USFWS 2008, p.
90).
The southern portion of the
distribution of Malacothamnus
clementinus spans the boundary of
SHOBA, which supports a variety of
training operations involving both live
and inert munitions fire. The majority of
this area serves as a buffer for areas of
more intense training and is less
susceptible to direct land use threats
than occurrences within TAR, IOA, or
Impact Areas. Six of 11 known
occurrences (54 percent; Canchalagua
Canyon, Horse Beach Canyon, Lower
China Canyon, Upper China Canyon,
Cave Canyon, and Chukit Canyon) fall
within SHOBA, where diffuse or
accidental impacts to M. clementinus
are likely to occur, and training might
result in the alteration of habitat by Off
Highway Vehicle (OHV) movement and
large-scale troop movements through
the military impact and training areas.
Within the Impact Areas, some
munitions exercises involve the use of
incendiary devices, such as illumination
rounds, white phosphorous, and tracer
rounds, which pose a high risk of fire
ignition (USFWS 2008, pp. 11–13). One
occurrence (Lower China Canyon) is
within the IOA, and could experience
direct impacts from troop and vehicle
movement through the area. Three
additional occurrences (Upper China
Canyon, Horse Beach Canyon, and
Lemon Tank Canyon) are near the IOA
(within 1,000 ft (305 m)), and could be
subjected to diffuse or accidental
impacts. Because of the elevated risk of
fire and disturbance associated with
training activities, live and inert
munitions fire are targeted towards two
delineated Impact Areas (I and II)
within SHOBA where bombardments
and land demolition are concentrated.
Three of 11 occurrences (27 percent;
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Upper China Canyon, Lower China
Canyon, and Horse Beach Canyon) are
within Impact Areas I or II, and are now
closed to nonmilitary personnel
(USFWS 2008, p. 50).
As a result, it is not possible to assess
the magnitude of the threat in these
areas, and the status of the three
occurrences remains unknown. These
occurrences, although limited in
number, contain the greatest numbers of
individuals and some of the highest
genetic diversity on the island
(Helenurm 1999, p. 40). The intense
training activities within the Impact
Areas pose a direct threat to habitat and
occurrences due to associated ground
disturbance and bombardment (USFWS
2008, pp. 83–84). The majority (8 of 11)
of Malacothamnus clementinus
occurrences are located outside of any
training areas (IOA, TAR, or Impact
Area) and are less likely to sustain
direct impacts from military activities
associated with land use; three
occurrences (Upper China Canyon,
Lower China Canyon, and Horse Beach
Canyon) are partially or wholly within
the boundaries of a training area (IOA,
TAR, or Impact Area).
The Lemon Tank Canyon occurrence
falls within an area identified by the
INRMP as needing environmental
cleanup pursuant to the Resource
Conservation and Recovery Act (RCRA)
and Comprehensive Environmental
Response, Compensation and Liability
Act (CERCLA) (Navy 2002, p. 2–18).
This site is still in the study phase and
has not been listed, or proposed for
listing, on the National Priorities List.
Habitat at this occurrence could receive
improvements by future environmental
cleanup (Munson 2011b, pers. comm.).
Initial surveys of the project footprint
have been completed, and
Malacothamnus clementinus was not
found in the project footprint (B.
Munson 2011e, pers. comm.), although
additional surveys will need to be
undertaken to ensure there is no impact
to the plant. RCRA and CERCLA require
that impacts to the species and its
habitat be avoided and minimized to the
extent practicable. This area has also
been closed to natural resource
personnel, and the status of the
occurrence in this area is unknown
(Munson 2011c, pers. comm.).
While the increase in military training
affects the species (as well as Acmispon
dendroideus var. traskiae and Castilleja
grisea), the Navy through
implementation of the INMRP is
avoiding and minimizing the impacts to
the extent practicable while meeting
operational needs. Land use is currently
impacting habitat of 4 of the 11
occurrences (36 percent; Lemon Tank
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Canyon, Lower China Canyon, Upper
China Canyon, and Horse Beach
Canyon) on the island, which may lead
to overall habitat degradation, and cause
the loss of individuals or groupings of
plants in a given area. Military
operations and training are island-wide
threats to M. clementinus, particularly
to the occurrences in or adjacent to
military training areas.
Erosion
Erosion and associated soil loss
caused by browsing of feral goats and
rooting of feral pigs likely modified the
island’s habitat (Navy 2002, p. 1–14).
Defoliation from overgrazing on San
Clemente Island increased erosion over
much of the island, especially on steep
slopes where denuded soils can quickly
wash away during storm events
(Johnson 1980, p. 107; Navy 2002, pp.
1–14, 3–9; Tierra Data Inc. 2007, pp. 6–
7). In the INRMP, erosion was identified
as a threat to canyon woodland and
maritime desert scrub vegetation
communities, which is Malacothamnus
clementinus habitat (Navy 2002, pp. 4–
3, 4–12). In the southwestern portion of
its distribution, M. clementinus is found
along coastal terraces, canyon rims, and
at the base of escarpments where
erosion is more prevalent. The erosion
process can remove soil that provides
nutrients and physical support for the
plants, displace seeds and deposit them
in unsuitable locations, and bury extant
individuals or small occurrences of the
plants. This stripping of soil and plants
can affect vegetation composition and
landscape long after the herbivores are
removed (Johnson 1980, p. 107). Erosion
has likely been exacerbated by
reductions in vegetation cover due to
drought and fire (Johnson 1980, pp.
105–118). Currently, the Navy has a
program run by SERG that grows and
outplants native vegetation to areas that
need to be restored (Navy 2002, pp. 3–
51 to 3–52). Restoration of native
vegetation helps retain soil and
ameliorate erosion in stripped areas.
Increased military activities,
especially where Malacothamnus
clementinus is found within training
area boundaries, cause erosion through
soil compaction or other soil
disturbances in occupied habitat near
roadways or vehicle maneuver areas
(Tierra Data Inc. 2007, p. 12). With the
exception of the main road, the roads on
San Clemente Island are largely
unpaved, and 5 of the 11 occurrences
(45 percent; Lower China Canyon, Horse
Beach Canyon, Middle Ranch Canyon,
Waymuck Canyon, and Lemon Tank
Canyon) are within 500 ft (152 m)) of a
road on the island (Forman and
Alexander 1998, p. 217). These
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occurrences could be subject to diffuse
disturbance (spread out over a large area
or not concentrated) and road effects
that degrade habitat quality. Roads can
concentrate water flow, causing incised
channels and eroded slopes (Forman
and Alexander 1998, pp. 216–217). This
increased erosion around roads can
degrade habitat, especially along steep
canyons and ridges. Erosion impacts are
likely greatest in SHOBA, where
bombardment has led to a pattern of
surface disturbance and recurrent fire
(Navy 2002, pp. 3–5). The Navy studied
the potential for erosion from several
proposed military activities (Tierra Data
Inc. 2007, pp. 1–45, Appendices). One
additional occurrence at Upper China
Canyon is also impacted by erosion.
Therefore, 6 of the 11 occurrences (54
percent; Lower China Canyon, Upper
China Canyon, Horse Beach Canyon,
Middle Ranch Canyon, Waymuck
Canyon, and Lemon Tank Canyon) of M.
clementinus are likely to be further
impacted by erosion (Table 1).
Erosion control measures are
incorporated into all site feasibility
studies and project planning, design,
and construction to minimize the
potential to exacerbate existing erosion
and avoid impacts to listed species
(Munson 2011a, pers. comm.). The
INRMP requires that all projects include
erosion conservation work and
associated funding (Navy 2002, p. 4–89).
These conservation actions include best
management practices for construction
and engineering, choosing sites that are
capable of sustaining disturbance with
minimum soil erosion, and stabilizing
disturbed sites with native plants (Navy
2002, pp. 4–89–4–91). Additionally,
large-scale island-wide maneuvers with
assault vehicles have been postponed
until an erosion control plan is drafted
and implemented. Due to potential new
training in the IOA and the Assault
Vehicle Maneuver Area (AVMA), an
erosion control plan to minimize the
effects of the potential training is
currently being developed for San
Clemente Island (Munson 2011a, pers.
comm.). The Navy has committed to
preparing this plan and implementing it
prior to any new training or operations
in the IOA or AVMA (Navy 2008b, pp.
5–29, 5–30). The proposed erosion
control plan includes development and
application of BMPs including:
establishing setbacks and buffers from
steep slopes, drainages, and sensitive
resources; constructing site-specific
erosion control structures; conducting
revegetation and routine maintenance;
and monitoring and adjusting the BMPs
as appropriate. Implementation of the
erosion control plan is expected to
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prevent soil erosion from adversely
affecting federally listed species,
including Malacothamnus clementinus,
and their habitats. Additionally, the
plan is designed to prevent soil erosion
from significantly impacting other
sensitive resources, including sensitive
plant and wildlife species and their
habitats. This erosion control plan will
address military operations associated
with the IOA, AVMA, and AFP;
however, since the plan is not yet
finalized, it does not currently
ameliorate the noted threats from
erosion.
The processes and results of erosion
are island-wide threats to the habitat of
Malacothamnus clementinus,
particularly to the occurrences in or
adjacent to military training areas or
roads. Erosion is currently impacting 6
of the 11 occurrences (54 percent) on
the island, which may lead to overall
habitat degradation, and cause the loss
of individuals or groupings of plants in
a given area. Of the six occurrences
currently impacted by erosion, four
(Lower China Canyon, Upper China
Canyon, Horse Beach Canyon, and
Lemon Tank Canyon) are in areas that
are operationally closed to access, and
likely not afforded conservation
measures to control or monitor erosion.
With these closures and continued
impacts, erosion remains a threat to the
habitat of M. clementinus.
Nonnative Species
One of the threats to Malacothamnus
clementinus identified in the final
listing rule was the spread of nonnative
plants into its habitat (42 FR 40682;
August 11, 1977). Nonnatives can alter
habitat structure, ecological processes
(such as fire regimes), nutrient cycling,
hydrology, and energy budgets and
compete for water, space, light, and
nutrients (Zink et al. 1995, p. 307;
Brooks 1999, pp. 16–17; Mack et al.
2000, p. 689). By 1992, researchers had
documented 99 nonnative plant species
on San Clemente Island (Kellogg and
Kellogg 1994, p. 5), and transfer of
nonnative species to the island
continues to be a problem today (Dunn
2006, pers. comm.; Junak 2006c, pers.
comm.; Kellogg 2006, pers. comm.;
O’Connor 2009c, pers. comm.).
Nonnative species of particular concern
include Foeniculum vulgare (fennel)
and Brassica tournefortii (Sahara
mustard), which have already invaded
M. clementinus habitat. Since nonnative
herbivores were removed from the
island, the most significant structural
alteration to the habitat has been the
proliferation of nonnative annual
grasses, such as Avena spp. (oats),
Bromus spp. (bromes), and Vulpia
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myuros (annual fescue). Annual grasses
vary in abundance with rainfall,
potentially changing the vegetative
community from shrubs to grasses, and
may increase the fuel load in wet years
(see Factor A—Fire section below).
Nonnative grasses are present in the
native maritime desert scrub vegetation
community where M. clementinus is
often found (Tierra Data Inc. 2005, pp.
36–42).
Although previous invasions of
nonnatives probably were introduced in
grazing fodder, current invasions are
typically introduced by military
activities and training on the island.
Nonnative plants likely come in with
equipment, vehicles, material, and
personnel, and are spread by their
movements. The primary pathway and
vector for nonnative species into arid
and semi-arid ecosystems are vehicles
and vehicular routes, and disturbances
along these routes and corridors enable
their establishment (Stylinski and Allen
1999, p. 551; Gelbard and Belnap 2003,
pp. 424–425; Von der Lippe and
Kowarik 2007, p. 986). Island
ecosystems and species are especially
vulnerable to nonnative plant invasions
due to the relative lack of biotic
diversity and natural predators (Mack
and Lonsdale 2002, p. 164).
Nonnative plants constitute a
rangewide threat to the endemic plant
community and habitat on San
Clemente Island, including the habitat
of all occurrences of Malacothamnus
clementinus. Five of 11 occurrences (45
percent; Lower China Canyon, Horse
Beach Canyon, Middle Ranch Canyon,
Waymuck Canyon, and Lemon Tank
Canyon) are within 500 ft (152 m) of
Ridge Road or China Point Road, and
may be subject to diffuse disturbance
and road effects that degrade habitat
quality along the road (Forman and
Alexander 1998, p. 217). Roadsides tend
to cultivate conditions (high
disturbance, seed dispersal by vehicles,
ample light, and water runoff) favorable
to nonnative species (Forman and
Alexander 1998, p. 210). Nonnatives,
including Foeniculum vulgare and
Mesembryanthemum crystallinum
(crystalline iceplant), have been found
in the disturbed shoulders along the
road between Ridge Road and China
Point in SHOBA (Braswell 2011, pers.
obs.).
Potential impacts from nonnative
plants to the habitats of the three taxa
analyzed in this finding are minimized
through annual implementation of the
Navy’s island-wide nonnative plant
control program (O’Connor 2009b, pers.
comm.; Munson 2011a, pers. comm.).
The focus of the nonnative plant species
program is to control plants on the
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island with the potential to adversely
impact habitat of federally listed
species, which includes the eradication
of isolated occurrences of nonnatives
and early detection and eradication of
new nonnative species (Navy 2008b, p.
5–28). This program targets nonnative
species for elimination using herbicide
and mechanical removal, with priorities
currently focused on new invasions and
particularly destructive nonnative
species. Nonnative species management
targets are identified and prioritized
annually by Navy natural resource
managers (Munson 2011a, pers. comm.).
These tactics have been successful in
isolating and limiting some species,
such as Foeniculum vulgare, to a few
locations (Howe 2011b, pers. comm.).
To reduce the potential for transport of
nonnative plants to San Clemente
Island, military and nonmilitary
personnel inspect tactical ground
vehicles and remove any visible plant
material, dirt, or mud on them prior to
going to San Clemente Island (USFWS
2008, p. 63). This cleaning helps
prevent nonnative plants from reaching
the island, but once there, nonnative
plants are easily spread from one area to
another by the movement of vehicles.
The Navy has implemented
preventative and control programs for
the nonnative plant species on the
island. Although nonnatives will
continue to pose a rangewide risk to the
habitat of Malacothamnus clementinus,
the Navy has taken steps to curtail
habitat conversion by nonnative plants.
Management and control of nonnative
plants is not in place at the four
occurrences that are closed to natural
resource managers. However, outside of
these areas, M. clementinus has
persisted on the island and, despite the
continued risk of encroachment by
nonnatives, its range has continued to
expand. Nonnatives remain a threat to
the M. clementinus’ habitat, particularly
in the four occurrences that are closed
to monitoring and management efforts.
Fire
Fire was not considered a threat to
Malacothamnus clementinus at the time
of listing (42 FR 40682; August 11,
1977). Since that time, however, over 50
percent of the island has experienced at
least one wildfire (Navy 2002, Map 3–
3, p. 3–32), and some areas have burned
multiple times with short intervals
between fires (Navy 2002, Map 3–4, p.
3–33). Between 1990 and 2004, there
were 114 wildfires on the island
suspected to be from Navy operational
sources (Navy 2008a, pp. 5–18, 5–19).
The majority of fires are concentrated in
SHOBA, and potentially impact the
habitat of 6 of 11 (54 percent) of M.
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29103
clementinus occurrences (Canchalagua
Canyon, Horse Beach Canyon, Lower
China Canyon, Upper China Canyon,
Cave Canyon, and Chukit Canyon).
Three of these occurrences (Upper
China Canyon, Lower China Canyon,
and Horse Beach Canyon) are in Impact
Areas I and II, where the risk of frequent
fire (less than 5 years apart) is especially
high (Navy 2002, pp. 5–93, 5–99). The
effects of fire on habitat within the
Impact Areas are currently unknown
due to closure to natural resource
personnel (USFWS 2008, p. 50).
The remaining land in SHOBA acts as
a buffer from fires and munitions
between the Impact Areas and the rest
of the island. Fires are occasionally
ignited by activities north of SHOBA,
posing a low-magnitude threat to the
remaining five occurrences (Lemon
Tank Canyon, Box Canyon, Norton
Canyon, Middle Ranch Canyon, and
Waymuck Canyon) (Navy 2002, Map 3–
4, p. 3–33). Due to the potential for
unexploded ordnance within SHOBA,
unless a fire threatens human life or
facilities, it usually is allowed to burn
itself out (Navy 2002, p. 3–32; Kellogg
2006, pers. comm.). This contrasts with
the northern portion of the island where
wildfires are usually suppressed
(Kellogg 2006, pers. comm.).
Increased fire frequency (more than
every 5 years) from intensified military
use could lead to localized changes in
vegetation. Nonnative annual grasses
can increase fuel load for fire ignition
and spread within the landscape. Dried
grasses provide a fuel that is easily
ignitable, and can extend the fire season
by more than a month because they
desiccate sooner than the native
herbaceous flora. These grasses can also
colonize a burned area better and more
quickly than native species, thereby
creating a cycle where fire and
nonnatives are positive feedbacks for
one another (Brooks et al. 2004, p. 677).
Frequent fires within and adjoining
military training areas have the
potential to alter the vegetative
community, resulting in the conversion
of shrublands to nonnative grasslands,
and a reduction in native perennial
bunchgrasses (O’Leary and Westman
1988, p. 779; D’Antonio and Vitousek
1992, p. 73; Minnich and Dezzani 1998,
pp. 383–384; Keeley et al. 2005, p. 2109;
Tierra Data Inc. 2005, p. 88).
At the time of listing, fire was not
identified as a threat because of lack of
fire history and the low intensity of
military training on the island. Since
that time, military training has
significantly increased, and we have
better records of the fire frequency on
the island. Fire is a rangewide threat to
the habitat of M. clementinus, and 6 of
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the 11 occurrences (54 percent) of
Malacothamnus clementinus occur
within areas that may be subject to
recurrent fire associated with military
training (Table 1; Canchalagua Canyon,
Horse Beach Canyon, Lower China
Canyon, Upper China Canyon, Cave
Canyon, and Chukit Canyon). The
remaining five occurrences are in
habitat with a lower risk of recurrent
fire and are less likely to experience
changes in vegetation community due to
fire. It is unlikely that fire control or
prevention measures will be undertaken
in the habitat at the three occurrences
within the Impact Areas that are
operationally closed. Fires that escape
designated training areas may threaten
other parts of the island, though because
of its broad distribution, it is unlikely
that one fire would be capable of
spreading throughout the entire range of
M. clementinus. The Navy’s
implementation of the MOFMP will
limit the frequency of fires that escape
Impact Areas. Through the annual
review process, the Navy identifies
mechanisms to reduce fire return
intervals in areas where this taxon is
concentrated (USFWS 2008, pp. 91–
122).
The Navy has implemented
preventative and control programs for
fire on the island. Although fire will
continue to pose a rangewide risk to the
habitat of Malacothamnus clementinus,
the Navy has taken steps to curtail
habitat conversion by frequent and
intense fire. Six of the 11 occurrences
(54 percent) of M. clementinus occur
within areas that may be subject to
recurrent fire associated with military
training. Management and control of fire
is not in place at the three occurrences
that are closed to natural resource
managers. However, M. clementinus has
persisted on the island and, despite the
continued risk of fire, its range has
continued to expand. Fire remains a
threat to the M. clementinus’ habitat,
particularly in the three occurrences in
the impact areas that are closed to
monitoring and management efforts.
Fire Management
In 2008, the Service issued a
biological opinion to the Navy on its
MOFMP on San Clemente Island
(USFWS 2008, pp. 1–244). The
biological opinion addressed impacts to
all 11 currently listed terrestrial taxa
known to occur on San Clemente Island,
including the three taxa analyzed in this
finding. Military activities contribute to
fires on San Clemente Island that may
adversely affect listed plants and
wildlife (USFWS 2008, p. 3). The Navy’s
focus on fire management is related to
military training and other human-
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related activities and facilities, as these
activities represent the primary source
of ignition on the island (USFWS 2008,
p. 3). Seasonal range and training
modifications, based on weather
patterns and moisture, are efforts taken
by the Navy to assist in the prevention
of fire ignition, containment, and fire
suppression (USFWS 2008, pp. 3–4).
In response to the potential hazard of
wildfires on San Clemente Island,
firefighting techniques have improved
for known operational-related ignition
sources (Navy 2008b, pp. 3.11–71).
Within the MOFMP, the Navy proposed
the expansion of military training, as
well as the implementation of a fire
management plan directed at fire
suppression, fire prevention, and fuels
management. This plan was developed
to provide flexibility for the timing of
military training, and will modify the
level of fire suppression resources
required to be present during training
activities. Real-time weather data and
fuels management, in combination with
the ready availability of fire suppression
resources, are used to minimize the risk
of fires spreading from areas approved
for the use of ordnance and incendiary
devices. The Navy has committed to
conducting an annual review of fire
management and fire occurrences that
will allow for adaptive management and
changes in the MOFMP (USFWS 2008,
pp. 91–122).
The MOFMP was developed by the
Navy to provide flexibility for the
timing of military training, and to
ensure that elevated fire suppression
resources were present to address an
increased level of training activities and
fire risk. In response to the potential
hazard of wildland fires on San
Clemente Island, firefighting techniques
have improved for known operationalrelated ignition sources (Navy 2008b,
pp. 3.11–71). The MOFMP defines the
conditions under which certain fire
protection resources must be available
and ready for use (for example, a
dedicated fire helicopter) (USFWS 2008,
p. 53). The MOFMP calls for the use of
real-time weather and fire forecasting to
determine when certain munitions may
be used and when helicopters must be
present. After extensive consultation
with the Navy, we issued a biological
opinion on the MOFMP that concluded
the MOFMP would not jeopardize the
continued existence of listed species,
including the three taxa analyzed in this
Finding (USFWS 2008, pp. 1–237).
While the increase in military training
and fire suppression could affect habitat
of Malacothamnus clementinus (as well
as Acmispon dendroideus var. traskiae
and Castilleja grisea), we have worked
with the Navy to avoid and minimize
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the impacts to habitat of individuals or
occurrences to the extent practicable
while meeting the operational needs of
the Navy.
Fire suppression activities described
in the MOFMP and used by the Navy
include creating firebreaks (bare soil
created through manual or herbicide
removal of vegetation), use of fire
retardants (spraying of fire retardants
along fire breaks) and aerial drops of
saltwater from aircraft. Fire management
on San Clemente Island includes the
creation of fuelbreaks within areas of
SHOBA that impact the habitat at three
Malacothamnus clementinus
occurrences (Horse Beach Canyon,
Lower China Canyon, and Upper China
Canyon) (USFWS 2008, p. 57).
Fuelbreaks are maintained along the
boundaries of Impact Areas I and II to
prevent the spread of fire outside of the
areas (USFWS 2008, p. 57). Fuelbreaks
on the island are created using
herbicides and strip burning, and
maintained using herbicides and fire
retardant (Phos-Chek D75F) (USFWS
2008, pp. 97–98). The use of fire
retardant or herbicide, as proposed in
the MOFMP, results in the loss of M.
clementinus and Castilleja grisea habitat
within the fuelbreak footprint (USFWS
2008, p. 81). The use of Phos-Chek may
also allow or facilitate the expansion
and persistence of nonnative species
due to the fertilizing effect of this
retardant (Larson et al. 1999, p. 115;
Kalabokidis 2000, p. 130). Fire
retardants act as a source of nitrogen
and phosphorous, which are nutrients
that can affect plant species
composition (Larson and Duncan 1982,
p. 702). The Navy has begun a study on
the effects of Phos-Chek on San
Clemente Island vegetation, and has
avoided application of Phos-Chek
within 300 ft (91.4 m) of mapped listed
species (including M. clementinus and
C. grisea) to the extent allowable with
fuelbreak installation (USFWS 2008, pp.
97–98).
It is anticipated that the Navy will
construct fuelbreaks to minimize the
risk of fire spreading from areas of live
fire and demolition training north of
SHOBA (USFWS 2008, p. 98). In the
MOFMP, the Navy agreed to conduct
preseason briefings for firefighting
personnel on the guidelines for fire
suppression, and the limitations
associated with the use of Phos-Chek
and saltwater drops (USFWS 2008, pp.
97–98). The impact of saltwater on the
habitat of M. clementinus (and Castilleja
grisea) has not yet been assessed.
However, if salt persists, the
composition of the plant community
could change to favor more salt-tolerant
taxa. Fire management could have a
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direct impact on the habitat and species
composition of at least three
occurrences of M. clementinus.
The Navy’s implementation of a
MOFMP will help to reduce the risk of
habitat conversion by fire, though the
habitat of Malacothamnus clementinus
could be altered by the management of
fire. Although the threat is ameliorated
through implementation of the MOFMP,
fire management remains a threat to M.
clementinus, particularly to the three
occurrences that fall within areas that
may be managed using fuel breaks and
fire suppression.
Summary of Factor A
From 1850 until 1934, San Clemente
Island was used for sheep ranching,
cattle ranching, goat grazing, and pig
farming (Navy 2002, pp. 3–4). The
effects of these grazers, which were not
completely removed from the island
until 1992, on the habitat and plants
were one of the original reasons for
classifying Malacothamnus clementinus
as endangered in the 1977 listing rule
(42 FR 40682); this threat is now
eliminated. Currently, M. clementinus is
threatened by the destruction and
modification of habitat caused by
impacts related to designated land use,
erosion, the spread of nonnative plants,
fire, and fire management practices. To
help ameliorate these threats, the Navy
is implementing a MOFMP and the
island-wide control of nonnative plants
as outlined in the INRMP (Navy 2002,
pp. 3–114–3–116; USFWS 2008, pp. 1–
237). The fire management plan within
the MOFMP has been used to inform
strategic decisions for training using live
fire or incendiary devices. Three
occurrences within the Impact Areas are
now closed to natural resource
monitoring and management, and
currently their status is unknown; a
fourth occurrence (Lemon Tank) is also
closed but is not within the Impact
Areas.
Per our 2008 biological opinion, the
Navy has postponed major troop and
assault vehicle maneuvers across the
island until it completes and
implements an erosion control plan
(USFWS 2008, pp. 62, 87). Natural
resource managers have been successful
at decreasing the prevalence of
particularly destructive nonnatives,
such as Foeniculum vulgare.
Management actions directed at
conservation of Malacothamnus
clementinus may not be fully
implemented at 4 of the 11 known
occurrences (Lower China Canyon,
Upper China Canyon, Horse Beach
Canyon, and Lemon Tank Canyon)
currently closed to natural resource
access. This will reduce and fragment
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the effectiveness of the conservation
measures. Although the species is
expanding, and ongoing and anticipated
conservation efforts contribute to its
conservation, military training
activities, erosion, nonnatives, and fire
have ongoing impacts to all M.
clementinus occurrences rangewide
both now and into the future.
Factor B. Overutilization for
Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682;
August 11, 1977), the Service did not
identify any threats from
overutilization, and there is no new
information to indicate that
overutilization is a threat to
Malacothamnus clementinus. Although
herbarium specimens of M. clementinus
and seeds have been collected for
research and seed banking,
overutilization of M. clementinus for
any purpose is not currently considered
a threat nor is expected to be in the
future.
Factor C. Disease or Predation
Grazing of feral goats and the rooting
of feral pigs was considered a threat
under this category to Malacothamnus
clementinus in the final listing rule (42
FR 40682, at 40684; August 11, 1977).
This threat was ameliorated by the
removal of the goats and pigs from San
Clemente Island in 1992, as recognized
in our 2007 status review (USFWS
2007a, p. 16). Currently, no other
predators or diseases on San Clemente
Island are known to pose a significant
threat to M. clementinus, nor are they
expected to in the future.
Factor D. Inadequacy of Existing
Regulatory Mechanisms
The Act requires us to examine the
adequacy of existing regulatory
mechanisms with respect to those
existing and foreseeable threats that may
affect Malacothamnus clementinus. The
inadequacy of existing regulatory
mechanisms was not indicated as a
threat to M. clementinus at listing (42
FR 40682; August 11, 1977). Since it
was listed as endangered, the Act has
been and continues to be the primary
Federal law that affords protection to M.
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. The
Service’s responsibilities in
administering the Act include sections
7, 9, and 10.
Section 7(a)(1) of the Act requires all
Federal agencies, including the Navy, to
utilize their authorities in furtherance of
the purposes of the Act by carrying out
programs for the conservation of
endangered and threatened species.
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Section 7(a)(2) of the Act requires
Federal agencies, including the Service
and the Navy, to ensure that actions
they fund, authorize, or carry out do not
‘‘jeopardize’’ the continued existence of
a listed species or result in the
destruction or adverse modification of
habitat in areas designated by the
Service to be critical. Critical habitat has
not been designated or proposed for this
taxon. A jeopardy determination is
made for a project that is reasonably
expected, either directly or indirectly, to
appreciably reduce the likelihood of
both the survival and recovery of a
listed species in the wild by reducing its
reproduction, numbers, or distribution
(50 CFR 402.02). A non-jeopardy
opinion may include reasonable and
prudent measures that minimize the
extent of impacts to listed species
associated with a project. Under section
9(a)(2) of the Act, with respect to
endangered plant taxa, it is unlawful to
remove and reduce to possession
(collect) any such taxon from areas
under Federal jurisdiction; maliciously
damage or destroy any such taxon on
any such area; or remove, cut, dig up,
or damage or destroy any such species
on any other area in knowing violation
of any law or regulation of any State or
in the course of any violation of a State
criminal trespass law.
Since it was first listed in 1977, the
Navy has consulted and coordinated
with us regarding the effects of various
activities on Malacothamnus
clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. In
November 2008, we completed a
biological opinion describing the impact
of the Navy’s military training program
proposed in the MOFMP on 11 federally
listed species that occur on San
Clemente Island (USFWS 2008, pp. 1–
237). We considered the status and
distribution of M. clementinus, the
various management strategies, and the
avoidance and minimization measures
in place and those the Navy will
implement with the new plan (as well
as A. d. var. traskiae and C. grisea).
Additionally, the Service made
conservation recommendations within
the biological opinion, including: (1)
Considering recommended actions from
the 5-year review in the upcoming
revision of the INRMP, and (2)
propagation and outplanting of
narrowly distributed, listed plant
species. We concluded that ongoing and
likely impacts from the proposed
increases in military training activities
would not jeopardize the continued
existence of M. clementinus, A. d. var.
traskiae, and C. grisea (USFWS 2008,
pp. 1–237).
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Thus, listing Malacothamnus
clementinus provided a variety of
protections, including the prohibitions
against removing or destroying plants
within areas under Federal jurisdiction
and the conservation mandates of
section 7 for all Federal agencies. If M.
clementinus were not listed, these
protections would not be provided.
Thus, we must evaluate whether other
regulatory mechanisms would provide
adequate protections absent the
protections of the Act.
Other Federal Protections
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National Environmental Policy Act
(NEPA)
All Federal agencies are required to
adhere to the National Environmental
Policy Act (NEPA) of 1970 (42 U.S.C.
4321 et seq.) for projects they fund,
authorize, or carry out. The Council on
Environmental Quality’s regulations for
implementing NEPA (40 CFR parts
1500–1518) state that agencies shall
include a discussion on the
environmental impacts of the various
project alternatives (including the
proposed action), any adverse
environmental effects that cannot be
avoided, and any irreversible or
irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA
is a disclosure law, and does not require
subsequent minimization or mitigation
measures by the Federal agency
involved. Although Federal agencies
may include conservation measures for
Malacothamnus clementinus as a result
of the NEPA process, any such measures
are typically voluntary in nature and are
not required by the statute. NEPA does
not itself regulate activities that might
affect M. clementinus, but it does
require full evaluation and disclosure of
information regarding the effects of
contemplated Federal actions on
sensitive species and their habitats.
On San Clemente Island, the Navy
must meet the NEPA requirements for
actions significantly affecting the
quality of the human environment.
Typically, the Navy prepares
Environmental Assessments and
Environmental Impact Statements on
operation plans and new or expanding
training actions. Absent the listing of M.
clementinus, we would expect the Navy
to continue to meet the procedural
requirements of NEPA for its actions,
including evaluating the environmental
impacts to rare plant species and other
natural resources. However, as
explained above, NEPA does not itself
regulate activities that might affect M.
clementinus.
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Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670)
authorizes the Secretary of Defense to
develop cooperative plans with the
Secretaries of Agriculture and the
Interior for natural resources on public
lands. The Sikes Act Improvement Act
of 1997 requires Department of Defense
installations to prepare Integrated
Natural Resources Management Plans
(INRMPs) that provide for the
conservation and rehabilitation of
natural resources on military lands
consistent with the use of military
installations to ensure the readiness of
the Armed Forces. An INRMP is a plan
intended ‘‘* * * to guide installation
commanders in managing their natural
resources in a manner that is consistent
with the sustainability of those
resources while ensuring continued
support of the military mission’’ (Navy
2002, p. 1–1). INRMPs are developed in
coordination with the State and the
Service, and are generally updated every
5 years. Although an INRMP is
technically not a regulatory mechanism
because its implementation is subject to
funding availability, it is an important
guiding document that helps to integrate
natural resource protection with
military readiness and training.
San Clemente Island Integrated Natural
Resources Management Plan (INRMP)
Pursuant to the Sikes Act, the Navy
adopted an INRMP for San Clemente
Island that targets multiple objectives
towards protection of Malacothamnus
clementinus and its habitat, and helps to
reduce threats to this taxon (Navy 2002).
The INRMP includes provisions to
comply with the Endangered Species
Act, the Comprehensive Environmental
Response, Compensation, and Liability
Act (42 U.S.C. 9601), the Resources
Conservation and Recovery Act (42
U.S.C. 6901), the Federal Noxious Weed
Act of 1974 (7 U.S.C. 2801), and the Soil
Conservation Act (16 U.S.C 3B). Goals
and objectives in the INRMP for
specified management units on the
island are identified based on each
unit’s ranking for both military and
natural resource value. Natural resource
management objectives for the
management units are stepped down
from broader natural resource objectives
identified for species and habitats. Of
relevance to the protection of M.
clementinus, the INRMP includes an
objective to: ‘‘Protect, monitor, and
restore plants and cryptograms in order
to manage for their long-term
sustainability on the island’’ (Navy
2002, p. 4–39).
The INRMP specifically includes the
following objectives for Malacothamnus
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clementinus management: removal of
nonnatives, restoration of native plant
communities, monitoring of the species,
studies of the species’ response to fire,
and studies and inventory of insect
pollinators (Navy 2002, pp. D–20, D–
21). Other INRMP strategies that target
the plant communities within which the
three species occur include: controlling
erosion, with priority given to locations
where erosion may be affecting listed
species; producing a new vegetation
map; reducing nonnative plant cover
from 1992–1993 baseline levels;
managing the size and intervals of fires;
experimenting with fire management to
improve native plant dominance while
protecting sensitive plant occurrences;
and conducting genetic and biological
studies of M. clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea across the island.
To date, multiple INRMP management
strategies, or aspects of them, have been
implemented. The Navy has
implemented rare plant surveys and has
documented new occurrences of
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea on the island. Genetic research
and natural history studies have also
been performed. Concerted efforts have
been made to control escape of fire from
military training activities, and the Navy
has annually implemented nonnative
plant species control activities, with a
focus on species that have the potential
to compete with listed species. Overall,
considerable progress has been made
toward the identified INRMP goals to
maintain sustainable occurrences and
implement strategies that help reduce
threats to M. clementinus, A. d. var.
traskiae, and C. grisea.
The INRMP is an important guiding
document that helps to integrate the
military’s mission with natural resource
protection on San Clemente Island.
Although the INRMP includes
objectives targeted toward habitat
protection of optimal Malacothamnus
Clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea
habitat, Navy operational needs may
diverge from INRMP natural resource
goals. For example, control measures for
erosion, fire, and nonnatives described
in the INRMP may not be implemented
effectively or consistently in those areas
that are operationally closed due to the
presence of unexploded ordnance. The
MOFMP, Erosion Control Plan, and
nonnative plant species control
conducted on the island are discussed
above under Factor A. The Present or
Threatened Destruction, Modification,
or Curtailment of Its Habitat or Range.
Absent listing under the Act, the Navy
would still be required to develop and
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implement INRMPs under the Sikes Act.
However, as noted under the other
factors, while the INRMP helps to
ameliorate threats and provides some
protection for M. clementinus
occurrences, those occurrences within
Impact Areas or operationally closed
areas may not benefit from the
conservation measures. While the
INRMP has reduced the severity of
threats and contributed to conservation
of the species, it still allows for land use
consistent with military readiness and
training. Thus, Navy activities will
continue to impact M. clementinus as
described under Factor A.
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State Protections
Since the time of listing,
Malacothamnus clementinus has
benefited from additional State
protections under the Native Plant
Protection Act (NPPA) and California
Endangered Species Act (CESA; listed
1982). However, the range of M.
clementinus is restricted to a Federal
military installation, so listing under
NPPA and CESA may only afford
protection to this species in rare
instances when the lead agency is a
non-Federal agency or when proposed
activities fall under other State laws.
Summary of Factor D
In continuance of a long history of
cooperative conservation efforts, the
Navy has implemented several
conservation actions that benefit this
taxon. The Navy has a MOFMP to
reduce the risk of fire on the island and
a nonnative plant species control
program. Following review of the
Navy’s MOFMP, we issued a nonjeopardy biological opinion, which
included measures that the Navy has
implemented to manage fires and avoid
and minimize the impacts of military
activities on listed plants. The
provisions included in the San
Clemente Island INRMP provide
protection to accessible Malacothamnus
clementinus occurrences, and adaptive
management of their habitat, to help
address threats from military activities
and nonnative plants. However, as
indicated in the discussion under Factor
A, not all of the management tools
described in the INRMP are in place,
and conservation measures may not be
implemented at several of the closed
occurrences of the species.
Malacothamnus clementinus
occurrences are afforded some
protection through Federal and military
mechanisms. However, in the absence of
the Act, the existing regulatory
mechanisms are not currently adequate
to provide for the long-term
conservation of M. clementinus.
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Factor E. Other Natural or Manmade
Factors Affecting Its Continued
Existence
The 1977 listing rule identified
nonnatives as a threat to
Malacothamnus clementinus under
Factor E: competition from nonnative
plants (42 FR 40682; August 11, 1977).
In this 5-factor analysis, impacts from
nonnative plants are discussed above
under Factor A as a threat to habitat.
Other Factor E threats identified since
listing that currently impact M.
clementinus plants include: (1)
Movement of vehicles and troops, (2)
fire, (3) climate change, and (4) genetic
diversity. Factor E addresses threats to
individuals of the species, rather than
the habitat modification threats that are
discussed in Factor A. Therefore, while
some threats are discussed in both
sections, in this section we are focusing
on the direct impacts to individuals of
M. clementinus.
Movement of Vehicles and Troops
Military training activities within
SWAT, TAR, and the IOA often entail
the movement of vehicles and troops
over the landscape with the potential of
trampling or crushing individual plants
of all three species. SWATs are large
areas that typically support the
movement of small groups to reach an
objective or destination. The dispersed
movement of troops through these areas
is likely to result in occasional
trampling of plants, with minor or
temporary impacts at the occurrence
level. TARs are generally smaller areas
designated to accommodate intensive
use and bombardment. Plants located
within TARs are therefore more
vulnerable to being trampled by vehicle
and troop movements, particularly as
the level of military training increases in
these areas.
Use of the IOA, at its highest
intensity, involves the movement of
battalion-sized landings of troops (1,500
individuals) from the northern to
southern end of the island several times
a year. During such operations, it is
anticipated that about half of the troops
will travel on roads in vehicles, while
the other half will proceed on foot.
Based on the distribution of
Malacothamnus clementinus
occurrences and type of troop
movements likely to occur, impacts due
to trampling and crushing are likely to
occur within the IOA, along roads and
in the Impact Areas. Specifically, major
troop movements and vehicle landings
are planned through Horse Beach and
the Horse Beach Canyon occurrence,
with troops and assault vehicles moving
north along Horse Beach Road from the
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beach (USFWS 2008, pp. 30, 41). These
operations could affect the Horse Beach
Canyon and Lower China Canyon
occurrences (USFWS 2008, pp. 85–86).
The implementation of conservation
measures and the status of the plants at
Horse Beach Canyon, Upper and Lower
China Canyon, and Lemon Tank Canyon
are currently unknown because they are
closed to natural resource personnel
(USFWS 2008, p. 50). Four of 11
occurrences (36 percent; Lower China
Canyon, Upper China Canyon, Horse
Beach Canyon, and Lemon Tank
Canyon) are partially or wholly within
the boundaries of a training area (Impact
Area or SWAT) and are likely to sustain
some losses due to trampling associated
with the proposed increases in troop
and vehicle movements. With the lack
of access to all four occurrences, the
management of this threat and the
ability to assess the plant’s condition is
compromised, and the full effects of
trampling on the species are unknown.
Therefore, the movement of troops and
vehicles is still considered a threat to M.
clementinus.
Fire
Although not specifically mentioned
in the listing rule, intense or frequent
fires impact plants at 6 of the 11
occurrences (54 percent) of
Malacothamnus clementinus. In the
Factor A discussion above, we
addressed impacts of fire on the habitat.
This section includes discussion on the
discrete threat to individuals of M.
clementinus. As discussed in the
Background section, it is unknown if M.
clementinus is adapted to fire, though it
is likely that this species is resilient to
occasional fires (USFWS 1984. p. 48;
Navy 2002, D–20; USFWS 2007a, p. 3).
No direct studies have been done on the
effects of fire on M. clementinus;
however, its continued presence in
areas that have burned (such as in
SHOBA), and its ability to vegetatively
reproduce, suggest it is at least tolerant
of periodic fire. The species’ adaptation
to fire frequency is unknown. In areas
that burn on a more frequent basis, the
seed bank may become depleted if
individuals burn before they produce
seeds. Additionally, M. clementinus was
observed to have low numbers of seeds
in natural populations (Junak and
Wilken 1998, p. 291). Frequent burns
might exhaust the already small seed
bank, and inhibit reproduction in M.
clementinus.
Malacothamnus clementinus occurs
in some areas of the island that may
experience elevated fire frequency, such
as in SHOBA and especially within the
Impact Areas (Lower China Canyon,
Upper China Canyon, and Horse Beach
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Canyon) (see Factor A above). The
Navy’s fire management practices are
expected to minimize ignitions as well
as the spread of fires (see Factor A).
However, fires ignited within the
boundaries of the Impact Areas will not
be suppressed due to closures and safety
restrictions within these areas. This
would affect the three occurrences of M.
clementinus found within these areas.
The Navy conducts annual reviews of
fire management and fire occurrences to
allow for adaptive management. These
measures should minimize the
frequency and spread of fires that could
result in the loss of M. clementinus
individuals or occurrences. The Navy’s
ongoing implementation of the MOFMP
will limit the frequency with which
fires escape Impact Areas and TAR, and
that, through the annual review process,
the Navy will identify mechanisms to
reduce fire return intervals in areas not
designated for incendiary use (USFWS
2008, pp. 76–91).
Although the Navy has planned and
implemented fire management, fire still
affects six occurrences of
Malacothamnus clementinus. Three of
these occurrences fall within areas that
are closed to natural resources
management and prone to fire due to
bombing of the area. Therefore, fires
within these areas are allowed to burn,
affecting the individuals and
occurrences. Due to these conditions
and the continued impacts of fire within
SHOBA, fire remains a Factor E threat
to the existence of M. clementinus both
currently and in the future.
Climate Change
Consideration of climate change is a
component of our analyses under the
Endangered Species Act, and applies in
this finding to our analysis of all three
taxa. In general terms, ‘‘climate change’’
refers to a change in the state of the
climate (whether due to natural
variability, human activity, or both) that
can be identified by changes in the
mean or variability of its properties, and
that persists for an extended period—
typically decades or longer
(Intergovernmental Panel on Climate
Change (IPCC) 2007a, p. 78).
Changes in climate are occurring.
Examples include warming of the global
climate system over recent decades, and
substantial increases in precipitation in
some regions of the world and decreases
in other regions (for these and other
examples see IPCC 2007a, p. 30;
Solomon et al. 2007, pp. 35–54, 82–85).
Most of the observed increase in
global average temperature since the
mid-20th century cannot be explained
by natural variability in climate, and is
very likely due to the observed increase
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in greenhouse gas concentrations in the
atmosphere as a result of human
activities, particularly emissions of
carbon dioxide from fossil fuel use
(IPCC 2007a, p. 5 and Figure SPM.3;
Solomon et al. 2007, pp. 21–35).
Therefore, to project future changes in
temperature and other climate
conditions, scientists use a variety of
climate models (which include
consideration of natural processes and
variability) in conjunction with various
scenarios of potential levels and timing
of greenhouse gas emissions (e.g., Meehl
et al. 2007 entire; Ganguly et al. 2009,
pp. 11555, 15558; Prinn et al. 2011, pp.
527, 529).
The projected magnitude of average
global warming for this century is very
similar under all combinations of
models and emissions scenarios until
about 2030. Thereafter, the projections
show greater divergence across
scenarios. Despite these differences in
projected magnitude, however, the
overall trajectory is one of increased
warming throughout this century under
all scenarios, including those which
assume a reduction of greenhouse gas
emissions (Meehl et al. 2007, pp. 760–
764; Ganguly et al. 2009, pp. 15555–
15558; Prinn et al. 2011, pp. 527, 529).
(For examples of other global climate
projections, see IPCC 2007b, p. 8).
Various types of changes in climate
can have direct or indirect effects on
species and these may be positive or
negative depending on the species and
other relevant considerations, including
interacting effects with existing habitat
fragmentation or other non-climate
variables. There are three main
components of vulnerability to climate
change: Exposure to changes in climate,
sensitivity to such changes, and
adaptive capacity (IPCC 2007, p. 89;
Glick et al 2011, pp. 19–22). Because
aspects of these components can vary by
species and situation, as can
interactions among climatic and non
climatic conditions, there is no single
way to conduct our analyses. We use the
best scientific and commercial data
available to identify potential impacts
and responses by species that may arise
in association with different
components of climate change,
including interactions with non climatic
conditions.
As is the case with all potential
threats, if a species is currently affected
or is expected to be affected in a
negative way by one or more climaterelated impacts, this does not
necessarily mean the species meets the
definition of a threatened or endangered
species as defined under the Act. The
impacts of climate change and other
conditions would need to be to the level
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that the species is in danger of
extinction, or likely to become so,
throughout all or a significant portion of
its range. If a species is listed as
threatened or endangered, knowledge
regarding the species’ vulnerability to,
and impacts from, climate-associated
changes in environmental conditions
can be used to help devise appropriate
strategies for its recovery.
While projections from global climate
model simulations are informative and
in some cases are the only or the best
scientific information available, various
downscaling methods are being used to
provide higher-resolution projections
that are more relevant to the spatial
scales used to assess impacts to a given
species (see Glick et al, 2011, pp. 58–
61). With regard to the area of analysis
for the San Clemente Island and
specifically for the three species at issue
here, downscaled projections are
available at least with respect to
southern California.
San Clemente Island is located within
a Mediterranean climatic regime, but
with a significant maritime influence.
Climate change models indicate a 1.8 to
5.4 degrees Fahrenheit (1 to 3 degrees
Celsius) increase in average temperature
for southern California by the year 2070
(Field et al. 1999, p. 5; Cayan et al.
2008, p. S26; PRBO 2011, p. 40). Over
the same time span, a 10 to 37 percent
decrease in annual precipitation is
predicted (PRBO 2011, p. 40), though
other models predict little to no change
in annual precipitation (Field et al.
1999, pp. 8–9; Cayan et al. 2008, p. S26).
Although the island has a short rainy
season, the presence of fog during the
summer months helps to reduce drought
stress for many plant species (Halvorson
et al. 1988, p. 111; Fischer et al. 2009,
p. 783). However, fog projections remain
uncertain (Field et al. 1999, pp. 21–22).
There is also substantial uncertainty in
precipitation projections, and relatively
little consensus concerning
precipitation patterns and projections
for southwestern California (PRBO 2011,
p. 40). San Clemente Island typically
gets less rainfall than the neighboring
mainland areas (Tierra Data 2005, p. 4).
Therefore, the models may
underestimate the effects of
precipitation changes on island
vegetation. Additionally,
Malacothamnus clementinus typically
occurs on the western side of the island,
which is a less productive and drier
climate (Tierra Data 2005, p. 7). Less
rainfall and warmer air temperatures
could limit the range of M. clementinus,
although there is no direct research on
the effects of climate change on the
species.
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The impacts of predicted future
climate change to Malacothamnus
clementinus remain unclear. The best
available information does not provide
sufficient certainty on how and when
climate change will affect the species,
the extent of average temperature
increases in California, or potential
changes to the level of threat posed by
fire on San Clemente Island. The most
recent literature on climate change
includes predictions of hydrological
changes, higher temperatures, and
expansion of drought areas (IPCC 2007a,
pp. 1–18). While we recognize that
climate change is an important issue
with potential effects to listed species
and their habitats, the best available
information does not inform accurate
predictions regarding its impacts to M.
Clementinus at this time.
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Genetic Diversity
As discussed in the Background
section, Malacothamnus clementinus
has low genetic variability when
compared with other island endemic
plant species (Helenurm 1999, p. 40).
This lack of diversity could hinder the
species’ ability to persist through a
fluctuating environment or stochastic
event. Although the number of known
occurrences of M. clementinus has
increased from 3 to 11 since its listing,
there appears to be little gene flow
among occurrences, and each comprises
a relatively small number of genetically
distinct individuals (Junak and Wilken
1998, p. 290; Helenurm 1999, p. 39).
Genetic fitness typically decreases with
decreasing genetic variation and
population size (Leimu et al. 2006, p.
942). Specifically, small population size
and low levels of genetic interchange
make M. clementinus occurrences
particularly vulnerable to inbreeding
depression and loss of genetic
variability due to genetic drift (the
change in the frequency of appearance
of a gene in a population of organisms
due to chance or random events)
(Ellstrand and Elam 1993, p. 217).
Genetic analysis suggests that M.
clementinus has very low genetic
variation at both the species and
population levels (Helenurm 1997, p.
50; Helenurm 1999, p. 39), even far
below average when compared to other
endemic plant species (Helernurm 1999,
p. 39). Low genetic variation may affect
the ability of occurrences to adjust to
novel or fluctuating environments,
survive stochastic events, or maintain
high levels of reproductive performance
(Huenneke 1991, p. 40). This constitutes
a species and rangewide threat for
which there is no immediate solution or
amelioration.
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Malacothamnus clementinus
occurrences have low seed production,
suggesting the existence of a selfincompatibility mechanism (Helenurm
1997, p. 50; Junak and Wilken 1998, p.
291; Helenurm 1999, p. 39). Low seed
production may also be the result of low
pollinator visitation and, in
combination with low genetic diversity,
could contribute to observed low
recruitment in populations (Huenneke
1991, pp. 37–40; Junak and Wilken
1998, p. 291; Helenurm 1999, pp. 39–
40). Although studies show that patches
of plants are not made up of a single
clonal individual (clump of genetically
identical stems resulting from vegetative
reproduction), it is still possible that
patches comprise closely related
individuals that share alleles controlling
their ability to successfully reproduce
with each other (Helenurm 1999, pp.
39–40). Although this species has
apparently expanded its range from that
known at the time of listing and
persisted through habitat disturbance, it
may still remain susceptible to
extirpation from low genetic variation
and genetic drift. A reduction in
occurrence size through years of grazing
could have substantially lowered
genetic variation (Helenurm 2005, p.
1221), which could decrease genetic
fitness and compromise the species’
ability to adapt to stochastic events
(Huenneke 1991, p. 40). The apparent
loss of genetic diversity resulting in
current low genetic variation and low
recruitment constitute a species and
rangewide threat to M. clementinus.
Summary of Factor E
Threats associated with trampling
from military activities, fire, climate
change, and low genetic diversity
continue to impact Malacothamnus
clementinus at all of the 11 occurrences
on San Clemente Island. Trampling and
crushing of individual plants are likely
to increase at four occurrences (36
percent) in association with increased
training levels on the island. However,
this taxon has expanded its distribution
on the island and the Navy is
implementing conservation measures
that will improve conditions for M.
clementinus. Military training activities
have the potential to ignite fires within
occurrences or that spread to habitat
supporting this species. In preparation
for these training efforts, the Navy
implemented a MOFMP to limit the
frequency of fires escaping from the
Impact Areas, although suppression
likely will not occur within the
boundaries of the Impact Areas. Climate
change may also likely influence M.
clementinus, though the effects are
largely unknown. The genetic fitness of
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M. clementinus may be threatened by
low genetic diversity and small
population size. The threats described
here affect all of the occurrences of M.
clementinus both now and in the future;
therefore, these threats also affect its
recovery.
Combination of Factors—
Malacothamnus clementinus
A species may be affected by more
than one threat in combination. Within
the preceding review of the five listing
factors, we have identified multiple
threats that may have interrelated
impacts on Malacothamnus clementinus
(these interrelated impacts also occur
for Acmispon dendroideus var. traskiae
and Castilleja grisea). For example, fires
(Factor A and E) may be more intense
or frequent in the habitat if there are
greater amounts of nonnative grass
(Factor A) present in the vegetative
community. Similarly, fires (Factor A
and E) also may become more frequent
if the climate changes (Factor E) into a
drier, hotter environment. The
movement of troops and vehicles
(Factor E) and land use (Factor A) can
also create more disturbance and
erosion (Factor A) in M. clementinus’
habitat (as well as A. d. var. traskiae and
C. grisea habitat). The historical past on
San Clemente is an illustration of
interacting threats: Nonnative
herbivores (Factor C) ate and killed
much of the vegetation, causing greater
impacts of erosion (Factor A) on the
island. Thus, the species’ productivity
may be reduced because of these threats,
either singularly or in combination.
However, it is not necessarily easy to
determine (nor is it necessarily
determinable) whether a particular
threat is the primary threat having the
greatest effect on the viability of the
species, or whether it is exacerbated by
or working in combination with other
threats to have cumulative or synergistic
effects on the species. While the
combination of factors is a threat to the
existence of M. clementinus, we are
unable to determine the magnitude or
extent of cumulative or synergistic
effects of the combination of factors on
the viability of the species at this time.
Acmispon dendroideus var. traskiae
(San Clemente Island lotus)
In the 2007 status review, we
acknowledged that the predominant
threat at listing (grazing and rooting
from feral herbivores) was ameliorated
with the removal of goats and pigs from
the island in 1992 (USFWS 2007b, pp.
1–22). Threats to Acmispon
dendroideus var. traskiae identified in
the 2007 status review include: (1)
Erosion, (2) nonnative species, (3) fire,
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(4) land use, (5) access to SHOBA, and
(6) hybridization. Impacts from erosion,
nonnatives, fire, and land use are
discussed below under Factor A, and
hybridization is discussed under Factor
E below. As discussed above, access to
SHOBA is not considered a threat,
though it limits our ability to assess all
occurrences of the taxon reviewed here.
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Factor A. The Present or Threatened
Destruction, Modification, or
Curtailment of Its Habitat or Range
The final listing rule (42 FR 40682;
August 11, 1977) identified the
following threats to Acmispon
dendroideus var. traskiae: Habitat
alteration and destruction, competition
from nonnative species, and direct
predation caused by nonnative
herbivores (goats and pigs). The
vegetation on San Clemente Island has
rebounded, and the status of many rare
plant occurrences, including A. d. var.
traskiae, has improved with the final
removal of herbivores in 1992 (Junak
and Wilken 1998, p. 18; Junak 2006a,
pers. comm.). Although the principle
threat to A. d. var. traskiae identified in
the final listing rule has been
eliminated, erosion as a result of
overgrazing and invasive nonnative
plants remain ongoing threats to habitat
of A. d. var. traskiae. Habitat alteration
and disturbance from the Navy’s use of
the island for military operation and
training were identified as additional
threats to the habitats occupied by A. d.
var. traskiae in the Recovery Plan and
the 2007 status review (USFWS 1984,
pp. 58–63; USFWS 2007b, pp. 11, 12).
Additional threats recognized since
listing include land use by military
training activities, and fire. As outlined
below, we discuss impacts of the
following threats that affect the habitat
or range of A. d. var. traskiae: (1) Land
use, (2) erosion, (3) nonnative plants,
and (4) fire.
Land Use
Eight of 29 Acmispon dendroideus
var. traskiae occurrences (28 percent;
Eagle Canyon, Bryce Canyon, North
Mosquito Cove, Canchalagua Canyon,
Thirst Canyon, Cave Canyon, Horse
Canyon, and Pyramid Head) occur
within SHOBA, where impacts are more
likely. Most of the land area of the
SHOBA serves as a buffer from the
Impact Areas, although military training
in parts of SHOBA could result in
habitat alteration due to OHV and largescale troop movements through the
military impact and training areas (IOA
and AVMA). Most of the occurrences
within SHOBA are located along the
eastern escarpment, which should
provide a level of protection from
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training impacts. Large-scale troop
movements are less likely in this area,
because of the extreme slope of the
escarpment. Training impacts may
become difficult to assess and manage
with the recent closure of the eastern
escarpment due to unexploded
ordnance.
Four of 29 of A. d. var. traskiae
occurrences (14 percent; Canchalagua
Canyon, Middle Island Plateau, North
Mosquito Cove, and Eagle Canyon) are
within or partially within the IOA and
may experience direct impacts, while
nine occurrences (31 percent; Upper
Middle Ranch Canyon, Warren Canyon,
Horton Canyon, Upper Wallrock
Canyon, Tota Canyon, Lemon Tank
Canyon, Larkspur Canyon, Chamish
Canyon, and North Island Terraces) are
within 1,000 ft (305 m) of the IOA, and
could experience diffuse or accidental
impacts associated with troop
movement. These areas near the IOA are
at less risk of disturbance than the
occurrences within the IOA, and would
only be likely to sustain diffuse or
accidental impacts to the habitat. While
the increase in military training could
affect the species, the Navy through
implementation of the INRMP will
avoid and minimize impacts to
individuals or occurrences of A. d. var.
traskiae (as a rare plant species), to the
extent practicable while meeting
operational needs (Navy 2002, p. 1–2)
(see above discussion on Land Use
under Malacothamnus clementine—
Factor A).
Because of the taxon’s close proximity
to Navy facilities, military activities
have the potential to impact habitat at
one of the largest known occurrences of
Acmispon dendroideus var. traskiae,
near Wilson Cove. All construction,
maintenance, and training activities in
the Wilson Cove area go through a site
approval request process. Through this
process, the areas are assessed to see if
the activities will potentially impact any
listed species, including A. d. var.
traskiae. Part of this occurrence is
within a TAR where tactical training
and movement are projected to occur,
possibly causing habitat damage
through troop traffic (USFWS 2008, pp.
119–120). Work was done recently at
Wilson Cove that affected A. d. var.
traskiae, and the Navy assessed the
impact to be a loss of habitat occupied
by 50 plants. The Navy worked to
salvage plant material and outplant back
to the site. Thus far, this outplanting has
been successful, the habitat has
rebounded, and more plants are present
in the area than before the work was
done (Munson 2011a, pers. comm.).
Twenty-four of 29 occurrences (83
percent) of A. d. var. traskiae are located
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outside of heavily impacted training
areas. Though five occurrences (17
percent; Wilson Cove, Canchalagua
Canyon, Middle Island Plateau, North
Mosquito Cove, and Eagle Canyon) are
partially or wholly within the
boundaries of an IOA or TAR, many of
the impacts to these occurrences would
be diffuse, and are unlikely to have a
high impact on the species’ habitat.
Although land use is likely to impact A.
d. var. traskiae habitat, the Navy has
demonstrated its commitment to help
conserve and manage listed species on
the island. Land use appears to pose a
high-magnitude threat to the habitat of
a small percentage of the occurrences of
A. d. var. traskiae on San Clemente
Island.
Erosion
Erosion and associated soil loss
caused by browsing of feral goats and
rooting of feral pigs likely modified the
island’s habitat (Navy 2002, p. 1–14).
Defoliation from overgrazing increased
erosion over much of San Clemente
Island. In the INRMP, erosion was
identified as a threat to the canyon
woodland habitat and maritime desert
scrub where Acmispon dendroideus var.
traskiae occurs (Navy 2002, p. 4–3).
Gullying and other processes may
concentrate surface runoff to unnatural
levels, leading to accelerated erosion in
the canyons below (Tierra Data Inc.
2007, p. 6). Acmispon dendroideus var.
traskiae occurs within steep canyon
areas where such concentration of flows
may be a threat to its habitat or range.
Although more vegetative cover is
now present than at the time of listing,
erosion is still a threat to the recovery
of Acmispon dendroideus var. traskiae,
especially in areas where it grows in
close proximity to roads. The Navy
studied the potential for erosion from
several proposed military activities
(Tierra Data Inc. 2007, pp. 1–45,
Appendices). Increased military
activities, especially where the taxon is
located within training area boundaries
(IOA), are expected to cause erosion
through soil compaction or other soil
disturbances in occupied habitat areas
associated with roadways or vehicle
maneuver areas (Tierra Data Inc. 2007,
p. 12). Four of 29 A. d. var. traskiae
occurrences (14 percent; Middle Island
Plateau, Canchalagua Canyon, North
Mosquito Cove, and Eagle Canyon) are
within or partially within the IOA, and
are likely to be further impacted by
erosion (Table 1). Three of these
occurrences (Canchalagua Canyon,
North Mosquito Cove, and Eagle
Canyon) are along the eastern
escarpment, which has recently been
closed to biological monitoring due to
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unexploded ordnance. The threat of
erosion to this area will be difficult to
assess if the closure remains into the
future. Nine of 29 occurrences (31
percent; Upper Middle Ranch Canyon,
Warren Canyon, Horton Canyon, Upper
Wallrock Canyon, Tota Canyon, Lemon
Tank Canyon, Larkspur Canyon,
Chamish Canyon, and Northern Island
Terraces) are near the IOA (within 1,000
ft (305 m)), and could experience
erosion from nearby training activities.
Roads can concentrate water flow
causing incised channels and erosion of
slopes (Forman and Alexander 1998, pp.
216–217). This increased erosion
around roads can degrade habitat,
especially along the steep canyons
associated with the eastern escarpment
of the island. Nine of 29 Acmispon
dendroideus var. traskiae occurrences
(31 percent; Eel Cove Canyon, Seal Cove
Terraces, Lemon Tank Canyon, Wilson’s
Cove, North Wilson’s Cove, Upper
Middle Ranch Canyon, Eagle Canyon,
North Mosquito Cove, and Canchalagua
Canyon) are within 500 ft (152 m) of a
road on the island (Forman and
Alexander 1998, p. 217). These
occurrences could be subject to diffuse
disturbance and road effects that
degrade habitat quality. The largest
known occurrence of A. d. var. traskiae,
Wilson Cove, occurs on gradual or steep
slopes where erosion is evident (USFWS
2008, p. 117). Military activities in this
area have the potential to adversely
affect the species habitat due to the
species’ proximity to Navy facilities and
the level of human activity and traffic in
the area.
The Navy incorporates erosion control
measures into all site feasibility studies
and project planning, design, and
construction to minimize the potential
to exacerbate existing erosion and avoid
impacts to listed species (Munson
2011a, pers. comm.). The INRMP
requires that all projects include erosion
conservation work and associated
funding (Navy 2002, p. 4–89). These
conservation actions include best
management practices for construction
and engineering, choosing sites that are
capable of sustaining disturbance with
minimum soil erosion, and stabilizing
disturbed sites with native plants (Navy
2002, pp. 4–89—4–91). Additionally,
large-scale island-wide maneuvers with
assault vehicles have been postponed
until an erosion control plan is drafted
and implemented. The erosion control
plan for San Clemente Island is being
developed to reduce the impacts of
erosion to Acmispon dendroideus var.
traskiae habitat in areas likely to
experience increased and expanded
military operations (Munson 2011a,
pers. comm.). This erosion control plan
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will address military operations
associated with the IOA, AVMA, and
AFP; however, since the plan is not yet
finalized, it does not currently
ameliorate the noted threats from
erosion.
The processes and results of erosion
are threats to the habitat of Acmispon
dendroideus var. traskiae, particularly
to 17 of 29 occurrences (59 percent;
Middle Island Plateau, Canchalagua
Canyon, North Mosquito Cove, Eagle
Canyon, Upper Middle Ranch Canyon,
Warren Canyon, Horton Canyon, Upper
Wallrock Canyon, Tota Canyon, Lemon
Tank Canyon, Larkspur Canyon,
Chamish Canyon, North Island Terraces,
Eel Cove Canyon, Seal Cove Terraces,
Wilson Cove, and North Wilson Cove)
that are within an IOA, within 1,000 ft
(305 m) of an IOA, or within 500 ft (152
m) of a road. Erosion may lead to overall
habitat degradation and the loss of
individuals or groupings of plants in a
given area. However, this taxon has
persisted despite current levels of
erosion. The processes and results of
erosion are island-wide threats to the
habitat or range of A. d. var. traskiae,
particularly to the 17 occurrences in or
adjacent to military training areas or
roads. Therefore, erosion is still
considered a threat to the existence of
A. d. var. traskiae.
Nonnative Species
One of the threats to Acmispon
dendroideus var. traskiae identified in
the final listing rule is the spread of
nonnative plants into its habitat (42 FR
40682). Nonnative plants can diminish
the abundance or survival of native
species by altering natural ecosystem
processes such as fire regimes, nutrient
cycling, hydrology, and energy budgets,
and competing with them for water,
space, light, and nutrients (Zink et al.
1995, p. 307; Brooks 1999, pp. 16–17;
Mack et al. 2000, p. 689). Nonnative
species of particular concern include
Avena barbata (slender oat), Bromus
spp., Foeniculum vulgare, and Brassica
tournefortii, which have already
invaded the habitat of most A. d. var.
traskiae occurrences. Another nonnative
species, Carpobrotus edulis (iceplant),
also appears to be hindering the
recovery of A. d. var. traskiae (Allan
1999, p. 92). This nonnative species
occupies large areas of Wilson Cove
where it may alter the habitat (Allan
1999, p. 92) by changing vegetation
structure and creating an environment
less hospitable to A. d. var. traskiae.
Annual grasses vary in abundance with
rainfall, potentially changing the
vegetative community from shrubs to
grasses and increasing the fuel load in
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wet years (see Factor A—Fire section
below).
Although previous invasions of
nonnatives probably occurred through
introductions in grazing fodder, current
nonnative species invasions are
typically introduced by military
activities and training on the island.
Nonnative plants constitute a rangewide
threat to the habitat of all native plants
on San Clemente Island, including all
occurrences of Acmispon dendroideus
var. traskiae. Nine of 29 occurrences (31
percent; Eel Cove Canyon, Seal Cove
Terraces, Lemon Tank Canyon, Wilson’s
Cove, North Wilson’s Cove, Upper
Middle Ranch Canyon, Eagle Canyon,
North Mosquito Cove, and Canchalagua
Canyon) are within 500 ft (152 m) of
roads on the island, and may be subject
to diffuse disturbance and road effects
that degrade habitat quality along the
road (Forman and Alexander 1998, p.
217). Roadsides tend to provide
conditions (high disturbance, seed
dispersal from vehicles, ample light and
water) preferable to nonnative species
(Forman and Alexander 1998, p. 210).
Potential impacts from nonnative
plants are minimized through annual
implementation of the Navy’s islandwide nonnative plant control program
(O’Connor 2009b, pers. comm.; Munson
2011a, pers. comm.). The focus of the
nonnative plant species program is to
control plants on the island with the
potential to adversely impact habitat of
federally listed species (see above
discussion on Nonnative Species under
Factor A—M. clementinus). Although
nonnative plants will continue to pose
a risk to the habitat or range of
Acmispon dendroideus var. traskiae, the
Navy has taken steps to curtail habitat
and plant community alteration from
nonnative plants. To reduce the
potential for transport of nonnative
plants to the island, military and
nonmilitary personnel inspect tactical
ground vehicles and remove any visible
plant material, dirt, or mud prior to
going on San Clemente Island (USFWS
2008, p. 63). This precaution helps to
control the movement of nonnative
plants to the island, but once on the
island, nonnative plants easily spread
through the movement of vehicles from
one area to another.
Acmispon dendroideus var. traskiae
has persisted on the island and, despite
the continued risk of encroachment to
habitat by nonnatives, the range of this
taxon has expanded from 6 to 29
occurrences since listing. Impacts from
nonnative plants may be a persistent,
but low-level, threat to A. d. var.
traskiae habitat.
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Fire
Fire was not considered a threat to
habitat occupied by Acmispon
dendroideus var. traskiae at the time of
listing (42 FR 40682; August 11, 1977).
Since that time, however, over 50
percent of the island has experienced at
least one wildfire (Navy 2002, Map 3–
3, p. 3–32), and some habitat has burned
multiple times with very short intervals
between fires (Navy 2002, Map 3–4, p.
3–33). The majority of fires are
concentrated in SHOBA, potentially
impacting habitat of 8 of 29 occurrences
(28 percent; Eagle Canyon, Bryce
Canyon, North Mosquito Cove,
Canchalagua Canyon, Thirst Canyon,
Cave Canyon, Horse Canyon, and
Pyramid Head) where military training
exercises within Impact Areas I and II
employ live ordnance and incendiary
devices. However, fires are occasionally
ignited by activities north of SHOBA,
such as training activities near Eel Point
(possibly impacting Seal Cove Terraces
and Eel Cove Canyon occurrences)
(Navy 2002, Map 3–4, p. 3–33).
Increased fire frequency resulting
from intensified military uses could
lead to localized changes in vegetation
on San Clemente Island. The Navy
recently approved a significant
expansion in the number of locations
where live fire and demolition training
will take place (Navy 2008a, pp. 2–3—
2–38), including TAR north of SHOBA
(TAR 17—Eel Cove Canyon and Seal
Cove Terraces, and TAR 14 and 15—
Larkspur and Chamish Canyon). These
higher levels of training have not
occurred in recent history, and will
likely expand from current levels. In
addition to demolitions, certain
proposed munitions exercises involve
the use of incendiary devices, such as
illumination rounds, white
phosphorous, and tracer rounds, which
pose a high risk of fire ignition.
Additionally, smoke, flares, and
pyrotechnics are proposed for use
within TAR 11 (Wilson’s Cove) towards
the eastern shore, and expanded live fire
and demolition training is proposed
within TAR 16 (Middle Island Plateau)
towards the center of the island. It is
likely that the fire pattern on the island
will change in response to this increase
in ignition sources, with fires becoming
more common within and adjoining the
training areas north of SHOBA.
At the time of listing, fire was not
identified as a habitat threat because of
lack of fire history and the low intensity
of military training on the island. Since
that time, military training has
significantly increased, and we have
better records of the fire frequency on
the island. Approximately 14 of the 29
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occurrences (48 percent) (Wilson’s
Cove, Middle Island Plateau, Eagle
Canyon, Bryce Canyon, North Mosquito
Cove, Canchalagua Canyon, Thirst
Canyon, Cave Canyon, Horse Canyon,
Pyramid Head, Eel Cove Canyon, Seal
Cove Terraces, Larkspur Canyon, and
Chamish Canyon) of Acmispon
dendroideus var. traskiae fall within
areas that may be subject to recurrent
fire associated with military training
(Table 1). This includes locations that
fall within 1,000 ft (305 m) of TAR
where the Navy conducts live fire and
demolition training, and occurrences
within SHOBA (SHOBA serves as a
buffer for Impact Areas I and II). Fires
that escape designated training areas
may threaten habitat on other parts of
the island, though, because of the broad
distribution of the species, it is unlikely
that one fire could spread throughout
the entire range. The Navy’s
implementation of the MOFMP will
limit the frequency with which fires
escape impact areas and TAR. Through
the annual review process, the Navy
identifies mechanisms to reduce fire
return intervals within areas where this
taxon is concentrated (USFWS 2008, pp.
91–122). The Navy’s implementation of
an MOFMP will help to reduce the risk
of habitat conversion by fire, although
the habitat of A. d. var. traskiae could
be altered by increased fire frequency
and spread of nonnative grass. Although
the threat is ameliorated through the
MOFMP, fire remains an island-wide
threat to A. d. var. traskiae, particularly
to the 14 occurrences that fall within
areas that may be subject to recurrent
fire associated with military training.
until an erosion control plan is
completed. Natural resource managers
have been successful in decreasing the
prevalence of particularly destructive
nonnatives, such as Foeniculum
vulgare. Though increased impacts
associated with military training could
threaten the species, 24 of 29
occurrences (83 percent) of A. d. var.
traskiae fall outside of training areas
(IOA or TAR) where the most intensive
habitat disturbances are likely to occur.
While it is anticipated that military
training activities, erosion, nonnatives,
and fire will have ongoing impacts to
the taxon’s habitat, based on its
distribution and current and anticipated
conservation efforts, impacts from these
threats are reduced and minimized for
A. d. var. traskiae. Therefore, the threats
to the habitat of A. d. var. traskiae will
not likely impact most of the known
occurrences both now and into the
future.
Summary of Factor A
San Clemente Island was used for
sheep ranching, cattle ranching, goat
grazing, and pig farming from 1850 until
1934 (Navy 2002, pp. 3–4). The effects
of these grazers, which were not
completely removed from the island
until 1992, on the habitat and plants
were one of the original reasons for
classifying Acmispon dendroideus var.
traskiae as endangered in the 1977
listing rule (42 FR 40682). Currently, the
habitat of A. d. var. traskiae is
threatened by destruction and
modification caused by land use,
erosion, nonnative plants, and fire. To
help ameliorate these threats, the Navy
is implementing an MOFMP, an INRMP,
and an island-wide nonnative species
control program (Navy 2002, pp. 1–1–8–
12; USFWS 2008, pp. 1–237). The
MOFMP has been helpful in informing
strategic decisions for training using live
fire or incendiary devices. The Navy has
postponed major troop and assault
vehicle maneuvers across the island
Factor C. Disease or Predation
Grazing of feral goats and rooting of
feral pigs were considered a direct
threat to Acmispon dendroideus var.
traskiae in the final listing rule (42 FR
40682; August 11, 1977). As stated
above, however, nonnative mammalian
herbivores were removed from San
Clemente Island in 1992, and this threat
was ameliorated, as recognized in our
2007 status review (USFWS 2007b, p.
13). Currently, no other predators or
diseases on San Clemente Island are
known to pose a significant threat to A.
d. var. traskiae both now and in the
future.
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Factor B. Overutilization for
Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682;
August 11, 1977), the Service did not
identify any threats from
overutilization, and there is no new
information to indicate that
overutilization is a threat to Acmispon
dendroideus var. traskiae. Although
voucher herbarium specimens of A. d.
var. traskiae and seeds have been
collected for research and seed banking,
overutilization of A. d. var. traskiae for
any purpose is not currently considered
a threat nor is expected to be in the
future.
Factor D. Inadequacy of Existing
Regulatory Mechanisms
The Act requires us to examine the
adequacy of existing regulatory
mechanisms with respect to those
existing and foreseeable threats that may
affect Acmispon dendroideus var.
traskiae. The inadequacy of existing
regulatory mechanisms was not
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considered a threat to A. d. var. traskiae
at listing (42 FR 40682; August 11,
1977). Since it was listed as endangered,
the Act has been and continues to be the
primary Federal law that affords
protection to A. d. var. traskiae. The
Service’s responsibilities in
administering the Act include sections
7, 9, and 10 (see above discussion in the
Malacothamnus clementinus—Factor D
section for more information on the
Service’s responsibilities for all three
species that are the subject of this
Finding). Critical habitat has not been
designated or proposed for this taxon.
Listing A. d. var. traskiae provided a
variety of protections, including the
prohibitions against removing or
destroying plants within areas under
Federal jurisdiction and the
conservation mandates of section 7 for
all Federal agencies. If A. d. var. traskiae
were not listed, these protections would
not be provided. Thus, we must
evaluate whether other regulatory
mechanisms would provide adequate
protections absent the protections of the
Act.
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Other Federal Protections
National Environmental Policy Act
(NEPA)
All Federal agencies are required to
adhere to the National Environmental
Policy Act (NEPA) of 1970 (42 U.S.C.
4321 et seq.) for projects they fund,
authorize, or carry out. The Council on
Environmental Quality’s regulations for
implementing NEPA (40 CFR parts
1500–1518) state that agencies shall
include a discussion on the
environmental impacts of the various
project alternatives (including the
proposed action), any adverse
environmental effects that cannot be
avoided, and any irreversible or
irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA
itself is a disclosure law, and does not
require subsequent minimization or
mitigation measures by the Federal
agency involved. Although Federal
agencies may include conservation
measures for Acmispon dendroideus
var. traskiae as a result of the NEPA
process, any such measures are typically
voluntary in nature and are not required
by the statute. NEPA does not itself
regulate activities that might affect A. d.
var. traskiae, but it does require full
evaluation and disclosure of
information regarding the effects of
contemplated Federal actions on
sensitive species and their habitats. On
San Clemente Island, the Navy must
meet the NEPA requirements for actions
significantly affecting the quality of the
human environment. Typically, the
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Navy prepares Environmental
Assessments and Environmental Impact
Statements on operation plans and new
or expanding training actions. Absent
the listing of A. d. var. traskiae, we
would expect the Navy to continue to
meet the procedural requirements of
NEPA for its actions, including
evaluating the environmental impacts to
rare plant species and other natural
resources. However, as explained above,
NEPA does not itself regulate activities
that might affect A. d. var. traskiae.
Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670)
authorizes the Secretary of Defense to
develop cooperative plans with the
Secretaries of Agriculture and the
Interior for natural resources on public
lands. The Sikes Act Improvement Act
of 1997 requires Department of Defense
installations to prepare INRMPs that
provide for the conservation and
rehabilitation of natural resources on
military lands consistent with the use of
military installations to ensure the
readiness of the Armed Forces. An
INRMP is a plan intended ‘‘* * * to
guide installation commanders in
managing their natural resources in a
manner that is consistent with the
sustainability of those resources while
ensuring continued support of the
military mission’’ (Navy 2002, p. 1–1).
INRMPs are developed in coordination
with the State and the Service, and are
generally updated every 5 years.
Although an INRMP is technically not a
regulatory mechanism because its
implementation is subject to funding
availability, it is an important guiding
document that helps to integrate natural
resource protection with military
readiness and training.
San Clemente Island Integrated Natural
Resources Management Plan (INRMP)
Pursuant to the Sikes Act, the Navy
adopted an INRMP for San Clemente
Island that identifies multiple objectives
for protecting Acmispon dendroideus
var. traskiae and its habitat to help to
reduce threats to this taxon (Navy 2002).
The INRMP discloses actions through
the NEPA process and to comply with
such legislation and regulations as the
Endangered Species Act, Federal
Noxious Weed Act of Act of 1974 (7
U.S.C. 2801), the Comprehensive
Environmental Response,
Compensation, and Liability Act (42
U.S.C. 9601), the Resources
Conservation and Recovery Act (42
U.S.C. 6901), and Soil Conservation Act
(16 U.S.C. 3B) (see above discussion on
INRMPs under Malacothamnus
clementinus—Factor D). Natural
resource objectives of relevance to the
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protection of A. d. var. traskiae in the
INRMP include: ‘‘Protect, monitor, and
restore plants and cryptograms in order
to manage for their long-term
sustainability on the island’’ (Navy
2002, p. 4–39). The INRMP specifically
includes the following objectives for A.
d. var. traskiae management: removal of
nonnatives, restoration of native grasses
and scrub species, monitoring of the
species, studies of response to fire, and
studies and inventory of insect
pollinators (Navy 2002, p. D–11). To
date, multiple INRMP management
strategies have been implemented for
the conservation of A. d. var. traskiae.
Other INRMP strategies that target the
plant communities within which this
species occurs include: Controlling
erosion, with priority given to locations
where erosion may be affecting listed
species; producing a new vegetation
map; reducing nonnative plant cover
from 1992–1993 baseline levels;
managing the size and intervals of fires;
experimenting with fire management to
improve native plant dominance while
protecting sensitive plant occurrences;
and conducting genetic and biological
studies of A. d. var. traskiae.
The MOFMP, Erosion Control Plan,
and nonnative plant species control
conducted on the island are discussed
above under Acmispon dendroideus var.
traskiae—Factor A. The Present or
Threatened Destruction, Modification,
or Curtailment of Its Habitat or Range.
Absent listing under the Act, the Navy
would still be required to develop and
implement INRMPs under the Sikes Act.
However, as noted under the other
factors, while the INRMP helps to
ameliorate threats and provides some
protection for A. d. var. traskiae
occurrences, those occurrences within
Impact Areas or operationally closed
areas may not benefit from the
conservation measures. While the
INRMP has reduced the severity of
threats and contributed to conservation
of the species, it still allows for land use
consistent with military readiness and
training. Thus, Navy activities will
continue to impact A. d. var. traskiae as
described under Factor A.
State Protections
Since the time of listing, Acmispon
dendroideus var. traskiae has benefited
from additional State protections under
the Native Plant Protection Act (NPPA)
and California Endangered Species Act
(CESA; listed 1982). However, the range
of A. d. var. traskiae is restricted to a
Federal military installation, so listing
under NPPA and CESA may only afford
protection to this species in rare
instances when the lead agency is a
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non-Federal agency or when proposed
activities fall under other State laws.
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Summary of Factor D
The regulatory mechanisms outlined
above provide for adequate conservation
of Acmispon dendroideus var. traskiae.
In continuance of a long history of
cooperative conservation efforts, the
Navy also implements several
conservation actions that benefit this
plant taxon. The Navy has implemented
a MOFMP to reduce the risk of fire on
the island and a nonnative plant species
control program. In response to the
conservation actions proposed and the
current status of the listed taxon, we
issued a non-jeopardy biological
opinion on the Navy’s MOFMP. The
provisions included in the San
Clemente Island INRMP provide
protection of A. d. var. traskiae
occurrences and adaptive management
of its habitat in order to help address
threats to the plant from military
activities and nonnative plants,
although implementation may not be
extended to occurrences in
operationally closed areas. A. d. var.
traskiae occurrences are afforded
protection through Federal and military
mechanisms, and thus the inadequacy
of existing regulatory mechanisms is not
considered a current threat to the
species. However, in the absence of the
Act, the existing regulatory mechanisms
are not adequate to conserve A. d. var.
traskiae throughout its range both now
and in the future.
Factor E. Other Natural or Manmade
Factors Affecting Its Continued
Existence
The 1977 listing rule identified
nonnatives as a threat to Acmispon
dendroideus var. traskiae under Factor
E (42 FR at 40684; August 11, 1977). In
this 5-factor analysis, impacts from
nonnative plants are discussed above
under Factor A as a threat to habitat.
Other threats attributable to Factor E
that have been identified since listing
include: (1) Movement of vehicles and
troops, (2) fire, (3) climate change, and
(4) hybridization. Factor E addresses
threats to individuals of the species,
rather than the habitat modification
threats that are discussed in Factor A.
Therefore, while some threats are
discussed in both sections, in this
section we are focusing on the direct
impacts to individuals of A. d. var.
traskiae.
Movement of Vehicles and Troops
Military training activities within
SWAT, TAR, and the IOA often entail
the movement of vehicles and troops
over the landscape, which has the
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potential of trampling or crushing
individual plants (for discussion of
SWAT, TAR, and IOA, see above under
Malacothamnus clementinus—Factor
E). Based on the distribution of
Acmispon dendroideus var. traskiae
occurrences, and type of troop
movements likely to occur, impacts due
to trampling and crushing are
considered a low-level threat to its longterm persistence, and are most likely to
occur occasionally within the IOA and
TAR. Approximately 13 of 29
occurrences (45 percent; Wilson Cove,
Canchalagua Canyon, Middle Island
Plateau, North Mosquito Cove, Eagle
Canyon, Larkspur Canyon, Chamish
Canyon, Lemon Tank Canyon, Seal Cove
Terraces, Eel Cove Canyon, Middle
Wallrock Canyon, Warren Canyon, and
North Island Terraces) of A. d. var.
traskiae are partially or wholly within
the boundaries of a training area (IOA,
TAR, or SWAT). Many of these
occurrences are in areas that are not
readily accessible to vehicles and
troops. Loss of individual plants from
proposed increases in troop and vehicle
movements within SWAT, TAR, and the
IOA is likely to increase, though this
will not significantly impact the
survival and recovery of this taxon
because of the diffuse nature of this
threat and the location of much of the
species along the eastern escarpment,
away from military training activities
(USFWS 2008, pp. 113–122).
Fire
Although not specifically mentioned
in the listing rule, intense or frequent
fires threaten individuals at 14 of 29 (48
percent) of Acmispon dendroideus var.
traskiae occurrences. In the Factor A
discussion above, we addressed impacts
of fire on the habitat. This section
covers the discrete threat to individuals
or occurrences of A. d. var. traskiae. As
discussed in the Background section, it
is unknown if A. d. var. traskiae is
adapted to periodic fires, though it is
likely that this taxon is resilient to
occasional fires (Navy 2002, p. D–10;
Tierra Data Inc. 2005, p. 80). Adult
plants have been lost in fires, but
subsequent recruitment from the seed
bank resulted in replacement numbers
of juvenile plants (Tierra Data Inc. 2005,
p. 80). Aside from this observation, the
relationship between fire and the life
history of A. d. var. traskiae has not
been adequately studied. Additionally,
the species’ tolerance to fire frequency
is unknown. In areas that burn more
frequently, the seed bank may become
depleted if individuals burn before they
produce seeds. Although an individual
plant has the ability to produce vast
amounts of seed, the seed bank must be
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replenished regularly for the species to
persist (Junak and Wilken 1998, p. 257).
Acmispon dendroideus var. traskiae
occurs in some areas of the island that
may experience elevated fire frequency,
such as in SHOBA and surrounding Eel
Point (Eagle Canyon, Bryce Canyon,
North Mosquito Cove, Canchalagua
Canyon, Thirst Canyon, Cave Canyon,
Horse Canyon, Pyramid Head, Seal Cove
Terraces, and Eel Cove Canyon)
(discussed in A. d. var. traskiae—Factor
A). Increased fire frequency from
intensified military use could also lead
to localized changes in vegetation,
resulting in indirect adverse effects on
A. d. var. traskiae. The potential for
frequent fire at many of the occurrences
within SHOBA is reduced by their
location on the eastern escarpment of
the island, away from Impact Areas I
and II. This threat may become difficult
to assess with the recent closure of the
eastern escarpment area due to
unexploded ordnance. The Navy’s fire
management practices are anticipated to
minimize frequency of ignitions as well
as the spread of fires (as described above
in Factor A).
The Navy conducts annual reviews of
fire management and fire occurrence
that allow for adaptive management.
These measures should minimize loss of
individuals or occurrences of A. d. var.
traskiae due to fire. At the present time,
fire management does not pose a threat
as fuelbreak locations have not been
proposed in the vicinity of this taxon.
Although the Navy has planned and
implemented fire management, fire
threatens 14 occurrences of Acmispon
dendroideus var. traskiae. Due to the
continued impacts of fire within
SHOBA, fire remains a Factor E threat
to the existence of A. d. var. traskiae.
Climate Change
For general information regarding
climate change impacts, see the climate
change discussion under
Malacothamnus clementinus—Factor E
above. Since listing of Acmispon
dendroideus var. traskiae, the potential
impact of ongoing, accelerated climate
change has become a recognized threat
to the flora and fauna of the United
States (IPCC 2007a, pp. 1–52; PRBO
2011, pp. 1–68). San Clemente is located
in a Mediterranean climatic regime, but
with a significant maritime influence.
Climate change models indicate an
increase in average temperature for
southern California (see above
discussion on climate change under
Malacothamnus clementinus—Factor
E). San Clemente Island typically
receives less rainfall than neighboring
mainland areas (Tierra Data Inc. 2005, p.
4). Therefore, the models may
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understate the effects to vegetation on
the island. Less rainfall and warmer air
temperatures could limit the range of A.
d. var. traskiae, although there is no
direct research on the effects of climate
change on the species. Additionally,
changes in sea level and temperature
may be more acute on small islands, due
to their high vulnerability (surrounded
by ocean) and low adaptive capacity
(from limited size) (IPCC 2007b, p. 1).
The impacts of future climate change to
A. d. var. traskiae remain unclear. The
most recent literature on climate change
predicts hydrological changes, higher
temperatures, and expansion of drought
areas (IPCC 2007a, pp. 1–18). While we
recognize that climate change is an
important issue with potential effects to
listed species and their habitats, the best
available information does not facilitate
accurate predictions regarding the
effects to A. d. var. traskiae at this time.
Hybridization
As discussed above in the Background
section, Acmispon dendroideus var.
traskiae is known to hybridize with
Acmispon argophyllus var. argenteus. In
1990, Liston et al. (p. 240) confirmed
hybridization between co-occurring
populations of A. d. var. traskiae and A.
argophyllus var. argenteus in Wilson
Cove. At that time, they detected only
four hybrid individuals out of 38
individuals tested, and failed to detect
hybridization in another area of cooccurrence at the southern end of the
island. Although hybrid individuals
seem to be restricted to Wilson Cove
(Liston 1990, p. 240; Allan 1999, p. 91),
other unconfirmed hybrids (no genetic
testing done) have been observed
elsewhere on the island (Howe 2009b,
pers. comm.; Braswell 2011, pers. obs.).
Liston et al. (1990, pp. 240–243)
offered three hypotheses for the scarcity
of confirmed hybrid individuals. First,
hybrids may have reduced fitness and
be selected against, or be sterile and
thus unable to produce viable seed even
if backcrossed to the parent taxa. In this
situation, hybridization would not be a
threat to the genetic integrity of A.
dendroideus var. traskiae. Second and
conversely, if the fertile hybrids are
recent in origin (within the last 20
years), and because both parental taxon
are long-lived, woody perennials, few
hybrid individuals would be expected
due to the slower development and
lifespan of the species. If this is correct,
the genetic integrity of the largestknown occurrence of A. d. var. traskiae
in Wilson Cove might be at risk of
introgressive hybridization
(introduction of genes from one species
to another resulting in fertile hybrids).
Introgressive hybridization could lead to
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the loss of genetic variation and lower
fitness of A. d. var. traskiae. Finally, the
limited number of hybrid plants (four)
might be an artifact of the genetic testing
method used by the study.
Liston et al. (1990, p. 243) suggested
that there be further investigation of
these hypotheses before management
recommendations are made to the Navy.
Allan (1999, p. 91) stated that A. d. var.
traskiae should be ‘‘closely monitored.’’
Although the species has expanded its
range and numbers, hybridization with
A. a. var. argenteus remains a concern
at the largest of the 29 occurrences
(Wilson’s Cove), although unconfirmed
hybrids have been observed in other
areas of the island (e.g., Norton Canyon).
Hybridization may threaten, and could
diminish, the genetic diversity of the
species, especially in the already
disturbed occurrence of Wilson Cove
(Allan 1999, pp. 91–92). Additional
study is needed to determine the extent
and magnitude of this threat to A. d. var.
traskiae.
Summary of Factor E
Threats associated with military
activities, fire, climate change, and
hybridization continue to impact
Acmispon dendroideus var. traskiae at
18 of 29 occurrences (62 percent;
Wilson Cove, Canchalagua Canyon,
Middle Island Plateau, North Mosquito
Cove, Eagle Canyon, Larkspur Canyon,
Chamish Canyon, Lemon Tank Canyon,
Seal Cove Terraces, Eel Cove Canyon,
Middle Wallrock Canyon, Warren
Canyon, North Island Terraces, Bryce
Canyon, Thirst Canyon, Cave Canyon,
Horse Canyon, and Pyramid Head) on
San Clemente Island. Trampling and
crushing of individual plants are
probably incidental, but are likely to
increase with increases in training
levels on the island. However, the Navy
is implementing conservation measures
that will improve conditions for A. d.
var. traskiae, which has expanded its
distribution on the island. Military
training activities have the potential to
ignite fires that can spread to habitat
supporting this species, though the
majority of the occurrences are outside
of the areas designated for live fire and
demolition. In preparation for these
training efforts, the Navy implemented
a fire management plan within the
MOFMP that will limit the frequency of
fires escaping the Impact Areas.
Climate change may also likely
impact Acmispon dendroideus var.
traskiae, though the magnitude of this
threat is largely unknown. The genetic
integrity of A. d. var. traskiae may be
threatened by hybridization with A.
adsurgens var. argenteus at one of the
largest occurrences and requires further
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investigation. However, the extent and
prevalence of this threat is unknown,
and only confirmed in one of 29
occurrences. Overall, the threats
described under Factor E are either of
low magnitude, low likelihood, or
adequately managed, while the potential
overall threat of climate change remains
unknown across this taxon’s range.
Although these threats could directly
impact individuals of this taxon, we are
of the view that they will not impede
the recovery of A. d. var. traskiae now
or in the future.
Combination of Factors—Acmispon
dendroideus var. traskiae
A species may be affected by more
than one threat in combination. Within
the preceding review of the five listing
factors, we have identified multiple
threats that may have interrelated
impacts on the species (see also above
discussion on combination of factors—
Malacothamnus clementinus). The
species’ productivity may be reduced
because of these threats, either
singularly or in combination. However,
it is not necessarily easy to determine
(nor is it necessarily determinable)
whether a particular threat is the
primary threat having the greatest effect
on the viability of the species, or
whether it is exacerbated by or working
in combination with other potential
threats to have cumulative or synergistic
effects on the species. While the
combination of factors is a threat to the
existence of Acmispon dendroideus var.
traskiae, we are unable to determine the
magnitude or extent of cumulative or
synergistic effects of the combination of
factors on the viability of the species at
this time.
Castilleja grisea (San Clemente Island
Paintbrush)
In the 2007 status review, we stated
that the predominant threat at listing
(nonnative herbivores) was removed
from San Clemente Island in 1992
(USFWS 2007c, pp. 1–19). Additional
threats to Castilleja grisea identified in
2007 include: (1) Erosion, (2) nonnative
species, (3) fire, (4) land use, and (5)
access to SHOBA. The first four of these
threats are discussed below under
Factor A. As discussed previously,
access to SHOBA is not considered a
threat, though it limits our ability to
assess all occurrences of the taxon
reviewed here.
Factor A. The Present or Threatened
Destruction, Modification, or
Curtailment of Their Habitat or Range
Under this listing factor in the final
listing rule, we identified habitat
modification by browsing feral goats
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and rooting feral pigs as threats to
Castilleja grisea and other island taxa
(42 FR 40682). As discussed above, the
Navy removed the last of the remaining
feral goats and pigs from San Clemente
Island in 1992 (Kellogg and Kellogg
1994, p. 5), which resulted in improved
habitat conditions, and led to changes in
the cover of native and nonnative plants
on the island (Tierra Data Inc. 2005, pp.
i–96; Kellogg 2006, pers. comm.). The
Recovery Plan identified habitat
alteration and disturbance from the
Navy’s use of the island for military
operational and training needs as
additional threats to the habitats
occupied by C. grisea (USFWS 1984, pp.
58–63). Additional threats identified
since listing include alteration of San
Clemente Island habitats by military
training activities, fire, and fire
management. As outlined below, we
discuss the impacts of the following
threats that affect the habitat or range of
C. grisea: (1) Land use, (2) erosion, (3)
nonnative plants, (4) fire, and (5) fire
management.
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Land Use
The distribution of Castilleja grisea
includes a single occurrence in the
north of the island at West Cove, with
the remaining 28 occurrences
distributed across the southern 15.5 mi
(25 km) of the island, particularly along
the eastern escarpment. Training
activities approved in the MOFMP
would include substantial increases in
vehicle and foot traffic in the IOA,
leading to habitat modification. Ten of
the 29 occurrences (34 percent; plain
northeast of Warren Canyon, Larkspur
Canyon, Lemon Tank Canyon, Eagle
Canyon, Bryce Canyon, Horse Beach
Canyon, China Canyon, Knob Canyon,
Canchalagua Canyon, and Pyramid
Head) are within or partially within the
IOA and experience direct habitat
impacts, while three of 29 occurrences
(10 percent; Thirst Canyon, SHOBA
Boundary Occurrence, and Upper Horse
Canyon) are near the IOA (within 1,000
ft (305 m)) and could experience diffuse
or accidental impacts to C. grisea
habitat. Recent area closures due to
unexploded ordnance could make
habitat impacts from training difficult to
assess for several occurrences (34
percent; Nanny Canyon, Lemon Tank
Canyon, Eel Point, Eagle Canyon, Bryce
Canyon, Horse Beach Canyon, China
Canyon, Knob Canyon, Canchalagua
Canyon, and Pyramid Head) in the
future. Additionally, one occurrence
(West Cove) is within an Assault
Vehicle Maneuver Area (AVMA) and
could be subject to habitat disturbance
from vehicles.
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The southern portion of Castilleja
grisea’s distribution extends through
SHOBA where impacts to the habitat are
likely. Certain munitions exercises
involve the use of incendiary devices,
such as illumination rounds, white
phosphorous, and tracer rounds, which
pose a high risk of fire ignition (USFWS
2008, p. 11–13). Because of the elevated
risk of fire associated with training
activities, live and inert munitions fire
are targeted towards Impact Areas I and
II within SHOBA where bombardments
and land demolition are concentrated.
Four of 29 occurrences (14 percent;
China Canyon, Red Canyon, Upper
Chenetti Canyon and Horse Beach
Canyon) are within or partially within
Impact Areas. Currently, the Impact
Areas are closed to nonmilitary
personnel, so the plant’s status at these
four occurrences is unknown, as well as
the status of any conservation action
that would otherwise be expected to be
implemented in these areas (USFWS
2008, p. 50).
Also within SHOBA, an occurrence of
C. grisea is located in lower Horse Beach
Canyon, above Horse Beach. Horse
Beach (TAR 21) is used for special
warfare training activities that include
the use of live fire, illumination rounds,
and tracers. Training activities within
parts of SHOBA pose a direct threat to
habitat due to associated ground
disturbance and land demolition.
Sixteen of 29 C. grisea occurrences (55
percent) are located outside of heavily
impacted training areas, and 13
occurrences (45 percent; West Cove,
Plain northeast of Warren Canyon,
Larkspur Canyon, Lemon Tank Canyon,
Eagle Canyon, Bryce Canyon, China
Canyon, Knob Canyon, Canchalagua
Canyon, Pyramid Head, Red Canyon,
Upper Chenetti Canyon and Horse
Beach Canyon) are at least partially
within the boundaries of a training area
(IOA, TAR, AVMA, or Impact Area).
Although, within training areas, many
of the impacts to these 13 occurrences
would be diffuse and are unlikely to
have a high impact on the species. The
Navy has demonstrated their efforts to
help conserve and manage listed species
on the island through amelioration of
habitat impacts by military activities
through implementation of the MOFMP
and INRMP. Land use appears to pose
a high-magnitude threat to the habitat of
a small number of occurrences of C.
grisea on San Clemente Island.
Erosion
Erosion and associated soil loss
caused by browsing of feral goats and
rooting of feral pigs likely modified the
island’s habitat (Navy 2002, p. 1–14).
Defoliation from overgrazing on San
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Clemente Island resulted in increased
erosion over much of the island,
especially on steep slopes where
denuded soils can be quickly washed
away during storm events (Johnson
1980, p. 107; Navy 2002, pp. 1–14, 3–
9; Tierra Data Inc. 2007, pp. 6–7). There
may be residual impacts from historical
grazing, and vegetation may be slow to
recover and hold soil. In the INRMP,
erosion was identified as a threat to the
canyon woodland habitat and maritime
desert scrub, which is habitat for
Castilleja grisea (Navy 2002, pp. 4–3, 4–
12). The process of soil erosion can lead
to destruction of terraces, steep slopes,
and canyons that support the growth
and reproduction of C. grisea. Castilleja
grisea plants occur within steep canyon
areas where such concentration of water
flows may be a threat (Navy 2002, p. D–
23).
Increased military activities where
Castilleja grisea occurs within training
area boundaries are expected to increase
erosion associated with roadways,
through soil compaction and other soil
disturbances. The impacts from erosion
are anticipated along the ridgeline of the
eastern escarpment, affecting eight
occurrences (Pyramid Head, Knob
Canyon, Canchalagua Canyon, Bryce
Canyon, Eagle Canyon, Thirst Canyon,
SHOBA Boundary occurrence, and
Horton Canyon) (Tierra Data Inc 2007,
pp.12–18; Navy 2008a, p. G–8). Closure
of the eastern escarpment within
SHOBA due to unexploded ordnance
could make assessing this threat and
implementing conservation measures in
these eight occurrences difficult in the
future.
The Navy studied the potential for
erosion from several proposed military
activities (Tierra Data Inc. 2007, pp. 1–
45, Appendices). Approximately 13 of
29 Castilleja grisea occurrences (45
percent; West Cove, Plain northeast of
Warren Canyon, Larkspur Canyon,
Lemon Tank Canyon, Eagle Canyon,
Bryce Canyon, China Canyon, Knob
Canyon, Canchalagua Canyon, Pyramid
Head, Red Canyon, Upper Chenetti
Canyon, and Horse Beach Canyon) fall
partially or wholly within the
boundaries of a designated training area
(IOA, TAR, AVMA, or Impact Area), and
are likely to be impacted by erosion.
Fifteen occurrences of C. grisea are at
least partially within 500 ft (152 m) of
a road (paved or unpaved) (China
Canyon, Horse Beach Canyon, Pyramid
Head, Knob Canyon, Canchalagua
Canyon, Bryce Canyon, Eagle Canyon,
Upper Horse Canyon, Plain northeast of
Warren Canyon, Horton Canyon, Seal
Cove Terraces, Lemon Tank Canyon,
Larkspur Canyon, Terrace Canyon, and
West Cove) (Forman and Alexander
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1998, p. 217). These occurrences could
be subject to diffuse disturbance and
road effects that degrade the habitat
quality. Roads can concentrate water
flow, causing incised channels and
erosion of slopes (Forman and
Alexander 1998, pp. 216–217). This
increased erosion near roads can
degrade habitat, especially along the
steep canyons and ridges.
Along the eastern escarpment,
Castilleja grisea is found in steep
canyons in proximity to roads where it
may be vulnerable to runoff during
storm events (Navy 2008a, pp. G–4, G–
8). At the southern end of the species’
range, one occurrence is downslope
from Horse Beach Canyon Road along a
poorly maintained dirt road that is
proposed to serve as part of the Assault
Vehicle Maneuver Corridor. This
location is likely to have an elevated
risk from erosion (USFWS 2008, p. 99).
The Navy incorporates erosion control
measures into all site feasibility studies
and project design to minimize the
potential to exacerbate existing erosion
and avoid impacts to listed species
(Munson 2011a, pers. comm.). The
INRMP requires that all projects include
erosion conservation work (Navy 2002,
p. 4–89). These conservation actions
include best management practices,
choosing sites that are capable of
sustaining disturbance with minimum
soil erosion, and stabilizing disturbed
sites (Navy 2002, pp. 4–89–4–91). An
erosion control plan for San Clemente
Island is in the development stage, with
expectations to reduce impacts of
erosion where Castilleja grisea occurs in
areas with increased and expanded
military operations (Munson 2011a,
pers. comm.). This erosion control plan
will address military operations
associated with the IOA, AVMA and
AFP; however, since the plan is not yet
finalized, it does not currently
ameliorate the noted threats from
erosion.
In areas that will not be covered
under the erosion control plan, erosion
control measures are already being
incorporated into project designs to
minimize the potential to exacerbate
existing erosion and avoid impacts to
listed species (Munson 2011a, pers.
comm.). Additionally, large-scale
island-wide maneuvers with assault
vehicles have been postponed until the
erosion control plan is enacted. The
processes and results of erosion are
island-wide threats to C. grisea,
particularly to the occurrences in or
adjacent to military training areas or
roads. Seventeen of 29 occurrences (55
percent; West Cove, Plain northeast of
Warren Canyon, Larkspur Canyon,
Lemon Tank Canyon, Eagle Canyon,
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Bryce Canyon, China Canyon, Knob
Canyon, Canchalagua Canyon, Pyramid
Head, Red Canyon, Upper Chenetti
Canyon, Horse Beach Canyon, Upper
Horse Canyon, Horton Canyon, Seal
Cove Terraces, and Terrace Canyon) of
C. grisea are in areas that could be
subject to, and threatened by, erosion
from training activities or road use.
Occurrences in operationally closed
areas may not be afforded the
conservation measures outlined by the
Navy.
Erosion can lead to overall habitat
degradation and loss of individuals or
groupings of plants. However, despite
existing levels of erosion on the island,
the distribution of Castilleja grisea has
increased since listing. The Navy
incorporates erosion control measures
into all projects to minimize the
potential to exacerbate existing erosion
and avoid impacts to habitat and listed
species. Although the Navy tries to
ameliorate erosion, management efforts
are not possible in areas that are closed
to natural resource personnel. The
processes and results of erosion are
island-wide threats to C. grisea,
particularly to the 17 occurrences in or
adjacent to military training areas or
roads. Therefore, erosion is still
considered a threat to the existence of
C. grisea.
Nonnative Plants
One of the threats to Castilleja grisea
identified in the final listing rule was
the spread of nonnative plants into its
habitat (42 FR 40682, 40684).
Nonnatives can alter habitat structure,
ecological processes such as fire
regimes, nutrient cycling, hydrology,
and energy budgets, and compete for
water, space, light, and nutrients (for
discussion of nonnatives on San
Clemente Island, see above discussion
on Nonnative Species under
Malacothamnus clementine—Factor A).
Castilleja grisea is often associated with
native maritime desert scrub vegetation
types, where nonnative grasses are
present but not a dominant component
of the plant community (Tierra Data Inc.
2005, pp. 29–42).
Although previous invasions of
nonnative species were probably
introduced in grazing fodder, current
invasions are typically introduced and
spread around the island by military
activities and training (see above
discussion on Nonnative Species under
Malacothamnus clementinus—Factor
A). Nonnative plants constitute a
rangewide threat to all native plants on
San Clemente Island, including all
occurrences of Castilleja grisea. A total
of 9 of 29 occurrences (31 percent;
China Canyon, Horse Beach Canyon,
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Pyramid Head, Knob Canyon,
Canchalagua Canyon, Bryce Canyon,
Eagle Canyon, Plain northeast of Warren
Canyon, and Lemon Tank Canyon) are
within 500 ft (152 m) of Ridge Road or
China Point Road, and may be subject
to diffuse disturbance and road effects
that degrade the habitat quality along
the road (Forman and Alexander 1998,
p. 217). Roadsides tend to create
conditions (high disturbance, seed
dispersal from vehicles, ample light and
water) preferred by nonnative species
(Forman and Alexander 1998, p. 210).
Nonnatives, including Foeniculum
vulgare and Mesembryanthemum
crystallinum (crystalline iceplant), have
been found in the disturbed shoulders
along the road between Ridge Road and
China Point in SHOBA (Braswell 2011,
pers. obs.).
Potential impacts from nonnative
plants are expected to be minimized by
annual implementation of the Navy’s
island-wide nonnative plant control
program (O’Connor 2009b, pers. comm.;
Munson 2011a, pers. comm.; see above
discussion on Nonnative Species under
Malacothamnus clementine—Factor A).
This program targets nonnative species
for elimination using herbicide and
mechanical removal, prioritizing species
that are new to the island or are
particularly destructive. The program
has been successful at isolating and
limiting some species, such as
Foeniculum vulgare, to a few locations
(Howe 2011b, pers. comm.). To reduce
the potential for transport of nonnative
plants to San Clemente Island, military
and nonmilitary personnel inspect
tactical ground vehicles, and remove
any visible plant material, dirt, or mud
prior to going onto the island (USFWS
2008, p. 63). This precaution helps to
control the movement of nonnative
plants onto the island, but once on the
island nonnatives are easily spread by
the movement of vehicles from one area
to another. Although nonnative plants
will continue to pose a rangewide risk
to C. grisea, it is a threat of low
intensity, and the Navy has taken steps
to curtail habitat conversion from
nonnative plants.
Nonnative plant species are an islandwide threat to the native vegetative
community. The Navy has taken
preventative and conservation measures
through funding and implementing
nonnative plant species control on the
island. Management and control of
nonnative plants is not in place at the
four occurrences (14 percent; China
Canyon, Red Canyon, Upper Chenetti
Canyon, and Horse Beach Canyon) that
are closed to natural resource managers.
However, outside of these areas,
Castilleja grisea has persisted on the
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island. Despite the continued risk of
encroachment by nonnatives, Castilleja
grisea remains on the island, and its
range has continued to expand. Impacts
from nonnative plants are a persistent,
but low-level, threat to C. grisea habitat.
Fire
Fire was not considered a threat to
Castilleja grisea habitat at the time of
listing (42 FR 40682; August 11, 1977).
Since that time, however, over 50
percent of the island has experienced at
least one wildfire (Navy 2002, Map 3–
3, p. 3–32). The majority of fires are
concentrated in SHOBA, potentially
impacting 15 of 29 occurrences (52
percent; Thirst Canyon, Eagle Canyon,
Bryce Canyon, Canchalagua Canyon,
Knob Canyon, Pyramid Head, Snake
Canyon, Upper Chenetti Canyon, Horse
Beach Canyon, China Canyon, Red
Canyon, Kinkipar Canyon, Cave
Canyon, Horse Canyon, and Upper
Horse Canyon). Seven occurrences
occur within the eastern escarpment in
SHOBA (Thirst Canyon, Eagle Canyon,
Bryce Canyon, Canchalagua Canyon,
Knob Canyon, Pyramid Head, and Snake
Canyon), where impacts from fire are
less likely. Recent closure of this area
limits the ability to assess the status and
manage habitat at these occurrences.
Because of the elevated risk of fire
associated with training activities, live
and inert munitions fire is targeted
towards two delineated Impact Areas.
The risk of frequent fire is higher in
Impact Areas I and II, potentially
affecting the habitat at four of 29
occurrences (14 percent; Upper Chenetti
Canyon, Horse Beach Canyon, China
Canyon, and Red Canyon). The effects of
fire, and the state of plants within the
Impact Areas, are currently unknown
due to closure of the area (USFWS 2008,
p. 50). Fires are occasionally ignited by
activities north of SHOBA, posing a
low-magnitude threat to the habitat at
14 of the 29 occurrences (48 percent;
SHOBA Boundary, Horton Canyon,
Lemon Tank Canyon, Nanny Canyon,
Larkspur Canyon, Box Canyon, Upper
Norton Canyon, Middle Ranch Canyon,
Waymuck Canyon, Plain northeast of
Warren Canyon, Seal Cove Terraces, Eel
Cove Canyon, Terrace Canyon, and West
Cove) (Navy 2002, Map 3–4, p. 3–33).
Increased fire frequency from
intensified military use could lead to
localized changes in vegetation (see
above discussion on fire frequency
under Malacothamnus clementinus—
Factor A). The Navy has significantly
expanded the number of locations
where live fire and demolition training
will take place (USFWS 2008, pp. 21–
37), including TAR north of SHOBA
(TAR 17—Eel Cove Canyon and Seal
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Cove Terraces, and TAR 14 and 15—
Larkspur Canyon). In addition to
demolitions, certain proposed
munitions exercises involve the use of
incendiary devices, such as illumination
rounds, white phosphorous, and tracer
rounds, which pose a high risk of fire
ignition. Expanded live fire and
demolition training is also approved
within TAR 16 (Lemon Tank Canyon)
toward the center of the island. It is
likely that the fire pattern on the island
will change due to this increase in
ignition sources, with fires becoming
more common within and adjoining the
training areas north of SHOBA.
At the time of listing, fire was not
identified as a threat because of lack of
fire history and the low intensity of
military training on the island. Since
that time, military training has
significantly increased, and we have
better records of the fire frequency on
the island. Approximately 19 of 29
occurrences (65 percent) of Castilleja
grisea fall within areas that may be
subject to recurrent fires associated with
military training. This includes
locations that fall within SHOBA that
serve as a buffer for Impact Areas I and
II, and occurrences near live fire and
demolition training areas. As described
in the Background section, occurrences
of C. grisea have been discovered within
and outside of the impact areas in
SHOBA (Junak and Wilken 1998, p. 298;
Navy 2002, p. D–20), indicating that the
species is tolerant of at least occasional
fire. High fire frequency may be a
potential threat that could limit the
distribution of C. grisea by
overwhelming its tolerance threshold
(Brooks et al. 2004, p. 683; Jacobson et
al. 2004, p. 1). Frequent fire may exceed
a plant taxon’s capacity to persist by
depleting seed banks and reducing
reproductive output when fire occurs at
higher than natural frequencies in C.
grisea habitat (Zedler et al. 1983, pp.
811–815).
Within the Impact Areas or
operationally closed zones, fire
suppression and firefighting are not
being implemented because of safety
hazards from the presence of
unexploded ordnance. Fires that escape
designated training areas threaten other
parts of the island, though it is unlikely
that one fire is capable of spreading
throughout the entire range of the
species due to its broad distribution
across the island. The Navy’s
implementation of the MOFMP will
limit the frequency with which fires
escape Impact Areas and TAR. Through
the annual review process, the Navy
will identify mechanisms to reduce fire
return intervals within areas and
habitats where this taxon is
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concentrated (USFWS 2008, pp. 91–
122). Although the threat is ameliorated
through the MOFMP, fire remains an
island-wide threat to C. grisea,
particularly to the habitat at the 19
occurrences that fall within areas that
may be subject to recurrent fire
associated with military training.
Fire Management
A fire management plan within the
MOFMP was developed by the Navy to
provide flexibility for the timing of
military training and to ensure that
adequate fire suppression resources
were present with an increased level of
training activities (see above discussion
on Fire Management under
Malacothamnus clementinus—Factor
A). The Navy constructed fuelbreaks
around the Impact Areas for safety
purposes and to manage the spread of
fire from the Impact Areas. Maintenance
of these fuelbreaks reduces the
likelihood and frequency of fires
spreading to sensitive areas and
habitats, such as those occupied by
Castilleja grisea. Fuelbreaks on San
Clemente Island are created using
herbicides and strip burning, and
maintained using herbicides and fire
retardant (Phos-Chek D75F) (USFWS
2008, pp. 97–98) (see above discussion
on Fire Management (including fire
retardant use) under Malacothamnus
clementinus—Factor A).
Four occurrences (Red Canyon, China
Canyon, Horse Beach Canyon, and
Upper Chenetti Canyon) of C. grisea
have been documented within the
Impact Areas, and are likely exposed to
impacts from higher intensity training,
such as bombardment and fire. Some of
these occurrences are near fuelbreaks
and may be impacted by a change in the
vegetation community from fuelbreak
maintenance, resulting in an increase in
erosion or invasive nonnative plants.
Additionally, occurrences on the eastern
escarpment near the firebreaks on Ridge
Road (Canchalagua Canyon, Knob
Canyon) might be impacted by the
creation and maintenance of firebreaks
(USFWS 2008, p. 57). The Navy has
committed to studying the effects of
Phos-Chek on San Clemente Island
vegetation, and has avoided application
of Phos-Chek within 300 ft (91.4 m) of
mapped listed species to the extent
allowable with fuelbreak installation
(USFWS 2008, pp. 97–98). In the
MOFMP, the Navy committed to
conducting preseason briefings for
firefighting personnel on the guidelines
for fire suppression and limitations
associated with the use of Phos-Chek
and saltwater drops (USFWS 2008, pp.
97–98). The impact of saltwater on the
habitat of C. grisea has not yet been
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assessed. However, if salt persists, the
composition in the plant community
could change to favor more salt-tolerant
taxa.
It is anticipated that the Navy will
construct additional fuelbreaks to
minimize the risk of fire spreading from
areas proposed for expansion of live fire
and demolition training north of
SHOBA (USFWS 2008, p. 98). To
minimize the potential for effects to
listed species, the Navy considers the
documented locations of listed species
on the island as fuelbreak lines are
developed. The majority of Castilleja
grisea habitat is not impacted by fire
management, and only 6 of 29
occurrences (21 percent) are associated
with fuelbreaks. Even if expanded in
conjunction with increased levels of
training activities, the benefits of
fuelbreaks outweigh the detrimental
impacts of recurrent fire to C. grisea
habitat. The threat of fire management
to C. grisea habitat is restricted mainly
to occurrences within SHOBA, and
particularly to occurrences in the
Impact Areas. Because of the isolated
nature of this threat and its role in
prevention of fire, fire management is a
low-magnitude threat to C. grisea in the
future.
Summary of Factor A
The habitat of Castilleja grisea is
threatened by destruction and
modification of habitat associated with
land use, erosion, the spread of
nonnatives, fire, and fire management.
To help ameliorate these threats, the
Navy is implementing a MOFMP, an
INRMP, and the island-wide control of
nonnative plants. (Navy 2002, pp. 1–1—
8–12; USFWS 2008, pp. 1–237). The
MOFMP has been helpful in informing
strategic decisions for training using live
fire or incendiary devices. The Navy has
postponed major troop and assault
vehicle maneuvers across the island
until an erosion control plan is
completed (Navy 2008b, pp. 5–29, 5–30;
USFWS 2008, pp. 62, 87). Natural
resource managers have been successful
at decreasing the prevalence of
particularly destructive nonnatives,
such as Foeniculum vulgare. In recent
years, access to Impact Areas I and II
within SHOBA for biological monitoring
and conservation actions has been
strictly prohibited (USFWS 2008, p. 50),
so the status of four occurrences (Red
Canyon, China Canyon, Horse Beach
Canyon, and Upper Chenetti Canyon)
remains unknown. Recently, closures
along the eastern escarpment in SHOBA
have also limited the monitoring and
management of four occurrences (Knob
Canyon, Canchalagua Canyon, Bryce
Canyon, and Eagle Canyon). However,
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16 of 29 occurrences (55 percent) of C.
grisea fall outside Impact Areas, IOA,
AVMA, TAR, and fuelbreaks, where the
most intensive habitat disturbances are
likely to take place. While it is
anticipated that military training
activities will likely increase, based on
the current range of C. grisea and
conservation efforts, the threats to the
habitat of C. grisea posed by land use,
erosion, nonnatives, fire and fire
management are decreasing in
magnitude.
Factor B. Overutilization for
Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682;
August 11, 1977), the Service did not
identify any threats from
overutilization, and there is no new
information to indicate that
overutilization is a threat to Castilleja
grisea. Although voucher herbarium
specimens of C. grisea and seeds have
been collected for research and seed
banking, overutilization of C. grisea for
any purpose is not currently considered
a threat nor expected to be in the future.
Factor C. Disease or Predation
Grazing of feral goats and rooting of
feral pigs were considered a direct
threat to Castilleja grisea in the final
listing rule (42 FR 40682; August 11,
1977). As stated above, this threat was
ameliorated by the removal of all goats
and pigs from San Clemente Island in
1992, as recognized in our 2007 status
review (USFWS 2007c, p. 11).
Currently, no other predators or diseases
on San Clemente Island are known to
pose a significant threat to C. grisea, nor
are they expected to become a threat in
the future.
Factor D. Inadequacy of Existing
Regulatory Mechanisms
The Act requires us to examine the
adequacy of existing regulatory
mechanisms with respect to those
existing and foreseeable threats that may
affect Castilleja grisea. The inadequacy
of existing regulatory mechanisms was
not indicated as a threat to C. grisea at
listing (42 FR 40682; August 11, 1977).
Since it was listed as endangered, the
Act has been and continues to be the
primary Federal law that affords
protection to C. grisea. The Service’s
responsibilities in administering the Act
include sections 7, 9, and 10 (for more
information on the Service’s
responsibilities, see above discussion
under Malacothamnus clementinus—
Factor D). Critical habitat has not been
designated or proposed for this taxon.
Listing C. grisea provided a variety of
protections, including the prohibitions
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against removing or destroying plants
within areas under Federal jurisdiction
and the conservation mandates of
section 7 for all Federal agencies. If C.
grisea were not listed, these protections
would not be provided. Thus, we must
evaluate whether other regulatory
mechanisms would provide adequate
protections absent the protections of the
Act.
Other Federal Protections
National Environmental Policy Act
(NEPA)
All Federal agencies are required to
adhere to the National Environmental
Policy Act (NEPA) of 1970 (42 U.S.C.
4321 et seq.) for projects they fund,
authorize, or carry out. The Council on
Environmental Quality’s regulations for
implementing NEPA (40 CFR parts
1500–1518) state that agencies shall
include a discussion on the
environmental impacts of the various
project alternatives (including the
proposed action), any adverse
environmental effects that cannot be
avoided, and any irreversible or
irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA
itself is a disclosure law, and does not
require subsequent minimization or
mitigation measures by the Federal
agency involved. Although Federal
agencies may include conservation
measures for Castilleja grisea as a result
of the NEPA process, any such measures
are typically voluntary in nature and are
not required by the statute. NEPA does
not itself regulate activities that might
affect C. grisea, but it does require full
evaluation and disclosure of
information regarding the effects of
contemplated Federal actions on
sensitive species and their habitats.
On San Clemente Island, the Navy
must meet the NEPA requirements for
actions significantly affecting the
quality of the human environment.
Typically, the Navy prepares
Environmental Assessments and
Environmental Impact Statement on
operational plans and new or expanding
training actions. Absent the listing of
Castilleja grisea, we would expect the
Navy to continue to meet the procedural
requirements of NEPA for its actions,
including evaluating the environmental
impacts to rare plant species and other
natural resources. However, as
explained above, NEPA does not itself
regulate activities that might affect C.
grisea.
Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670)
authorizes the Secretary of Defense to
develop cooperative plans with the
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Secretaries of Agriculture and the
Interior for natural resources on public
lands. The Sikes Act Improvement Act
of 1997 requires Department of Defense
installations to prepare INRMPs that
provide for the conservation and
rehabilitation of natural resources on
military lands consistent with the use of
military installations to ensure the
readiness of the Armed Forces. An
INRMP is a plan intended ‘‘* * * to
guide installation commanders in
managing their natural resources in a
manner that is consistent with the
sustainability of those resources while
ensuring continued support of the
military mission’’ (Navy 2002, p. 1–1).
INRMPs are developed in coordination
with the State and the Service, and are
generally updated every 5 years.
Although an INRMP is technically not a
regulatory mechanism because its
implementation is subject to funding
availability, it is an important guiding
document that helps to integrate the
military’s mission with natural resource
protection.
San Clemente Island Integrated Natural
Resources Management Plan (INRMP)
Pursuant to the Sikes Act, the Navy
adopted an INRMP for San Clemente
Island that identifies multiple objectives
for protecting Castilleja grisea and its
habitat to help reduce threats to this
taxon (Navy 2002). The INRMP also
disclosed actions through the NEPA
process, and to comply with such
legislation and regulations as the
Endangered Species Act, the Federal
Noxious Weed Act of 1974 (7 U.S.C.
2801), the Comprehensive
Environmental Response,
Compensation, and Liability Act (42
U.S.C. 9601), the Resources
Conservation and Recovery Act (42
U.S.C. 6901), and the Soil Conservation
Act (16 U.S.C. 3B) (see INRMP section
above under Malacothamnus
clementinus—Factor D). Natural
resource objectives of relevance to the
protection of C. grisea in the INRMP
include an objective to: ‘‘Protect,
monitor, and restore plants and
cryptograms in order to manage for their
long-term sustainability on the island’’
(Navy 2002, p. 4–39). The INRMP
specifically includes the following
objectives for C. grisea management:
recovery of native shrub communities
that are host plants for the species, the
removal of nonnatives, monitoring of
the species, studies of preferred host
plants, study of plant’s response to fire,
and studies and inventory of insect
pollinators (Navy 2002, pp. D–20, D–
21). Multiple INRMP management
strategies have been implemented for
the conservation of C. grisea. Other
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INRMP strategies that target the plant
communities within which this species
occurs include: Controlling erosion,
with priority given to locations where
erosion may be affecting listed species;
producing a new vegetation map;
reducing nonnative plant cover from
1992–1993 baseline levels; managing
the size and intervals of fires;
experimenting with fire management to
improve native plant dominance while
protecting sensitive plant occurrences;
and conducting genetic and biological
studies of C. grisea across the island.
The MOFMP, Erosion Control Plan,
and nonnative plant species control
conducted on the island are discussed
above under Castilleja grisea—Factor A.
The Present or Threatened Destruction,
Modification, or Curtailment of Its
Habitat or Range. Absent listing under
the Act, the Navy would still be
required to develop and implement
INRMPs under the Sikes Act. However,
as noted under the other factors, while
the INRMP helps to ameliorate threats
and provides some protection for C.
grisea occurrences, those occurrences
within Impact Areas or operationally
closed areas may not benefit from the
conservation measures. While the
INRMP has reduced the severity of
threats and contributed to conservation
of the species, it still allows for land use
consistent with military readiness and
training. Thus, Navy activities will
continue to impact C. grisea as
described under Factor A and E.
State Protections
Since the time of listing, Castilleja
grisea has benefited from additional
State protections under the Native Plant
Protection Act (NPPA) and California
Endangered Species Act (CESA; listed
1982). However, the range of C. grisea is
restricted to a Federal military
installation, so listing under NPPA and
CESA may only afford protection to this
species in rare instances when the lead
agency is a non-Federal agency or when
proposed activities fall under other
State laws.
Summary of Factor D
The regulatory mechanisms outlined
above provide for adequate conservation
of Castilleja grisea. In continuance of a
long history of cooperative conservation
efforts, the Navy also implemented
several conservation actions that benefit
this plant taxon. The Navy has
implemented an MOFMP to reduce the
risk of fire on the island and a nonnative
plant species control program. In
response to the conservation actions
proposed and the current status of the
listed taxon, we issued a non-jeopardy
biological opinion on the Navy’s
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MOFMP. The provisions included in the
San Clemente Island INRMP provide
protection to all C. grisea occurrences
and adaptive management of its habitat
in order to help address threats to the
plant from military activities and
nonnative plants. However, as indicated
in the discussion under Factor A, not all
management tools described in the
INRMP are in place, and conservation
management may not be implemented at
several of the known occurrences that
have been closed to natural resource
managers. Castilleja grisea occurrences
are afforded protection through Federal
and military mechanisms, and thus the
inadequacy of existing regulatory
mechanisms is not considered a threat
to the species now or in the future.
However, in the absence of the Act, the
existing regulatory mechanisms are not
adequate to conserve C. grisea
throughout its range both now and in
the future.
Factor E. Other Natural or Manmade
Factors Affecting Their Continued
Existence
The 1977 listing rule identified
nonnatives as a threat to Castilleja
grisea under Factor E: competition from
nonnative plants (42 FR 40682; August
11, 1977). In this 5-factor analysis,
impacts from nonnative plants are
discussed above under Factor A as a
threat to habitat. Other Factor E threats
identified since listing that currently
impact C. grisea plants include: (1)
Movement of vehicles and troops, (2)
fire, and (3) climate change. Factor E
addresses threats to individuals of the
species, rather than the habitat
modification threats that are discussed
in Factor A. Therefore, while some
threats are discussed in both sections, in
this section we are focusing on the
direct impacts to individuals of C.
grisea.
Movement of Vehicles and Troops
Military training activities within
training areas often entail the movement
of vehicles and troops over the
landscape with the potential of
trampling or crushing individual plants
(for discussion of SWAT, TAR, and IOA,
see above discussion for
Malacothamnus clementinus—Factor
E). Based on the distribution of
Castilleja grisea occurrences and type of
troop movements likely to occur,
impacts due to trampling and crushing
are likely to occur within the IOA or
AVMA, along roads, and in the Impact
Areas. Specifically, major troop
movements and vehicle landings are
planned through Horse Beach and the
Horse Beach Canyon occurrence, with
troops and assault vehicles moving
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north along Horse Beach Road from the
beach (USFWS 2008, pp. 30, 41). These
operations could affect the Horse Beach
Canyon and China Canyon occurrences
(USFWS 2008, pp. 85–86). The status of
these plants is currently unknown
because of closure of the Impact Areas
(USFWS 2008, p. 50).
Sixteen of 29 occurrences
(approximately 55 percent; West Cove,
Terrace Canyon, Larkspur Canyon,
Nanny Canyon, Lemon Tank Canyon,
Seal Cove Canyon, Eel Cove Canyon,
Plain northeast of Warren Canyon, Eagle
Canyon, Bryce Canyon, Horse Beach
Canyon, China Canyon, Red Canyon,
Knob Canyon, Canchalagua Canyon, and
Pyramid Head) are partially or wholly
within the boundaries of a training area
(IOA, TAR, AVMA, SWAT, or Impact
Area), and may be impacted by
trampling. Recent documentation of C.
grisea within these training areas
suggests that, while the individual
plants have the potential to be impacted
by the activities described above, they
are able to sustain themselves under the
recent levels of traffic from vehicles and
troops associated with training activities
(SERG 2009–2011, GIS data). Steep
slopes along the eastern escarpment
may also afford the eight C. grisea
occurrences there some topographic
protection from vehicle and troop
movements. The anticipated loss of
individual plants from proposed
increases in troop and vehicle
movement is likely to increase, though
this will likely be a low-level impact to
the survival and recovery of C. grisea
because it is diffuse and managed by the
Navy (USFWS 2008, pp. 91–102).
Fire
Although not specifically mentioned
in the listing rule, intense or frequent
fires could threaten Castilleja grisea. In
the Factor A discussion above, we
addressed impacts of fire on the habitat;
this section covers the discrete threats to
individuals of C. grisea. As discussed in
the Background section, it is unknown
if C. grisea is adapted to periodic fires,
though it is likely that this taxon is
resilient to occasional fires (Navy 2002,
p. D–10; Tierra Data Inc. 2005, p. 80).
Castilleja grisea has recently been
documented in portions of Horse Beach
Canyon that burned up to three times
since 1979, and a large occurrence was
discovered in Pyramid Cove the year
following a fire (Navy 1996, p. 5–2). The
mechanisms and conditions under
which C. grisea can tolerate fire, and at
what frequency, are unknown. At higher
than natural fire frequencies, fire has the
potential to exceed a plant’s capacity to
persist by depleting seed banks and
reducing reproductive output (Zedler et
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al. 1983, pp. 811–815). The response of
C. grisea to fire may also be governed by
the response of its host species to fire.
Castilleja grisea occurs in some areas
of the island that may experience
elevated fire frequency, such as SHOBA
and especially the Impact Areas (Red
Canyon, China Canyon, Horse Beach
Canyon, Upper Chenetti Canyon)
(discussed in Factor A above). The
potential for frequent fire at many of the
occurrences within SHOBA is reduced
by their location on the eastern side of
the island, away from Impact Areas I
and II. In conjunction with its
expansion of training activities, the
Navy implemented a fire management
plan within the MOFMP that is focused
on fire prevention, fuels management,
and fire suppression. These measures
should minimize the frequency and
spread of fires that could result in loss
of C. grisea individuals.
Cu astilleja grisea is likely to
withstand occasional fires, as
demonstrated through its stability on
the island since listing. Although fire
ignition points are concentrated in the
military training areas, fires that escape
these areas can spread to most other
areas of the island. However, fires that
escape from training areas are not likely
to disturb the entire distribution of C.
grisea at one time because this taxon is
widely distributed across San Clemente
Island, and associated with steep
canyon areas where fires are less likely
to impact the plant. Nine of 29 C. grisea
occurrences (31 percent; Eel Cove
Canyon, Seal Cove Terraces, Red
Canyon, China Canyon, Horse Beach
Canyon, Upper Chenetti Canyon,
Larkspur Canyon, Lemon Tank Canyon,
and Snake Canyon) are more vulnerable
to the spread of fire associated with
military training. These occurrences
include locations that fall within 0.5 mi
(805 m) of TAR, or within Impact Areas
where live fire and demolition training
will be performed.
The Navy’s fire management practices
minimize ignitions as well as the spread
of fires (as described above in Factor A).
The Navy is conducting annual reviews
of fire management and fire occurrences
that will allow for adaptive
management. These measures should
minimize the frequency and spread of
fires that could result in loss of
individuals of C. grisea. Although, in
areas operationally closed to natural
resource managers, conservation actions
may not be implemented, and the
plant’s status remains unknown. We
anticipate that the Navy’s
implementation of the MOFMP will
limit the frequency with which fires
escape Impact Areas and TAR and that,
through the annual review process, the
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Navy will identify mechanisms to
reduce fire return intervals in areas not
designated for incendiary use (USFWS
2008, pp. 91–122). Therefore, the impact
of fire on individual C. grisea plants is
likely a low-level threat to long-term
persistence of this taxon.
Climate Change
For general information regarding
climate change impacts, see above
discussion on climate change under
Malacothamnus clementinus—Factor E.
Since listing of Castilleja grisea (USFWS
1977, p. 40684), the potential impacts of
ongoing, accelerated climate change
have become a recognized threat to the
flora and fauna of the United States
(IPCC 2007a, pp. 1–52; PRBO 2011, pp.
1–68) (for discussion of climate change
scenarios in California, see
Malacothamnus clementinus—Factor E
above). San Clemente is located within
a Mediterranean climatic regime, but
with a significant maritime influence.
Climate change models predict an
increase in average temperature for
southern California. There is substantial
uncertainty in precipitation projections,
and relatively little consensus
concerning precipitation patterns and
projections for southwestern California
(PRBO 2011, p. 40). Less rainfall and
warmer air temperatures could limit the
range of C. grisea, although there is no
direct research on the effects of climate
change on the species. Castilleja grisea
occurs in great numbers on the eastern
side of the island, where fog contributes
to a wetter climate. This area could
become drier if fog is less frequent,
possibly affecting moisture availability
for C. grisea. The impacts of predicted
future climate change to C. grisea
remain unclear. While we recognize that
climate change is an important issue
with potential effects to listed species
and their habitats, information is not
available to make accurate predictions
regarding its effects to C. grisea at this
time.
Summary of Factor E
Castilleja grisea continues to be
impacted by military activities and fire
at 17 of the 29 (59 percent) occurrences
on San Clemente Island. Military
training activities have the potential to
ignite fires within C. grisea habitat,
though the majority of occurrences are
outside of the Impact Areas and TAR
where the highest impacts are
recognized. The threat from fire is
reduced by implementation of the
Navy’s MOFMP, which should limit the
frequency of fires escaping from the
Impact Areas, although suppression will
not likely occur within the boundaries
of the Impact Areas. Threats from
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trampling and crushing of individual
plants are likely to increase due to
increases in training on the island.
However, C. grisea has expanded its
distribution on the island, and the Navy
is implementing conservation measures
that will continue to improve conditions
for this taxon. Finally, climate change
may likely influence this taxon, though
the magnitude of this rangewide threat
or how it may affect this taxon is
unknown at this time. Given the
distribution of the species and the
conservation measures that will be
implemented by the Navy, the threats
described here currently and in the
future are either of limited extent or
adequately managed to reduce and
minimize impacts to the species, while
the potential overall threat of climate
change remains unknown across this
taxon’s range.
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Combination of Factors—Castilleja
grisea
A species may be affected by more
than one threat in combination. Within
the preceding review of the five listing
factors, we have identified multiple
threats that may have interrelated
impacts on the species (see above
discussion on Combination of Factors
under Malacothamnus clementinus—
Factor E). The species’ productivity may
be reduced because of these threats,
either singularly or in combination.
However, it is not necessarily easy to
determine (nor is it necessarily
determinable) whether a particular
threat is the primary threat having the
greatest effect on the viability of the
species, or whether it is exacerbated by
or working in combination with other
potential threats to have cumulative or
synergistic effects on the species. While
the combination of factors is a threat to
the existence of Castilleja grisea, we are
unable to determine the magnitude or
extent of cumulative or synergistic
effects of the combination of factors on
the viability of the species at this time.
Finding
An assessment of the need for a
species’ protection under the Act is
based on threats to that species and the
regulatory mechanisms in place to
ameliorate impacts from these threats.
As required by section 4(a)(1) of the Act,
we conducted a review of the status of
these taxa and assessed the five factors
in consideration of whether
Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja
grisea are threatened or endangered
throughout all of their range. We
examined the best scientific and
commercial information available
regarding the past, present, and future
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threats faced by the species. We
reviewed information presented in the
May 18, 2010, petition, information
available in our files, and through our
90-day finding in response to this
petition, and other available published
and unpublished information. We also
consulted with species experts and
Navy staff, who are actively managing
for the conservation of M. clementinus,
A. d. var. traskiae, and C. grisea on San
Clemente Island.
In considering what factors might
constitute threats, we must look beyond
the mere exposure of the species to the
factor to determine whether the
exposure causes actual impacts to the
species. If there is exposure to a factor,
but no response, or only a positive
response, that factor is not a threat. If
there is exposure and the species
responds negatively, the factor may be
a threat and we then attempt to
determine how significant the threat is.
If the threat is significant, it may drive,
or contribute to, the risk of extinction of
the species such that the species
warrants listing as threatened or
endangered as those terms are defined
by the Act. This does not necessarily
require empirical proof of a threat. The
combination of exposure and some
corroborating evidence of how the
species is likely impacted could suffice.
The mere identification of factors that
could impact a species negatively is not
sufficient to compel a finding that
listing is appropriate; we require
evidence that these factors are operative
threats that act on the species to the
point that the species meets the
definition of threatened or endangered
under the Act.
A direct threat identified in the listing
rule (42 FR 40682), grazing from feral
herbivores, was eliminated by 1992
through the complete removal of goats
and pigs from the island (Factors A and
C). This action also fulfilled one of the
primary goals of the Recovery Plan
under Objective 2 (USFWS 1984, p.
107). However, as a result of years of
grazing, impacts from nonnative plants
and erosion have continued to increase
on the island. Our review of the status
of Malacothamnus clementinus,
Acmispon dendroideus var. traskiae,
and Castilleja grisea determined that
threats to these species under Factors A,
D, and E are present. The Navy’s natural
resource management and INRMP for
the island have helped to ameliorate
many of the threats to these species. The
Navy implements natural resource
management through the control of
nonnative species, execution of the fire
management plan, and avoidance of
federally listed species. Despite current
impacts from these threats to the habitat
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and individuals of these taxa, surveys
indicate that the range of each taxon has
increased since the time of listing.
Increased survey efforts and survey
accuracy have also shown that these
taxa occupy significantly more sites
than were known at listing. The extent
to which this represents the detection of
previously unknown occurrences,
recruitment from the existing seed bank,
or recolonization associated with
dispersal events, or positive response to
management and conservation efforts is
not known. Regardless, the increase of
both the range and number of
occurrences for all species indicates an
overall improved status for these species
since listing.
The surveys and discoveries of new
occurrences also contribute to the
achievement of objectives in the
Recovery Plan (Objective 6; USFWS
1984, p. 107). The Navy has taken
measures to locate the heaviest impacts
of military operations away from the
species to the extent feasible while
meeting operational needs, which will
minimize, but not fully eliminate, the
damage or destruction of individuals or
occurrences of M. clementinus, A. d.
var. traskiae, and C. grisea, partially
fulfilling Objective 1 of the Recovery
Plan (USFWS 1984, p. 107; USFWS
2008, pp. 90, 101, 121). However, the
largest and most diverse occurrences of
Malacothamnus clementinus are closed
to natural resource monitoring and
management, and their status remains
unknown.
Malacothamnus clementinus
Since the removal of feral goats and
pigs, the distribution of Malacothamnus
clementinus has expanded from 3 to 11
occurrences on San Clemente Island.
However, there are still significant
threats to the species, including threats
to habitat from military training
activities directly related to land use,
erosion, nonnative plants, fire, and fire
management (see Malacothamnus
clementinus—Factor A). Habitat impacts
are caused by the movement of troops
and vehicles over the landscape, as well
as by the use of live fire, demolitions,
and bombardments. Six of the 11 known
occurrences of M. clementinus are
within SHOBA, much of which serves
as a buffer from military training
impacts for the rest of the island. Three
M. clementinus occurrences are directly
within the Impact Areas, where frequent
fire, habitat disturbance (bombardment),
and troop and vehicle movement occur.
This includes the occurrence at Horse
Beach Canyon that comprises the
greatest number of point localities and
one of the two occurrences with the
greatest genetic variability (Helenurm
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1999, p. 39). Through implementation of
the INRMP, the Navy developed an
MOFMP and a nonnative plant
management plan to help minimize or
ameliorate these threats to the species.
However, the status of M. clementinus at
Lemon Tank Canyon and the three
occurrences in Impact Areas within
SHOBA remains unknown at this time,
because these areas are closed to natural
resource personnel (USFWS 2008, p.
50).
Threats to individual Malacothamnus
clementinus plants also affect the
species and include: Movement of
vehicles and troops, fire, climate
change, and low genetic diversity (see
Malacothamnus clementinus—Factor
E). The steps that the Navy has taken to
minimize impacts and avoid
endangered species to the extent
practicable have helped ameliorate the
threats caused by training to the
individual M. clementinus plants.
Climate change may impact M.
clementinus, though the effect is largely
unknown. The genetic makeup of the
species has been studied (fulfilling
Objective 4 of the Recovery Plan),
revealing that genetic variation within
the species is low. Combined with a low
seed production rate and vegetative
reproduction, low genetic diversity puts
the species at risk of low genetic fitness
and extinction by stochastic events.
The Navy implemented an INRMP to
coordinate the management of natural
resources on the island. Providing a
framework for military operations, this
plan helps to ameliorate threats to the
endangered species on the island, and
provides for long-term conservation
planning within the scope of military
readiness. Provisions included in the
INRMP provide some protection for
Malacothamnus clementinus
occurrences (including Acmispon
dendroideus var. traskiae, and Castilleja
grisea), and allows adaptive
management of the habitat in order to
help address threats from military
activities and nonnative plants.
Occurrences within Impact Areas or
operationally closed areas may not
benefit from the conservation measures
associated with the MOFMP due to lack
of access for natural resources
personnel. Existing regulatory
mechanisms, absent the protections of
the Act, provide insufficient certainty
that efforts needed to address long-term
conservation of the species will be
implemented, or that they will be
effective in reducing the level of threats
to M. clementinus throughout its range.
Under the INRMP, occurrences of M.
clementinus, including the largest and
most genetically diverse occurrences,
will continue to be impacted by military
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activities necessary for military
readiness and training, and the closure
of some areas creates uncertainty as to
the status of the occurrences within
those areas and whether those
occurrences will benefit from
conservation measures.
As discussed in the Factor Analysis,
a species may be affected by more than
one threat in combination. For example,
fires (Factors A and E) may be more
intense or frequent in the habitat if there
are greater amounts of nonnative grasses
(Factor A) present in the vegetative
community. Additionally, military
activities or erosion may lead to
increased nonnatives in an area. Thus,
the species’ viability may be reduced
because of synergistic effects when
multiple threats are present at one time.
Therefore, the combination of factors is
a threat to the existence of
Malacothamnus clementinus, but we are
unable to determine the magnitude or
extent of any synergistic effects of the
various factors and their impact at this
time.
In conclusion, we have carefully
assessed the best scientific and
commercial information available
regarding the past, present, and future
threats faced by this species. Our review
of the information pertaining to the five
threat factors does not support a
conclusion that the threats have been
sufficiently removed, or that their
imminence, intensity, or magnitude
have been reduced to the extent that the
species no longer requires the
protections of the Act. Four of the 11
known occurrences of the species have
been closed to nonmilitary personnel,
such that we are unable to assess the
impacts of the threats described under
the five listing factors above, nor are we
able to document the status of a
substantial portion of the occurrences of
Malacothamnus clementinus. This
includes one occurrence with the
highest number of point localities and
the greatest genetic variability. Under
provision of section 4(a)(1) of the Act,
we must assess the status in order to list
or change the status of a species from
endangered to threatened.
The 2007 status review listed land
use, fire, nonnative species, erosion,
natural factors, fire management, and
access to SHOBA as threats to the
species (USFWS 2007, p. 1–23).
Although we recommended downlisting
in our 2007 status review, at this time
we conclude that Malacothamnus
clementinus continues to be in danger of
extinction throughout its range because
of the change in intensity of training
and associated impacts enacted in the
2008 MOFMP. These changes include
the escalation in frequency and
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intensity of bombardments in Impact
Areas I and II and the movement of large
groups of troops and vehicles through
M. clementinus habitat. The threats to
M. clementinus, coupled with low
genetic fitness, place this taxon at risk
of extinction throughout all of its range,
and reclassification from endangered to
threatened is not warranted at this time.
Acmispon dendroideus var. traskiae
Since listing and the removal of feral
goats and pigs on San Clemente Island,
the distribution of Acmispon
dendroideus var. traskiae has expanded
from 6 to 29 occurrences, mainly along
the western terraces and eastern
escarpment. These significant gains
demonstrate alleviation of threats from
feral ungulates and that the species is
persisting despite existing and
remaining threats across the landscape.
The taxon faces impacts from military
training activities and land use, erosion,
nonnative plants, and fire (see
Acmispon dendroideus var. traskiae—
Factor A). Impacts from land use
include movement of troops and
vehicles over the landscape, as well as
the use of live fire, demolitions, and
bombardments. Much of this activity is
concentrated in training areas within
the range of A. d. var. traskiae.
However, many of these occurrences are
along the eastern escarpment that is
more protected from fire and military
activity. Additionally, the majority of
locations occupied by A. d. var. traskiae
(24 of 29 occurrences, or 83 percent) fall
outside of training areas, and thus do
not receive intensive habitat
disturbance. Access to the eastern
escarpment, within SHOBA and east of
Ridge Road, was recently closed for
safety concerns. As a result, the status
of 4 of 29 occurrences (14 percent)
could be difficult to monitor in the
future.
The Navy implemented a nonnative
plant management plan and an MOFMP
to ameliorate habitat threats to the
species. Erosion control measures are
incorporated into all project designs to
minimize the potential to exacerbate
existing erosion and avoid impacts to
listed species (Munson 2011a, pers.
comm.). Additionally, large-scale
island-wide maneuvers with assault
vehicles have been postponed until an
erosion control plan is drafted and
implemented. While it is anticipated
that military training activities, erosion,
nonnatives, and fire will have ongoing
impacts to the taxon’s habitat, based on
the current distribution of this taxon
and existing conservation efforts,
impacts from these threats are reduced
and minimized for Acmispon
dendroideus var. traskiae.
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Under the Sikes Act, the Navy has
implemented an INRMP to organize the
management of natural resources on the
island (also see above discussion in the
Finding section for Malacothamnus
clementinus). Existing regulatory
mechanisms, absent the protections of
the Act, provide insufficient certainty
that efforts needed to address long-term
conservation of the species will be
implemented, or that they will be
effective in reducing the level of threats
to Acmispon dendroideus var. traskiae
throughout its range. Under the INRMP,
occurrences of A. d. var. traskiae will
continue to be impacted by military
activities necessary for military
readiness and training.
Individual Acmispon dendroideus
var. traskiae plants also face threats on
the island. Movement of vehicles and
troops, fire, climate change, and
hybridization with related species all
impact the status of the species (see
Acmispon dendroideus var. traskiae—
Factor E). The steps that the Navy has
taken to minimize impacts and avoid
endangered species to the extent
practicable are ameliorating the threat of
trampling individual A. d. var. traskiae
plants caused by training. Hybridization
has also been studied (fulfilling
Objective 4 of the Recovery Plan), with
confirmed hybrids occurring in Wilson
Cove (Wilson Cove). The genetic
integrity of A. d. var. traskiae may be
threatened by hybridization with A.
argophyllus var. argenteus at one of the
largest occurrences, and requires further
investigation. The threats described here
(Factor E) are either of limited or
undetermined magnitude, or reduced to
the extent that we anticipate they will
not impede the recovery of A. d. var.
traskiae.
As discussed above in the Factor
Analysis, a species may be affected by
more than one threat in combination.
For example, fires (Factors A and E)
may be more intense or frequent in the
habitat if there are greater amounts of
nonnative grasses (Factor A) present in
the vegetative community. Thus, the
species’ viability may be reduced
because of threats in combination.
Therefore, the combination of factors is
a threat to the existence of Acmispon
dendroideus var. traskiae, but we are
unable to determine the magnitude or
extent of any synergistic effects of the
various factors and their impact at this
time.
In conclusion, we have carefully
assessed the best scientific and
commercial information available
regarding the past, present, and future
threats faced by this species. After
review of the information pertaining to
the five threat factors, we find that the
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ongoing threats are not of sufficient
imminence, intensity, or magnitude to
indicate that Acmispon dendroideus
var. traskiae is presently in danger of
extinction throughout its range and does
not, therefore, meet the definition of an
endangered species. While A. d. var.
traskiae will continue to be impacted by
military training activities and land use,
erosion, nonnative plants, and fire, the
expanded number of occurrences
reduces the severity and magnitude of
threats and the likelihood that any one
event would affect all occurrences of the
species. The extent of hybridization
within the species is also not known
and could affect the genetic integrity of
the plant. Additionally, the plant occurs
in recently closed areas, and these
occurrences will not be able to be
accessed or managed in the future with
these closures.
Though these threats to Acmispon
dendroideus var. traskiae still exist and
will continue into the foreseeable
future, the range of this taxon has
substantially increased since listing, and
the Navy is implementing conservation
actions through their INRMP to reduce
threats impacting A. d. var. traskiae.
Therefore, we find that the petitioned
action to downlist A. d. var. traskiae to
threatened is warranted. Please see the
Significant Portion of the Range
Analysis section below for our
evaluation as to whether this species
may or may not be in danger of
extinction in a significant portion of its
range.
Castilleja grisea
The known distribution of Castilleja
grisea has expanded from 19 to 29
known occurrences since listing, likely
due to the removal of feral goats and
pigs from the island in 1992. These
significant gains demonstrate some
alleviation of threats from feral
ungulates and that the species is
persisting despite existing and
remaining threats across the landscape.
Castilleja grisea faces impacts from
military training activities and land use,
erosion, nonnative plants, fire, and fire
management (see Castilleja grisea—
Factor A). The movement of troops and
vehicles over the landscape, as well as
use of live fire, demolitions, and
bombardments, results in destruction
and degradation of habitat occupied by
C. grisea. Much of this activity is
concentrated in SHOBA within training
areas and Impact Areas. Four
occurrences are within the Impact
Areas, where frequent fire, habitat
disturbance (bombardment), and troop
and vehicle movement take place in the
heavily used ranges. Access to parts of
SHOBA, including the eastern
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escarpment and east of Ridge Road, was
recently closed for safety concerns. The
status of the four occurrences may be
difficult to assess in the future, although
these areas may be more protected from
fire and military activity and are likely
less impacted by habitat threats. A large
proportion of C. grisea occurrences fall
outside Impact Areas, TAR, and
fuelbreaks, where the most intensive
habitat disturbances are likely to take
place.
Threats impacting individual plants
of Castilleja grisea on the island
include: movement of vehicles and
troops, fire, and potentially climate
change (see Castilleja grisea—Factor E).
The Navy has ameliorated the threats to
individual plants by taking steps to
minimize training impacts and
measures to avoid endangered species to
the extent practicable. The threats
described under Factor E are either of
limited extent or adequately managed
and are not likely to impede the
recovery of C. grisea.
Under the Sikes Act, the Navy has
implemented an INRMP to organize the
management of natural resources on the
island (also see above discussion in the
Finding section for Malacothamnus
clementinus). Existing regulatory
mechanisms, absent the protections of
the Act, provide insufficient certainty
that efforts needed to address long-term
conservation of the species will be
implemented, or that they will be
effective in reducing the level of threats
to Castilleja grisea throughout its range.
Under the INRMP, occurrences of C.
grisea will continue to be impacted by
military activities necessary for military
readiness and training.
As discussed above in the Factor
Analysis, a species may be affected by
more than one threat in combination.
For example, fires (Factors A and E)
may be more intense or frequent in the
habitat if there are greater amounts of
nonnative grasses (Factor A) present in
the vegetative community. Thus, the
species’ viability may be reduced
because of threats in combination.
Therefore, the combination of factors is
a threat to the existence of Castilleja
grisea, but we are unable to determine
the magnitude or extent of any
synergistic effects of the various factors
and their impact at this time.
In conclusion, we have carefully
assessed the best scientific and
commercial information available
regarding the past, present, and future
threats faced by this species. After
review of the information pertaining to
the five threat factors, we find the
ongoing threats are not of sufficient
imminence, intensity, or magnitude to
indicate that Castilleja grisea is
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presently in danger of extinction across
its range. While C. grisea will continue
to be impacted by military training
activities and land use, erosion,
nonnative plants, and fire, the expanded
number of occurrences reduces the
severity and magnitude of threats and
the likelihood that any one event would
affect all occurrences of the species.
Additionally, the plant occurs in
operationally closed areas, such as the
Impact Areas, where threats are
concentrated and occurrences cannot be
accessed or managed with these
closures.
Though threats to Castilleja grisea
still exist and will continue into the
foreseeable future, the range of this
taxon has substantially increased since
listing, and the Navy is implementing
conservation actions through their
INRMP to reduce threats impacting C.
grisea. Therefore, we find that the
petitioned action to downlist C. grisea
to threatened is warranted at this time.
Please see the Significant Portion of the
Range Analysis section below for our
evaluation as to whether this species
may or may not be in danger of
extinction in a significant portion of its
range.
Significant Portion of the Range
Analysis
The Act defines ‘‘endangered species’’
as any species which is ‘‘in danger of
extinction throughout all or a significant
portion of its range,’’ and ‘‘threatened
species’’ as any species which is ‘‘likely
to become an endangered species within
the foreseeable future throughout all or
a significant portion of its range.’’ The
definition of ‘‘species’’ is also relevant
to this discussion. The Act defines the
term ‘‘species’’ as follows: ‘‘The term
‘species’ includes any subspecies of fish
or wildlife or plants, and any distinct
population segment [DPS] of any
species of vertebrate fish or wildlife
which interbreeds when mature.’’ The
phrase ‘‘significant portion of its range’’
(SPR) is not defined by the statute, and
we have never addressed in our
regulations: (1) The consequences of a
determination that a species is either
endangered or likely to become so
throughout a significant portion of its
range, but not throughout all of its
range; or (2) what qualifies a portion of
a range as ‘‘significant.’’
Two recent district court decisions
have addressed whether the SPR
language allows the Service to list or
protect less than all members of a
defined ‘‘species’’: Defenders of Wildlife
v. Salazar, 729 F. Supp. 2d 1207 (D.
Mont. 2010), concerning the Service’s
delisting of the Northern Rocky
Mountain gray wolf (74 FR 15123, Apr.
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12, 2009); and WildEarth Guardians v.
Salazar, 2010 U.S. Dist. LEXIS 105253
(D. Ariz. Sept. 30, 2010), concerning the
Service’s 2008 finding on a petition to
list the Gunnison’s prairie dog (73 FR
6660, Feb. 5, 2008). The Service had
asserted in both of these determinations
that it had authority, in effect, to protect
only some members of a ‘‘species,’’ as
defined by the Act (i.e., species,
subspecies, or DPS), under the Act. Both
courts ruled that the determinations
were arbitrary and capricious on the
grounds that this approach violated the
plain and unambiguous language of the
Act. The courts concluded that reading
the SPR language to allow protecting
only a portion of a species’ range is
inconsistent with the Act’s definition of
‘‘species.’’ The courts concluded that
once a determination is made that a
species (i.e., species, subspecies, or
DPS) meets the definition of
‘‘endangered species’’ or ‘‘threatened
species,’’ it must be placed on the list
in its entirety and the Act’s protections
applied consistently to all members of
that species (subject to modification of
protections through special rules under
sections 4(d) and 10(j) of the Act).
Consistent with that interpretation,
and for the purposes of this finding, we
interpret the phrase ‘‘significant portion
of its range’’ in the Act’s definitions of
‘‘endangered species’’ and ‘‘threatened
species’’ to provide an independent
basis for listing; thus there are two
situations (or factual bases) under which
a species would qualify for listing: A
species may be endangered or
threatened throughout all of its range; or
a species may be endangered or
threatened in only a significant portion
of its range. If a species is in danger of
extinction throughout an SPR, it, the
species, is an ‘‘endangered species.’’
The same analysis applies to
‘‘threatened species.’’ Therefore, the
consequence of finding that a species is
endangered or threatened in only a
significant portion of its range is that the
entire species shall be listed as
endangered or threatened, respectively,
and the Act’s protections shall be
applied across the species’ entire range.
We conclude, for the purposes of this
finding, that interpreting the SPR phrase
as providing an independent basis for
listing is the best interpretation of the
Act because it is consistent with the
purposes and the plain meaning of the
key definitions of the Act; it does not
conflict with established past agency
practice (i.e., prior to the 2007
Solicitor’s Opinion), as no consistent,
long-term agency practice has been
established; and it is consistent with the
judicial opinions that have most closely
examined this issue. Having concluded
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that the phrase ‘‘significant portion of
its range’’ provides an independent
basis for listing and protecting the entire
species, we next turn to the meaning of
‘‘significant’’ to determine the threshold
for when such an independent basis for
listing exists.
Although there are potentially many
ways to determine whether a portion of
a species’ range is ‘‘significant,’’ we
conclude, for the purposes of this
finding, that the significance of the
portion of the range should be
determined based on its biological
contribution to the conservation of the
species. For this reason, we describe the
threshold for ‘‘significant’’ in terms of
an increase in the risk of extinction for
the species. We conclude that a
biologically based definition of
‘‘significant’’ best conforms to the
purposes of the Act, is consistent with
judicial interpretations, and best
ensures species’ conservation. Thus, for
the purposes of this finding, a portion
of the range of a species is ‘‘significant’’
if its contribution to the viability of the
species is so important that, without
that portion, the species would be in
danger of extinction.
We evaluate biological significance
based on the principles of conservation
biology using the concepts of
redundancy, resiliency, and
representation. Resiliency describes the
characteristics of a species that allow it
to recover from periodic disturbance.
Redundancy (having multiple
populations distributed across the
landscape) may be needed to provide a
margin of safety for the species to
withstand catastrophic events.
Representation (the range of variation
found in a species) ensures that the
species’ adaptive capabilities are
conserved. Redundancy, resiliency, and
representation are not independent of
each other, and some characteristic of a
species or area may contribute to all
three. For example, distribution across a
wide variety of habitats is an indicator
of representation, but it may also
indicate a broad geographic distribution
contributing to redundancy (decreasing
the chance that any one event affects the
entire species), and the likelihood that
some habitat types are less susceptible
to certain threats, contributing to
resiliency (the ability of the species to
recover from disturbance). None of these
concepts is intended to be mutually
exclusive, and a portion of a species’
range may be determined to be
‘‘significant’’ due to its contributions
under any one of these concepts.
For the purposes of this finding, we
determine if a portion’s biological
contribution is so important that the
portion qualifies as ‘‘significant’’ by
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asking whether, without that portion,
the representation, redundancy, or
resiliency of the species would be so
impaired that the species would have an
increased vulnerability to threats to the
point that the overall species would be
in danger of extinction (i.e., would be
‘‘endangered’’). Conversely, we would
not consider the portion of the range at
issue to be ‘‘significant’’ if there is
sufficient resiliency, redundancy, and
representation elsewhere in the species’
range that the species would not be in
danger of extinction throughout its
range if the population in that portion
of the range in question became
extirpated (extinct locally).
We recognize that this definition of
‘‘significant’’ establishes a threshold
that is relatively high. On the one hand,
given that the consequences of finding
a species to be endangered or threatened
in an SPR would be listing the species
throughout its entire range, it is
important to use a threshold for
‘‘significant’’ that is robust. It would not
be meaningful or appropriate to
establish a very low threshold whereby
a portion of the range can be considered
‘‘significant’’ even if only a negligible
increase in extinction risk would result
from its loss. Because nearly any portion
of a species’ range can be said to
contribute some increment to a species’
viability, use of such a low threshold
would require us to impose restrictions
and expend conservation resources
disproportionately to conservation
benefit: listing would be rangewide,
even if only a portion of the range of
minor conservation importance to the
species is imperiled. On the other hand,
it would be inappropriate to establish a
threshold for ‘‘significant’’ that is too
high. This would be the case if the
standard were, for example, that a
portion of the range can be considered
‘‘significant’’ only if threats in that
portion result in the entire species’
being currently endangered or
threatened. Such a high bar would not
give the SPR phrase independent
meaning, as the Ninth Circuit held in
Defenders of Wildlife v. Norton, 258
F.3d 1136 (9th Cir. 2001).
The definition of ‘‘significant’’ used in
this finding carefully balances these
concerns. By setting a relatively high
threshold, we minimize the degree to
which restrictions will be imposed or
resources expended that do not
contribute substantially to species
conservation. But we have not set the
threshold so high that the phrase ‘‘in a
significant portion of its range’’ loses
independent meaning. Specifically, we
have not set the threshold as high as it
was under the interpretation presented
by the Service in the Defenders
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litigation. Under that interpretation, the
portion of the range would have to be
so important that current imperilment
there would mean that the species
would be currently imperiled
everywhere. Under the definition of
‘‘significant’’ used in this finding, the
portion of the range need not rise to
such an exceptionally high level of
biological significance. (We recognize
that if the species is imperiled in a
portion that rises to that level of
biological significance, then we should
conclude that the species is in fact
imperiled throughout all of its range,
and that we would not need to rely on
the SPR language for such a listing.)
Rather, under this interpretation we ask
whether the species would be
endangered everywhere without that
portion, i.e., if that portion were
completely extirpated. In other words,
the portion of the range need not be so
important that even being in danger of
extinction in that portion would be
sufficient to cause the remainder of the
range to be endangered; rather, the
complete extirpation (in a hypothetical
future) of the species in that portion
would be required to cause the
remainder of the range to be
endangered.
The range of a species can
theoretically be divided into portions in
an infinite number of ways. However,
there is no purpose to analyzing
portions of the range that have no
reasonable potential to be significant
and threatened or endangered. To
identify only those portions that warrant
further consideration, we determine
whether there is substantial information
indicating that: (1) The portions may be
‘‘significant,’’ and (2) the species may be
in danger of extinction there or likely to
become so within the foreseeable future.
Depending on the biology of the species,
its range, and the threats it faces, it
might be more efficient for us to address
the significance question first or the
status question first. Thus, if we
determine that a portion of the range is
not ‘‘significant,’’ we do not need to
determine whether the species is
endangered or threatened there; if we
determine that the species is not
endangered or threatened in a portion of
its range, we do not need to determine
if that portion is ‘‘significant.’’ In
practice, a key part of the portion status
analysis is whether the threats are
geographically concentrated in some
way. If the threats to the species are
essentially uniform throughout its
range, no portion is likely to warrant
further consideration. Moreover, if any
concentration of threats applies only to
portions of the species’ range that
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clearly would not meet the biologically
based definition of ‘‘significant,’’ such
portions will not warrant further
consideration.
Having determined that Acmispon
dendroideus var. traskiae and Castilleja
grisea are no longer endangered
throughout their ranges as a
consequence of the threats evaluated
under the five factors in the Act, we
must next consider whether there are
any significant portions of these two
species’ ranges where they are currently
endangered. A portion of a species’
range is significant if it is part of the
current range of the species and is
important to the conservation of the
species as evaluated based upon its
representation, resiliency, or
redundancy.
Acmispon dendroideus var. traskiae
Applying the process described
above, we evaluated the range of
Acmispon dendroideus var. traskiae to
determine if any units could be
considered a significant portion of its
range. This taxon is an island endemic
restricted to a single, small island, with
no natural division in its range. Because
of its limited range and number of
occurrences in close proximity to one
another, no portion is likely to have a
greater contribution to representation,
resiliency, or redundancy than other
portions. Furthermore, the existing and
potential primary direct and indirect
threats from military training activities,
nonnative plant species, fire, and
erosion are relatively uniform across
San Clemente Island, indicating that no
portions of its range are experiencing a
greater severity or magnitude of threats.
We conclude that there are no portions
that warrant further consideration under
this analysis.
In summary, the primary threats to
Acmispon dendroideus var. traskiae are
relatively uniform throughout its range.
We determined that none of the existing
or potential threats, either alone or in
combination with others, currently
place A. d. var. traskiae in danger of
extinction throughout all or a significant
portion of its range. However, without
the continued protections of the Act,
this taxon is likely to become
endangered throughout its range in the
foreseeable future. Threatened status is
therefore appropriate for A. d. var.
traskiae throughout its entire range.
Castilleja grisea
Applying the process described
above, we evaluated the range of
Castilleja grisea to determine if any
units could be considered a significant
portion of its range (also see the
Significant Portion of the Range
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Analysis section above for Acmispon
dendroideus var. traskiae). This island
endemic is restricted to a single, small
island with no natural division in its
range. Because of its limited range and
number of occurrences in close
proximity to one another, no portion is
likely to have a greater contribution to
its representation, resiliency, or
redundancy than other portions. The
primary threats to C. grisea, military
training activities, nonnative plant
species, fire, and erosion, are relatively
uniform throughout its range (San
Clemente Island), indicating that no
portion is experiencing a greater
severity or magnitude of threats. We
conclude that there are no portions that
warrant further consideration under this
analysis. We determined that none of
the existing or potential threats, either
alone or in combination with others,
currently place C. grisea in danger of
extinction throughout all of its range.
However, without the continued
protections of the Act, this taxon is
likely to become endangered throughout
its range in the foreseeable future.
Threatened status is therefore
appropriate for C. grisea throughout its
entire range.
Effects of This Rule
If this proposed rule is made final, it
would revise 50 CFR 17.12(h) to
reclassify Acmispon dendroideus var.
traskiae and Castilleja grisea from
endangered to threatened on the List of
Endangered and Threatened Plants and
to correct the scientific and common
names for Acmispon dendroideus var.
traskiae. However, this reclassification
does not significantly change the
protections afforded these species under
the Act. The regulatory protections of
section 9 and section 7 of the Act (see
Factor D, above) would remain in place.
Pursuant to section 7 of the Act, all
Federal agencies must ensure that any
actions they authorize, fund, or carry
out are not likely to jeopardize the
continued existence of A. d. var.
traskiae and C. grisea. Whenever a
species is listed as threatened, the Act
allows promulgation of special rules
under section 4(d) that modify the
standard protections for threatened
species found under section 9 of the Act
and Service regulations at 50 CFR 17.31
and 17.71, when it is deemed necessary
and advisable to provide for the
conservation of the species. There are
no 4(d) rules in place or proposed for A.
d. var. traskiae and C. grisea, because
there is currently no conservation need
to do so for these species.
Recovery actions directed at
Acmispon dendroideus var. traskiae and
Castilleja grisea will continue to be
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implemented as outlined in the
Recovery Plan for the Endangered and
Threatened Species of the California
Channel Islands (USFWS 1984). This
recovery plan addresses 10 plants
(including Malacothamnus clementinus,
A. d. var. traskiae, and C. grisea) and
animals distributed among three of the
Channel Islands (USFWS 1984).
of the methods listed in the ADDRESSES
section. To better help us revise the
rule, your comments should be as
specific as possible. For example, you
should tell us the names of the sections
or paragraphs that are unclearly written,
which sections or sentences are too
long, the sections where you feel lists or
tables would be useful, etc.
Peer Review
In accordance with our joint policy on
peer review published in the Federal
Register on July 1, 1994 (59 FR 34270),
we will seek the expert opinions of at
least three appropriate and independent
specialists regarding this proposed rule
to reclassify Acmispon dendroideus var.
traskiae and Castilleja grisea from
endangered to threatened. The purpose
of peer review is to ensure that our
proposed rule is based on scientifically
sound data, assumptions, and analyses.
We have invited these peer reviewers to
comment during this public comment
period on our proposed downlisting.
We will consider all comments and
information we receive during this
comment period on this proposed rule
during our preparation of the final
determination. Accordingly, the final
decision may differ from this proposal.
Executive Order 13211
Public Hearings
Section 4(b)(5) of the Act provides for
one or more public hearings on this
proposal, if requested. We must receive
your request within 45 days after the
date of this Federal Register
publication. Send your request to the
address shown in the FOR FURTHER
INFORMATION CONTACT section. We will
schedule public hearings on this
proposal, if any are requested, and
announce the dates, times, and places of
those hearings, as well as how to obtain
reasonable accommodations, in the
Federal Register and local newspapers
at least 15 days before the hearing.
Required Determinations
Clarity of the Rule
We are required by Executive Orders
12866 and 12988 and by the
Presidential Memorandum of June 1,
1998, to write all rules in plain
language. This means that each rule we
publish must:
(a) Be logically organized;
(b) Use the active voice to address
readers directly;
(c) Use clear language rather than
jargon;
(d) Be divided into short sections and
sentences; and
(e) Use lists and tables wherever
possible.
If you feel that we have not met these
requirements, send us comments by one
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Executive Order 13211 requires
agencies to prepare Statements of
Energy Effects when undertaking certain
actions. This rule is not expected to
significantly affect energy supplies,
distribution, or use. Therefore, this
action is not a significant energy action
and no Statement of Energy Effects is
required.
Paperwork Reduction Act of 1995
Office of Management and Budget
(OMB) regulations at 5 CFR part 1320,
which implement provisions of the
Paperwork Reduction Act (44 U.S.C.
3501 et seq.), require that Federal
agencies obtain approval from OMB
before collecting information from the
public. This rule does not contain any
new collections of information that
require approval by OMB under the
Paperwork Reduction Act. This rule will
not impose recordkeeping or reporting
requirements on State or local
governments, individuals, businesses, or
organizations. An agency may not
conduct or sponsor, and a person is not
required to respond to, a collection of
information unless it displays a
currently valid OMB control number.
National Environmental Policy Act
We determined we do not need to
prepare an Environmental Assessment
or an Environmental Impact Statement,
as defined under the authority of the
National Environmental Policy Act of
1969 (42 U.S.C. 4321 et seq.), in
connection with regulations adopted
pursuant to section 4(a) of the Act. We
published a notice outlining our reasons
for this determination in the Federal
Register on October 25, 1983 (48 FR
49244).
References Cited
A complete list of references cited in
this rulemaking is available on the
Internet at https://www.regulations.gov
and upon request from the Carlsbad
Fish and Wildlife Office (see FOR
FURTHER INFORMATION CONTACT).
Author(s)
The primary authors of this package
are the staff members of the Carlsbad
Fish and Wildlife Office.
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List of Subjects in 50 CFR Part 17
50 of the Code of Federal Regulations,
as set forth below:
Endangered and threatened species,
Exports, Imports, Reporting and
recordkeeping requirements,
Transportation.
PART 17—ENDANGERED AND
THREATENED WILDLIFE AND PLANTS
Proposed Regulation Promulgation
1. The authority citation for part 17
continues to read as follows:
Accordingly, we propose to amend
part 17, subchapter B of chapter I, title
Authority: 16 U.S.C. 1361–1407; 16 U.S.C.
1531–1544; 16 U.S.C. 4201–4245; Pub. L. 99–
625, 100 Stat. 3500; unless otherwise noted.
Species
Scientific name
Historic
range
Common name
Family
2. Amend § 17.12(h) under
‘‘Flowering Plants’’ by removing the
entry for ‘‘Lotus dendroideus var.
traskiae’’ and adding an entry for
‘‘Acmispon dendroideus var. traskiae’’
and revising the entry for ‘‘Castilleja
grisea’’ to read as follows:
§ 17.12
*
Endangered and threatened plants.
*
*
(h) * * *
Status
*
When
listed
*
Critical
habitat
Special
rules
FLOWERING PLANTS
*
Acmispon
dendroideus var.
traskiae.
*
San Clemente Island
lotus.
*
U.S.A. (CA) ..............
*
*
Fabaceae ................. T
*
26
NA
*
Castilleja grisea .......
*
San Clemente Island
Paintbrush.
*
U.S.A. (CA) ..............
*
*
Orobanchaceae ....... T
*
26
NA
*
*
*
Authority
The authority for this action is section
4 of the Endangered Species Act of
*
*
1973, as amended (16 U.S.C. 1531 et
seq.).
*
*
NA
*
NA
*
Dated: May 1, 2012.
David L. Cottingham,
Acting Director, Fish and Wildlife Service.
[FR Doc. 2012–11339 Filed 5–15–12; 8:45 am]
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]]>Agencies
[Federal Register Volume 77, Number 95 (Wednesday, May 16, 2012)]
[Proposed Rules]
[Pages 29078-29128]
From the Federal Register Online via the Government Printing Office [www.gpo.gov]
[FR Doc No: 2012-11339]
[[Page 29077]]
Vol. 77
Wednesday,
No. 95
May 16, 2012
Part V
Department of the Interior
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Fish and Wildlife Service
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50 CFR Part 17
Endangered and Threatened Wildlife and Plants; 12-Month Finding on a
Petition To Downlist Three San Clemente Island Plant Species; Proposed
Rule To Reclassify Two San Clemente Island Plant Species; Taxonomic
Correction; Proposed Rule
Federal Register / Vol. 77 , No. 95 / Wednesday, May 16, 2012 /
Proposed Rules
[[Page 29078]]
-----------------------------------------------------------------------
DEPARTMENT OF THE INTERIOR
Fish and Wildlife Service
50 CFR Part 17
[Docket No. FWS-R8-ES-2012-0007; FXES11130900000C5-123-FF09E32000]
RIN 1018-AY04
Endangered and Threatened Wildlife and Plants; 12-Month Finding
on a Petition To Downlist Three San Clemente Island Plant Species;
Proposed Rule To Reclassify Two San Clemente Island Plant Species;
Taxonomic Correction
AGENCY: Fish and Wildlife Service, Interior.
ACTION: Notice of 12-month petition finding and proposed rule.
-----------------------------------------------------------------------
SUMMARY: We, the U.S. Fish and Wildlife Service, announce our 12-month
findings on a petition to reclassify San Clemente Island lotus, and San
Clemente Island paintbrush under the Endangered Species Act are
warranted and we propose to change the status of these two species from
endangered to threatened. We also propose to correct the scientific and
common names of San Clement Island lotus. We are also announcing our
12-month finding on a petition to reclassify San Clemente Island bush
mallow is not warranted at this time, and therefore we are not
proposing to change the status of this species. We are taking these
actions as a result of a petition to reclassify these three species.
DATES: The finding announced in this document was made on May 16, 2012
Regarding the proposed rule to reclassify Acmispon dendroideus var.
traskiae and Castilleja grisea, we will accept comments received or
postmarked on or before July 16, 2012. We must receive requests for
public hearings, in writing, at the address shown in the FOR FURTHER
INFORMATION CONTACT section by July 2, 2012.
ADDRESSES: This finding is available on the Internet at https://www.regulations.gov at Docket Number [FWS-R8-ES-2012-0007]. Supporting
documentation we used in preparing this finding is available for public
inspection, by appointment, during normal business hours at the U.S.
Fish and Wildlife Service, Carlsbad Fish and Wildlife Office, 6010
Hidden Valley Road, Suite 101, Carlsbad, CA, 92011. Please submit any
new information, materials, comments, or questions concerning this
finding to the above address. Regarding the proposed rule to reclassify
Acmispon dendroideus var. traskiae and Castilleja grisea, you may
submit comments by one of the following methods:
Federal eRulemaking Portal: https://www.regulations.gov. Follow the
instructions for submitting comments for Docket No. [FWS-R8-ES-2012-
0007].
U.S. mail or hand delivery: Public Comments Processing, Attn:
Docket No. [FWS-R8-ES-2012-0007]; Division of Policy and Directives
Management; U.S. Fish and Wildlife Service; 4401 N. Fairfax Drive,
Suite 222; Arlington, VA 22203.
We will not accept email or faxes. We will post all comments on
https://www.regulations.gov. This generally means that we will post any
personal information you provide us (see the Public Comments Solicited
section below for more information).
FOR FURTHER INFORMATION CONTACT: Jim Bartel, Field Supervisor, Carlsbad
Fish and Wildlife Office (see ADDRESSES); by telephone at 760-431-9440;
or by facsimile (fax) at 760-431-9624. If you use a telecommunications
device for the deaf (TDD), please call the Federal Information Relay
Service (FIRS) at 800-877-8339.
SUPPLEMENTARY INFORMATION:
Executive Summary
This document contains: (1) 12-month findings in response to a
petition to reclassify Malacothamnus clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea as threatened; and (2) a proposed
rule to reclassify A. d. var. traskiae and C. grisea as threatened
under the Act.
Species addressed. Malacothamnus clementinus (San Clemente Island
bush mallow), Acmispon (previously listed as Lotus) dendroideus var.
traskiae (previously San Clemente Island broom and currently known as
San Clemente Island lotus), and Castilleja grisea (San Clemente Island
paintbrush) are endemic to San Clemente Island, which is located 64
miles (mi) (103 kilometers (km)) west of San Diego, California. Current
habitat conditions for M. clementinus, A. d. var. traskiae, and C.
grisea on San Clemente Island are the result of present and historical
land use practices. San Clemente Island is owned by the U.S. Department
of the Navy and, with its associated offshore range complex, is the
primary maritime training area for the Navy Pacific Fleet and Navy Sea,
Air and Land teams (SEALs). The island also supports training by the
U.S. Marine Corps, the U.S. Air Force, and other military
organizations.
Purpose of the Regulatory Action. Under the Endangered Species Act,
we may be petitioned to list, delist or reclassify a species. In 2010,
we received a petition from the Pacific Legal Foundation requesting
that the Service reclassify Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea from endangered to
threatened. These species are currently listed as endangered under the
Act. In 2011, we published our 90-day finding on the petition which
concluded that the petition contained substantial information
indicating reclassification of the three San Clemente Island plants may
be warranted. We therefore also announced that we were initiating
status reviews for these taxa as required under the Act. A change in
listing status can only be done by issuing a rule.
Basis for the Regulatory Action. Under the Endangered Species Act,
a species may be determined to be endangered or threatened based on any
of five factors: (A) The present or threatened destruction,
modification, or curtailment of its habitat or range; (B)
Overutilization for commercial, recreational, scientific, or
educational purposes; (C) Disease or predation; (D) The inadequacy of
existing regulatory mechanisms; or (E) Other natural or manmade factors
affecting its continued existence.
We reviewed all available scientific and commercial information
pertaining to the five threat factors in our status review of each
species.
We summarize the results of our status review for each species
below.
Malacothamnus clementinus (San Clemente Island Bush Mallow)
Our review does not support a conclusion that the threats
have been sufficiently removed, or that their imminence, intensity, or
magnitude have been reduced to the extent that the species no longer
meets the definition of an endangered species. Threats associated with
military activities, erosion, nonnatives, fire, climate change, and low
genetic diversity continue to impact Malacothamnus clementinus at all
of the 11 occurrences on San Clemente Island. M. clementinus continues
to be impacted throughout its range because of the change in intensity
of training and associated impacts enacted in the 2008 San Clemente
Island Military Operations and Fire Management Plan (MOFMP).
Additionally, closure of areas on San Clemente Island to natural
resource personnel creates uncertainty regarding the status of 4 of 11
occurrences, including the largest and most genetically diverse, and
whether those
[[Page 29079]]
occurrences will benefit from conservation measures.
We find that reclassifying Malacothamnus clementinus is
not warranted at this time.
Although we recommended downlisting in our 2007 status
review, at this time we believe that Malacothamnus clementinus
continues to be in danger of extinction throughout its range.
Acmispon dendroideus var. traskiae (San Clemente Island Lotus)
We find that the ongoing threats are not of sufficient
imminence, intensity, or magnitude to indicate that Acmispon
dendroideus var. traskiae is presently in danger of extinction
throughout its range and does not, therefore, meet the definition of an
endangered species.
Since listing and the removal of feral goats and pigs on
San Clemente Island, the distribution of Acmispon dendroideus var.
traskiae has expanded from 6 to 29 occurrences. Significant gains in
distribution demonstrate that the species is persisting despite
existing threats across the landscape.
The Navy is implementing an Island Integrated Natural
Resources Management Plan (INRMP) to coordinate the management of
natural resources and provide for long-term conservation planning
within the scope of military readiness.
While it is anticipated that military training activities,
erosion, nonnatives, and fire will have ongoing impacts to A. d. var.
traskiae habitat, impacts from these threats are reduced and minimized
based on its distribution and current and anticipated conservation
efforts for the taxon.
We find that reclassifying Acmispon dendroideus var.
traskiae as threatened is warranted.
Castilleja grisea (San Clemente Island Paintbrush)
We find the ongoing threats are not of sufficient
imminence, intensity, or magnitude to indicate that Castilleja grisea
is presently in danger of extinction across its range and does not,
therefore, meet the definition of an endangered species.
Since listing and the removal of feral goats and pigs on
San Clemente Island, the distribution of Castilleja grisea has expanded
from 19 to 29 known occurrences. This significant increase in
occurrences shows that the species is persisting despite existing
threats across the landscape.
The Navy is implementing an Island Integrated Natural
Resources Management Plan (INRMP) to coordinate the management of
natural resources and provide for long-term conservation planning
within the scope of military readiness.
While it is anticipated that military training activities,
erosion, nonnatives, and fire will have ongoing impacts to Castilleja
grisea habitat, impacts from these threats are reduced and minimized
based on its distribution and current and anticipated conservation
efforts for the taxon.
We find that reclassifying Castilleja grisea as
threatened is warranted.
We are proposing the following changes to the List of Threatened
and Endangered Plants:
Correct the scientific and common names of Acmispon
dendroideus var. traskiae, formerly known as Lotus dendroideus var.
traskiae (San Clemente broom).
Change the status of Acmispon dendroideus var. traskiae
from endangered to threatened.
Change the status of Castilleja grisea from endangered to
threatened.
Acronyms Used
We use several acronyms throughout the preamble to this proposed
rule. To assist the reader, we set them forth here:
AFP = Artillery Firing Point
AVMA = Assault Vehicle Maneuver Area
BMP = Best Management Practices
CERCLA = Comprehensive Environmental Response, Compensation and
Liability Act
CESA = California Endangered Species Act
CDFG = California Department of Fish and Game
CNDDB = California Natural Diversity Database
CNPS = California Native Plant Society
DPS = Distinct Population Segment
EO = California Natural Diversity Database element occurrence
GIS = Geographic Information System
INRMP = Integrated Natural Resources Management Plan
IOA = Infantry Operations Areas
IPCC = Intergovernmental Panel on Climate Change
MOFMP = Military Operations and Fire Management Plan
Navy = United States Department of the Navy
NEPA = National Environmental Policy Act
NPPA = Native Plant Protection Act
OHV = Off Highway Vehicle
OMB = Office of Management and Budget
PL = Point Location
RCRA = Resource Conservation and Recovery Act
SEALs = Navy Sea, Air, and Land teams
SERG = San Diego State University Soil Ecology and Restoration Group
SHOBA = Shore Bombardment Area
SPR = Significant Portion of the Range
SWAT = Special Warfare Training Areas
TAR = Training Area Ranges
USFWS = United States Fish and Wildlife Service
Public Comments Solicited
Our intent is to use the best available commercial and scientific
data as the foundation for all endangered and threatened species
classification decisions. Therefore, we request comments or information
from the public, other concerned governmental agencies, Native American
tribes, the scientific community, industry, or any other interested
parties concerning this proposed rule to downlist Acmispon dendroideus
var. traskiae and Castilleja grisea. We particularly seek comments
concerning:
(1) Reasons why we should or should not reclassify Acmispon
dendroideus var. traskiae and Castilleja grisea under the Act.
(2) New biological, trade, or other relevant information and data
concerning any threat (or lack thereof) to A. d. var. traskiae and C.
grisea.
(3) New information and data on the projected and reasonably likely
impacts to A. d. var. traskiae and C. grisea associated with climate
change.
(4) The location of, and status, trends, and threats to, any
additional occurrences of A. d. var. traskiae and C. grisea.
(5) New information and data concerning the range, distribution,
occurrence size, and occurrence trends of A. d. var. traskiae and C.
grisea.
(6) New information and data on the current or planned activities
within the geographic range of A. d. var. traskiae and C. grisea that
may adversely affect or benefit the species.
(7) New information on the host plants of C. grisea.
(8) Information and data on the hybridization of A. d. var.
traskiae, and the impacts of this hybridization on the species.
We will also continue to accept new information that becomes
available concerning the status or threats to the Malacothamnus
clementinus or its habitat at any time.
We will post your entire comment on https://www.regulations.gov.
Before including your address, phone number, email address, or other
personal identifying information in your comment, you should be aware
that your entire comment--including your personal identifying
information--may be made publicly available at any time. While you can
ask us in your comment to withhold your personal identifying
information from public review, we cannot guarantee that we will be
able to do so.
Comments and materials we receive, as well as supporting
documentation we used in preparing this proposed rule,
[[Page 29080]]
will be available for public inspection on https://www.regulations.gov,
or by appointment during normal business hours at the Carlsbad Fish and
Wildlife Office (see ADDRESSES).
Public Hearing
The Act provides for one or more public hearings on this proposal,
if requested. Requests must be received by the date specified in DATES.
Such requests must be made in writing and addressed to the Field
Supervisor (see FOR FURTHER INFORMATION CONTACT section above).
Background
Section 4(b)(3)(B) of the Endangered Species Act of 1973, as
amended (Act; 16 U.S.C. 1531 et seq.), requires that, for any petition
to revise the Federal Lists of Endangered and Threatened Wildlife and
Plants that contains substantial scientific or commercial information
that reclassifying the species may be warranted, we make a finding
within 12 months of the date of receipt of the petition. In this
finding, we will determine whether the petitioned action is: (a) Not
warranted, (b) warranted, or (c) warranted, but the immediate proposal
of a regulation implementing the petitioned action is precluded by
other pending proposals to determine whether species are endangered or
threatened, and expeditious progress is being made to add or remove
qualified species from the Federal Lists of Endangered and Threatened
Wildlife and Plants. We must publish these 12-month findings in the
Federal Register.
Previous Federal Actions
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea were listed as endangered under the Act on August 11,
1977 (42 FR 40682). Subsequently, a Recovery Plan for Channel Island
species, including M. clementinus, A. d. var. traskiae, and C. grisea,
was finalized in 1984 (USFWS 1984, pp. 1-165), and 5-year status
reviews were completed for each of these taxa in 2007 (USFWS 2007a, pp.
1-28; USFWS 2007b, pp. 1-22; USFWS 2007c, pp. 1-19). These status
reviews recommended reclassification of M. clementinus, A. d. var.
traskiae, and C. grisea from endangered to threatened status.
On May 18, 2010, we received a petition dated May 13, 2010, from
the Pacific Legal Foundation requesting that the Service delist
Oenothera californica (avita) subsp. eurekensis (Eureka Valley evening-
primrose) and Swallenia alexandrae (Eureka Valley dunegrass), and
downlist tidewater goby (Eucyclogobius newberryi), Acmispon dendroideus
(Lotus scoparius subsp.) var. traskiae, Malacothamnus clementinus, and
Castilleja grisea from endangered to threatened under the Act. The
petition was based on the analysis and recommendations contained in the
2007 5-year reviews for these taxa. In a letter to the petitioner dated
September 10, 2010, we acknowledged receipt of the petition and
initiated a review of the petition under a provision of section 4 of
the Act. We stated that we anticipated making an initial 90-day finding
in Fiscal Year 2011 (based on available staffing and funding) as to
whether or not the petition presented substantial information
indicating that the requested action may be warranted.
On January 19, 2011, we published a 90-day finding (76 FR 3069) in
which we concluded that the petition and information in our files
provided substantial information that the reclassification of these
species may be warranted, and announced that we were initiating status
reviews for these species. Five-year reviews pursuant to section
4(c)(2)(A) of the Act for Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea were previously
initiated on May 21, 2010 (75 FR 28636). We will base our 5-year review
recommendations on the information and conclusions provided in this
finding, and we expect to finalize those reviews following publication
of this finding. To ensure that the status reviews are comprehensive,
we requested in the 90-day finding any scientific or commercial data
and other information regarding these taxa be submitted by March 21,
2011. This document includes: (1) A notice that constitutes the 12-
month finding in response to the petition to reclassify M. clementinus,
A. d. var. traskiae, and C. grisea as threatened (the 12-month findings
for O. californica (avita) subsp. eurekensis, S. alexandrae, and
tidewater goby will be addressed in separate documents); and (2) a
proposed rule to reclassify A. d. var. traskiae and C. grisea from
endangered to threatened under the Act.
Species Information
For purposes of this finding, we present the species description
and taxonomy for each individual plant species below. However, the
remaining species information, where possible, is combined for all
three taxa to avoid redundancy, followed by applicable species-specific
information by taxon.
Species Description and Taxonomy--Malacothamnus clementinus
Malacothamnus clementinus is a rounded subshrub (stems woody only
at the base) in the Malvaceae (mallow family). Plants are 2.3 to 3.3
feet (ft) (0.7 to 1 meters (m)) tall with numerous hairy branched stems
arising from the base of the plant (Munz and Johnston 1924, p. 296;
Munz 1959, pp. 122-125; Bates 1993, p. 752; Junak 2006a, pers. comm.).
Plants have the ability to spread vegetatively by underground rhizomes,
resulting in patches of spatially separate, but genetically identical,
individuals (Evans and Bohn 1987, p. 538). The leaves are 1.2 to 2
inches (in) (3 to 5 centimeters (cm)) wide and conspicuously bicolored,
with green upper surfaces covered in short fine hairs and veiny, white
undersurfaces that are densely matted with hairs (Munz and Johnston
1924, p. 296). Flowers are clustered in the uppermost leaf axils,
forming interrupted spikes 3.9 to 7.9 in (10 to 20 cm) long (Munz 1959,
p. 125). Flowers are bisexual and variously described as having pink or
white and fading lavender petals (Munz and Johnston 1924, p. 296; Bates
1993, p. 752). Each flower can produce about 10 seeds that are 0.08 in
(2 millimeters (mm)) long (Munz 1959, p. 122; Navy 2002, p. C-43). The
fruits mature and open slowly and irregularly on the plant (Navy 2002,
p. C-43). The genus Malacothamnus includes 20 species found in the
southwestern region of the United States (Junak and Wilken 1998, p.
290). Malacothamnus clementinus is endemic to San Clemente Island and
is the only species within the genus that occurs there (Bates 1993, p.
752; Tierra Data Inc. 2005, p. C-8).
No taxonomic classifications or nomenclature changes affecting this
taxon have been published since it was listed as endangered in 1977.
The Jepson Manual, the standard reference flora for the State,
continued to treat this species under the same name, Malacothamnus
clementinus, in the recent edition (Bates 2012, pp. 1-2).
Species Description and Taxonomy--Acmispon dendroideus var. traskiae
Acmispon dendroideus var. traskiae is a suffrutescent (semi-woody),
short-lived (less than 5 years), floriferous (flower bearing) subshrub
in the legume family Fabacaeae (pea family). It is endemic to San
Clemente Island (Isely 1993, p. 619), and is one of five taxa in the
genus Acmispon found on the island (Tierra Data Inc. 2005, p. C-8;
Brouillet 2008, pp. 388-392). There are no other varieties of A.
dendroideus found on the island. This variety can be distinguished from
other varieties of A. dendroideus by its bushy habit and elongated
fruits (Allan 1999, p. 88). Acmispon dendroideus var. traskiae is
typically
[[Page 29081]]
less than 4 ft (1.2 m) tall with slender erect green branches (Munz
1974, pp. 449-450; USFWS 1984, p. 59; Allan 1999, p. 82). Each leaf has
three to five leaflets, each approximately 0.2 to 0.3 in (5 to 9 mm)
long and uniformly glabrous (surface without hair) to finely hairy
(USFWS 1984, p. 59; Allan 1999, p. 82). Acmispon dendroideus var.
traskiae has small yellow flowers that are bisexual and arranged in one
to five flowered clusters on stalks that arise from axils between the
stem and leaf of terminal shoots (Junak and Wilken 1998, p. 256).
Pistils are initially yellow, turning orange then red as the fruit
matures (USFWS 1984, p. 59; California Native Plant Society (CNPS)
2001, p. 208).
Acmispon dendroideus var. traskiae has undergone taxonomic
realignments since the 1977 listing. We accept the change of scientific
name to Acmispon dendroideus (Greene) Brouillet var. traskiae (Noddin)
Brouillet from Lotus dendroideus (Nutt.) Ottley subsp. traskiae. This
change is supported by morphological and molecular data (Allan and
Porter 2000, p. 1876; Sokoloff 2000, p. 128; Brouillet 2008, p. 389).
The name used for this taxon when it was listed in 1977 (42 FR
40682) was Lotus scoparius (Nutt.) Ottley subsp. traskiae (Abrams)
Raven. Subsequently, Isely (1978, p. 467) separated this and two other
Channel Islands endemic taxa (L. scoparius var. veatchi Ottley and L.
scoparius var. dendroideus (Greene) Ottley) from mainland Lotus
scoparius. He recognized them as varieties (considered equivalent to
subspecies in plants) of a single species, Lotus dendroideus, which was
the oldest name among the three taxa. The name, Lotus dendroideus var.
traskiae, was published by Isely in 1978 (p. 467), and recognized in
floristic (Isely 1993, p. 619) and systematic treatments (Isely 1998,
p. 646). Following Isely's taxonomic revision, we amended the list of
endangered and threatened plants (50 CFR 17.12), but incorrectly
transcribed the name as Lotus dendroideus subsp. traskiae (USFWS 1980,
45 FR 82483). This combination, as a subspecies and not a variety, was
never validly published and thus cannot be used.
Recent morphological (Sokoloff 2000, p. 128) and molecular (Allan
and Porter 2000, p. 1876) data support recognition of a separate genus,
Acmispon, from Lotus. The required nomenclatural combination Acmispon
dendroideus (Greene) Brouillet var. traskiae (Noddin) Brouillet was
made in 2008 (Brouillet 2008, p. 389). This name is recognized and
accepted by the scientific community in floristic works, the Jepson
Manual revision for California (Brouillet 2012), and the continental
Flora of North America, as well as by the California Native Plant
Society (CNPS 2011). We concur with the scientific evidence and
acceptance by the scientific community and likewise accept the name
Acmispon dendroideus var. traskiae. Based upon this acceptance, we will
make appropriate corrections to this taxon's references in our
regulations (50 C.F.R. 17.12) and will use this nomenclature in future
notices regarding this taxon. Moreover, in previous documents, this
taxon has been referred to by other common names (such as Trask's
Island lotus, San Clemente Island broom, and San Clemente Island lotus)
(Isely 1993, p. 619; 76 FR 3069, January 19, 2011; 42 FR 40682, August
11, 1977). In this document, we use San Clemente Island lotus to
represent A. d. var. traskiae. The taxonomic and nomenclatural changes
described here do not alter the description, distribution, or listing
status of the taxon.
Species Description and Taxonomy--Castilleja grisea
Castilleja grisea is a highly branched hemiparasitic (plant that
can be either free-living or parasitic) perennial herb to subshrub in
the Orobanchaceae (broomrape family) (Chuang and Heckard 1993, p. 1016;
Young et al. 1999, p. 890; Olmstead et al. 2001, p. 352). Castilleja
grisea is endemic to San Clemente Island and the only species of the
genus found there (Chuang and Heckard 1993, p. 1021; Helenurm et al.
2005, p. 1222; Tierra Data Inc. 2005, p. A-7). Castilleja grisea plants
are 1.3 to 2 ft (0.4 to 0.6 m) tall and ash-gray in color with densely
hairy leaves (Chuang and Heckard 1993, p. 1021). The leaves are
alternate and linear, and 0.4 to 2 in (1 to 5 cm) long with 0 to 3
lobes (Chuang and Heckard 1993, p. 1021). The yellow bisexual flowers
are borne in terminal spikes. The fruit is a semi-woody capsule, 0.4 to
0.5 in (10 to 12 mm) long, bearing many small seeds (Chuang and Heckard
1993, p. 1021; Junak and Wilken 1998, p. 83). Seeds have a deeply
netted seedcoat, and are 0.4 to 0.6 in (1 to 1.5 mm) in diameter
(Muller and Junak 2011, p. 12).
Castilleja grisea was described by Dunkle (p. 31) in 1943. The name
has not changed since the species was listed, although the family
affiliation has been changed to the Orobanchaceae (broomrape family)
from the Scrophulariaceae (figwort family; Olmstead et al. 2001, p.
352). We will revise our regulations at 50 C.F.R. 17.12 to reflect this
change in family affiliation. This taxonomic change remains consistent
in the upcoming edition of the Jepson Manual (Chuang and Heckard,
Weatherwax, rev. 2012).
Species Location
Description and Land Use of San Clemente Island
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea are endemic to San Clemente Island (Raven 1965, p.
60), which is located 64 miles (mi) (103 kilometers (km)) west of San
Diego, California (USFWS 1984, p. 5). The island is approximately 56
square mi (145 square km) (Junak and Wilken 1998, p. 2) and is long and
narrow: 21 mi (34 km) long by 1.5 mi (2.4 km) wide at the north end and
4 mi (6.4 km) wide at the south end (USFWS 1984, p. 5).
The historical ranges and distributions of Malacothamnus
clementinus, Acmispon dendroideus var. traskiae, and Castilleja grisea
on San Clemente Island are unknown because botanical studies were not
conducted on the island prior to grazing, which began in the 1800s
(Kellogg and Kellogg 1994, p. 4). The first herbarium specimens were
collected in 1894 for M. clementinus and C. grisea, and in 1905 for A.
d. var. traskiae. Although herbarium specimens were collected from time
to time, the first surveys for these species did not occur until the
1970s (USFWS 2007b, p. 4).
San Clemente Island is owned by the U.S. Department of the Navy
(Navy) and, with its associated offshore range complex, is the primary
maritime training area for the Pacific Fleet and SEALs. The island also
supports training by the U.S. Marine Corps, the U.S. Air Force, and
other military organizations. As the western most training range in the
eastern Pacific Basin where training operations are performed prior to
troop deployments, portions of the island receive intensive use by the
military (Navy 2008b, p. 2-2). Various training activities occur within
particular land use designations and training areas on the island,
which are coincidentally concentrated in habitat that supports
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea. In 2008, the Navy adopted the MOFMP to increase the
amount and intensity of training on San Clemente Island (Navy 2008b,
pp. 2-1 to 2-52). The impact to habitat from military activities is
increasing under this plan (USFWS 2008, pp. 1-237).
Military training activities within Naval Special Warfare Training
Areas (SWAT), Training Area Ranges (TAR), Impact Areas, and the
Infantry
[[Page 29082]]
Operations Areas (IOA) involve the movement of vehicles and troops over
the landscape, and can include live munitions fire, incendiaries,
demolitions, and bombardment. These activities have multiple impacts,
including disturbances to soil and vegetation, spread of nonnative
plant species, creation of road ruts and trails, and compaction of
soils (USFWS 2008, pp. 83-87). TARs cover a total of 1,840 acres (ac)
(744 hectares (ha)), or 5.4 percent of the island, while IOAs encompass
8,815 ac (3,567 ha) or approximately 25 percent of the island, SWATs
cover a total of 10,897 ac (4410 ha) or approximately 30 percent of the
island, and Impact Areas cover 3,459 ac (1,400 ha) or approximately 10
percent of the island (Navy 2008a, pp. 2-17, 2-45; Navy 2008b, p. 3.11-
52).
The Navy has delineated areas of military use to define where
specific activities will take place. These delineated areas include the
Shore Bombardment Area (SHOBA), constituting the southern one third of
the island. Please note that while the SHOBA boundary is illustrated in
Figures 1 to 3, no other boundaries are shown for security reasons,
although other training areas will be discussed in the text of this
document. SHOBA, which covers approximately 10,061 ac (4071 ha) (Navy
2009, p. 2-4), serves as a buffer around Impact Areas I and II and
supports a variety of training operations. Parts of SHOBA are not
subject to training activities and serve only as a buffer, while other
areas support military activities, including movement of troops and
vehicles or bombing exercises (Navy 2002, p. 2-4). The Impact Areas
sustain heavy live fire and are a recurrent source of wildfires. Fuel
breaks are applied each year prior to fire season to help prevent
spread of fire to areas outside of the Impact Areas.
Because parts of SHOBA are used for ship-to-shore bombardment,
access to this area is restricted for nonmilitary personnel on days
when bombing is occurring. Individuals conducting surveys or working on
invasive species control projects are granted access to areas outside
of the Impact Areas within SHOBA when military activities requiring
exclusive use are not occurring. Because of the frequency of training,
access to SHOBA can be restricted for long periods of time. Range
operators are aware of the natural resource obligations within SHOBA,
and at least 1 day a week is usually allowed for natural resource
programs to conduct their activities. Weeks with reduced natural
resource access, including infrequent events that exclude natural
resource personnel from SHOBA for 10 to 20 days, are announced in
advance and provide natural resource managers the opportunity to plan
accordingly.
Safety concerns relative to the presence of unexploded ordnance
within SHOBA have recently prompted the Navy to review access policies
(O'Connor 2006, pers. comm.; USFWS 2008, p. 50; Munson 2011c, pers.
comm.). In the Navy's MOFMP (Navy 2008a; pp. 2-38 to 2-44), Impact
Areas I and II were indefinitely closed ``for any purpose, including
monitoring and management of endangered and sensitive species and their
habitat'' for safety reasons (Navy 2008a, p. 2-45). Impact Areas I and
II cover approximately 3,459 ac (1,400 ha), or approximately 10 percent
of the island's 36,000 ac (14,568 ha; Navy 2008a, p. 2-45. The Navy is
revising its INRMP to develop solutions to monitor species and their
threats in these areas potentially through unmanned vehicles, aircraft,
or with the assistance of range maintenance personnel that regularly
access the areas. In the meantime, there are no monitoring or
management actions occurring in these areas.
Access to additional areas on the island where unexploded ordnance
has been found is now also restricted for natural resource personnel
(such as areas in the eastern escarpment within SHOBA, Eel Point,
Pyramid Head, and Lemon Tank Canyon) (Munson 2011c, pers. comm.).
Restricted access to these sites limits the opportunities to acquire
information on the status of Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea occurrences, and
inhibits the ability to manage threats in those areas. The Navy is
developing plans to trim the vegetation in these areas so that sweeps
by specially trained technicians can clear the areas of unexploded
ordnance to allow access by nonmilitary personnel (Munson 2011c, pers.
comm.).
As part of its monitoring and recovery efforts for listed species,
the Navy initiated several rare plant surveys on San Clemente Island
(Junak and Wilken 1998, pp. 1-416, GIS data; Junak 2006, pp. 1-176, GIS
data; Tierra Data Inc. 2008, pp. 1-24, appendices and GIS data; SERG
2009-2011, GIS data). These surveys involved the collection of point
locations that represent discrete localities of plants detected during
field surveys. Temporal and spatial variation among data points from
these surveys is likely due to differences between individual
researchers' survey techniques or accuracy of data records. Groups of
plants were described in the past using many different terms including:
Point localities, populations, occurrences, and element occurrences.
Unless referring to a specific author's research and language, we refer
to identifiable and separable groups of plants as ``occurrences'' in
this finding and proposed rule. We defined these occurrences by mapping
smaller groupings of plants (point locations) and combining point
locations that fall within 0.25 mi (402 m) of one another with any
corresponding California Natural Diversity Database (CNDDB) polygons.
These combined points meet the broader California Department of Fish
and Game (CDFG) definition of an element occurrence, which is a record
of an observation or series of observations. Discussion of occurrences
throughout this 12-month finding includes groupings of CNDDB element
occurrences and point localities within a 0.25-mi (402 m) radius of a
given occurrence. Information for each occurrence of these three taxa
is described in Table 1.
[[Page 29083]]
Table 1--Distribution and Status of Occurrences of Malacothamnus clementinus (San Clemente Island Bush Mallow), Acmispon dendroideus var. traskiae (San
Clemente Island Lotus), and Castilleja grisea (San Clemente Island Paintbrush)
--------------------------------------------------------------------------------------------------------------------------------------------------------
Element occurrence
(EO) and Status \2\ at listing; Current status
Location description point location (PL) year of first record (reference) Current threats \3\ Military use \4\
\1\
--------------------------------------------------------------------------------------------------------------------------------------------------------
Malacothamnus clementinus
--------------------------------------------------------------------------------------------------------------------------------------------------------
Canchalagua Canyon................. No EO; 1 PL........... Unknown............... Presumed Extant (SERG A: Nonnative, Fire; Low Military Value;
2011). E: Fire, Climate, Area Recently
Genetic. Closed.
Horse Beach Canyon................. EO 3; 48 PLs.......... Unknown............... Presumed Extant A: Land Use, Erosion, High Military Value;
(Junak 2005). Nonnative, Fire, Area Closed.
Fire Management; E:
Movement, Fire,
Climate, Genetic.
Lower China Canyon................. EO 1; 9 PLs........... Extant; 1975 herbarium Presumed Extant A: Land Use, Erosion, High Military Value;
record. (Junak 1997, SERG Nonnative, Fire, Area Closed.
2009). Fire Management; E:
Movement, Fire,
Climate, Genetic.
Upper China Canyon (including Upper No EO; 4 PLs.......... Extant; 1975 herbarium Extant (SERG 2010)... A: Land Use, Erosion, Low Military Value.
Horse Beach Canyon). record. Nonnative, Fire,
Fire Management; E:
Movement, Fire,
Climate, Genetic.
Cave Canyon (including Kinkipar No EO; 27 PLs......... Unknown............... Extant (SERG 2010)... A: Nonnative, Fire; Medium Military
Canyon). E: Fire, Climate, Value.
Genetic.
Chukit Canyon...................... 2 PLs................. Unknown............... Extant (Junak 2004).. A: Nonnative, Fire; Low Military Value.
E: Fire, Climate,
Genetic.
Lemon Tank Canyon.................. EO 2.................. Extant; 1923 herbarium Presumed Extant A: Land Use, Erosion, Low Military Value;
record. (CNDDB 1996). Nonnative; E: Area Closed.
Movement, Climate,
Genetic.
Box Canyon......................... EO 4; 9 PLs........... Unknown............... Extant (SERG 2009)... A: Nonnative; E: Low Military Value.
Climate, Genetic.
Norton Canyon...................... EO 7; 27 PLs.......... Unknown............... Extant--(SERG 2011).. A: Nonnative; E: Low Military Value.
Climate, Genetic.
Middle Ranch Canyon................ EO 5; 5 PLs........... Unknown............... Extant (SERG 2008)... A: Erosion, Low Military Value.
Nonnative; E:
Climate, Genetic.
Waymuck Canyon..................... EO 6; 1 PL............ Unknown............... Presumed Extant A: Erosion, High Military Value.
(CNDDB 1985). Nonnative; E:
Climate, Genetic.
--------------------------------------------------------------------------------------------------------------------------------------------------------
Acmispon dendroideus var. traskiae
--------------------------------------------------------------------------------------------------------------------------------------------------------
Eagle Canyon....................... EO 1, 9 PLs........... Extant; 1980 CNDDB.... Extant (Junak 2006, A: Land Use, Erosion, Low Military Value;
SERG 2008). Nonnative, Fire; E: Area Recently
Movement, Fire, Closed.
Climate.
Bryce Canyon....................... No EO, 14 PLs......... Unknown............... Extant (SERG 2009)... A: Nonnative, Fire; : Low Military Value;
Fire, Climate. Area Recently
Closed.
North Mosquito Cove................ EO 8, 14 PLs.......... Extant; 1939 herbarium Extant (SERG 2010)... A: Land Use, Erosion, Low Military Value;
record. Nonnative, Fire; E: Area Recently
Movement, Fire, Closed.
Climate.
Canchalagua Canyon (including south EO 4, 21 PLs.......... Unknown............... Extant (SERG 2011)... A: Land Use, Erosion, Low Military Value;
Mosquito Cove). Nonnative, Fire; E: Area Recently
Movement, Fire, Closed.
Climate.
Thirst Canyon (including Vista No EO, 8 PLs.......... Unknown............... Extant (SERG 2009)... A: Nonnative, Fire; Medium Military
Canyon). E: Fire, Climate. Value.
Cave Canyon........................ No EO, 3 PLs.......... Unknown............... Presumed Extant A: Nonnative, Fire; Medium Military
(Junak 1997). E: Fire, Climate. Value.
Horse Canyon....................... No EO, 2 PLs.......... Unknown............... Presumed Extant A: Nonnative, Fire; Medium Military
(Junak 1997). E: Fire, Climate. Value.
Pyramid Head....................... EO 5, 1 PL............ Extant; 1979 CNDDB.... Presumed Extant A: Nonnative, Fire; High Military Value;
(Junak 1997). E: Fire, Climate. Area Closed.
[[Page 29084]]
SHOBA Boundary (north to Twin Dams No EO, 8 PLs.......... Unknown............... Presumed Extant A: Nonnative; E: Medium Military
Canyon). (Junak 1996). Climate. Value.
Twin Dams Canyon................... No EO, 2 PLs.......... Unknown............... Extant (Junak 2006).. A: Nonnative; E: Medium Military
Climate. Value.
Horton Canyon (including Stone, EO 13, 27 PLs......... Unknown............... Extant (SERG 2010)... A: Erosion, Medium Military
Burn's, and Horton Canyons). Nonnative; E: Value.
Climate.
Tota Canyon........................ No EO, 7 PLs.......... Unknown............... Presumed Extant (SERG A: Erosion, Low Military Value.
2010). Nonnative; E:
Climate.
Lemon Tank Canyon (including Nanny No EO, 19 PLs......... Unknown............... Extant (Junak 2004).. A: Erosion, Low Military Value;
Canyon). Nonnative; E: Area Partially
Movement, Climate. Closed.
Larkspur Canyon.................... EO 16, 2 PLs.......... Unknown............... Extant (SERG 2011)... A: Erosion, Low Military Value.
Nonnative, Fire; E:
Movement, Fire,
Climate.
Chamish Canyon..................... EO 3, 1 PL............ Extant; 1980 CNDDB.... Presumed Extant A: Erosion, Low Military Value.
(Junak 1997). Nonnative, Fire; E:
Movement, Fire,
Climate.
Box Canyon......................... No EO, 2 PLs.......... Unknown............... Presumed Extant A: Nonnative; E: Low Military Value.
(Junak 1997). Climate.
Norton Canyon...................... No EO, 1 PL........... Unknown............... Extant (Junak 2004).. A: Nonnative; E: Low Military Value.
Climate,
Hybridization.
Upper Middle Ranch Canyon.......... EO 10, 5 PLs.......... Unknown............... Extant (Junak 2004).. A: Erosion, Low Military Value.
Nonnative; E:
Climate.
Lower Middle Ranch Canyon.......... No EO, 3 PLs.......... Unknown............... Extant (SERG 2008)... A: Nonnative; E: Low Military Value.
Climate.
Waymuck Canyon..................... No EO, 4 PLs.......... Unknown............... Extant (SERG 2011)... A: Nonnative; E: High Military Value.
Climate.
Warren Canyon...................... EO 12, 20 PLs......... Unknown............... Extant (SERG 2011)... A: Erosion, High Military Value.
Nonnative; E:
Movement, Climate.
Middle Wallrock Canyon............. No EO, 10 PLs......... Unknown............... Extant (Junak 2004).. A: Nonnative; E: High Military Value.
Movement, Climate.
Upper Wallrock Canyon.............. No EO, 3 PLs.......... Unknown............... Extant (Junak 2006).. A: Erosion, High Military Value.
Nonnative; E:
Climate.
Seal Cove Terraces................. No EO, 3 PLs.......... Unknown............... Extant (Junak 2004).. A: Erosion, High Military Value.
Nonnative, Fire; E:
Movement, Fire,
Climate.
Eel Cove Canyon (including EO 14, 6 PLs.......... Unknown............... Extant (SERG 2010)... A: Erosion, High Military Value.
terraces). Nonnative, Fire; E:
Movement, Fire,
Climate.
Middle Island Plateau.............. EO 7, 6 PLs........... Unknown............... Extant (Tierra Data A: Land Use, Erosion, High Military Value.
2007). Nonnative, Fire; E:
Movement, Fire,
Climate.
Wilson Cove........................ EO 11, 52 PLs......... Extant; 1981 CNDDB.... Extant (SERG 2010)... A: Land Use, Erosion, High Military Value.
Nonnative, Fire; E:
Movement, Fire,
Climate,
Hybridization.
North Wilson Cove.................. EO 9, no PLs.......... Extant; 1959 herbarium Unknown.............. A: Erosion, High Military Value.
record. Nonnative; E:
Climate.
North Island Terraces.............. EO 15, no PLs......... Unknown............... Presumed Extant A: Erosion, Medium Military
(CNDDB 1996). Nonnative; E: Value.
Movement, Climate.
--------------------------------------------------------------------------------------------------------------------------------------------------------
Castilleja grisea
--------------------------------------------------------------------------------------------------------------------------------------------------------
Thirst Canyon (including Vista EO 10, 11 & 40; 21 PLs Extant; 1980 CNDDB.... Extant (SERG 2010)... A: Nonnative, Fire; Medium Military
Canyon). E: Climate. Value.
[[Page 29085]]
Eagle Canyon (including Grove EO 7 & 30; 50 PLs..... Extant; 1979 herbarium Extant (Tierra Data A: Land Use, Erosion, Low Military Value;
Canyon). record. 2006). Nonnative, Fire; E: Area Recently
Movement, Climate. Closed.
Bryce Canyon....................... EO 3, 8 & 47; 43 PLs.. Extant; 1979 GIS data. Extant (SERG 2010)... A: Land Use, Erosion, Low Military Value;
Nonnative, Fire; E: Area Recently
Movement, Climate. Closed.
Canchalagua Canyon (including south EO 4 & 27; 56 PLs..... Extant; 1963 herbarium Extant (SERG 2011)... A: Land Use, Erosion, Low Military Value;
Mosquito Cove and Matriarch record. Nonnative, Fire, Area Recently
Canyon). Fire Management; E: Closed.
Movement, Climate.
Knob Canyon........................ EO 2 & 49; 21 PLs..... Extant; 1979 CNDDB.... Extant (Tierra Data A: Land Use, Erosion, Low Military Value;
2006, SERG 2008). Nonnative, Fire, Area Recently
Fire Management; E: Closed.
Movement, Climate.
Pyramid Head....................... EO 1 & 15; 25 PLs..... Extant; 1965 herbarium Extant (SERG 2011)... A: Land Use, Erosion, High Military Value;
record. Nonnative, Fire; E: Partially Recently
Movement, Climate. Closed.
Snake Canyon (including Sun Point). EO 23; 4 PLs.......... Extant; 1939 CNDDB.... Presumed Extant A: Nonnative, Fire; High Military Value;
(Junak 1997). E: Fire, Climate. Area Closed.
Upper Chenetti Canyon.............. EO 34; 1 PL........... Unknown............... Extant (Junak 2004).. A: Nonnative, High Military Value;
Erosion, Fire, Fire Area Closed.
Management; E: Fire,
Climate.
Horse Beach Canyon................. EO 33 & 35; 49 PLs.... Extant; 1939 herbarium Presumed Extant A: Land Use, Erosion, High Military Value;
record. (Junak 2005). Nonnative, Fire, Area Closed.
Fire Management; E:
Movement, Fire,
Climate.
China Canyon....................... EO 25, 37 & 46; 6 PLs. Extant; 1939 herbarium Presumed Extant A: Land Use, Erosion, High Military Value;
record. (Junak 1997; SERG Nonnative, Fire, Area Closed.
2009). Fire Management; E:
Movement, Fire,
Climate.
Red Canyon......................... EO 36; no PLs......... Extant; 1975 herbarium Presumed Extant A: Land Use, Erosion, High Military Value;
record. (CNDDB 1986). Nonnative, Fire, Area Closed.
Fire Management; E:
Movement, Fire,
Climate.
Kinkipar Canyon.................... No EO; 2 PLs.......... Unknown............... Extant (SERG 2006)... A: Nonnative, Fire; Medium Military
E: Climate. Value.
Cave Canyon........................ EO 17, 18 & 45; 9 PLs. Extant; 1980 CNDDB.... Extant (SERG 2009)... A: Nonnative, Fire; Medium Military
E: Climate. Value.
Horse Canyon....................... No EO; 6 PLs.......... Unknown............... Extant (SERG 2010)... A: Nonnative, Fire; Medium Military
E: Climate. Value.
Upper Horse Canyon................. EO 19 & 39; 1 PL...... Extant; 1979 CNDDB.... Extant (Junak 2004).. A: Erosion, Medium Military
Nonnative, Fire; E: Value.
Climate.
SHOBA Boundary (north to and EO 31; 55 PLs......... Extant; 1965 CNDDB.... Extant (Junak 2006, A: Nonnative; E: Medium Military
including Twin Dams Canyon). SERG 2011). Climate. Value.
Horton Canyon (including Stone and EO 12 & 44; 24 PLs.... Extant; 1981 CNDDB.... Extant (Junak 2006, A: Erosion, Medium Military
Burn's Canyons). SERG 2010). Nonnative; E: Value.
Climate.
Lemon Tank Canyon (including Tota No EO; 14 PLs......... Unknown............... Extant (SERG 2010)... A: Land Use, Erosion, Low Military Value;
Canyon). Nonnative, Fire; E: Area Closed.
Movement, Fire,
Climate.
Nanny Canyon....................... EO 13; 3 PLs.......... Extant; 1979 CNDDB.... Extant (Junak 2004).. A: Nonnative; E: Low Military Value;
Movement, Climate. Area Partially
Closed.
[[Page 29086]]
Larkspur Canyon (including Chamish EO 14 & 48; 15 PLs.... Extant; 1981 CNDDB.... Extant (SERG 2006-- A: Land Use, Erosion, Low Military Value.
Canyon). 2011). Nonnative, Fire; E:
Movement, Fire,
Climate.
Box Canyon......................... EO 20 & 41; 22 PLs.... Extant; 1979 CNDDB.... Extant (SERG 2011)... A: Nonnative; E: Low Military Value.
Climate.
Upper Norton Canyon................ EO 21; 6 PLs.......... Extant; 1979 CNDDB.... Extant (SERG 2011)... A: Nonnative; E: Low Military Value.
Climate.
Middle Ranch Canyon................ EO 24; 8 PLs.......... Extant; 1981 CNDDB.... Extant (SERG 2008)... A: Nonnative; E: Low Military Value.
Climate.
Waymuck Canyon..................... EO 22; 1 PL........... Unknown............... Extant (Junak 2004).. A: Nonnative; E: High Military Value.
Climate.
Plain northeast of Warren Canyon... No EO; 4 PLs.......... Unknown............... Extant (Tierra Data A: Land Use, Erosion, Medium Military
2007). Nonnative; E: Value.
Movement, Climate.
Seal Cove Terraces................. EO 43; 2 PLs.......... Unknown............... Extant (CNDDB 1985, A: Erosion, High Military Value.
SERG 2010). Nonnative, Fire; E:
Movement, Fire,
Climate.
Eel Cove Canyon (including No EO; 3 PLs.......... Unknown............... Extant (Junak 2004).. A: Nonnative, Fire; High Military Value.
terraces). E: Movement, Fire,
Climate.
Terrace Canyon (south to terraces No EO; 6 PLs.......... Unknown............... Presumed Extant (SERG A: Erosion, High Military Value.
around Spray). 2004). Nonnative; E:
Movement, Climate.
West Cove.......................... No EO; 3 PLs.......... Unknown............... Extant (Tierra Data A: Land Use, Erosion, Medium Military
2006). Nonnative; E: Value.
Movement, Climate.
--------------------------------------------------------------------------------------------------------------------------------------------------------
\1\ EO: element occurrence, as defined and described according to the California Natural Diversity Database. PL: point locations of plants.
\2\ Threats identified in the listing rule for these three taxa include: Factor A: habitat modification by feral animals; Factor C: grazing by animals;
Factor E: nonnative plants.
\3\ Current threats: Nonnative = Nonnative Plants; Movement = Movement of Vehicles and Troops; Climate = Climate Change; Genetic = Genetic Diversity.
\4\ Military value as defined in the Navy's 2002 Integrated Natural Resources Management Plan (INRMP). Values defined according to the management
emphasis, with high-value areas designated for maximum military use and low-value areas retaining the greatest flexibility for maintaining natural
resource values.
Species Distribution--Malacothamnus clementinus
For many decades prior to its listing, Malacothamnus clementinus
was only known from the type locality (the area where the species is
first identified and described) at Lemon Tank Canyon, on the eastern
side of the middle of the island (Kearney 1951, p. 128; USFWS 1984, p.
48). Dumping of scrap metal actually protected this occurrence from the
ongoing threat of feral goat herbivory by preventing the goats from
destroying the plants (USFWS 1984, p. 48). The historical range and
distribution of M. clementinus on San Clemente Island is unknown
because surveys were not carried out before the plant's decline. In the
Recovery Plan, we noted that a public citizen commented in the Listing
Rule on the discovery of two to three small plants on the edge of an
inaccessible ledge in China Canyon (now described as two occurrences--
Lower China Canyon and Upper China Canyon; 42 FR at 40683; USFWS 1984,
p. 48). These two occurrences, along with the occurrence at Lemon Tank,
were known at the time of listing. Since listing, eight new occurrences
of M. clementinus have been discovered among the generally
southwesterly facing coastal terraces and their associated escarpments
in the southern and middle regions of San Clemente Island (Junak and
Wilken 1998, pp. 1-416, GIS data; Junak 2006, pp. 1-176, GIS data;
Tierra Data Inc. 2008, pp. 1-24, appendices and GIS data; SERG 2009-
2011, GIS data; Figure 1). Many of these new occurrences have appeared
since feral goats and pigs were removed from the island in the early
1990s. This suggests the possibility that the plants reemerged from
underground stems that survived grazing by feral herbivores (Junak
2006a, pers. comm.).
Malacothamnus clementinus occurrences are scattered below canyon
rims, at the base of terrace escarpments, and in flat areas from
approximately Middle Ranch Canyon in the north to Horse Beach Canyon in
the south. A large, genetically diverse occurrence is found within
Horse Beach Canyon (Helenurm 1999, pp. 39-40). Ten of the 11 known
occurrences are located throughout the southwestern region of the
island; in addition, the Lemon Tank Canyon occurrence is located in the
northeastern region of the island (Figure 1). Six of the occurrences
are within SHOBA, and five are to the north outside of SHOBA. The main
southern distribution of M. clementinus is disconnected from the
historical type locality (the area where the species is first
identified and described) of the species, which is the Lemon Tank
Canyon occurrence. Lemon Tank lies about 3.6 mi (5.8 km) to the
northeast of the nearest occurrence (Waymuck Canyon). The Lemon Tank
Canyon occurrence has not been resurveyed since 1996, and its current
status is uncertain and presumed extant (CNDDB
[[Page 29087]]
2011a, p. 2). Beyond the 11 known occurrences, there is an additional
record of M. clementinus in the northern plateau area of the island,
near Ridge Road, but this has not been confirmed despite targeted
searches for the plant (SERG 2006, GIS data; Howe 2011a, pers. comm.).
We are not considering this record as a known occurrence at this time
due to the possibility of error.
The known range of M. clementinus has expanded to the south on San
Clemente Island since its listing, with the distance between the
northernmost and southernmost occurrence spanning about 9.5 mi (15.3
km). Occurrences within Impact Areas I and II in the southwestern
portion of the island (within SHOBA) have not been surveyed since 2006,
largely due to area closures implemented through the recent MOFMP (Navy
2008a, pp. 2-38 to 2-44; Munson 2011a, pers. comm.). Because of these
closures, we were unable to evaluate the status of occurrences in Horse
Beach Canyon, Lower China Canyon, and part of Upper China Canyon for
this review. While the remaining eight occurrences fall outside of
these Impact Areas, one of the largest and most genetically diverse of
the 11 known occurrences, Horse Beach Canyon, is within the restricted
area.
BILLING CODE 4310-55-P
[[Page 29088]]
[GRAPHIC] [TIFF OMITTED] TP16MY12.002
Aerial stems of Malacothamnus clementinus can sprout from spreading
underground stems (rhizomes). This makes it difficult to distinguish
individual plants among groups of stems. Consequently, the size of an
occurrence has been variously measured by counting the number of stem
groupings or ``clumps,'' counting the total number of stems within a
clump, and measuring the approximate area covered by plant groupings.
These inconsistent survey methods make it difficult to document
occurrence trends beyond the appearance of new
[[Page 29089]]
occurrences. There is no detailed information about the abundance
(number or density of plants) of M. clementinus at the time of its
listing in 1977 (42 FR 40683). Occurrences documented in 1996 to 1997
ranged in size from 1 to 50 clumps (Junak and Wilken 1998, p. 301). The
Navy recently estimated 1,516 individuals of M. clementinus recorded
since 2006 (Munson 2011d, pers. comm.). However, given the challenge in
distinguishing individuals in a group of plants, and variability in
methods of estimating the number of individuals, it is difficult to
accurately quantify the abundance of M. clementinus on San Clemente
Island and, as such, numbers should be interpreted cautiously.
Despite difficulties in determining species abundance, extensive
surveys for Malacothamnus clementinus have detected 8 new occurrences
since listing, for a total of 11 occurrences. This suggests that the
species is responding favorably to the elimination of grazing pressure
from feral herbivores on San Clemente Island. It is unknown to what
extent this increase is attributable to more intensive survey efforts,
detection of previously undetected individuals, recruitment from the
seed bank, resprouting from rhizomes, recolonization associated with
dispersal events, or management efforts.
Species Distribution--Acmispon dendroideus var. traskiae
Since the 1970s, the distribution of Acmispon dendroideus var.
traskiae has been documented on north-facing slopes over most of the
eastern and western sides of the island (USFWS 1984, p. 59; Junak and
Wilken 1998, p. 256; Navy 2002, p. D-9; Junak 2006, p. 125). Twenty-
nine occurrences of this taxon have been identified, which span the
entire length of the island from Wilson Cove to the southern tip east
of Pyramid Cove, a distance of approximately 19 mi (31 km) (Junak and
Wilken 1998, p. 261; Junak 2006, Map A-C) (Figure 2). The majority of
occurrences tend to be clustered on north-facing slopes on the eastern
side of the island (Table 1). The distribution of A. d. var. traskiae
spans the boundary of SHOBA at the southern end of the island: 8
occurrences fall within SHOBA and 21 are outside (Junak and Wilken
1998, pp. 1-416, GIS data; Junak 2006, pp. 1-176, GIS data; Tierra Data
Inc. 2008, pp. 1-24, appendices and GIS data; SERG 2009-2011, GIS
data). Approximately 13 of 29 (45 percent) of the occurrences (Wilson
Cove, Canchalagua Canyon, Middle Island Plateau, North Mosquito Cove,
Eagle Canyon, Larkspur Canyon, Chamish Canyon, Lemon Tank Canyon, Seal
Cove Terraces, Eel Cove Canyon, Middle Wallrock Canyon, Warren Canyon,
and North Island Terraces) are partially or wholly within the
boundaries of a training area (IOA, TAR, or SWAT).
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Acmispon dendroideus var. traskiae tends to occur in small groups
of 10 to 50 individuals (Allan 1999, p. 84). There is no information
about the abundance of A. d. var. traskiae at the time of its listing
in 1977. In the 1984 Recovery Plan (USFWS, p. 59), six occurrences of
A. d. var. traskiae were recognized, all generally associated with
rocky areas. However, no other specific information regarding species
location or numbers of individuals at those six sites was provided in
the Recovery Plan, except the statement that ``the largest number of
plants grow in the vicinity of
[[Page 29091]]
Wilson Cove'' (USFWS 1984, p. 59). Additionally, there are only a few
herbarium specimens of the taxon, making historical distribution and
condition of the species difficult to assess. For purposes of
comparison to the current status, we will use the number of occurrences
cited in the recovery plan as the most conservative estimate of
species' distribution around the time of its listing (Table 1). Thus,
the historical range (based on herbarium records, CNDDB records, and
the recovery plan) includes occurrences in the northern part of the
island (Wilson Cove) down to the southern point (Pyramid Head).
CNDDB currently lists 14 element occurrences of Acmispon
dendroideus var. traskiae (as Lotus dendroideus subsp. traskiae) (CNDDB
2011b) that are presumed extant. These occurrences are located on both
the western and eastern sides of the island and are distributed across
almost the entire length of the island. Recently, survey efforts have
concentrated on discovering new plant occurrences, rather than tracking
the status of historical occurrences (Junak 2006a, pers. comm.). New
observations were mainly concentrated on north-facing slopes in the
middle of the island, both on the eastern and western sides. Analysis
of these newer point localities revealed proximity to individuals
detected during the 1996 and 1997 surveys. These element occurrences
and point localities combined total 29 separate A. d. var. traskiae
occurrences (Table 1).
Abundance is difficult to determine for this species because range-
wide surveys were not conducted each year. Instead, monitoring took
place over multiple years with varying conditions. A recent estimate
from the Navy reported 3,525 individuals of Acmispon dendroideus var.
traskiae recorded since 2006 (Munson 2011d, pers. comm.). Even though
there is uncertainty in the number of individuals, the number of
occurrences has increased from 6 to 29. Thus, extensive survey findings
suggest that A. d. var. traskiae has increased throughout most of its
historical range, and there are more occurrences now than there were at
the time of listing. It is unknown to what extent this increase is
attributable to more intensive survey efforts, detection of previously
undetected individuals, recruitment from the seed bank, recolonization
associated with dispersal events, or management efforts. The increase
in number of occurrences could indicate an increase in the distribution
of A. d. var. traskiae on San Clemente Island.
Species Distribution--Castilleja grisea
Castilleja grisea was described as relatively common on San
Clemente Island in the 1930s, and subsequently declined as a result of
unchecked grazing by introduced feral herbivores (Helenurm et al. 2005,
p. 1222). The historical range and distribution of C. grisea on San
Clemente Island is unknown because botanical studies were not completed
before the plant's decline. Herbarium records documented the species on
the south and east sides of the island before the time of listing
(California Consortium of Herbaria 2011, records for C. grisea). By
1963, C. grisea was reported as rare or occasional (Raven 1963, p.
337). Since the complete removal of goats and pigs from San Clemente
Island in 1992, C. grisea has been detected across much of the island
(Helenurm et al. 2005, pp. 1221, 1226; Junak 2006, p. 47; USFWS 2007c,
p. 14). Plants have been recorded across the southern two-thirds of the
island, and a single disjunct occurrence was documented at the northern
end in West Cove (Junak and Wilken 1998, pp. 1-416, GIS data; Junak
2006, pp. 1-176, GIS data; Tierra Data Inc. 2008, pp. 1-24, appendices
and GIS data; SERG 2009-2011, GIS data) (Figure 3). The distribution of
any parasitic or hemiparasitic plant is limited by the distribution of
its host or hosts. However, host availability does not appear to be
limiting the abundance of this species.
The linear distance between the northernmost and southernmost
occurrences is 19.7 mi (32 km), with plants primarily distributed
across the southern 15.5 mi (25 km) of the island. Occurrences on the
southern end of the island on both the western and eastern sides are
reported in the CNDDB (CNDDB 2011c). We combined CNDDB element
occurrences with adjacent point localities from island surveys to
identify Castilleja grisea occurrences (Table 1). The known
distribution for C. grisea documented since 1992 reflects a more
continuous and slightly expanded distribution since the time of listing
(Tierra Data Inc. 2008, p. B-3). Survey efforts have concentrated on
discovering new occurrences rather than tracking the status of
historical occurrences (Junak, 2006a, pers. comm.). Using available GIS
and distribution data, we have determined there are 29 occurrences of
C. grisea currently on the island; only 19 of these were known at
listing.
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(Table 1). The extant occurrences at listing are derived from herbarium
records, CNDDB records, and information in the Recovery Plan.
Distribution of C. grisea extends into SHOBA at the southern end of the
island; 15 occurrences fall within and 14 outside of SHOBA.
A number of surveys have found new occurrences throughout the
island (Junak and Wilken 1998, GIS data; Junak 2006, GIS data; Tierra
Data Inc. 2008, GIS data; SERG 2009-2011, GIS data; CNDDB 2011c). Most
new observations were concentrated in steep canyons on the western side
of the island, although a few were discovered near previously
[[Page 29093]]
recorded individuals in the eastern canyons. Recent counts, based on
the Navy's data, estimate 11,733 individuals of Castilleja grisea since
2006 (Munson 2011d, pers. comm.). Extensive survey efforts since 1992
suggest C. grisea has filled in its known historical range on the
island, and there are more individuals now than at listing. Even though
there is uncertainty in the number of individuals, the number of
occurrences of species has increased from 19 to 29. It remains unknown
how much of this apparent increase in range density can be attributed
to more intensive survey efforts, detection of previously undetected
individuals, recruitment from the seed bank, recolonization associated
with dispersal events, or management efforts. However, the increase in
the number of occurrences suggests an expansion of the species across
the island.
Habitat
General Habitat Conditions
Current habitat conditions for Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea on San Clemente Island
are the result of present and historical land use practices. San
Clemente Island has been inhabited by humans for thousands of years
(Schoenherr et al. 1999, p. 317). There is evidence that the Gabrielino
people used the island for harvesting marine organisms before European
settlers arrived. The first lease for sheep ranching was granted in
1848 (Schoenherr et al. 1999, p. 317). From 1850 until 1934, San
Clemente Island was used for sheep and cattle ranching, goat grazing,
and pig farming (Navy 2002, pp. 3-4). Some accounts even report goats
present on the island as early as 1827 (Dunkle 1950, p. 261). These
nonnative herbivores greatly changed the vegetative landscape of San
Clemente Island, and were cited in the final listing rule (42 FR 40682;
August 11, 1977) for M. clementinus, A. d. var. traskiae, and C. grisea
as the main cause of these species' decline. Sheep were removed from
the island in the 1930s, but feral goats and pigs were not completely
eradicated until 1992. Since the removal of goats and pigs, the
vegetation on San Clemente Island has rebounded, and the condition of
many rare plants has improved (Junak 2006a, pers. comm.). As a
persistent historical impact to the landscape, overgrazing also led to
the creation of bare trails, denuded areas, and severe erosion. Grazing
animals also facilitated the introduction and spread of nonnative
plants. Specifically, nonnative grasses were spread through grazing and
ranching on the island (Navy 2002, p. 3-31).
Fire
Past and current fire regimes (pattern, frequency, and intensity of
fire in an area) have influenced the distribution of native and
nonnative plants on San Clemente Island (Navy 2002, p. 3-28). Although
the natural fire regime of the island is unknown, there have only been
three documented lightning ignitions of wildfires on the Channel
Islands in 140 years (Carroll et al. 1993, p. 83). Natural fire
ignition was probably rare, as lightning-caused fires tend to be less
frequent with proximity to the coastline, due to higher fuel moisture
levels and a cooler climate (Keeley 1982, pp. 436-437; Keeley 2002, p.
305). While the island was used for ranching, fires were set
intermittently to increase the forb and grass cover (Navy 2002, p. 3-
29). After purchase by the Navy in 1934, fire ignited by military
training activities became a more common occurrence throughout much of
the island.
It was assumed in previous descriptions that Malacothamnus
clementinus is adapted to, and tolerant of, the periodic fires that
probably occurred in a prehistorical, lightning-ignition fire regime,
although there is no direct research to support this assumption (USFWS
1984. p. 48; Navy 2002, D-20; USFWS 2007a, p. 3). Other species in the
same genus are fire tolerant and able to adapt, such as Malacothamnus
fremontii (Fremont's bushmallow), a primary successional species that
can form the major shrub cover after a fire (Rundel 1982, p. 86). The
seeds of M. fremontii are stimulated by heat shock treatments,
suggesting that it is adapted to germinate after fires (Keeley et al.
2005, p. 175). Another related species, M. fasciculatus (Mendocino
bushmallow), germinates after being stimulated by heat and is known to
flourish after fires (Swensen et al. 1995, pp. 412-413; Beyers and
Wakeman 1997, p. 2). Malacothamnus clementinus has underground stems,
and can resprout after disturbance to reproduce vegetatively. The fire
tolerance of the genus and its ability to resprout suggest that M.
clementinus may be adapted to fire. Although no direct research has
been done on the effects of fire on M. clementinus, its continued
presence in areas that have burned (such as SHOBA) indicates that it is
tolerant of at least occasional fire (intervals of at least 5 years)
(Navy 2008b, pp. 3.11-24, 3.11-81). However, frequent fires could
exceed its tolerance of fire intensity and frequency.
The fire tolerance of Acmispon dendroideus var. traskiae is
unknown. Some studies have shown that the related mainland species,
Lotus scoparius (deerweed), is fire tolerant and becomes more abundant
in years after fire (Nilsen and Schlesinger 1981, p. 217; Westman and
O'Leary 1986, pp. 184-185). Other studies indicate that intense or
frequent burns (three times in 6 years) of L. scoparius lead to
establishment of fewer seedlings (Westman and O'Leary 1986, p. 185;
Haidinger and Keeley 1993, p. 141). In San Clemente Island species,
observations show that Acmispon argophyllus var. adsurgens (San
Clemente Island bird's-foot trefoil) germination is slowed or depressed
after fire, but A. argophyllus var. argenteus (silver bird's-foot
trefoil) flourishes in burn areas (Allan 1999, pp. 90-91). Observations
of A. d. var. traskiae before and several years following a fire in
Canchalagua Canyon found that adult plants were usually killed by fire,
but were replaced with a similar number of seedlings after the fire
(Navy 2002, p. D-10; Tierra Data Inc. 2005, p. 80). Based on A. d. var.
traskiae's growth characteristics and occurrence increases in areas
affected by fire, and the fire adaptations of related species, A. d.
var. traskiae may be resilient to at least occasional fire. Frequent
fires could exceed its tolerance of fire intensity and frequency, and
exhaust the seed bank in repeatedly burned areas. Until studies can be
conducted specifically on A. d. var. traskiae, it is prudent to avoid
the conclusion that the species benefits from, or germinates with,
fire.
The fire tolerance of Castilleja grisea is unknown at this time. We
do not know of any studies conducted on the fire tolerance of this
species, and there is very little information from related species to
infer fire tolerance for the genus Castilleja. A related rare species,
C. levisecta (golden Indian paintbrush), tolerates fire and performs
better in areas that have burned in the past (Dunwiddie 2002, p. 1;
Dunwiddie 2009, p. 5). Castilleja grisea has survived and expanded its
distribution in areas that have burned. It is generally assumed that
the species has some tolerance of infrequent fire (Navy 2002, D-32)
based on C. grisea occurrence increases in areas affected by fire, and
the fire adaptations of other plants in the genus. However, until
species-specific research is conducted, we cannot conclude with
certainty that C. grisea is adapted to fire. Additionally, research is
needed on the fire tolerance of potential host plants and their impacts
on establishment of C. grisea.
Although the three species share the same island habitat, they
inhabit different niches. The habitat
[[Page 29094]]
characteristics of each species are discussed below.
Habitat--Malacothamnus clementinus
Malacothamnus clementinus occurs in a variety of habitats on San
Clemente Island. Historically, it was observed on rocky canyon walls
and ridges, presumably because foraging goats did not graze those
areas. More recently, M. clementinus has been found at the base of
escarpments between coastal terraces on the western side of the island
within maritime cactus scrub (Navy 2002, pp. D-19, D-20). It can also
occur on low canyon benches and in rocky grasslands. Malacothamnus
clementinus is found at approximately 30 to 900 ft (10 to 275 m)
elevation (CNPS 2001, p. 215). Moisture that collects in rock crevices
and at the base of canyon walls and escarpments may provide favorable
conditions for this species (Junak 2006a, pers. comm.). Based on its
habitat range on the island and the ease of cultivating the plant, M.
clementinus appears to tolerate a broad range of soil types (USFWS
1984, p. 50). It is often associated with maritime cactus scrub
vegetation on coastal flats at the southwestern end of the island
(Junak and Wilken 1998, p. 256). In the INRMP, M. clementinus is listed
as associated with canyon woodlands (approximately 696 ac (282 ha)),
maritime desert scrub-prickly pear vegetation community (approximately
8,921 ac (3,610 ha)), and maritime sage scrub (approximately 369 ac
(149 ha)) (Navy 2002, pp. 3-57, 3-63, 3-66). According to Junak and
Wilken (1998, p. 290), it is associated with numerous plant species,
including: Artemisia californica (California sage brush), Avena fatua
(wild oat), Bromus spp. (brome grass), Calystegia macrostegia subsp.
amplissima (island morning glory), Encelia californica (California
brittlebush), Nassella cernua (nodding needlegrass), Nassella lepida
(foothill stipa), Opuntia littoralis (western prickly pear), Opuntia
oricola (chaparral prickly pear), Opuntia prolifera (cholla), and Rhus
intergrifolia (lemonade sumac).
Habitat--Acmispon dendroideus var. traskiae
Acmispon dendroideus var. traskiae occurs on north-facing slopes,
canyon bottoms, or ridgelines (Junak 2006, p. 125). Plants grow
somewhat colonially around rock outcrops and boulders in grassy areas,
and along the interface between grassland and maritime sage scrub
(Allan 1999, p. 84; Navy 2002, p. D-9). Acmispon dendroideus var.
traskiae occurs between 25 and 1,400 ft (7.6 to 463 m) in elevation on
well-drained soils where adequate soil moisture is available to the
plant (Junak and Wilken 1998, p. 256; Navy 2002, p. D-9). Some plants
have been found in close proximity to buildings, roads, and pipelines,
indicating that A. d. var. traskiae is capable of colonizing disturbed
areas (Allan 1999, p. 84; Navy 2002, p. D-9). A. d. var. traskiae is
associated with two habitat types on the island: Canyon woodland
supported on approximately 696 ac (282 ha) and maritime desert scrub
along the northeastern escarpment supported on approximately 6,228 ac
(2,520 ha) (Navy 2002, pp. 3-57, 3-58). According to Junak and Wilken
(1998, p. 256), A. d. var. traskiae is associated with numerous plant
species including, but not limited to: Artemisia californica, Avena
fatua, Bromus spp., Calystegia macrostegia subsp. amplissima,
Dichelostemma capitatum (wild hyacinth), Gnaphalium bicolor (bicolored
everlasting), Hemizonia clementina (island tarplant), Opuntia spp.
(prickly pear), Nassella pulchra (purple stipa), and Quercus
tomentella (island live oak).
Habitat--Castilleja grisea
Castilleja grisea is often associated with coastal sage scrub found
on approximately 369 ac (149 ha) of the island and maritime desert
scrub plant communities found on approximately 5,858 ac (2,371 ha),
with scattered concentrations of plants in canyon woodland
(approximately 696 ac (282 ha)) and grassland habitat (approximately
8,921 ac (3,610 ha)) (Navy 2002, pp. 3-58, 3-63, 3-66). Plants are
located in steep, rocky canyons on both the eastern escarpment and
western side of the island, although some have been observed on coastal
bluffs, slopes, and terraces around the island's perimeter. Some of the
largest concentrations of plants are located in bowl-shaped swales on
coastal terraces (Junak and Wilken 1998, p. 82). Castilleja grisea
grows between 32 and 2,000 ft (10 and 365 m) in elevation. This
hemiparasitic plant is known to parasitize many different plants,
although a definitive understanding of host-plant associations is
currently unknown. Potential host plants include Calystegia macrostegia
subsp. amplissima (island morning glory), Opuntia littoralis (prickly
pear), and Constancia nevinii (Nevin's eriophyllum). These may be
important habitat components for C. grisea. Junak and Wilken (1998, p.
82) suggest that habitat conditions must be of sufficient quality to
sustain potential host plants and provide opportunities for C. grisea
establishment. Numerous plant species are associated with C. grisea
including, but not limited to: Artemisia californica, Calystegia
macrostegia subsp. amplissima, Encelia californica, Constancia nevinii
(Nevin's woolly sunflower), Hemizonia clementina, Isocoma menziesii
(Menzies' goldenbush), Lycium californicum (California boxthorn), and
Opuntia spp. (Junak and Wilken 1998, p. 82).
Biology and Genetics
Biology--Malacothamnus clementinus
Malacothamnus clementinus is an herbaceous clonal plant (descended
asexually from a single individual) that may spread locally by
underground rhizomes that produce aerial stems. On average there are 90
flowers per inflorescence (a flower cluster) (Junak and Wilken 1998, p.
291). The species flowers in the spring, typically from March to August
(Kearney 1951, p. 115; Navy 2002, D-19; California Native Plant Society
2011). Junak and Wilken (1998, p. 291) found that M. clementinus is
self-compatible (capable of self-fertilization), but not self-
pollinating. The plant produced seed when hand pollinated with pollen
from the same plant, but not when flowers were bagged to prevent
pollinator visitations (Junak and Wilken 1998, p. 291). It is generally
thought that M. clementinus is pollinated by insects, although no
specific pollinator for this species is known. Other species in the
family Malvaceae are pollinated by specialist bees in the genus
Diadasia (Sipes and Tepedino 2005, p. 487). Given the evidence that
suggests pollinators may be necessary for successful seed production, a
decline in M. clementinus may in part be due to a decline in
pollinators or an absence of pollinator visitations (Junak and Wilken
1998, p. 291).
Each fertilized flower produces three to four seeds on average
(Junak and Wilken 1998, p. 291). Seed production in natural occurrences
of Malacothamnus clementinus is very low (Helenurm 1997, p. 51;
Helenurm 1999, p. 39; Junak 2006a, pers. comm.), as is germination,
with low germination rates of only 4 to 35 percent (Evans and Bohn
1987, p. 538; Junak and Wilken 1998, p. 291). Junak and Wilken (1998,
p. 291) hypothesized that the relatively low number of seeds produced
in situ could be due to low pollinator visitation rates or some other
unknown factor. Seed germination may be stimulated by heat associated
with fire in other Malvaceae species, although this has not been
studied in M. clementinus (Keeley et al. 2005, p. 175). Junak and
Wilken (1998, p. 291) tried scarifying seeds (softening the outer coat
of a seed through
[[Page 29095]]
mechanical or chemical means) to promote germination, but this did not
significantly increase germination rates. Based on these limited
studies of seed production and germination in M. clementinus, it is
difficult to determine the cause of its low reproductive output.
In addition to sexual reproduction, Malacothamnus clementinus can
reproduce vegetatively, or clonally, by sprouting from rhizomes (Evans
and Bohn 1987, p. 538). Because M. clementinus typically occurs in
clusters of stems, it is difficult to differentiate between
individuals, as rhizome sprouts can also look like seedlings.
Therefore, it can be a challenge to determine in the field if a small
plant is a seedling or a sprout without digging up the root system
(Junak 2006b, pers. comm.). The life history of M. clementinus suggests
that many of the newly detected occurrences have sprouted from
underground rhizomes (Junak 2006a, pers. comm.).
Genetics--Malacothamnus clementinus
Genetic studies have provided insights into the clonal nature of
Malacothamnus clementinus. Overall, genetic diversity found in the M.
clementinus occurrences is very low compared with other island endemic
plant taxa (Helenurm 1999, p. 40). However, individuals in a patch do
not represent the same genetic individual, and there is genetic
diversity within patches of M. clementinus (Helenurm 1999, p. 39). A
substantial proportion of the genetic diversity in M. clementinus is
found among different occurrences rather than within a single
occurrence. This research indicates that each occurrence may contain
unique genetic variation not found elsewhere, and that there is not
much cross pollination or gene flow between occurrences or even patches
in the same area (Helenurm 1999, pp. 39-40); this underscores the high
conservation value of each of the different occurrences to the long-
term survival and recovery of the species.
Malacothamnus clementinus may have low genetic fitness due to small
occurrence numbers, low seed production, and low genetic diversity.
Helenurm (1999, p. 40) found that most of the species' genetic
variation is within the Box Canyon and Horse Beach Canyon occurrences,
although other occurrences may contain unique genetic material not
found elsewhere (Helenurm 1999, p. 40). Occurrences of M. clementinus
could be vulnerable to inbreeding depression (loss of vigor and general
health) and reduced seed production due to apparently limited
outcrossing (reproduction between individuals of different strains) of
the plant (Helenurm 1997, p. 50; Helenurm 1999, p. 40).
Biology--Acmispon dendroideus var. traskiae
Acmispon dendroideus var. traskiae flowers between February and
August, with halictid bees (a family of small solitary bees that
typically nest in the ground), bumblebees, and small beetles observed
foraging on the flowers (Junak and Wilken 1998, p. 257; Allan 1999, pp.
64, 85). The taxon is self-compatible (Allan 1999, pp. 85-86), but
plants may also rely on insects for more effective pollination (Arroyo
1981, pp. 728-729). Fertilized ovaries develop into a slender, beak-
like fruit 1 to 2 in (2.5 to 5 cm) long containing up to six seeds
(Isely 1993, p. 619; Junak and Wilken 1998, p. 257; Allan 1999, p. 82).
The fruits do not split open to release their seeds at maturity (Isely
1993, p. 619), so it is likely that they disperse close to the parent
plants, which may limit the ability of A. d. var. traskiae to colonize
unoccupied suitable habitat. Junak and Wilken (1998, p. 257) found
that, on average, a single A. d. var. traskiae individual can produce
approximately 36 to 64 flowering shoots, 118 to 144 flowers per shoot,
and 4 to 6 seeds per fruit. This suggests that, under ideal conditions,
an individual A. d. var. traskiae can produce a high volume of seeds
(16,000 or more). Like most legumes, A. d. var. traskiae seeds require
scarification or gradual seed coat degradation to germinate (Wall 2011,
pers. comm.).
Genetics--Acmispon dendroideus var. traskiae
Allan (1999, pp. 1-105) analyzed 10 California mainland and Channel
Island taxa of Lotus (all of which are now in the genus Acmispon and
referred to as such here), including Acmispon dendroideus var.
traskiae. Of the 29 occurrences of A. d. var. traskiae on San Clemente
Island, Allan (1999, pp. 50-53) sampled only the Wilson Cove
occurrence. The Acmispon island populations, including A. d. var.
traskiae, tended to have lower genetic variability than mainland
populations (Allan 1999, p. 63). There are several possible
explanations for this lower genetic variation, including small
occurrence size, genetic bottlenecks associated with the establishment
of new island occurrences, stochastic events (a random incident such as
local extinctions), and genetic isolation (Allan 1999, p. 63). Allan's
(1999, p. 61) analysis of genetic diversity also found that the
majority (67 percent) of A. d. var. traskiae's variability is found
among, rather than within, occurrences. He postulated that the low
genetic variability within a given occurrence may be due to endemism
(native to or confined to a certain region), partial inbreeding,
isolation, and stochastic events in small occurrences (Allan 1999, pp.
63-64).
Acmispon dendroideus var. traskiae has been known to hybridize with
A. argophyllus var. argenteus in disturbed areas in Wilson Cove (Liston
et al. 1990, pp. 239-240; Allan 1999, p. 86). Based on intermediate
characteristics, the hybrid plants appear to be first generation plants
(F1 generation) from a cross between the two varieties. It
is not known whether these plants are capable of producing viable seeds
by backcrossing between the hybrids or with the putative parent plants
(Allan 1999, p. 86). Plants of intermediate morphology were first
observed by R.M. Beauchamp in 1986 (Liston et al. 1990, p. 239). In
April 1989, Liston et al. (1990, pp. 239-240) noted a small number of
suspected hybrids in the same area as the largest known occurrence of
A. d. var. traskiae in Wilson Cove. A smaller group of nonhybrid A.
argophyllus var. argenteus was found approximately 80 ft (24.4 m)
upwind; the two taxa were separated by a road. No documented evidence
of hybridization has been recorded anywhere else on the island (Allan
1999, p. 86), although there are unconfirmed reports in other areas
(e.g., Warren Canyon; A. Braswell 2011, pers. obs.).
Biology--Castilleja grisea
All taxa of Castilleja are considered hemiparasitic. Plants are
capable of photosynthesis and can exist without a host, but are able to
derive water, nutrients, or photosynthates from a host plant if present
(Heckard 1962, p. 25). Castilleja roots have haustorial attachments
(specialized absorbing structures) that penetrate the host plant's root
tissue, forming an organic bridge with the host (Heckard 1962, p. 27).
In field settings, species of Castilleja tend to establish haustorial
connections with one or more hosts (Heckard 1962, p. 27; Atsatt and
Strong 1970, p. 280). In greenhouse studies, seedlings of C. grisea
grown in the absence of host plants did not perform well and died
shortly after germination, suggesting that host plants are important
for this species (Junak and Wilken 1998, p. 84). Greenhouse studies
have also shown that overall performance and fecundity of parasitic
plants are usually higher with a host than without one (Heckard 1962,
p. 29; Atsatt and Strong 1970, p. 280).
[[Page 29096]]
Castilleja grisea appears to be capable of forming haustorial
connections with a range of plant species (Heckard 1962, p. 28; Atsatt
and Strong 1970, p. 280; Marvier 1996, p. 1399; Adler 2002, p. 2704;
Adler 2003, p. 2086). Nassella pulchra, Calystegia macrostegia subsp.
amplissima, and Constancia nevinii are considered potential hosts
(Muller 2009, pers. comm.). Twelve co-occurring plant taxa have been
found consistently in C. grisea occurrences (Muller and Junak 2011, p.
5). However, further study is needed to determine which of these plants
serve as hosts to C. grisea, and at what frequency. Castilleja grisea
may rely on more than one host species for growth and reproduction.
Therefore, recovery may depend on the conservation of a community of
host species (Marvier and Smith 1997, p. 846).
Castilleja grisea flowers between February and May, producing
yellow bisexual flowers (Chuang and Heckard 1993, pp. 1016-1024; Navy
2002, p. D-31). Castilleja grisea is likely self-incompatible (unable
to produce viable seed through self-fertilization), as observed in
other species of the genus (Carpenter 1983, p. 218; Junak and Wilken
1998, p. 84). Among four populations of C. grisea examined, Junak and
Wilken (1998, pp. 83-84) found limited flower-to-fruit conversion (67
to 71 percent of flowers produced fruits) and large variation in the
number of seeds set per fruit. Castilleja grisea appears to produce
seed primarily through outcrossing, and relies on pollinators for
sexual reproduction (Junak and Wilken 1998, p. 84; Helenurm et al.
2005, p. 1225).
Castilleja grisea is most closely related to, and shares floral
traits with, other species in the genus primarily adapted for bee
pollination (Chuang and Heckard 1991, p. 658). A single bee from the
family Andrenidae, covered in pollen, was recently collected from a
flowering C. grisea plant in Canchalagua Canyon on San Clemente Island
(Howe 2009a, pers. comm.). The fruit of C. grisea is an ovoid capsule,
less than 0.5 in (1.27 cm) long, and contains approximately 150 seeds
(Junak and Wilken 1998, pp. 82-83). The seed coats are deeply netted,
which indicates they can float and may be able to disperse via water
(Muller and Junak 2011, pp. 12, 16). During attempts to propagate C.
grisea plants from seed, no significant differences were found between
seed viability (79.5 to 85 percent) and germination (68.3 to 76.7
percent), suggesting that most viable seed are able to germinate
immediately without a period of dormancy to induce germination (Junak
and Wilken 1998, pp. 83-84).
Genetics--Castilleja grisea
Genetic variation within Castilleja grisea is moderately high for
an insular endemic plant, particularly given its history of extreme
rarity (Helenurm et al. 2005, p. 1225). This suggests C. grisea may
have retained substantial genetic variation through the period of
overgrazing. Consistent with an outcrossing breeding system, most of
the genetic variation in C. grisea is within, rather than among,
occurrences (Helenurm et al. 2005, p. 1225). Historically, there were
likely high rates of gene flow between occurrences. The transmittal of
genes between occurrences in the past influenced the genetic similarity
found between occurrences by Helenurm et al. (2005, p. 1226). While all
occurrences are important for maintaining levels of gene flow, the loss
of any single occurrence is unlikely to represent a significant loss of
genetic diversity to the species (Helenurm et al. 2005, p. 1226).
Overall, this species likely does not have low fitness due to limiting
genetic factors (Helenurm et al. 2005, p. 1226).
Recovery
Section 4(f) of the Act directs us to develop and implement
recovery plans for the conservation and survival of endangered and
threatened species unless we determine that such a plan will not
promote the conservation of the species. The Act directs that, to the
maximum extent practicable, we incorporate into each plan:
(1) Site-specific management actions that may be necessary to
achieve the plan's goals for conservation and survival of the species;
(2) Objective, measurable criteria, which when met would result in
a determination, in accordance with the provisions of section 4 of the
Act, that the species be removed from the list; and
(3) Estimates of the time required and cost to carry out the plan.
However, revisions to the list (adding, removing, or reclassifying
a species) must reflect determinations made in accordance with sections
4(a)(1) and 4(b) of the Act. Section 4(a)(1) requires that the
Secretary determine whether a species is endangered or threatened (or
not) because of one or more of five threat factors. Therefore, recovery
criteria must indicate when a species is no longer endangered or
threatened by any of the five factors. In other words, objective,
measurable criteria, or recovery criteria contained in recovery plans,
must indicate when we would anticipate an analysis of the five threat
factors under section 4(a)(1) would result in a determination that a
species is no longer endangered or threatened. Section 4(b) of the Act
requires that the determination be made ``solely on the basis of the
best scientific and commercial data available.''
Thus, while recovery plans are intended to provide guidance to the
Service, States, and other partners on methods of minimizing threats to
listed species and on criteria that may be used to determine when
recovery is achieved, they are not regulatory documents and cannot
substitute for the determinations and promulgation of regulations
required under section 4(a)(1) of the Act. Determinations to remove a
species from the list made under section 4(a)(1) of the Act must be
based on the best scientific and commercial data available at the time
of the determination, regardless of whether that information differs
from the recovery plan.
In the course of implementing conservation actions for a species,
new information is often gained that requires recovery efforts to be
modified accordingly. There are many paths to accomplishing recovery of
a species, and recovery may be achieved without all criteria being
fully met. For example, one or more recovery criteria may have been
exceeded while other criteria may not have been accomplished, yet the
Service may judge that, overall, the threats have been minimized
sufficiently, and the species is robust enough, that the Service may
reclassify the species from endangered to threatened or perhaps delist
the species. In other cases, recovery opportunities may have been
recognized that were not known at the time the recovery plan was
finalized. These opportunities may be used instead of methods
identified in the recovery plan.
Likewise, information on the species may be learned that was not
known at the time the recovery plan was finalized. The new information
may change the extent that criteria need to be met for recognizing
recovery of the species. Overall, recovery of species is a dynamic
process requiring adaptive management, planning, implementing, and
evaluating the degree of recovery of a species that may, or may not,
fully follow the guidance provided in a recovery plan.
Thus, while the recovery plan provides important guidance on the
direction and strategy for recovery, and indicates when a rulemaking
process may be initiated, the determination to remove a species from
the Federal List of Endangered and Threatened Plants (50 CFR 17.12) is
ultimately based on an
[[Page 29097]]
analysis of whether a species is no longer endangered or threatened.
The following discussion provides a brief review of recovery planning
for Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea, as well as an analysis of the recovery criteria and
goals as they relate to evaluating the status of the taxa.
In 1984, the Service published the Recovery Plan for the Endangered
and Threatened Species of the California Channel Islands (Recovery
Plan) that addresses 10 plants (including Malacothamnus clementinus,
Acmispon dendroideus var. traskiae, and Castilleja grisea) and animals
distributed among three of the Channel Islands (USFWS 1984). Recovery
plans are intended to guide actions to recover listed species and to
provide measurable objectives against which to measure progress towards
recovery. Following guidance in effect at that time, the Recovery Plan
was not focused on criteria that specifically addressed the point at
which threats identified for each species in the listing rule would be
removed or sufficiently ameliorated. Given the threats in common to the
10 species addressed, the Recovery Plan is broad in scope and focuses
on restoration of habitats and ecosystem function. Instead of specific
criteria, it included six general objectives covering all 10 of the
plant and animal species:
Objective 1: Identify present adverse impacts to biological
resources and strive to eliminate them.
Objective 2: Protect known resources from further degradation by:
(a) Removal of feral herbivores, carnivores, and selected exotic plant
species; (b) control of erosion in sensitive locations; and (c) direct
military operations and adverse recreational uses away from
biologically sensitive areas.
Objective 3: Restore habitats by revegetation of disturbed areas
using native species.
Objective 4: Identify areas of San Clemente Island where habitat
restoration and population increase of certain addressed taxa may be
achieved through a careful survey of the island and research on habitat
requirements of each taxon.
Objective 5: Delist or upgrade the listing status of those taxa
that achieve vigorous, self-sustaining population levels as the result
of habitat stabilization, restoration, and preventing or minimizing
adverse human-related impacts.
Objective 6: Monitor effectiveness of recovery effort by
undertaking baseline quantitative studies and subsequent follow-up work
(USFWS 1984, pp. 106-107).
Progress has been made toward achieving these objectives. Our
review of the Recovery Plan focuses on the actions identified that
promote the recovery of Malacothamnus clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. The Recovery Plan adopts a
generalized strategy of eliminating or controlling selected nonnative
species and restoring habitat conditions on the Channel Islands to
support viable, self-sustaining occurrences of each of the addressed
taxa. The Recovery Plan states that ``[o]nce the threats to these taxa
have been removed or minimized and the habitats are restored,
adequately protected, and properly managed, reclassification for some
taxa may be considered'' (USFWS 1984, p. 108). Actions specified in the
Recovery Plan that are pertinent to recovery of the endangered San
Clemente Island plant taxa include:
(1) Removing feral animals;
(2) Removing or controlling selected nonnative plants;
(3) Controlling erosion;
(4) Revegetating eroded and disturbed areas;
(5) Reintroducing and reestablishing listed plant species
populations;
(6) Modifying existing management plans to minimize habitat
disturbance and incorporate recovery actions into natural resource
management plans;
(7) Protecting habitat by minimizing habitat loss and disturbance
and by preventing the introduction of additional nonnative organisms;
(8) Determining the habitat and other ecological requirements of
the listed plant taxa (such as reproductive biology and fire
tolerance);
(9) Evaluating the success of management actions;
(10) Increasing public support for recovery efforts; and,
(11) Using existing laws and regulations to protect each taxon.
Recovery Plan Implementation
The primary objective of the Recovery Plan is to restore endangered
and threatened species to nonlisted status. Though specific size and
number of occurrences needed for self-sustaining populations for each
species was not identified, habitat restoration and protection that
would result in achieving self-sustaining populations (see Objective 5)
were discussed. The Recovery Plan stated that reclassification of these
taxa may be considered after threats have been removed or sufficiently
minimized and the habitat is restored. Specific criteria for
determining when threats have been removed or sufficiently minimized
were not identified in the Recovery Plan, but six objectives were
described in general to achieve recovery of the Channel Island species.
This section provides a summary of actions and activities that have
been implemented according to the 1984 Recovery Plan (USFWS 1984, pp.
106-107) and contribute to achievement of these objectives.
Objective 1: Identify Present Adverse Impacts to Biological Resources
and Strive To Eliminate Them
The Navy has taken steps to eliminate incidental impacts to the
three species by educating Navy personnel stationed on San Clemente
Island. To increase support for recovery efforts, the Navy has created
the position of Island Operations Manager. This individual's role is to
act as a liaison between the Navy's natural resource branch and other
island users (Larson 2009, pers. comm.). The Island Operations Manager
educates users of the island to the uniqueness and fragility of the
island's ecosystem, and briefs new operational groups as they come onto
the island (Larson 2009, pers. comm.). These briefings inform
operational groups of the Navy's natural resource management
responsibilities under the law, and may include additional information
about threats to, and locations of, listed taxa.
The Recovery Plan recommends that existing laws and regulations be
used to protect Malacothamnus clementinus, Acmispon dendroideus var.
traskiae, and Castilleja grisea from threats on San Clemente Island.
Based on the occurrence of these taxa on federally owned land, the
primary laws with potential to protect them include the National
Environmental Policy Act (NEPA) and the Act. NEPA requires Federal
action agencies to integrate environmental values into their decision
making processes by considering the environmental impacts of their
proposed actions and reasonable alternatives to those actions. The Navy
has implemented NEPA since its enactment in 1970. Likewise, the Navy
has a history of consultation and coordination with the Service under
the Act regarding the effects of various San Clemente Island activities
on federally listed species since taxa on the island were first listed
in 1977. Finally, pursuant to the Sikes Act Improvement Act, the Navy
adopted an INRMP for San Clemente Island in 2002 that helps guide the
management and protection of these taxa (Navy 2002, pp. 1.1-8.12). An
INRMP is a plan that is intended ``* * * to guide installation
commanders in managing their natural resources in a manner that is
consistent with the sustainability of those resources while
[[Page 29098]]
ensuring continued support of the military mission'' (Navy 2002, p. 1-
1). To achieve this, the INRMP identifies goals and objectives for
specified management units and their natural resources. The following
objectives have been incorporated as part of the INRMP to address the
Recovery Plan task of incorporating recovery actions into existing
management plans:
(1) Protect, monitor, and restore plants and cryptograms (soil
crusts composed of living cyanobacteria, algae, fungi, or moss) in
order to manage for their long-term sustainability on the island;
(2) Consider Malacothamnus clementinus, Acmispon dendroideus var.
traskiae, or Castilleja grisea as ``Management Focus Plants,'' such
that they are considered independently from their plant communities as
special management focuses (habitat protection alone is not assumed to
be sufficient for their protection);
(3) Conduct status surveys for listed plants;
(4) Ensure that Management Focus Plants have a network of suitable
sites;
(5) Perform studies to determine the pollinators of Malacothamnus
clementinus, Acmispon dendroideus var. traskiae, or Castilleja grisea;
and
(6) Continue to apply genetic research and management approaches to
rare plant management.
Through these mechanisms, the Navy is required to identify and
address all threats to these species during the INRMP planning process.
If possible, threats are ameliorated, eliminated, or mitigated through
this procedure. The Navy has strived to fulfill this objective through
both internal planning (INRMP) and through compliance with Federal law
(consultations with the Service under the Act and preparing
environmental review documents under NEPA). As discussed below under
the five factors, the actions taken by the Navy under the INRMP have
not completely eliminated all adverse impacts, but many threats have
been greatly reduced. These contributions to the elimination of adverse
impacts partially fulfill, but do not fully achieve, the objective for
all three species.
Objective 2: Protect Known Resources From Further Degradation By: (a)
Removal of Feral Herbivores, Carnivores, and Selected Exotic Plant
Species; (b) Control of Unnatural Erosion in Sensitive Locations; and
(c) Directing Military Operations and Adverse Recreational Uses Away
From Biologically Sensitive Areas
In 1992, the Navy fulfilled a major part of this objective by
removing the last of the feral goats and pigs from San Clemente Island
(as described above in the Habitat section). Nonnative plants have also
been targeted for removal from San Clemente Island, and efforts to
control nonnatives have been implemented on an annual basis since
approximately 1993 (O'Connor 2009a, pers. comm.). The specific
nonnative plants targeted and amount of money allocated to this program
are adjusted on an annual basis (O'Connor 2009b, pers. comm.; Munson
2011a, pers. comm.). The effectiveness of this program was recently
improved by providing authorization to apply herbicides (O'Connor
2009b, pers. comm.). Priorities in the nonnative plant program are
currently focused on new nonnatives to the island and particularly
destructive nonnative species.
The Navy is also taking steps to minimize the effects of erosion on
the island. Erosion control measures are being incorporated into
project designs to minimize the potential to exacerbate existing
erosion (O'Connor 2009c, pers. comm.). With the expansion of military
operational areas, the Navy committed to prepare and implement an
erosion control plan that will minimize soil erosion within and
adjoining the operational areas (Navy 2008b, pp. 5-30; USFWS 2008 p.
62). However, this plan has not been finalized nor yet implemented, and
it is unclear whether erosion control measures will be implemented
consistently or at all in areas that are operationally closed to
monitoring and access due to unexploded ordnance. The proposed erosion
control plan includes development and application of best management
practices (BMPs) such as: Establishing setbacks and buffers from steep
slopes, drainages, and sensitive resources; constructing site-specific
erosion control structures; conducting revegetation and routine
maintenance; and monitoring and adjusting the BMPs as appropriate.
While the erosion control plan is being prepared, the Navy has
postponed all major battalion movements and training, and is using BMPs
when creating and approving projects that might contribute to erosion
on the island. The Navy has taken steps to reduce the threat of erosion
on the island and contribute to the achievement of this objective.
The Navy is taking precautions to avoid plants when possible to
minimize direct impacts to Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea resulting from
military activities. For example, in the MOFMP, the Navy proposed to
develop a Training Area Range (TAR) that contained A. d. var. traskiae
within its boundaries. After consultation with USFWS, the Navy revised
these boundaries to avoid most of the A. d. var. traskiae and minimize
the impact of training on the species (USFWS 2008, p. 118).
This objective has been largely met for Acmispon dendroideus var.
traskiae and Castilleja grisea. Feral herbivores have been removed,
erosion control measures are being implemented, and military activities
are avoiding direct impacts to plants whenever possible. The Navy is
also developing an erosion control plan for military activities.
However, many occurrences of Malacothamnus clementinus are located in
areas that continue to be impacted, or their status remains unknown due
to closures. Therefore, Objective 2 has not been sufficiently satisfied
for this taxon.
Objective 3: Restore Habitats by Revegetation of Disturbed Areas Using
Native Species
Since 2001, the Navy has contracted with the San Diego State
University Soil Ecology and Restoration Group (SERG) to propagate and
outplant (transplant individuals from the greenhouse to vegetative
communities) native species on the island (Howe 2009b, pers. comm.).
The SERG propagates and outplants approximately 4,000 native plants per
year, and has initiated restoration at approximately 28 sites (O'Connor
2009b, pers. comm.). This program has not included propagation and
outplanting of listed plant taxa, except in one recent instance to
replace Acmispon dendroideus var. traskiae plants that were extirpated
during a scrap metal removal project (Munson 2011a, pers. comm.). The
outplanting of native species is primarily focused on restoring
sensitive island habitats and improving habitat conditions for
endangered animal taxa (such as the San Clemente loggerhead shrike
(Lanius ludovicianus mearnsi)), with some revegetation of eroded and
disturbed areas (O'Connor 2009, pers. comm.). Although only one of the
restoration efforts was specifically designed for the benefit of one of
the three plant taxa addressed in this finding, restoration of the
island's vegetation communities should help improve habitat suitability
for all three taxa by reducing the spread of invasive nonnative plants
and restoring ecological processes. Although progress has been made
towards restoring disturbed areas, there are still areas (e.g.,
especially within SHOBA) that need further restoration of native
species. Therefore, while restoration is occurring, the objective has
not been
[[Page 29099]]
fully met at this time for the three species.
Objective 4: Identify Areas of San Clemente Island Where Habitat
Restoration and Population Increase of Certain Addressed Taxa May be
Achieved Through a Careful Survey of the Island and Research on Habitat
Requirements of Each Taxon
Since they were listed, a number of studies have addressed the
ecology, taxonomy, and genetics of the three plant taxa. Evans and Bohn
(1987, pp. 537-545) observed insects on plants, collected seeds, and
studied the germination of Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea. Junak and Wilken
(1998, pp. 1-426) studied flowering and fruiting in natural populations
and performed germination trials with collected seeds from all three
taxa. Allan (1999, pp. 46-105) observed pollinators and germinated
seeds collected from A. d. var. traskiae. Liston et al. (1990)
confirmed suspected hybridization between A. d. var. traskiae and A.
argophyllus var. argenteus using genetic techniques. Additionally,
Allan (1999, pp. 46-105) surveyed the genetics of a number of taxa
within the genus Lotus, including a group that includes A. d. var.
traskiae, to compare genetic divergence between California mainland and
island taxa. Helenurm et al. (2005, pp. 1221-1227) studied patterns of
genetic variation among occurrences of C. grisea. Helenurm (1997, pp.
41-51; 1999, pp. 29-40) studied the genetic variation and clonal nature
of M. clementinus. These studies have helped to elucidate potential
plant pollinators and mating systems, plant propagation techniques, and
to design management strategies that take into consideration genetic
factors. There is a growing body of knowledge on the habitat
requirements and life history of listed species on the island. This
research, encouraged and supported by the Navy, has contributed to
achieving Objective 4 and to planning successful restoration of habitat
and recovery of the three taxa. Additional surveys and research
necessary to identify appropriate restoration, management, and recovery
actions include: further genetic studies for M. clementinus, research
on the degree of hybridization in A. d. var. traskiae and study of the
host plants of C. grisea. Thus, this objective has not been fully
achieved at this time for the three species.
Objective 5: Delist or Upgrade the Listing Status of Those Taxa That
Achieve Vigorous, Self-Sustaining Population Levels as the Result of
Habitat Stabilization, Restoration, and Preventing or Minimizing
Adverse Human-Related Impacts
The distributions of Acmispon dendroideus var. traskiae and
Castilleja grisea have increased substantially over much of the island
since listing. There are now vigorous, self-sustaining occurrences of
A. d. var. traskiae and C. grisea on San Clemente Island, as described
above. Threats to these taxa have also been reduced to levels such that
they are no longer in danger of extinction throughout all of their
range (USFWS 2007b, pp. 1-22; USFWS 2007c, pp. 1-19). Although the goal
of delisting has not yet been met, the objective to improve the status
of A. d. var. traskiae and C. grisea to the point they can be
reclassified has been met. Because many occurrences of Malacothamnus
clementinus are located in areas that continue to be impacted, or their
status remains unknown due to closures, we have not yet met either
standard of this objective to reclassify or delist this species.
Objective 6: Monitor Effectiveness of Recovery Efforts by Undertaking
Baseline Quantitative Studies and Subsequent Follow Up Work
To evaluate the success of management actions undertaken to benefit
the three plant taxa, the Navy implemented a long-term vegetation
monitoring study (Tierra Data Inc. 2005, pp. i-96 and Appendices) and
commissioned sensitive plant surveys (Junak and Wilken 1998, pp. 1-416;
Junak 2006, pp. 1-176). Overall, vegetation trend monitoring reveals
that the cover of both native and nonnative plant species has changed
since the removal of feral goats and pigs, but the response of
individual species and vegetative communities has varied, with some
species and communities exhibiting greater changes than others.
Discerning long-term vegetative community trends is difficult because
the vegetative community study was preceded by a wet year that likely
had a strong influence on the data collected (Tierra Data Inc. 2005, p.
29). Within the few monitoring plots that included the three plant
taxa, occurrence counts varied among years and did not provide a clear
indication of trend (Tierra Data Inc. 2005, pp. 79-80). The clearest
indication of the success of feral animal removals for the three plant
taxa was obtained from rare plant survey data (Junak and Wilken 1998,
pp. 1-416, GIS data; Junak 2006, pp. 1-176, GIS data; Tierra Data Inc.
2008, pp. 1-24, appendices and GIS data; SERG 2009-2011, GIS data).
These surveys have added substantially to the number of documented
occurrences of each of the three taxa.
Rare plant surveys and island flora studies have documented many
more locations occupied by Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea than were known at the
time of listing. Since listing, 8 additional occurrences of M.
clementinus, 23 occurrences of A. d. var. traskiae, and 10 occurrences
of C. grisea have been documented (Table 1). It is unknown whether the
higher number of occurrences represents detections due to increased
survey efforts, recruitment from the seed bank, or recolonization by
the plants as a result of management actions implemented by the Navy to
conserve listed species on the island (see Distribution section for
each taxon above). However, this improvement in the documented status
of each of these taxa suggests that feral goats and pigs were a
significant threat to each. Thus, their improved status may largely be
due to the implementation of a single action identified in the Recovery
Plan. Because portions of the island remain closed, monitoring
effectiveness of recovery efforts is not being fully implemented.
Occurrences for each species, as described above, are closed to access
for monitoring or any recovery efforts. Thus, Objective 6 cannot be
fully met for the three taxa under current operational closure
directives.
Summary of Recovery Plan Implementation
In summary, while the Recovery Plan does not include taxon-specific
downlisting or delisting criteria for measuring the recovery of
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea, many of the actions identified in the Recovery Plan
have been implemented to benefit these taxa. Most significantly, the
Navy removed feral goats and pigs from San Clemente Island in 1992. The
improvement in the documented status of each of these listed plant taxa
suggests that the removal of these animals was integral to their
ability to establish vigorous, self-sustaining occurrences. Though the
distribution of Malacothamnus clementinus has continued to increase on
the island, the majority of its range occurs within SHOBA. Since access
to Impact Areas within SHOBA is restricted to military personnel, the
status of three M. clementinus
[[Page 29100]]
occurrences is uncertain at this time. A fourth occurrence, with a
significant amount of genetic diversity, outside of the impact areas is
also closed at this time. Due to limited access to these areas, there
are insufficient data to indicate that the objectives have been
successfully met. In addition, limited access precludes natural
resource managers from implementing management actions, such as
nonnative control and fire suppression.
In contrast, threats are reduced in areas occupied by Acmispon
dendroideus var. traskiae and Castilleja grisea, and many of the
objectives have been met in part or full. Complementing the success of
these conservation measures, the ecology and genetics of each of these
taxa have been studied, and a number of programs are now in place to
improve habitat suitability, prevent introductions of nonnative
species, guide and track management efforts, and protect occurrences of
these plant taxa. We investigated other potential threats for these
taxa and concluded that they do not pose significant impacts. Based on
our review of the Recovery Plan, we conclude that the status of
Acmispon dendroideus var. traskiae and Castilleja grisea has improved
due to activities being implemented by the Navy on San Clemente Island.
The effects of these activities on the status of the three taxa are
discussed in further detail below.
Summary of Factors Affecting the Species
Section 4 of the Act and its implementing regulations (50 CFR part
424) set forth procedures for listing species, reclassifying species,
or removing species from the Federal Lists of Endangered and Threatened
Wildlife and Plants. ``Species'' is defined by the Act as including any
species or subspecies of fish or wildlife or plants, and any distinct
vertebrate population segment of fish or wildlife that interbreeds when
mature (16 U.S.C. 1532(16)). Once the ``species'' is determined, we
then evaluate whether that species may be endangered or threatened
because of one or more of the five factors described in section 4(a)(1)
of the Act. Those factors are:
(A) The present or threatened destruction, modification, or
curtailment of its habitat or range;
(B) Overutilization for commercial, recreational, scientific, or
educational purposes;
(C) Disease or predation;
(D) The inadequacy of existing regulatory mechanisms; or
(E) Other natural or manmade factors affecting its continued
existence.
We must consider these same five factors in reclassifying or delisting
a species. Listing, reclassifying, or delisting may be warranted based
on any of the above threat factors, either singly or in combination.
For species that are already listed as threatened or endangered, an
analysis of threats is an evaluation of both the threats currently
facing the species and the threats that are reasonably likely to affect
the species in the foreseeable future following the delisting or
downlisting.
Under section 3 of the Act, a species is ``endangered'' if it is in
danger of extinction throughout all or a significant portion of its
range, and is ``threatened'' if it is likely to become endangered in
the foreseeable future throughout all or a significant portion of its
range. The word ``range'' refers to the range in which the species
currently exists, and the word ``significant'' refers to the value of
that portion of the range being considered to the conservation of the
species. The ``foreseeable future'' is the period of time over which
events or effects reasonably can or should be anticipated, or trends
extrapolated.
We considered and evaluated the best available scientific and
commercial information for this analysis. Information pertaining to
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea in relation to the five factors provided in section
4(a)(1) of the Act is discussed below. For the purposes of this
analysis, we will first evaluate whether the currently listed species
should be considered threatened or endangered throughout all their
ranges. If we determine that the species are threatened, then we will
consider whether there are any significant portions of their ranges
where they are in danger of extinction or likely to become endangered
within the foreseeable future. The five factors listed under section
4(a)(1) of the Act and their applications to M. clementinus, A. d. var.
traskiae, and C. grisea are presented below.
Malacothamnus clementinus (San Clemente Island Bush Mallow)
In the 2007 status review, we acknowledged that the predominant
threat at listing (grazing from feral herbivores) was ameliorated with
the removal of goats and pigs from the island in 1992 (USFWS 2007a, pp.
1-28). Threats to Malacothamnus clementinus identified in 2007
included: (1) Land use, (2) fire, (3) nonnative species, (4) erosion,
(5) natural factors, (6) fire management, and (7) limited access to
SHOBA. Land use, fire, nonnatives, erosion, and fire management are
discussed as habitat threats below under Factor A. Natural factors in
the 2007 status review refer to the low genetic diversity of this taxon
and are discussed in Factor E below. In 2007, access to SHOBA was
described as a threat because it ``undermines the effectiveness of
surveys and management efforts'' (USFWS 2007a, p. 21). While lack of
access to portions of the island still limits our ability to assess the
status of the taxon, access to SHOBA is not considered a threat.
Rather, the lack of access contributes to uncertainty in assessing
threats and the species' response to those threats and to actions taken
to ameliorate threats. In this finding, we focus on threats responsible
for impacting the listed entity or habitat where it occurs, not our
inability to access these areas.
Factor A. The Present or Threatened Destruction, Modification, or
Curtailment of Its Habitat or Range
The final listing rule (42 FR 40682; August 11, 1977) identified
the following threats to Malacothamnus clementinus: Habitat alteration
and destruction, competition from nonnative species, and direct
predation by nonnative herbivores (goats and pigs). With the final
removal of these herbivores in 1992, the vegetation on San Clemente
Island has rebounded, and the status of many rare plant occurrences,
including M. clementinus, has improved (Tierra Data Inc. 2005, p. 8;
Junak 2006a, pers. comm.). Although the direct threat from predation to
M. clementinus identified in the final listing rule has been
eliminated, erosion as a result of overgrazing and invasive nonnative
plants remain ongoing threats to habitat of M. clementinus. The
Recovery Plan also identified habitat alteration and disturbance from
the Navy's use of the island for military operational and training
needs as additional threats to the habitats occupied by M. clementinus
(USFWS 1984, pp. 58-63). Additional threats identified since listing
include alteration of San Clemente Island habitats by military training
activities, fire, and fire management. As outlined below, we discuss in
this section the impacts of the following threats that affect the
habitat or range of M. clementinus: (1) Land use, (2) erosion, (3)
nonnative plants, (4) fire, and (5) fire management.
Land Use
In this section we describe threats considered likely based on land
use designations. A total of 11 Malacothamnus clementinus occurrences
are distributed on San
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Clemente Island, including one mid-island (Lemon Tank Canyon) and the
remaining 10 approximately 9.5 mi (15.3 km) along the southwesterly
facing coastal terraces at the southern end of the island.
Historically, the island was used for grazing and ranching. At the time
of listing, the Navy had acquired the island, although military
operations were not intense and feral grazers were still on the island.
Since listing, training activities and land use by the Navy have
increased significantly. Since it was first listed in 1977, the Navy
has consulted and coordinated with us regarding the effects of various
activities on M. clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea (USFWS 2002, pp. 1-21; USFWS 2003, p. 1; USFWS 2004,
pp. 1-2; USFWS 2008, pp. 1-237). These consultations have addressed
numerous activities including training, fire management, the
installation of wind turbines, missile tests, maintenance and
construction of Ridge Road and the assault vehicle maneuver route,
construction of berthing buildings, and development and use of training
areas.
Most recently, training activities approved in the MOFMP include
substantial increases in vehicle and foot traffic in the IOA (Navy
2008b, pp. 2-1 to 2-52). In November 2008, we completed a biological
opinion describing the impact of the Navy's military training program
proposed in the MOFMP on 11 federally listed species on San Clemente
Island, including the three taxa that are the subject of this finding
(USFWS 2008, pp. 1-237). This consultation addressed the proposed
expansion of the frequency and amount of military training on the
island, along with enhanced training complex capabilities, construction
of new gates and buildings, use of an IOA, change in fire management
strategies, and use of an assault vehicle maneuver corridor. Examples
of projected increases in training levels relative to a representative
year of training prior to 2008 include: 11 percent increase in naval
fire support exercises, 23 percent increase in land bombing exercises,
150 percent increase in explosive ordnance disposal, 60 percent
increase in artillery operations, 90 percent increase in land
demolitions, 19 percent increase in land navigation exercises, and 96
percent increase in SEAL platoon operations (USFWS 2008, p. 11).
We considered the status and distribution of Malacothamnus
clementinus, and the various management, avoidance, and minimization
measures in place, including those the Navy will implement with the new
MOFMP in our 2008 biological opinion (we also considered impacts to
Acmispon dendroideus var. traskiae and Castilleja grisea).
Additionally, the Service made conservation recommendations within the
biological opinion, including: (1) Considering recommended actions from
the 5-year review in the upcoming revision of the INRMP, (2)
propagation and outplanting of narrowly distributed, listed plant
species, and (3) the collection of M. clementinus cuttings and seeds
from Horse Beach Canyon for the propagation and outplanting of
individuals in areas without military training. We concluded that
ongoing and likely impacts from the proposed increases in military
training activities would not jeopardize the continued existence of M.
clementinus, A. d. var. traskiae, and C. grisea (USFWS 2008, p. 90).
The southern portion of the distribution of Malacothamnus
clementinus spans the boundary of SHOBA, which supports a variety of
training operations involving both live and inert munitions fire. The
majority of this area serves as a buffer for areas of more intense
training and is less susceptible to direct land use threats than
occurrences within TAR, IOA, or Impact Areas. Six of 11 known
occurrences (54 percent; Canchalagua Canyon, Horse Beach Canyon, Lower
China Canyon, Upper China Canyon, Cave Canyon, and Chukit Canyon) fall
within SHOBA, where diffuse or accidental impacts to M. clementinus are
likely to occur, and training might result in the alteration of habitat
by Off Highway Vehicle (OHV) movement and large-scale troop movements
through the military impact and training areas. Within the Impact
Areas, some munitions exercises involve the use of incendiary devices,
such as illumination rounds, white phosphorous, and tracer rounds,
which pose a high risk of fire ignition (USFWS 2008, pp. 11-13). One
occurrence (Lower China Canyon) is within the IOA, and could experience
direct impacts from troop and vehicle movement through the area. Three
additional occurrences (Upper China Canyon, Horse Beach Canyon, and
Lemon Tank Canyon) are near the IOA (within 1,000 ft (305 m)), and
could be subjected to diffuse or accidental impacts. Because of the
elevated risk of fire and disturbance associated with training
activities, live and inert munitions fire are targeted towards two
delineated Impact Areas (I and II) within SHOBA where bombardments and
land demolition are concentrated. Three of 11 occurrences (27 percent;
Upper China Canyon, Lower China Canyon, and Horse Beach Canyon) are
within Impact Areas I or II, and are now closed to nonmilitary
personnel (USFWS 2008, p. 50).
As a result, it is not possible to assess the magnitude of the
threat in these areas, and the status of the three occurrences remains
unknown. These occurrences, although limited in number, contain the
greatest numbers of individuals and some of the highest genetic
diversity on the island (Helenurm 1999, p. 40). The intense training
activities within the Impact Areas pose a direct threat to habitat and
occurrences due to associated ground disturbance and bombardment (USFWS
2008, pp. 83-84). The majority (8 of 11) of Malacothamnus clementinus
occurrences are located outside of any training areas (IOA, TAR, or
Impact Area) and are less likely to sustain direct impacts from
military activities associated with land use; three occurrences (Upper
China Canyon, Lower China Canyon, and Horse Beach Canyon) are partially
or wholly within the boundaries of a training area (IOA, TAR, or Impact
Area).
The Lemon Tank Canyon occurrence falls within an area identified by
the INRMP as needing environmental cleanup pursuant to the Resource
Conservation and Recovery Act (RCRA) and Comprehensive Environmental
Response, Compensation and Liability Act (CERCLA) (Navy 2002, p. 2-18).
This site is still in the study phase and has not been listed, or
proposed for listing, on the National Priorities List. Habitat at this
occurrence could receive improvements by future environmental cleanup
(Munson 2011b, pers. comm.). Initial surveys of the project footprint
have been completed, and Malacothamnus clementinus was not found in the
project footprint (B. Munson 2011e, pers. comm.), although additional
surveys will need to be undertaken to ensure there is no impact to the
plant. RCRA and CERCLA require that impacts to the species and its
habitat be avoided and minimized to the extent practicable. This area
has also been closed to natural resource personnel, and the status of
the occurrence in this area is unknown (Munson 2011c, pers. comm.).
While the increase in military training affects the species (as
well as Acmispon dendroideus var. traskiae and Castilleja grisea), the
Navy through implementation of the INMRP is avoiding and minimizing the
impacts to the extent practicable while meeting operational needs. Land
use is currently impacting habitat of 4 of the 11 occurrences (36
percent; Lemon Tank
[[Page 29102]]
Canyon, Lower China Canyon, Upper China Canyon, and Horse Beach Canyon)
on the island, which may lead to overall habitat degradation, and cause
the loss of individuals or groupings of plants in a given area.
Military operations and training are island-wide threats to M.
clementinus, particularly to the occurrences in or adjacent to military
training areas.
Erosion
Erosion and associated soil loss caused by browsing of feral goats
and rooting of feral pigs likely modified the island's habitat (Navy
2002, p. 1-14). Defoliation from overgrazing on San Clemente Island
increased erosion over much of the island, especially on steep slopes
where denuded soils can quickly wash away during storm events (Johnson
1980, p. 107; Navy 2002, pp. 1-14, 3-9; Tierra Data Inc. 2007, pp. 6-
7). In the INRMP, erosion was identified as a threat to canyon woodland
and maritime desert scrub vegetation communities, which is
Malacothamnus clementinus habitat (Navy 2002, pp. 4-3, 4-12). In the
southwestern portion of its distribution, M. clementinus is found along
coastal terraces, canyon rims, and at the base of escarpments where
erosion is more prevalent. The erosion process can remove soil that
provides nutrients and physical support for the plants, displace seeds
and deposit them in unsuitable locations, and bury extant individuals
or small occurrences of the plants. This stripping of soil and plants
can affect vegetation composition and landscape long after the
herbivores are removed (Johnson 1980, p. 107). Erosion has likely been
exacerbated by reductions in vegetation cover due to drought and fire
(Johnson 1980, pp. 105-118). Currently, the Navy has a program run by
SERG that grows and outplants native vegetation to areas that need to
be restored (Navy 2002, pp. 3-51 to 3-52). Restoration of native
vegetation helps retain soil and ameliorate erosion in stripped areas.
Increased military activities, especially where Malacothamnus
clementinus is found within training area boundaries, cause erosion
through soil compaction or other soil disturbances in occupied habitat
near roadways or vehicle maneuver areas (Tierra Data Inc. 2007, p. 12).
With the exception of the main road, the roads on San Clemente Island
are largely unpaved, and 5 of the 11 occurrences (45 percent; Lower
China Canyon, Horse Beach Canyon, Middle Ranch Canyon, Waymuck Canyon,
and Lemon Tank Canyon) are within 500 ft (152 m)) of a road on the
island (Forman and Alexander 1998, p. 217). These occurrences could be
subject to diffuse disturbance (spread out over a large area or not
concentrated) and road effects that degrade habitat quality. Roads can
concentrate water flow, causing incised channels and eroded slopes
(Forman and Alexander 1998, pp. 216-217). This increased erosion around
roads can degrade habitat, especially along steep canyons and ridges.
Erosion impacts are likely greatest in SHOBA, where bombardment has led
to a pattern of surface disturbance and recurrent fire (Navy 2002, pp.
3-5). The Navy studied the potential for erosion from several proposed
military activities (Tierra Data Inc. 2007, pp. 1-45, Appendices). One
additional occurrence at Upper China Canyon is also impacted by
erosion. Therefore, 6 of the 11 occurrences (54 percent; Lower China
Canyon, Upper China Canyon, Horse Beach Canyon, Middle Ranch Canyon,
Waymuck Canyon, and Lemon Tank Canyon) of M. clementinus are likely to
be further impacted by erosion (Table 1).
Erosion control measures are incorporated into all site feasibility
studies and project planning, design, and construction to minimize the
potential to exacerbate existing erosion and avoid impacts to listed
species (Munson 2011a, pers. comm.). The INRMP requires that all
projects include erosion conservation work and associated funding (Navy
2002, p. 4-89). These conservation actions include best management
practices for construction and engineering, choosing sites that are
capable of sustaining disturbance with minimum soil erosion, and
stabilizing disturbed sites with native plants (Navy 2002, pp. 4-89-4-
91). Additionally, large-scale island-wide maneuvers with assault
vehicles have been postponed until an erosion control plan is drafted
and implemented. Due to potential new training in the IOA and the
Assault Vehicle Maneuver Area (AVMA), an erosion control plan to
minimize the effects of the potential training is currently being
developed for San Clemente Island (Munson 2011a, pers. comm.). The Navy
has committed to preparing this plan and implementing it prior to any
new training or operations in the IOA or AVMA (Navy 2008b, pp. 5-29, 5-
30). The proposed erosion control plan includes development and
application of BMPs including: establishing setbacks and buffers from
steep slopes, drainages, and sensitive resources; constructing site-
specific erosion control structures; conducting revegetation and
routine maintenance; and monitoring and adjusting the BMPs as
appropriate. Implementation of the erosion control plan is expected to
prevent soil erosion from adversely affecting federally listed species,
including Malacothamnus clementinus, and their habitats. Additionally,
the plan is designed to prevent soil erosion from significantly
impacting other sensitive resources, including sensitive plant and
wildlife species and their habitats. This erosion control plan will
address military operations associated with the IOA, AVMA, and AFP;
however, since the plan is not yet finalized, it does not currently
ameliorate the noted threats from erosion.
The processes and results of erosion are island-wide threats to the
habitat of Malacothamnus clementinus, particularly to the occurrences
in or adjacent to military training areas or roads. Erosion is
currently impacting 6 of the 11 occurrences (54 percent) on the island,
which may lead to overall habitat degradation, and cause the loss of
individuals or groupings of plants in a given area. Of the six
occurrences currently impacted by erosion, four (Lower China Canyon,
Upper China Canyon, Horse Beach Canyon, and Lemon Tank Canyon) are in
areas that are operationally closed to access, and likely not afforded
conservation measures to control or monitor erosion. With these
closures and continued impacts, erosion remains a threat to the habitat
of M. clementinus.
Nonnative Species
One of the threats to Malacothamnus clementinus identified in the
final listing rule was the spread of nonnative plants into its habitat
(42 FR 40682; August 11, 1977). Nonnatives can alter habitat structure,
ecological processes (such as fire regimes), nutrient cycling,
hydrology, and energy budgets and compete for water, space, light, and
nutrients (Zink et al. 1995, p. 307; Brooks 1999, pp. 16-17; Mack et
al. 2000, p. 689). By 1992, researchers had documented 99 nonnative
plant species on San Clemente Island (Kellogg and Kellogg 1994, p. 5),
and transfer of nonnative species to the island continues to be a
problem today (Dunn 2006, pers. comm.; Junak 2006c, pers. comm.;
Kellogg 2006, pers. comm.; O'Connor 2009c, pers. comm.). Nonnative
species of particular concern include Foeniculum vulgare (fennel) and
Brassica tournefortii (Sahara mustard), which have already invaded M.
clementinus habitat. Since nonnative herbivores were removed from the
island, the most significant structural alteration to the habitat has
been the proliferation of nonnative annual grasses, such as Avena spp.
(oats), Bromus spp. (bromes), and Vulpia
[[Page 29103]]
myuros (annual fescue). Annual grasses vary in abundance with rainfall,
potentially changing the vegetative community from shrubs to grasses,
and may increase the fuel load in wet years (see Factor A--Fire section
below). Nonnative grasses are present in the native maritime desert
scrub vegetation community where M. clementinus is often found (Tierra
Data Inc. 2005, pp. 36-42).
Although previous invasions of nonnatives probably were introduced
in grazing fodder, current invasions are typically introduced by
military activities and training on the island. Nonnative plants likely
come in with equipment, vehicles, material, and personnel, and are
spread by their movements. The primary pathway and vector for nonnative
species into arid and semi-arid ecosystems are vehicles and vehicular
routes, and disturbances along these routes and corridors enable their
establishment (Stylinski and Allen 1999, p. 551; Gelbard and Belnap
2003, pp. 424-425; Von der Lippe and Kowarik 2007, p. 986). Island
ecosystems and species are especially vulnerable to nonnative plant
invasions due to the relative lack of biotic diversity and natural
predators (Mack and Lonsdale 2002, p. 164).
Nonnative plants constitute a rangewide threat to the endemic plant
community and habitat on San Clemente Island, including the habitat of
all occurrences of Malacothamnus clementinus. Five of 11 occurrences
(45 percent; Lower China Canyon, Horse Beach Canyon, Middle Ranch
Canyon, Waymuck Canyon, and Lemon Tank Canyon) are within 500 ft (152
m) of Ridge Road or China Point Road, and may be subject to diffuse
disturbance and road effects that degrade habitat quality along the
road (Forman and Alexander 1998, p. 217). Roadsides tend to cultivate
conditions (high disturbance, seed dispersal by vehicles, ample light,
and water runoff) favorable to nonnative species (Forman and Alexander
1998, p. 210). Nonnatives, including Foeniculum vulgare and
Mesembryanthemum crystallinum (crystalline iceplant), have been found
in the disturbed shoulders along the road between Ridge Road and China
Point in SHOBA (Braswell 2011, pers. obs.).
Potential impacts from nonnative plants to the habitats of the
three taxa analyzed in this finding are minimized through annual
implementation of the Navy's island-wide nonnative plant control
program (O'Connor 2009b, pers. comm.; Munson 2011a, pers. comm.). The
focus of the nonnative plant species program is to control plants on
the island with the potential to adversely impact habitat of federally
listed species, which includes the eradication of isolated occurrences
of nonnatives and early detection and eradication of new nonnative
species (Navy 2008b, p. 5-28). This program targets nonnative species
for elimination using herbicide and mechanical removal, with priorities
currently focused on new invasions and particularly destructive
nonnative species. Nonnative species management targets are identified
and prioritized annually by Navy natural resource managers (Munson
2011a, pers. comm.). These tactics have been successful in isolating
and limiting some species, such as Foeniculum vulgare, to a few
locations (Howe 2011b, pers. comm.). To reduce the potential for
transport of nonnative plants to San Clemente Island, military and
nonmilitary personnel inspect tactical ground vehicles and remove any
visible plant material, dirt, or mud on them prior to going to San
Clemente Island (USFWS 2008, p. 63). This cleaning helps prevent
nonnative plants from reaching the island, but once there, nonnative
plants are easily spread from one area to another by the movement of
vehicles.
The Navy has implemented preventative and control programs for the
nonnative plant species on the island. Although nonnatives will
continue to pose a rangewide risk to the habitat of Malacothamnus
clementinus, the Navy has taken steps to curtail habitat conversion by
nonnative plants. Management and control of nonnative plants is not in
place at the four occurrences that are closed to natural resource
managers. However, outside of these areas, M. clementinus has persisted
on the island and, despite the continued risk of encroachment by
nonnatives, its range has continued to expand. Nonnatives remain a
threat to the M. clementinus' habitat, particularly in the four
occurrences that are closed to monitoring and management efforts.
Fire
Fire was not considered a threat to Malacothamnus clementinus at
the time of listing (42 FR 40682; August 11, 1977). Since that time,
however, over 50 percent of the island has experienced at least one
wildfire (Navy 2002, Map 3-3, p. 3-32), and some areas have burned
multiple times with short intervals between fires (Navy 2002, Map 3-4,
p. 3-33). Between 1990 and 2004, there were 114 wildfires on the island
suspected to be from Navy operational sources (Navy 2008a, pp. 5-18, 5-
19). The majority of fires are concentrated in SHOBA, and potentially
impact the habitat of 6 of 11 (54 percent) of M. clementinus
occurrences (Canchalagua Canyon, Horse Beach Canyon, Lower China
Canyon, Upper China Canyon, Cave Canyon, and Chukit Canyon). Three of
these occurrences (Upper China Canyon, Lower China Canyon, and Horse
Beach Canyon) are in Impact Areas I and II, where the risk of frequent
fire (less than 5 years apart) is especially high (Navy 2002, pp. 5-93,
5-99). The effects of fire on habitat within the Impact Areas are
currently unknown due to closure to natural resource personnel (USFWS
2008, p. 50).
The remaining land in SHOBA acts as a buffer from fires and
munitions between the Impact Areas and the rest of the island. Fires
are occasionally ignited by activities north of SHOBA, posing a low-
magnitude threat to the remaining five occurrences (Lemon Tank Canyon,
Box Canyon, Norton Canyon, Middle Ranch Canyon, and Waymuck Canyon)
(Navy 2002, Map 3-4, p. 3-33). Due to the potential for unexploded
ordnance within SHOBA, unless a fire threatens human life or
facilities, it usually is allowed to burn itself out (Navy 2002, p. 3-
32; Kellogg 2006, pers. comm.). This contrasts with the northern
portion of the island where wildfires are usually suppressed (Kellogg
2006, pers. comm.).
Increased fire frequency (more than every 5 years) from intensified
military use could lead to localized changes in vegetation. Nonnative
annual grasses can increase fuel load for fire ignition and spread
within the landscape. Dried grasses provide a fuel that is easily
ignitable, and can extend the fire season by more than a month because
they desiccate sooner than the native herbaceous flora. These grasses
can also colonize a burned area better and more quickly than native
species, thereby creating a cycle where fire and nonnatives are
positive feedbacks for one another (Brooks et al. 2004, p. 677).
Frequent fires within and adjoining military training areas have the
potential to alter the vegetative community, resulting in the
conversion of shrublands to nonnative grasslands, and a reduction in
native perennial bunchgrasses (O'Leary and Westman 1988, p. 779;
D'Antonio and Vitousek 1992, p. 73; Minnich and Dezzani 1998, pp. 383-
384; Keeley et al. 2005, p. 2109; Tierra Data Inc. 2005, p. 88).
At the time of listing, fire was not identified as a threat because
of lack of fire history and the low intensity of military training on
the island. Since that time, military training has significantly
increased, and we have better records of the fire frequency on the
island. Fire is a rangewide threat to the habitat of M. clementinus,
and 6 of
[[Page 29104]]
the 11 occurrences (54 percent) of Malacothamnus clementinus occur
within areas that may be subject to recurrent fire associated with
military training (Table 1; Canchalagua Canyon, Horse Beach Canyon,
Lower China Canyon, Upper China Canyon, Cave Canyon, and Chukit
Canyon). The remaining five occurrences are in habitat with a lower
risk of recurrent fire and are less likely to experience changes in
vegetation community due to fire. It is unlikely that fire control or
prevention measures will be undertaken in the habitat at the three
occurrences within the Impact Areas that are operationally closed.
Fires that escape designated training areas may threaten other parts of
the island, though because of its broad distribution, it is unlikely
that one fire would be capable of spreading throughout the entire range
of M. clementinus. The Navy's implementation of the MOFMP will limit
the frequency of fires that escape Impact Areas. Through the annual
review process, the Navy identifies mechanisms to reduce fire return
intervals in areas where this taxon is concentrated (USFWS 2008, pp.
91-122).
The Navy has implemented preventative and control programs for fire
on the island. Although fire will continue to pose a rangewide risk to
the habitat of Malacothamnus clementinus, the Navy has taken steps to
curtail habitat conversion by frequent and intense fire. Six of the 11
occurrences (54 percent) of M. clementinus occur within areas that may
be subject to recurrent fire associated with military training.
Management and control of fire is not in place at the three occurrences
that are closed to natural resource managers. However, M. clementinus
has persisted on the island and, despite the continued risk of fire,
its range has continued to expand. Fire remains a threat to the M.
clementinus' habitat, particularly in the three occurrences in the
impact areas that are closed to monitoring and management efforts.
Fire Management
In 2008, the Service issued a biological opinion to the Navy on its
MOFMP on San Clemente Island (USFWS 2008, pp. 1-244). The biological
opinion addressed impacts to all 11 currently listed terrestrial taxa
known to occur on San Clemente Island, including the three taxa
analyzed in this finding. Military activities contribute to fires on
San Clemente Island that may adversely affect listed plants and
wildlife (USFWS 2008, p. 3). The Navy's focus on fire management is
related to military training and other human-related activities and
facilities, as these activities represent the primary source of
ignition on the island (USFWS 2008, p. 3). Seasonal range and training
modifications, based on weather patterns and moisture, are efforts
taken by the Navy to assist in the prevention of fire ignition,
containment, and fire suppression (USFWS 2008, pp. 3-4).
In response to the potential hazard of wildfires on San Clemente
Island, firefighting techniques have improved for known operational-
related ignition sources (Navy 2008b, pp. 3.11-71). Within the MOFMP,
the Navy proposed the expansion of military training, as well as the
implementation of a fire management plan directed at fire suppression,
fire prevention, and fuels management. This plan was developed to
provide flexibility for the timing of military training, and will
modify the level of fire suppression resources required to be present
during training activities. Real-time weather data and fuels
management, in combination with the ready availability of fire
suppression resources, are used to minimize the risk of fires spreading
from areas approved for the use of ordnance and incendiary devices. The
Navy has committed to conducting an annual review of fire management
and fire occurrences that will allow for adaptive management and
changes in the MOFMP (USFWS 2008, pp. 91-122).
The MOFMP was developed by the Navy to provide flexibility for the
timing of military training, and to ensure that elevated fire
suppression resources were present to address an increased level of
training activities and fire risk. In response to the potential hazard
of wildland fires on San Clemente Island, firefighting techniques have
improved for known operational-related ignition sources (Navy 2008b,
pp. 3.11-71). The MOFMP defines the conditions under which certain fire
protection resources must be available and ready for use (for example,
a dedicated fire helicopter) (USFWS 2008, p. 53). The MOFMP calls for
the use of real-time weather and fire forecasting to determine when
certain munitions may be used and when helicopters must be present.
After extensive consultation with the Navy, we issued a biological
opinion on the MOFMP that concluded the MOFMP would not jeopardize the
continued existence of listed species, including the three taxa
analyzed in this Finding (USFWS 2008, pp. 1-237). While the increase in
military training and fire suppression could affect habitat of
Malacothamnus clementinus (as well as Acmispon dendroideus var.
traskiae and Castilleja grisea), we have worked with the Navy to avoid
and minimize the impacts to habitat of individuals or occurrences to
the extent practicable while meeting the operational needs of the Navy.
Fire suppression activities described in the MOFMP and used by the
Navy include creating firebreaks (bare soil created through manual or
herbicide removal of vegetation), use of fire retardants (spraying of
fire retardants along fire breaks) and aerial drops of saltwater from
aircraft. Fire management on San Clemente Island includes the creation
of fuelbreaks within areas of SHOBA that impact the habitat at three
Malacothamnus clementinus occurrences (Horse Beach Canyon, Lower China
Canyon, and Upper China Canyon) (USFWS 2008, p. 57). Fuelbreaks are
maintained along the boundaries of Impact Areas I and II to prevent the
spread of fire outside of the areas (USFWS 2008, p. 57). Fuelbreaks on
the island are created using herbicides and strip burning, and
maintained using herbicides and fire retardant (Phos-Chek D75F) (USFWS
2008, pp. 97-98). The use of fire retardant or herbicide, as proposed
in the MOFMP, results in the loss of M. clementinus and Castilleja
grisea habitat within the fuelbreak footprint (USFWS 2008, p. 81). The
use of Phos-Chek may also allow or facilitate the expansion and
persistence of nonnative species due to the fertilizing effect of this
retardant (Larson et al. 1999, p. 115; Kalabokidis 2000, p. 130). Fire
retardants act as a source of nitrogen and phosphorous, which are
nutrients that can affect plant species composition (Larson and Duncan
1982, p. 702). The Navy has begun a study on the effects of Phos-Chek
on San Clemente Island vegetation, and has avoided application of Phos-
Chek within 300 ft (91.4 m) of mapped listed species (including M.
clementinus and C. grisea) to the extent allowable with fuelbreak
installation (USFWS 2008, pp. 97-98).
It is anticipated that the Navy will construct fuelbreaks to
minimize the risk of fire spreading from areas of live fire and
demolition training north of SHOBA (USFWS 2008, p. 98). In the MOFMP,
the Navy agreed to conduct preseason briefings for firefighting
personnel on the guidelines for fire suppression, and the limitations
associated with the use of Phos-Chek and saltwater drops (USFWS 2008,
pp. 97-98). The impact of saltwater on the habitat of M. clementinus
(and Castilleja grisea) has not yet been assessed. However, if salt
persists, the composition of the plant community could change to favor
more salt-tolerant taxa. Fire management could have a
[[Page 29105]]
direct impact on the habitat and species composition of at least three
occurrences of M. clementinus.
The Navy's implementation of a MOFMP will help to reduce the risk
of habitat conversion by fire, though the habitat of Malacothamnus
clementinus could be altered by the management of fire. Although the
threat is ameliorated through implementation of the MOFMP, fire
management remains a threat to M. clementinus, particularly to the
three occurrences that fall within areas that may be managed using fuel
breaks and fire suppression.
Summary of Factor A
From 1850 until 1934, San Clemente Island was used for sheep
ranching, cattle ranching, goat grazing, and pig farming (Navy 2002,
pp. 3-4). The effects of these grazers, which were not completely
removed from the island until 1992, on the habitat and plants were one
of the original reasons for classifying Malacothamnus clementinus as
endangered in the 1977 listing rule (42 FR 40682); this threat is now
eliminated. Currently, M. clementinus is threatened by the destruction
and modification of habitat caused by impacts related to designated
land use, erosion, the spread of nonnative plants, fire, and fire
management practices. To help ameliorate these threats, the Navy is
implementing a MOFMP and the island-wide control of nonnative plants as
outlined in the INRMP (Navy 2002, pp. 3-114-3-116; USFWS 2008, pp. 1-
237). The fire management plan within the MOFMP has been used to inform
strategic decisions for training using live fire or incendiary devices.
Three occurrences within the Impact Areas are now closed to natural
resource monitoring and management, and currently their status is
unknown; a fourth occurrence (Lemon Tank) is also closed but is not
within the Impact Areas.
Per our 2008 biological opinion, the Navy has postponed major troop
and assault vehicle maneuvers across the island until it completes and
implements an erosion control plan (USFWS 2008, pp. 62, 87). Natural
resource managers have been successful at decreasing the prevalence of
particularly destructive nonnatives, such as Foeniculum vulgare.
Management actions directed at conservation of Malacothamnus
clementinus may not be fully implemented at 4 of the 11 known
occurrences (Lower China Canyon, Upper China Canyon, Horse Beach
Canyon, and Lemon Tank Canyon) currently closed to natural resource
access. This will reduce and fragment the effectiveness of the
conservation measures. Although the species is expanding, and ongoing
and anticipated conservation efforts contribute to its conservation,
military training activities, erosion, nonnatives, and fire have
ongoing impacts to all M. clementinus occurrences rangewide both now
and into the future.
Factor B. Overutilization for Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682; August 11, 1977), the Service did
not identify any threats from overutilization, and there is no new
information to indicate that overutilization is a threat to
Malacothamnus clementinus. Although herbarium specimens of M.
clementinus and seeds have been collected for research and seed
banking, overutilization of M. clementinus for any purpose is not
currently considered a threat nor is expected to be in the future.
Factor C. Disease or Predation
Grazing of feral goats and the rooting of feral pigs was considered
a threat under this category to Malacothamnus clementinus in the final
listing rule (42 FR 40682, at 40684; August 11, 1977). This threat was
ameliorated by the removal of the goats and pigs from San Clemente
Island in 1992, as recognized in our 2007 status review (USFWS 2007a,
p. 16). Currently, no other predators or diseases on San Clemente
Island are known to pose a significant threat to M. clementinus, nor
are they expected to in the future.
Factor D. Inadequacy of Existing Regulatory Mechanisms
The Act requires us to examine the adequacy of existing regulatory
mechanisms with respect to those existing and foreseeable threats that
may affect Malacothamnus clementinus. The inadequacy of existing
regulatory mechanisms was not indicated as a threat to M. clementinus
at listing (42 FR 40682; August 11, 1977). Since it was listed as
endangered, the Act has been and continues to be the primary Federal
law that affords protection to M. clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea. The Service's responsibilities in
administering the Act include sections 7, 9, and 10.
Section 7(a)(1) of the Act requires all Federal agencies, including
the Navy, to utilize their authorities in furtherance of the purposes
of the Act by carrying out programs for the conservation of endangered
and threatened species. Section 7(a)(2) of the Act requires Federal
agencies, including the Service and the Navy, to ensure that actions
they fund, authorize, or carry out do not ``jeopardize'' the continued
existence of a listed species or result in the destruction or adverse
modification of habitat in areas designated by the Service to be
critical. Critical habitat has not been designated or proposed for this
taxon. A jeopardy determination is made for a project that is
reasonably expected, either directly or indirectly, to appreciably
reduce the likelihood of both the survival and recovery of a listed
species in the wild by reducing its reproduction, numbers, or
distribution (50 CFR 402.02). A non-jeopardy opinion may include
reasonable and prudent measures that minimize the extent of impacts to
listed species associated with a project. Under section 9(a)(2) of the
Act, with respect to endangered plant taxa, it is unlawful to remove
and reduce to possession (collect) any such taxon from areas under
Federal jurisdiction; maliciously damage or destroy any such taxon on
any such area; or remove, cut, dig up, or damage or destroy any such
species on any other area in knowing violation of any law or regulation
of any State or in the course of any violation of a State criminal
trespass law.
Since it was first listed in 1977, the Navy has consulted and
coordinated with us regarding the effects of various activities on
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea. In November 2008, we completed a biological opinion
describing the impact of the Navy's military training program proposed
in the MOFMP on 11 federally listed species that occur on San Clemente
Island (USFWS 2008, pp. 1-237). We considered the status and
distribution of M. clementinus, the various management strategies, and
the avoidance and minimization measures in place and those the Navy
will implement with the new plan (as well as A. d. var. traskiae and C.
grisea). Additionally, the Service made conservation recommendations
within the biological opinion, including: (1) Considering recommended
actions from the 5-year review in the upcoming revision of the INRMP,
and (2) propagation and outplanting of narrowly distributed, listed
plant species. We concluded that ongoing and likely impacts from the
proposed increases in military training activities would not jeopardize
the continued existence of M. clementinus, A. d. var. traskiae, and C.
grisea (USFWS 2008, pp. 1-237).
[[Page 29106]]
Thus, listing Malacothamnus clementinus provided a variety of
protections, including the prohibitions against removing or destroying
plants within areas under Federal jurisdiction and the conservation
mandates of section 7 for all Federal agencies. If M. clementinus were
not listed, these protections would not be provided. Thus, we must
evaluate whether other regulatory mechanisms would provide adequate
protections absent the protections of the Act.
Other Federal Protections
National Environmental Policy Act (NEPA)
All Federal agencies are required to adhere to the National
Environmental Policy Act (NEPA) of 1970 (42 U.S.C. 4321 et seq.) for
projects they fund, authorize, or carry out. The Council on
Environmental Quality's regulations for implementing NEPA (40 CFR parts
1500-1518) state that agencies shall include a discussion on the
environmental impacts of the various project alternatives (including
the proposed action), any adverse environmental effects that cannot be
avoided, and any irreversible or irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA is a disclosure law, and does not
require subsequent minimization or mitigation measures by the Federal
agency involved. Although Federal agencies may include conservation
measures for Malacothamnus clementinus as a result of the NEPA process,
any such measures are typically voluntary in nature and are not
required by the statute. NEPA does not itself regulate activities that
might affect M. clementinus, but it does require full evaluation and
disclosure of information regarding the effects of contemplated Federal
actions on sensitive species and their habitats.
On San Clemente Island, the Navy must meet the NEPA requirements
for actions significantly affecting the quality of the human
environment. Typically, the Navy prepares Environmental Assessments and
Environmental Impact Statements on operation plans and new or expanding
training actions. Absent the listing of M. clementinus, we would expect
the Navy to continue to meet the procedural requirements of NEPA for
its actions, including evaluating the environmental impacts to rare
plant species and other natural resources. However, as explained above,
NEPA does not itself regulate activities that might affect M.
clementinus.
Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670) authorizes the Secretary of Defense
to develop cooperative plans with the Secretaries of Agriculture and
the Interior for natural resources on public lands. The Sikes Act
Improvement Act of 1997 requires Department of Defense installations to
prepare Integrated Natural Resources Management Plans (INRMPs) that
provide for the conservation and rehabilitation of natural resources on
military lands consistent with the use of military installations to
ensure the readiness of the Armed Forces. An INRMP is a plan intended
``* * * to guide installation commanders in managing their natural
resources in a manner that is consistent with the sustainability of
those resources while ensuring continued support of the military
mission'' (Navy 2002, p. 1-1). INRMPs are developed in coordination
with the State and the Service, and are generally updated every 5
years. Although an INRMP is technically not a regulatory mechanism
because its implementation is subject to funding availability, it is an
important guiding document that helps to integrate natural resource
protection with military readiness and training.
San Clemente Island Integrated Natural Resources Management Plan
(INRMP)
Pursuant to the Sikes Act, the Navy adopted an INRMP for San
Clemente Island that targets multiple objectives towards protection of
Malacothamnus clementinus and its habitat, and helps to reduce threats
to this taxon (Navy 2002). The INRMP includes provisions to comply with
the Endangered Species Act, the Comprehensive Environmental Response,
Compensation, and Liability Act (42 U.S.C. 9601), the Resources
Conservation and Recovery Act (42 U.S.C. 6901), the Federal Noxious
Weed Act of 1974 (7 U.S.C. 2801), and the Soil Conservation Act (16
U.S.C 3B). Goals and objectives in the INRMP for specified management
units on the island are identified based on each unit's ranking for
both military and natural resource value. Natural resource management
objectives for the management units are stepped down from broader
natural resource objectives identified for species and habitats. Of
relevance to the protection of M. clementinus, the INRMP includes an
objective to: ``Protect, monitor, and restore plants and cryptograms in
order to manage for their long-term sustainability on the island''
(Navy 2002, p. 4-39).
The INRMP specifically includes the following objectives for
Malacothamnus clementinus management: removal of nonnatives,
restoration of native plant communities, monitoring of the species,
studies of the species' response to fire, and studies and inventory of
insect pollinators (Navy 2002, pp. D-20, D-21). Other INRMP strategies
that target the plant communities within which the three species occur
include: controlling erosion, with priority given to locations where
erosion may be affecting listed species; producing a new vegetation
map; reducing nonnative plant cover from 1992-1993 baseline levels;
managing the size and intervals of fires; experimenting with fire
management to improve native plant dominance while protecting sensitive
plant occurrences; and conducting genetic and biological studies of M.
clementinus, Acmispon dendroideus var. traskiae, and Castilleja grisea
across the island.
To date, multiple INRMP management strategies, or aspects of them,
have been implemented. The Navy has implemented rare plant surveys and
has documented new occurrences of Malacothamnus clementinus, Acmispon
dendroideus var. traskiae, and Castilleja grisea on the island. Genetic
research and natural history studies have also been performed.
Concerted efforts have been made to control escape of fire from
military training activities, and the Navy has annually implemented
nonnative plant species control activities, with a focus on species
that have the potential to compete with listed species. Overall,
considerable progress has been made toward the identified INRMP goals
to maintain sustainable occurrences and implement strategies that help
reduce threats to M. clementinus, A. d. var. traskiae, and C. grisea.
The INRMP is an important guiding document that helps to integrate
the military's mission with natural resource protection on San Clemente
Island. Although the INRMP includes objectives targeted toward habitat
protection of optimal Malacothamnus Clementinus, Acmispon dendroideus
var. traskiae, and Castilleja grisea habitat, Navy operational needs
may diverge from INRMP natural resource goals. For example, control
measures for erosion, fire, and nonnatives described in the INRMP may
not be implemented effectively or consistently in those areas that are
operationally closed due to the presence of unexploded ordnance. The
MOFMP, Erosion Control Plan, and nonnative plant species control
conducted on the island are discussed above under Factor A. The Present
or Threatened Destruction, Modification, or Curtailment of Its Habitat
or Range. Absent listing under the Act, the Navy would still be
required to develop and
[[Page 29107]]
implement INRMPs under the Sikes Act. However, as noted under the other
factors, while the INRMP helps to ameliorate threats and provides some
protection for M. clementinus occurrences, those occurrences within
Impact Areas or operationally closed areas may not benefit from the
conservation measures. While the INRMP has reduced the severity of
threats and contributed to conservation of the species, it still allows
for land use consistent with military readiness and training. Thus,
Navy activities will continue to impact M. clementinus as described
under Factor A.
State Protections
Since the time of listing, Malacothamnus clementinus has benefited
from additional State protections under the Native Plant Protection Act
(NPPA) and California Endangered Species Act (CESA; listed 1982).
However, the range of M. clementinus is restricted to a Federal
military installation, so listing under NPPA and CESA may only afford
protection to this species in rare instances when the lead agency is a
non-Federal agency or when proposed activities fall under other State
laws.
Summary of Factor D
In continuance of a long history of cooperative conservation
efforts, the Navy has implemented several conservation actions that
benefit this taxon. The Navy has a MOFMP to reduce the risk of fire on
the island and a nonnative plant species control program. Following
review of the Navy's MOFMP, we issued a non-jeopardy biological
opinion, which included measures that the Navy has implemented to
manage fires and avoid and minimize the impacts of military activities
on listed plants. The provisions included in the San Clemente Island
INRMP provide protection to accessible Malacothamnus clementinus
occurrences, and adaptive management of their habitat, to help address
threats from military activities and nonnative plants. However, as
indicated in the discussion under Factor A, not all of the management
tools described in the INRMP are in place, and conservation measures
may not be implemented at several of the closed occurrences of the
species. Malacothamnus clementinus occurrences are afforded some
protection through Federal and military mechanisms. However, in the
absence of the Act, the existing regulatory mechanisms are not
currently adequate to provide for the long-term conservation of M.
clementinus.
Factor E. Other Natural or Manmade Factors Affecting Its Continued
Existence
The 1977 listing rule identified nonnatives as a threat to
Malacothamnus clementinus under Factor E: competition from nonnative
plants (42 FR 40682; August 11, 1977). In this 5-factor analysis,
impacts from nonnative plants are discussed above under Factor A as a
threat to habitat. Other Factor E threats identified since listing that
currently impact M. clementinus plants include: (1) Movement of
vehicles and troops, (2) fire, (3) climate change, and (4) genetic
diversity. Factor E addresses threats to individuals of the species,
rather than the habitat modification threats that are discussed in
Factor A. Therefore, while some threats are discussed in both sections,
in this section we are focusing on the direct impacts to individuals of
M. clementinus.
Movement of Vehicles and Troops
Military training activities within SWAT, TAR, and the IOA often
entail the movement of vehicles and troops over the landscape with the
potential of trampling or crushing individual plants of all three
species. SWATs are large areas that typically support the movement of
small groups to reach an objective or destination. The dispersed
movement of troops through these areas is likely to result in
occasional trampling of plants, with minor or temporary impacts at the
occurrence level. TARs are generally smaller areas designated to
accommodate intensive use and bombardment. Plants located within TARs
are therefore more vulnerable to being trampled by vehicle and troop
movements, particularly as the level of military training increases in
these areas.
Use of the IOA, at its highest intensity, involves the movement of
battalion-sized landings of troops (1,500 individuals) from the
northern to southern end of the island several times a year. During
such operations, it is anticipated that about half of the troops will
travel on roads in vehicles, while the other half will proceed on foot.
Based on the distribution of Malacothamnus clementinus occurrences and
type of troop movements likely to occur, impacts due to trampling and
crushing are likely to occur within the IOA, along roads and in the
Impact Areas. Specifically, major troop movements and vehicle landings
are planned through Horse Beach and the Horse Beach Canyon occurrence,
with troops and assault vehicles moving north along Horse Beach Road
from the beach (USFWS 2008, pp. 30, 41). These operations could affect
the Horse Beach Canyon and Lower China Canyon occurrences (USFWS 2008,
pp. 85-86).
The implementation of conservation measures and the status of the
plants at Horse Beach Canyon, Upper and Lower China Canyon, and Lemon
Tank Canyon are currently unknown because they are closed to natural
resource personnel (USFWS 2008, p. 50). Four of 11 occurrences (36
percent; Lower China Canyon, Upper China Canyon, Horse Beach Canyon,
and Lemon Tank Canyon) are partially or wholly within the boundaries of
a training area (Impact Area or SWAT) and are likely to sustain some
losses due to trampling associated with the proposed increases in troop
and vehicle movements. With the lack of access to all four occurrences,
the management of this threat and the ability to assess the plant's
condition is compromised, and the full effects of trampling on the
species are unknown. Therefore, the movement of troops and vehicles is
still considered a threat to M. clementinus.
Fire
Although not specifically mentioned in the listing rule, intense or
frequent fires impact plants at 6 of the 11 occurrences (54 percent) of
Malacothamnus clementinus. In the Factor A discussion above, we
addressed impacts of fire on the habitat. This section includes
discussion on the discrete threat to individuals of M. clementinus. As
discussed in the Background section, it is unknown if M. clementinus is
adapted to fire, though it is likely that this species is resilient to
occasional fires (USFWS 1984. p. 48; Navy 2002, D-20; USFWS 2007a, p.
3). No direct studies have been done on the effects of fire on M.
clementinus; however, its continued presence in areas that have burned
(such as in SHOBA), and its ability to vegetatively reproduce, suggest
it is at least tolerant of periodic fire. The species' adaptation to
fire frequency is unknown. In areas that burn on a more frequent basis,
the seed bank may become depleted if individuals burn before they
produce seeds. Additionally, M. clementinus was observed to have low
numbers of seeds in natural populations (Junak and Wilken 1998, p.
291). Frequent burns might exhaust the already small seed bank, and
inhibit reproduction in M. clementinus.
Malacothamnus clementinus occurs in some areas of the island that
may experience elevated fire frequency, such as in SHOBA and especially
within the Impact Areas (Lower China Canyon, Upper China Canyon, and
Horse Beach
[[Page 29108]]
Canyon) (see Factor A above). The Navy's fire management practices are
expected to minimize ignitions as well as the spread of fires (see
Factor A). However, fires ignited within the boundaries of the Impact
Areas will not be suppressed due to closures and safety restrictions
within these areas. This would affect the three occurrences of M.
clementinus found within these areas. The Navy conducts annual reviews
of fire management and fire occurrences to allow for adaptive
management. These measures should minimize the frequency and spread of
fires that could result in the loss of M. clementinus individuals or
occurrences. The Navy's ongoing implementation of the MOFMP will limit
the frequency with which fires escape Impact Areas and TAR, and that,
through the annual review process, the Navy will identify mechanisms to
reduce fire return intervals in areas not designated for incendiary use
(USFWS 2008, pp. 76-91).
Although the Navy has planned and implemented fire management, fire
still affects six occurrences of Malacothamnus clementinus. Three of
these occurrences fall within areas that are closed to natural
resources management and prone to fire due to bombing of the area.
Therefore, fires within these areas are allowed to burn, affecting the
individuals and occurrences. Due to these conditions and the continued
impacts of fire within SHOBA, fire remains a Factor E threat to the
existence of M. clementinus both currently and in the future.
Climate Change
Consideration of climate change is a component of our analyses
under the Endangered Species Act, and applies in this finding to our
analysis of all three taxa. In general terms, ``climate change'' refers
to a change in the state of the climate (whether due to natural
variability, human activity, or both) that can be identified by changes
in the mean or variability of its properties, and that persists for an
extended period--typically decades or longer (Intergovernmental Panel
on Climate Change (IPCC) 2007a, p. 78).
Changes in climate are occurring. Examples include warming of the
global climate system over recent decades, and substantial increases in
precipitation in some regions of the world and decreases in other
regions (for these and other examples see IPCC 2007a, p. 30; Solomon et
al. 2007, pp. 35-54, 82-85).
Most of the observed increase in global average temperature since
the mid-20th century cannot be explained by natural variability in
climate, and is very likely due to the observed increase in greenhouse
gas concentrations in the atmosphere as a result of human activities,
particularly emissions of carbon dioxide from fossil fuel use (IPCC
2007a, p. 5 and Figure SPM.3; Solomon et al. 2007, pp. 21-35).
Therefore, to project future changes in temperature and other climate
conditions, scientists use a variety of climate models (which include
consideration of natural processes and variability) in conjunction with
various scenarios of potential levels and timing of greenhouse gas
emissions (e.g., Meehl et al. 2007 entire; Ganguly et al. 2009, pp.
11555, 15558; Prinn et al. 2011, pp. 527, 529).
The projected magnitude of average global warming for this century
is very similar under all combinations of models and emissions
scenarios until about 2030. Thereafter, the projections show greater
divergence across scenarios. Despite these differences in projected
magnitude, however, the overall trajectory is one of increased warming
throughout this century under all scenarios, including those which
assume a reduction of greenhouse gas emissions (Meehl et al. 2007, pp.
760-764; Ganguly et al. 2009, pp. 15555-15558; Prinn et al. 2011, pp.
527, 529). (For examples of other global climate projections, see IPCC
2007b, p. 8).
Various types of changes in climate can have direct or indirect
effects on species and these may be positive or negative depending on
the species and other relevant considerations, including interacting
effects with existing habitat fragmentation or other non-climate
variables. There are three main components of vulnerability to climate
change: Exposure to changes in climate, sensitivity to such changes,
and adaptive capacity (IPCC 2007, p. 89; Glick et al 2011, pp. 19-22).
Because aspects of these components can vary by species and situation,
as can interactions among climatic and non climatic conditions, there
is no single way to conduct our analyses. We use the best scientific
and commercial data available to identify potential impacts and
responses by species that may arise in association with different
components of climate change, including interactions with non climatic
conditions.
As is the case with all potential threats, if a species is
currently affected or is expected to be affected in a negative way by
one or more climate-related impacts, this does not necessarily mean the
species meets the definition of a threatened or endangered species as
defined under the Act. The impacts of climate change and other
conditions would need to be to the level that the species is in danger
of extinction, or likely to become so, throughout all or a significant
portion of its range. If a species is listed as threatened or
endangered, knowledge regarding the species' vulnerability to, and
impacts from, climate-associated changes in environmental conditions
can be used to help devise appropriate strategies for its recovery.
While projections from global climate model simulations are
informative and in some cases are the only or the best scientific
information available, various downscaling methods are being used to
provide higher-resolution projections that are more relevant to the
spatial scales used to assess impacts to a given species (see Glick et
al, 2011, pp. 58-61). With regard to the area of analysis for the San
Clemente Island and specifically for the three species at issue here,
downscaled projections are available at least with respect to southern
California.
San Clemente Island is located within a Mediterranean climatic
regime, but with a significant maritime influence. Climate change
models indicate a 1.8 to 5.4 degrees Fahrenheit (1 to 3 degrees
Celsius) increase in average temperature for southern California by the
year 2070 (Field et al. 1999, p. 5; Cayan et al. 2008, p. S26; PRBO
2011, p. 40). Over the same time span, a 10 to 37 percent decrease in
annual precipitation is predicted (PRBO 2011, p. 40), though other
models predict little to no change in annual precipitation (Field et
al. 1999, pp. 8-9; Cayan et al. 2008, p. S26). Although the island has
a short rainy season, the presence of fog during the summer months
helps to reduce drought stress for many plant species (Halvorson et al.
1988, p. 111; Fischer et al. 2009, p. 783). However, fog projections
remain uncertain (Field et al. 1999, pp. 21-22). There is also
substantial uncertainty in precipitation projections, and relatively
little consensus concerning precipitation patterns and projections for
southwestern California (PRBO 2011, p. 40). San Clemente Island
typically gets less rainfall than the neighboring mainland areas
(Tierra Data 2005, p. 4). Therefore, the models may underestimate the
effects of precipitation changes on island vegetation. Additionally,
Malacothamnus clementinus typically occurs on the western side of the
island, which is a less productive and drier climate (Tierra Data 2005,
p. 7). Less rainfall and warmer air temperatures could limit the range
of M. clementinus, although there is no direct research on the effects
of climate change on the species.
[[Page 29109]]
The impacts of predicted future climate change to Malacothamnus
clementinus remain unclear. The best available information does not
provide sufficient certainty on how and when climate change will affect
the species, the extent of average temperature increases in California,
or potential changes to the level of threat posed by fire on San
Clemente Island. The most recent literature on climate change includes
predictions of hydrological changes, higher temperatures, and expansion
of drought areas (IPCC 2007a, pp. 1-18). While we recognize that
climate change is an important issue with potential effects to listed
species and their habitats, the best available information does not
inform accurate predictions regarding its impacts to M. Clementinus at
this time.
Genetic Diversity
As discussed in the Background section, Malacothamnus clementinus
has low genetic variability when compared with other island endemic
plant species (Helenurm 1999, p. 40). This lack of diversity could
hinder the species' ability to persist through a fluctuating
environment or stochastic event. Although the number of known
occurrences of M. clementinus has increased from 3 to 11 since its
listing, there appears to be little gene flow among occurrences, and
each comprises a relatively small number of genetically distinct
individuals (Junak and Wilken 1998, p. 290; Helenurm 1999, p. 39).
Genetic fitness typically decreases with decreasing genetic variation
and population size (Leimu et al. 2006, p. 942). Specifically, small
population size and low levels of genetic interchange make M.
clementinus occurrences particularly vulnerable to inbreeding
depression and loss of genetic variability due to genetic drift (the
change in the frequency of appearance of a gene in a population of
organisms due to chance or random events) (Ellstrand and Elam 1993, p.
217).
Genetic analysis suggests that M. clementinus has very low genetic
variation at both the species and population levels (Helenurm 1997, p.
50; Helenurm 1999, p. 39), even far below average when compared to
other endemic plant species (Helernurm 1999, p. 39). Low genetic
variation may affect the ability of occurrences to adjust to novel or
fluctuating environments, survive stochastic events, or maintain high
levels of reproductive performance (Huenneke 1991, p. 40). This
constitutes a species and rangewide threat for which there is no
immediate solution or amelioration.
Malacothamnus clementinus occurrences have low seed production,
suggesting the existence of a self-incompatibility mechanism (Helenurm
1997, p. 50; Junak and Wilken 1998, p. 291; Helenurm 1999, p. 39). Low
seed production may also be the result of low pollinator visitation
and, in combination with low genetic diversity, could contribute to
observed low recruitment in populations (Huenneke 1991, pp. 37-40;
Junak and Wilken 1998, p. 291; Helenurm 1999, pp. 39-40). Although
studies show that patches of plants are not made up of a single clonal
individual (clump of genetically identical stems resulting from
vegetative reproduction), it is still possible that patches comprise
closely related individuals that share alleles controlling their
ability to successfully reproduce with each other (Helenurm 1999, pp.
39-40). Although this species has apparently expanded its range from
that known at the time of listing and persisted through habitat
disturbance, it may still remain susceptible to extirpation from low
genetic variation and genetic drift. A reduction in occurrence size
through years of grazing could have substantially lowered genetic
variation (Helenurm 2005, p. 1221), which could decrease genetic
fitness and compromise the species' ability to adapt to stochastic
events (Huenneke 1991, p. 40). The apparent loss of genetic diversity
resulting in current low genetic variation and low recruitment
constitute a species and rangewide threat to M. clementinus.
Summary of Factor E
Threats associated with trampling from military activities, fire,
climate change, and low genetic diversity continue to impact
Malacothamnus clementinus at all of the 11 occurrences on San Clemente
Island. Trampling and crushing of individual plants are likely to
increase at four occurrences (36 percent) in association with increased
training levels on the island. However, this taxon has expanded its
distribution on the island and the Navy is implementing conservation
measures that will improve conditions for M. clementinus. Military
training activities have the potential to ignite fires within
occurrences or that spread to habitat supporting this species. In
preparation for these training efforts, the Navy implemented a MOFMP to
limit the frequency of fires escaping from the Impact Areas, although
suppression likely will not occur within the boundaries of the Impact
Areas. Climate change may also likely influence M. clementinus, though
the effects are largely unknown. The genetic fitness of M. clementinus
may be threatened by low genetic diversity and small population size.
The threats described here affect all of the occurrences of M.
clementinus both now and in the future; therefore, these threats also
affect its recovery.
Combination of Factors--Malacothamnus clementinus
A species may be affected by more than one threat in combination.
Within the preceding review of the five listing factors, we have
identified multiple threats that may have interrelated impacts on
Malacothamnus clementinus (these interrelated impacts also occur for
Acmispon dendroideus var. traskiae and Castilleja grisea). For example,
fires (Factor A and E) may be more intense or frequent in the habitat
if there are greater amounts of nonnative grass (Factor A) present in
the vegetative community. Similarly, fires (Factor A and E) also may
become more frequent if the climate changes (Factor E) into a drier,
hotter environment. The movement of troops and vehicles (Factor E) and
land use (Factor A) can also create more disturbance and erosion
(Factor A) in M. clementinus' habitat (as well as A. d. var. traskiae
and C. grisea habitat). The historical past on San Clemente is an
illustration of interacting threats: Nonnative herbivores (Factor C)
ate and killed much of the vegetation, causing greater impacts of
erosion (Factor A) on the island. Thus, the species' productivity may
be reduced because of these threats, either singularly or in
combination. However, it is not necessarily easy to determine (nor is
it necessarily determinable) whether a particular threat is the primary
threat having the greatest effect on the viability of the species, or
whether it is exacerbated by or working in combination with other
threats to have cumulative or synergistic effects on the species. While
the combination of factors is a threat to the existence of M.
clementinus, we are unable to determine the magnitude or extent of
cumulative or synergistic effects of the combination of factors on the
viability of the species at this time.
Acmispon dendroideus var. traskiae (San Clemente Island lotus)
In the 2007 status review, we acknowledged that the predominant
threat at listing (grazing and rooting from feral herbivores) was
ameliorated with the removal of goats and pigs from the island in 1992
(USFWS 2007b, pp. 1-22). Threats to Acmispon dendroideus var. traskiae
identified in the 2007 status review include: (1) Erosion, (2)
nonnative species, (3) fire,
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(4) land use, (5) access to SHOBA, and (6) hybridization. Impacts from
erosion, nonnatives, fire, and land use are discussed below under
Factor A, and hybridization is discussed under Factor E below. As
discussed above, access to SHOBA is not considered a threat, though it
limits our ability to assess all occurrences of the taxon reviewed
here.
Factor A. The Present or Threatened Destruction, Modification, or
Curtailment of Its Habitat or Range
The final listing rule (42 FR 40682; August 11, 1977) identified
the following threats to Acmispon dendroideus var. traskiae: Habitat
alteration and destruction, competition from nonnative species, and
direct predation caused by nonnative herbivores (goats and pigs). The
vegetation on San Clemente Island has rebounded, and the status of many
rare plant occurrences, including A. d. var. traskiae, has improved
with the final removal of herbivores in 1992 (Junak and Wilken 1998, p.
18; Junak 2006a, pers. comm.). Although the principle threat to A. d.
var. traskiae identified in the final listing rule has been eliminated,
erosion as a result of overgrazing and invasive nonnative plants remain
ongoing threats to habitat of A. d. var. traskiae. Habitat alteration
and disturbance from the Navy's use of the island for military
operation and training were identified as additional threats to the
habitats occupied by A. d. var. traskiae in the Recovery Plan and the
2007 status review (USFWS 1984, pp. 58-63; USFWS 2007b, pp. 11, 12).
Additional threats recognized since listing include land use by
military training activities, and fire. As outlined below, we discuss
impacts of the following threats that affect the habitat or range of A.
d. var. traskiae: (1) Land use, (2) erosion, (3) nonnative plants, and
(4) fire.
Land Use
Eight of 29 Acmispon dendroideus var. traskiae occurrences (28
percent; Eagle Canyon, Bryce Canyon, North Mosquito Cove, Canchalagua
Canyon, Thirst Canyon, Cave Canyon, Horse Canyon, and Pyramid Head)
occur within SHOBA, where impacts are more likely. Most of the land
area of the SHOBA serves as a buffer from the Impact Areas, although
military training in parts of SHOBA could result in habitat alteration
due to OHV and large-scale troop movements through the military impact
and training areas (IOA and AVMA). Most of the occurrences within SHOBA
are located along the eastern escarpment, which should provide a level
of protection from training impacts. Large-scale troop movements are
less likely in this area, because of the extreme slope of the
escarpment. Training impacts may become difficult to assess and manage
with the recent closure of the eastern escarpment due to unexploded
ordnance.
Four of 29 of A. d. var. traskiae occurrences (14 percent;
Canchalagua Canyon, Middle Island Plateau, North Mosquito Cove, and
Eagle Canyon) are within or partially within the IOA and may experience
direct impacts, while nine occurrences (31 percent; Upper Middle Ranch
Canyon, Warren Canyon, Horton Canyon, Upper Wallrock Canyon, Tota
Canyon, Lemon Tank Canyon, Larkspur Canyon, Chamish Canyon, and North
Island Terraces) are within 1,000 ft (305 m) of the IOA, and could
experience diffuse or accidental impacts associated with troop
movement. These areas near the IOA are at less risk of disturbance than
the occurrences within the IOA, and would only be likely to sustain
diffuse or accidental impacts to the habitat. While the increase in
military training could affect the species, the Navy through
implementation of the INRMP will avoid and minimize impacts to
individuals or occurrences of A. d. var. traskiae (as a rare plant
species), to the extent practicable while meeting operational needs
(Navy 2002, p. 1-2) (see above discussion on Land Use under
Malacothamnus clementine--Factor A).
Because of the taxon's close proximity to Navy facilities, military
activities have the potential to impact habitat at one of the largest
known occurrences of Acmispon dendroideus var. traskiae, near Wilson
Cove. All construction, maintenance, and training activities in the
Wilson Cove area go through a site approval request process. Through
this process, the areas are assessed to see if the activities will
potentially impact any listed species, including A. d. var. traskiae.
Part of this occurrence is within a TAR where tactical training and
movement are projected to occur, possibly causing habitat damage
through troop traffic (USFWS 2008, pp. 119-120). Work was done recently
at Wilson Cove that affected A. d. var. traskiae, and the Navy assessed
the impact to be a loss of habitat occupied by 50 plants. The Navy
worked to salvage plant material and outplant back to the site. Thus
far, this outplanting has been successful, the habitat has rebounded,
and more plants are present in the area than before the work was done
(Munson 2011a, pers. comm.).
Twenty-four of 29 occurrences (83 percent) of A. d. var. traskiae
are located outside of heavily impacted training areas. Though five
occurrences (17 percent; Wilson Cove, Canchalagua Canyon, Middle Island
Plateau, North Mosquito Cove, and Eagle Canyon) are partially or wholly
within the boundaries of an IOA or TAR, many of the impacts to these
occurrences would be diffuse, and are unlikely to have a high impact on
the species' habitat. Although land use is likely to impact A. d. var.
traskiae habitat, the Navy has demonstrated its commitment to help
conserve and manage listed species on the island. Land use appears to
pose a high-magnitude threat to the habitat of a small percentage of
the occurrences of A. d. var. traskiae on San Clemente Island.
Erosion
Erosion and associated soil loss caused by browsing of feral goats
and rooting of feral pigs likely modified the island's habitat (Navy
2002, p. 1-14). Defoliation from overgrazing increased erosion over
much of San Clemente Island. In the INRMP, erosion was identified as a
threat to the canyon woodland habitat and maritime desert scrub where
Acmispon dendroideus var. traskiae occurs (Navy 2002, p. 4-3). Gullying
and other processes may concentrate surface runoff to unnatural levels,
leading to accelerated erosion in the canyons below (Tierra Data Inc.
2007, p. 6). Acmispon dendroideus var. traskiae occurs within steep
canyon areas where such concentration of flows may be a threat to its
habitat or range.
Although more vegetative cover is now present than at the time of
listing, erosion is still a threat to the recovery of Acmispon
dendroideus var. traskiae, especially in areas where it grows in close
proximity to roads. The Navy studied the potential for erosion from
several proposed military activities (Tierra Data Inc. 2007, pp. 1-45,
Appendices). Increased military activities, especially where the taxon
is located within training area boundaries (IOA), are expected to cause
erosion through soil compaction or other soil disturbances in occupied
habitat areas associated with roadways or vehicle maneuver areas
(Tierra Data Inc. 2007, p. 12). Four of 29 A. d. var. traskiae
occurrences (14 percent; Middle Island Plateau, Canchalagua Canyon,
North Mosquito Cove, and Eagle Canyon) are within or partially within
the IOA, and are likely to be further impacted by erosion (Table 1).
Three of these occurrences (Canchalagua Canyon, North Mosquito Cove,
and Eagle Canyon) are along the eastern escarpment, which has recently
been closed to biological monitoring due to
[[Page 29111]]
unexploded ordnance. The threat of erosion to this area will be
difficult to assess if the closure remains into the future. Nine of 29
occurrences (31 percent; Upper Middle Ranch Canyon, Warren Canyon,
Horton Canyon, Upper Wallrock Canyon, Tota Canyon, Lemon Tank Canyon,
Larkspur Canyon, Chamish Canyon, and Northern Island Terraces) are near
the IOA (within 1,000 ft (305 m)), and could experience erosion from
nearby training activities.
Roads can concentrate water flow causing incised channels and
erosion of slopes (Forman and Alexander 1998, pp. 216-217). This
increased erosion around roads can degrade habitat, especially along
the steep canyons associated with the eastern escarpment of the island.
Nine of 29 Acmispon dendroideus var. traskiae occurrences (31 percent;
Eel Cove Canyon, Seal Cove Terraces, Lemon Tank Canyon, Wilson's Cove,
North Wilson's Cove, Upper Middle Ranch Canyon, Eagle Canyon, North
Mosquito Cove, and Canchalagua Canyon) are within 500 ft (152 m) of a
road on the island (Forman and Alexander 1998, p. 217). These
occurrences could be subject to diffuse disturbance and road effects
that degrade habitat quality. The largest known occurrence of A. d.
var. traskiae, Wilson Cove, occurs on gradual or steep slopes where
erosion is evident (USFWS 2008, p. 117). Military activities in this
area have the potential to adversely affect the species habitat due to
the species' proximity to Navy facilities and the level of human
activity and traffic in the area.
The Navy incorporates erosion control measures into all site
feasibility studies and project planning, design, and construction to
minimize the potential to exacerbate existing erosion and avoid impacts
to listed species (Munson 2011a, pers. comm.). The INRMP requires that
all projects include erosion conservation work and associated funding
(Navy 2002, p. 4-89). These conservation actions include best
management practices for construction and engineering, choosing sites
that are capable of sustaining disturbance with minimum soil erosion,
and stabilizing disturbed sites with native plants (Navy 2002, pp. 4-
89--4-91). Additionally, large-scale island-wide maneuvers with assault
vehicles have been postponed until an erosion control plan is drafted
and implemented. The erosion control plan for San Clemente Island is
being developed to reduce the impacts of erosion to Acmispon
dendroideus var. traskiae habitat in areas likely to experience
increased and expanded military operations (Munson 2011a, pers. comm.).
This erosion control plan will address military operations associated
with the IOA, AVMA, and AFP; however, since the plan is not yet
finalized, it does not currently ameliorate the noted threats from
erosion.
The processes and results of erosion are threats to the habitat of
Acmispon dendroideus var. traskiae, particularly to 17 of 29
occurrences (59 percent; Middle Island Plateau, Canchalagua Canyon,
North Mosquito Cove, Eagle Canyon, Upper Middle Ranch Canyon, Warren
Canyon, Horton Canyon, Upper Wallrock Canyon, Tota Canyon, Lemon Tank
Canyon, Larkspur Canyon, Chamish Canyon, North Island Terraces, Eel
Cove Canyon, Seal Cove Terraces, Wilson Cove, and North Wilson Cove)
that are within an IOA, within 1,000 ft (305 m) of an IOA, or within
500 ft (152 m) of a road. Erosion may lead to overall habitat
degradation and the loss of individuals or groupings of plants in a
given area. However, this taxon has persisted despite current levels of
erosion. The processes and results of erosion are island-wide threats
to the habitat or range of A. d. var. traskiae, particularly to the 17
occurrences in or adjacent to military training areas or roads.
Therefore, erosion is still considered a threat to the existence of A.
d. var. traskiae.
Nonnative Species
One of the threats to Acmispon dendroideus var. traskiae identified
in the final listing rule is the spread of nonnative plants into its
habitat (42 FR 40682). Nonnative plants can diminish the abundance or
survival of native species by altering natural ecosystem processes such
as fire regimes, nutrient cycling, hydrology, and energy budgets, and
competing with them for water, space, light, and nutrients (Zink et al.
1995, p. 307; Brooks 1999, pp. 16-17; Mack et al. 2000, p. 689).
Nonnative species of particular concern include Avena barbata (slender
oat), Bromus spp., Foeniculum vulgare, and Brassica tournefortii, which
have already invaded the habitat of most A. d. var. traskiae
occurrences. Another nonnative species, Carpobrotus edulis (iceplant),
also appears to be hindering the recovery of A. d. var. traskiae (Allan
1999, p. 92). This nonnative species occupies large areas of Wilson
Cove where it may alter the habitat (Allan 1999, p. 92) by changing
vegetation structure and creating an environment less hospitable to A.
d. var. traskiae. Annual grasses vary in abundance with rainfall,
potentially changing the vegetative community from shrubs to grasses
and increasing the fuel load in wet years (see Factor A--Fire section
below).
Although previous invasions of nonnatives probably occurred through
introductions in grazing fodder, current nonnative species invasions
are typically introduced by military activities and training on the
island. Nonnative plants constitute a rangewide threat to the habitat
of all native plants on San Clemente Island, including all occurrences
of Acmispon dendroideus var. traskiae. Nine of 29 occurrences (31
percent; Eel Cove Canyon, Seal Cove Terraces, Lemon Tank Canyon,
Wilson's Cove, North Wilson's Cove, Upper Middle Ranch Canyon, Eagle
Canyon, North Mosquito Cove, and Canchalagua Canyon) are within 500 ft
(152 m) of roads on the island, and may be subject to diffuse
disturbance and road effects that degrade habitat quality along the
road (Forman and Alexander 1998, p. 217). Roadsides tend to provide
conditions (high disturbance, seed dispersal from vehicles, ample light
and water) preferable to nonnative species (Forman and Alexander 1998,
p. 210).
Potential impacts from nonnative plants are minimized through
annual implementation of the Navy's island-wide nonnative plant control
program (O'Connor 2009b, pers. comm.; Munson 2011a, pers. comm.). The
focus of the nonnative plant species program is to control plants on
the island with the potential to adversely impact habitat of federally
listed species (see above discussion on Nonnative Species under Factor
A--M. clementinus). Although nonnative plants will continue to pose a
risk to the habitat or range of Acmispon dendroideus var. traskiae, the
Navy has taken steps to curtail habitat and plant community alteration
from nonnative plants. To reduce the potential for transport of
nonnative plants to the island, military and nonmilitary personnel
inspect tactical ground vehicles and remove any visible plant material,
dirt, or mud prior to going on San Clemente Island (USFWS 2008, p. 63).
This precaution helps to control the movement of nonnative plants to
the island, but once on the island, nonnative plants easily spread
through the movement of vehicles from one area to another.
Acmispon dendroideus var. traskiae has persisted on the island and,
despite the continued risk of encroachment to habitat by nonnatives,
the range of this taxon has expanded from 6 to 29 occurrences since
listing. Impacts from nonnative plants may be a persistent, but low-
level, threat to A. d. var. traskiae habitat.
[[Page 29112]]
Fire
Fire was not considered a threat to habitat occupied by Acmispon
dendroideus var. traskiae at the time of listing (42 FR 40682; August
11, 1977). Since that time, however, over 50 percent of the island has
experienced at least one wildfire (Navy 2002, Map 3-3, p. 3-32), and
some habitat has burned multiple times with very short intervals
between fires (Navy 2002, Map 3-4, p. 3-33). The majority of fires are
concentrated in SHOBA, potentially impacting habitat of 8 of 29
occurrences (28 percent; Eagle Canyon, Bryce Canyon, North Mosquito
Cove, Canchalagua Canyon, Thirst Canyon, Cave Canyon, Horse Canyon, and
Pyramid Head) where military training exercises within Impact Areas I
and II employ live ordnance and incendiary devices. However, fires are
occasionally ignited by activities north of SHOBA, such as training
activities near Eel Point (possibly impacting Seal Cove Terraces and
Eel Cove Canyon occurrences) (Navy 2002, Map 3-4, p. 3-33).
Increased fire frequency resulting from intensified military uses
could lead to localized changes in vegetation on San Clemente Island.
The Navy recently approved a significant expansion in the number of
locations where live fire and demolition training will take place (Navy
2008a, pp. 2-3--2-38), including TAR north of SHOBA (TAR 17--Eel Cove
Canyon and Seal Cove Terraces, and TAR 14 and 15--Larkspur and Chamish
Canyon). These higher levels of training have not occurred in recent
history, and will likely expand from current levels. In addition to
demolitions, certain proposed munitions exercises involve the use of
incendiary devices, such as illumination rounds, white phosphorous, and
tracer rounds, which pose a high risk of fire ignition. Additionally,
smoke, flares, and pyrotechnics are proposed for use within TAR 11
(Wilson's Cove) towards the eastern shore, and expanded live fire and
demolition training is proposed within TAR 16 (Middle Island Plateau)
towards the center of the island. It is likely that the fire pattern on
the island will change in response to this increase in ignition
sources, with fires becoming more common within and adjoining the
training areas north of SHOBA.
At the time of listing, fire was not identified as a habitat threat
because of lack of fire history and the low intensity of military
training on the island. Since that time, military training has
significantly increased, and we have better records of the fire
frequency on the island. Approximately 14 of the 29 occurrences (48
percent) (Wilson's Cove, Middle Island Plateau, Eagle Canyon, Bryce
Canyon, North Mosquito Cove, Canchalagua Canyon, Thirst Canyon, Cave
Canyon, Horse Canyon, Pyramid Head, Eel Cove Canyon, Seal Cove
Terraces, Larkspur Canyon, and Chamish Canyon) of Acmispon dendroideus
var. traskiae fall within areas that may be subject to recurrent fire
associated with military training (Table 1). This includes locations
that fall within 1,000 ft (305 m) of TAR where the Navy conducts live
fire and demolition training, and occurrences within SHOBA (SHOBA
serves as a buffer for Impact Areas I and II). Fires that escape
designated training areas may threaten habitat on other parts of the
island, though, because of the broad distribution of the species, it is
unlikely that one fire could spread throughout the entire range. The
Navy's implementation of the MOFMP will limit the frequency with which
fires escape impact areas and TAR. Through the annual review process,
the Navy identifies mechanisms to reduce fire return intervals within
areas where this taxon is concentrated (USFWS 2008, pp. 91-122). The
Navy's implementation of an MOFMP will help to reduce the risk of
habitat conversion by fire, although the habitat of A. d. var. traskiae
could be altered by increased fire frequency and spread of nonnative
grass. Although the threat is ameliorated through the MOFMP, fire
remains an island-wide threat to A. d. var. traskiae, particularly to
the 14 occurrences that fall within areas that may be subject to
recurrent fire associated with military training.
Summary of Factor A
San Clemente Island was used for sheep ranching, cattle ranching,
goat grazing, and pig farming from 1850 until 1934 (Navy 2002, pp. 3-
4). The effects of these grazers, which were not completely removed
from the island until 1992, on the habitat and plants were one of the
original reasons for classifying Acmispon dendroideus var. traskiae as
endangered in the 1977 listing rule (42 FR 40682). Currently, the
habitat of A. d. var. traskiae is threatened by destruction and
modification caused by land use, erosion, nonnative plants, and fire.
To help ameliorate these threats, the Navy is implementing an MOFMP, an
INRMP, and an island-wide nonnative species control program (Navy 2002,
pp. 1-1-8-12; USFWS 2008, pp. 1-237). The MOFMP has been helpful in
informing strategic decisions for training using live fire or
incendiary devices. The Navy has postponed major troop and assault
vehicle maneuvers across the island until an erosion control plan is
completed. Natural resource managers have been successful in decreasing
the prevalence of particularly destructive nonnatives, such as
Foeniculum vulgare. Though increased impacts associated with military
training could threaten the species, 24 of 29 occurrences (83 percent)
of A. d. var. traskiae fall outside of training areas (IOA or TAR)
where the most intensive habitat disturbances are likely to occur.
While it is anticipated that military training activities, erosion,
nonnatives, and fire will have ongoing impacts to the taxon's habitat,
based on its distribution and current and anticipated conservation
efforts, impacts from these threats are reduced and minimized for A. d.
var. traskiae. Therefore, the threats to the habitat of A. d. var.
traskiae will not likely impact most of the known occurrences both now
and into the future.
Factor B. Overutilization for Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682; August 11, 1977), the Service did
not identify any threats from overutilization, and there is no new
information to indicate that overutilization is a threat to Acmispon
dendroideus var. traskiae. Although voucher herbarium specimens of A.
d. var. traskiae and seeds have been collected for research and seed
banking, overutilization of A. d. var. traskiae for any purpose is not
currently considered a threat nor is expected to be in the future.
Factor C. Disease or Predation
Grazing of feral goats and rooting of feral pigs were considered a
direct threat to Acmispon dendroideus var. traskiae in the final
listing rule (42 FR 40682; August 11, 1977). As stated above, however,
nonnative mammalian herbivores were removed from San Clemente Island in
1992, and this threat was ameliorated, as recognized in our 2007 status
review (USFWS 2007b, p. 13). Currently, no other predators or diseases
on San Clemente Island are known to pose a significant threat to A. d.
var. traskiae both now and in the future.
Factor D. Inadequacy of Existing Regulatory Mechanisms
The Act requires us to examine the adequacy of existing regulatory
mechanisms with respect to those existing and foreseeable threats that
may affect Acmispon dendroideus var. traskiae. The inadequacy of
existing regulatory mechanisms was not
[[Page 29113]]
considered a threat to A. d. var. traskiae at listing (42 FR 40682;
August 11, 1977). Since it was listed as endangered, the Act has been
and continues to be the primary Federal law that affords protection to
A. d. var. traskiae. The Service's responsibilities in administering
the Act include sections 7, 9, and 10 (see above discussion in the
Malacothamnus clementinus--Factor D section for more information on the
Service's responsibilities for all three species that are the subject
of this Finding). Critical habitat has not been designated or proposed
for this taxon. Listing A. d. var. traskiae provided a variety of
protections, including the prohibitions against removing or destroying
plants within areas under Federal jurisdiction and the conservation
mandates of section 7 for all Federal agencies. If A. d. var. traskiae
were not listed, these protections would not be provided. Thus, we must
evaluate whether other regulatory mechanisms would provide adequate
protections absent the protections of the Act.
Other Federal Protections
National Environmental Policy Act (NEPA)
All Federal agencies are required to adhere to the National
Environmental Policy Act (NEPA) of 1970 (42 U.S.C. 4321 et seq.) for
projects they fund, authorize, or carry out. The Council on
Environmental Quality's regulations for implementing NEPA (40 CFR parts
1500-1518) state that agencies shall include a discussion on the
environmental impacts of the various project alternatives (including
the proposed action), any adverse environmental effects that cannot be
avoided, and any irreversible or irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA itself is a disclosure law, and
does not require subsequent minimization or mitigation measures by the
Federal agency involved. Although Federal agencies may include
conservation measures for Acmispon dendroideus var. traskiae as a
result of the NEPA process, any such measures are typically voluntary
in nature and are not required by the statute. NEPA does not itself
regulate activities that might affect A. d. var. traskiae, but it does
require full evaluation and disclosure of information regarding the
effects of contemplated Federal actions on sensitive species and their
habitats. On San Clemente Island, the Navy must meet the NEPA
requirements for actions significantly affecting the quality of the
human environment. Typically, the Navy prepares Environmental
Assessments and Environmental Impact Statements on operation plans and
new or expanding training actions. Absent the listing of A. d. var.
traskiae, we would expect the Navy to continue to meet the procedural
requirements of NEPA for its actions, including evaluating the
environmental impacts to rare plant species and other natural
resources. However, as explained above, NEPA does not itself regulate
activities that might affect A. d. var. traskiae.
Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670) authorizes the Secretary of Defense
to develop cooperative plans with the Secretaries of Agriculture and
the Interior for natural resources on public lands. The Sikes Act
Improvement Act of 1997 requires Department of Defense installations to
prepare INRMPs that provide for the conservation and rehabilitation of
natural resources on military lands consistent with the use of military
installations to ensure the readiness of the Armed Forces. An INRMP is
a plan intended ``* * * to guide installation commanders in managing
their natural resources in a manner that is consistent with the
sustainability of those resources while ensuring continued support of
the military mission'' (Navy 2002, p. 1-1). INRMPs are developed in
coordination with the State and the Service, and are generally updated
every 5 years. Although an INRMP is technically not a regulatory
mechanism because its implementation is subject to funding
availability, it is an important guiding document that helps to
integrate natural resource protection with military readiness and
training.
San Clemente Island Integrated Natural Resources Management Plan
(INRMP)
Pursuant to the Sikes Act, the Navy adopted an INRMP for San
Clemente Island that identifies multiple objectives for protecting
Acmispon dendroideus var. traskiae and its habitat to help to reduce
threats to this taxon (Navy 2002). The INRMP discloses actions through
the NEPA process and to comply with such legislation and regulations as
the Endangered Species Act, Federal Noxious Weed Act of Act of 1974 (7
U.S.C. 2801), the Comprehensive Environmental Response, Compensation,
and Liability Act (42 U.S.C. 9601), the Resources Conservation and
Recovery Act (42 U.S.C. 6901), and Soil Conservation Act (16 U.S.C. 3B)
(see above discussion on INRMPs under Malacothamnus clementinus--Factor
D). Natural resource objectives of relevance to the protection of A. d.
var. traskiae in the INRMP include: ``Protect, monitor, and restore
plants and cryptograms in order to manage for their long-term
sustainability on the island'' (Navy 2002, p. 4-39). The INRMP
specifically includes the following objectives for A. d. var. traskiae
management: removal of nonnatives, restoration of native grasses and
scrub species, monitoring of the species, studies of response to fire,
and studies and inventory of insect pollinators (Navy 2002, p. D-11).
To date, multiple INRMP management strategies have been implemented for
the conservation of A. d. var. traskiae. Other INRMP strategies that
target the plant communities within which this species occurs include:
Controlling erosion, with priority given to locations where erosion may
be affecting listed species; producing a new vegetation map; reducing
nonnative plant cover from 1992-1993 baseline levels; managing the size
and intervals of fires; experimenting with fire management to improve
native plant dominance while protecting sensitive plant occurrences;
and conducting genetic and biological studies of A. d. var. traskiae.
The MOFMP, Erosion Control Plan, and nonnative plant species
control conducted on the island are discussed above under Acmispon
dendroideus var. traskiae--Factor A. The Present or Threatened
Destruction, Modification, or Curtailment of Its Habitat or Range.
Absent listing under the Act, the Navy would still be required to
develop and implement INRMPs under the Sikes Act. However, as noted
under the other factors, while the INRMP helps to ameliorate threats
and provides some protection for A. d. var. traskiae occurrences, those
occurrences within Impact Areas or operationally closed areas may not
benefit from the conservation measures. While the INRMP has reduced the
severity of threats and contributed to conservation of the species, it
still allows for land use consistent with military readiness and
training. Thus, Navy activities will continue to impact A. d. var.
traskiae as described under Factor A.
State Protections
Since the time of listing, Acmispon dendroideus var. traskiae has
benefited from additional State protections under the Native Plant
Protection Act (NPPA) and California Endangered Species Act (CESA;
listed 1982). However, the range of A. d. var. traskiae is restricted
to a Federal military installation, so listing under NPPA and CESA may
only afford protection to this species in rare instances when the lead
agency is a
[[Page 29114]]
non-Federal agency or when proposed activities fall under other State
laws.
Summary of Factor D
The regulatory mechanisms outlined above provide for adequate
conservation of Acmispon dendroideus var. traskiae. In continuance of a
long history of cooperative conservation efforts, the Navy also
implements several conservation actions that benefit this plant taxon.
The Navy has implemented a MOFMP to reduce the risk of fire on the
island and a nonnative plant species control program. In response to
the conservation actions proposed and the current status of the listed
taxon, we issued a non-jeopardy biological opinion on the Navy's MOFMP.
The provisions included in the San Clemente Island INRMP provide
protection of A. d. var. traskiae occurrences and adaptive management
of its habitat in order to help address threats to the plant from
military activities and nonnative plants, although implementation may
not be extended to occurrences in operationally closed areas. A. d.
var. traskiae occurrences are afforded protection through Federal and
military mechanisms, and thus the inadequacy of existing regulatory
mechanisms is not considered a current threat to the species. However,
in the absence of the Act, the existing regulatory mechanisms are not
adequate to conserve A. d. var. traskiae throughout its range both now
and in the future.
Factor E. Other Natural or Manmade Factors Affecting Its Continued
Existence
The 1977 listing rule identified nonnatives as a threat to Acmispon
dendroideus var. traskiae under Factor E (42 FR at 40684; August 11,
1977). In this 5-factor analysis, impacts from nonnative plants are
discussed above under Factor A as a threat to habitat. Other threats
attributable to Factor E that have been identified since listing
include: (1) Movement of vehicles and troops, (2) fire, (3) climate
change, and (4) hybridization. Factor E addresses threats to
individuals of the species, rather than the habitat modification
threats that are discussed in Factor A. Therefore, while some threats
are discussed in both sections, in this section we are focusing on the
direct impacts to individuals of A. d. var. traskiae.
Movement of Vehicles and Troops
Military training activities within SWAT, TAR, and the IOA often
entail the movement of vehicles and troops over the landscape, which
has the potential of trampling or crushing individual plants (for
discussion of SWAT, TAR, and IOA, see above under Malacothamnus
clementinus--Factor E). Based on the distribution of Acmispon
dendroideus var. traskiae occurrences, and type of troop movements
likely to occur, impacts due to trampling and crushing are considered a
low-level threat to its long-term persistence, and are most likely to
occur occasionally within the IOA and TAR. Approximately 13 of 29
occurrences (45 percent; Wilson Cove, Canchalagua Canyon, Middle Island
Plateau, North Mosquito Cove, Eagle Canyon, Larkspur Canyon, Chamish
Canyon, Lemon Tank Canyon, Seal Cove Terraces, Eel Cove Canyon, Middle
Wallrock Canyon, Warren Canyon, and North Island Terraces) of A. d.
var. traskiae are partially or wholly within the boundaries of a
training area (IOA, TAR, or SWAT). Many of these occurrences are in
areas that are not readily accessible to vehicles and troops. Loss of
individual plants from proposed increases in troop and vehicle
movements within SWAT, TAR, and the IOA is likely to increase, though
this will not significantly impact the survival and recovery of this
taxon because of the diffuse nature of this threat and the location of
much of the species along the eastern escarpment, away from military
training activities (USFWS 2008, pp. 113-122).
Fire
Although not specifically mentioned in the listing rule, intense or
frequent fires threaten individuals at 14 of 29 (48 percent) of
Acmispon dendroideus var. traskiae occurrences. In the Factor A
discussion above, we addressed impacts of fire on the habitat. This
section covers the discrete threat to individuals or occurrences of A.
d. var. traskiae. As discussed in the Background section, it is unknown
if A. d. var. traskiae is adapted to periodic fires, though it is
likely that this taxon is resilient to occasional fires (Navy 2002, p.
D-10; Tierra Data Inc. 2005, p. 80). Adult plants have been lost in
fires, but subsequent recruitment from the seed bank resulted in
replacement numbers of juvenile plants (Tierra Data Inc. 2005, p. 80).
Aside from this observation, the relationship between fire and the life
history of A. d. var. traskiae has not been adequately studied.
Additionally, the species' tolerance to fire frequency is unknown. In
areas that burn more frequently, the seed bank may become depleted if
individuals burn before they produce seeds. Although an individual
plant has the ability to produce vast amounts of seed, the seed bank
must be replenished regularly for the species to persist (Junak and
Wilken 1998, p. 257).
Acmispon dendroideus var. traskiae occurs in some areas of the
island that may experience elevated fire frequency, such as in SHOBA
and surrounding Eel Point (Eagle Canyon, Bryce Canyon, North Mosquito
Cove, Canchalagua Canyon, Thirst Canyon, Cave Canyon, Horse Canyon,
Pyramid Head, Seal Cove Terraces, and Eel Cove Canyon) (discussed in A.
d. var. traskiae--Factor A). Increased fire frequency from intensified
military use could also lead to localized changes in vegetation,
resulting in indirect adverse effects on A. d. var. traskiae. The
potential for frequent fire at many of the occurrences within SHOBA is
reduced by their location on the eastern escarpment of the island, away
from Impact Areas I and II. This threat may become difficult to assess
with the recent closure of the eastern escarpment area due to
unexploded ordnance. The Navy's fire management practices are
anticipated to minimize frequency of ignitions as well as the spread of
fires (as described above in Factor A).
The Navy conducts annual reviews of fire management and fire
occurrence that allow for adaptive management. These measures should
minimize loss of individuals or occurrences of A. d. var. traskiae due
to fire. At the present time, fire management does not pose a threat as
fuelbreak locations have not been proposed in the vicinity of this
taxon. Although the Navy has planned and implemented fire management,
fire threatens 14 occurrences of Acmispon dendroideus var. traskiae.
Due to the continued impacts of fire within SHOBA, fire remains a
Factor E threat to the existence of A. d. var. traskiae.
Climate Change
For general information regarding climate change impacts, see the
climate change discussion under Malacothamnus clementinus--Factor E
above. Since listing of Acmispon dendroideus var. traskiae, the
potential impact of ongoing, accelerated climate change has become a
recognized threat to the flora and fauna of the United States (IPCC
2007a, pp. 1-52; PRBO 2011, pp. 1-68). San Clemente is located in a
Mediterranean climatic regime, but with a significant maritime
influence. Climate change models indicate an increase in average
temperature for southern California (see above discussion on climate
change under Malacothamnus clementinus--Factor E). San Clemente Island
typically receives less rainfall than neighboring mainland areas
(Tierra Data Inc. 2005, p. 4). Therefore, the models may
[[Page 29115]]
understate the effects to vegetation on the island. Less rainfall and
warmer air temperatures could limit the range of A. d. var. traskiae,
although there is no direct research on the effects of climate change
on the species. Additionally, changes in sea level and temperature may
be more acute on small islands, due to their high vulnerability
(surrounded by ocean) and low adaptive capacity (from limited size)
(IPCC 2007b, p. 1). The impacts of future climate change to A. d. var.
traskiae remain unclear. The most recent literature on climate change
predicts hydrological changes, higher temperatures, and expansion of
drought areas (IPCC 2007a, pp. 1-18). While we recognize that climate
change is an important issue with potential effects to listed species
and their habitats, the best available information does not facilitate
accurate predictions regarding the effects to A. d. var. traskiae at
this time.
Hybridization
As discussed above in the Background section, Acmispon dendroideus
var. traskiae is known to hybridize with Acmispon argophyllus var.
argenteus. In 1990, Liston et al. (p. 240) confirmed hybridization
between co-occurring populations of A. d. var. traskiae and A.
argophyllus var. argenteus in Wilson Cove. At that time, they detected
only four hybrid individuals out of 38 individuals tested, and failed
to detect hybridization in another area of co-occurrence at the
southern end of the island. Although hybrid individuals seem to be
restricted to Wilson Cove (Liston 1990, p. 240; Allan 1999, p. 91),
other unconfirmed hybrids (no genetic testing done) have been observed
elsewhere on the island (Howe 2009b, pers. comm.; Braswell 2011, pers.
obs.).
Liston et al. (1990, pp. 240-243) offered three hypotheses for the
scarcity of confirmed hybrid individuals. First, hybrids may have
reduced fitness and be selected against, or be sterile and thus unable
to produce viable seed even if backcrossed to the parent taxa. In this
situation, hybridization would not be a threat to the genetic integrity
of A. dendroideus var. traskiae. Second and conversely, if the fertile
hybrids are recent in origin (within the last 20 years), and because
both parental taxon are long-lived, woody perennials, few hybrid
individuals would be expected due to the slower development and
lifespan of the species. If this is correct, the genetic integrity of
the largest-known occurrence of A. d. var. traskiae in Wilson Cove
might be at risk of introgressive hybridization (introduction of genes
from one species to another resulting in fertile hybrids).
Introgressive hybridization could lead to the loss of genetic variation
and lower fitness of A. d. var. traskiae. Finally, the limited number
of hybrid plants (four) might be an artifact of the genetic testing
method used by the study.
Liston et al. (1990, p. 243) suggested that there be further
investigation of these hypotheses before management recommendations are
made to the Navy. Allan (1999, p. 91) stated that A. d. var. traskiae
should be ``closely monitored.'' Although the species has expanded its
range and numbers, hybridization with A. a. var. argenteus remains a
concern at the largest of the 29 occurrences (Wilson's Cove), although
unconfirmed hybrids have been observed in other areas of the island
(e.g., Norton Canyon). Hybridization may threaten, and could diminish,
the genetic diversity of the species, especially in the already
disturbed occurrence of Wilson Cove (Allan 1999, pp. 91-92). Additional
study is needed to determine the extent and magnitude of this threat to
A. d. var. traskiae.
Summary of Factor E
Threats associated with military activities, fire, climate change,
and hybridization continue to impact Acmispon dendroideus var. traskiae
at 18 of 29 occurrences (62 percent; Wilson Cove, Canchalagua Canyon,
Middle Island Plateau, North Mosquito Cove, Eagle Canyon, Larkspur
Canyon, Chamish Canyon, Lemon Tank Canyon, Seal Cove Terraces, Eel Cove
Canyon, Middle Wallrock Canyon, Warren Canyon, North Island Terraces,
Bryce Canyon, Thirst Canyon, Cave Canyon, Horse Canyon, and Pyramid
Head) on San Clemente Island. Trampling and crushing of individual
plants are probably incidental, but are likely to increase with
increases in training levels on the island. However, the Navy is
implementing conservation measures that will improve conditions for A.
d. var. traskiae, which has expanded its distribution on the island.
Military training activities have the potential to ignite fires that
can spread to habitat supporting this species, though the majority of
the occurrences are outside of the areas designated for live fire and
demolition. In preparation for these training efforts, the Navy
implemented a fire management plan within the MOFMP that will limit the
frequency of fires escaping the Impact Areas.
Climate change may also likely impact Acmispon dendroideus var.
traskiae, though the magnitude of this threat is largely unknown. The
genetic integrity of A. d. var. traskiae may be threatened by
hybridization with A. adsurgens var. argenteus at one of the largest
occurrences and requires further investigation. However, the extent and
prevalence of this threat is unknown, and only confirmed in one of 29
occurrences. Overall, the threats described under Factor E are either
of low magnitude, low likelihood, or adequately managed, while the
potential overall threat of climate change remains unknown across this
taxon's range. Although these threats could directly impact individuals
of this taxon, we are of the view that they will not impede the
recovery of A. d. var. traskiae now or in the future.
Combination of Factors--Acmispon dendroideus var. traskiae
A species may be affected by more than one threat in combination.
Within the preceding review of the five listing factors, we have
identified multiple threats that may have interrelated impacts on the
species (see also above discussion on combination of factors--
Malacothamnus clementinus). The species' productivity may be reduced
because of these threats, either singularly or in combination. However,
it is not necessarily easy to determine (nor is it necessarily
determinable) whether a particular threat is the primary threat having
the greatest effect on the viability of the species, or whether it is
exacerbated by or working in combination with other potential threats
to have cumulative or synergistic effects on the species. While the
combination of factors is a threat to the existence of Acmispon
dendroideus var. traskiae, we are unable to determine the magnitude or
extent of cumulative or synergistic effects of the combination of
factors on the viability of the species at this time.
Castilleja grisea (San Clemente Island Paintbrush)
In the 2007 status review, we stated that the predominant threat at
listing (nonnative herbivores) was removed from San Clemente Island in
1992 (USFWS 2007c, pp. 1-19). Additional threats to Castilleja grisea
identified in 2007 include: (1) Erosion, (2) nonnative species, (3)
fire, (4) land use, and (5) access to SHOBA. The first four of these
threats are discussed below under Factor A. As discussed previously,
access to SHOBA is not considered a threat, though it limits our
ability to assess all occurrences of the taxon reviewed here.
Factor A. The Present or Threatened Destruction, Modification, or
Curtailment of Their Habitat or Range
Under this listing factor in the final listing rule, we identified
habitat modification by browsing feral goats
[[Page 29116]]
and rooting feral pigs as threats to Castilleja grisea and other island
taxa (42 FR 40682). As discussed above, the Navy removed the last of
the remaining feral goats and pigs from San Clemente Island in 1992
(Kellogg and Kellogg 1994, p. 5), which resulted in improved habitat
conditions, and led to changes in the cover of native and nonnative
plants on the island (Tierra Data Inc. 2005, pp. i-96; Kellogg 2006,
pers. comm.). The Recovery Plan identified habitat alteration and
disturbance from the Navy's use of the island for military operational
and training needs as additional threats to the habitats occupied by C.
grisea (USFWS 1984, pp. 58-63). Additional threats identified since
listing include alteration of San Clemente Island habitats by military
training activities, fire, and fire management. As outlined below, we
discuss the impacts of the following threats that affect the habitat or
range of C. grisea: (1) Land use, (2) erosion, (3) nonnative plants,
(4) fire, and (5) fire management.
Land Use
The distribution of Castilleja grisea includes a single occurrence
in the north of the island at West Cove, with the remaining 28
occurrences distributed across the southern 15.5 mi (25 km) of the
island, particularly along the eastern escarpment. Training activities
approved in the MOFMP would include substantial increases in vehicle
and foot traffic in the IOA, leading to habitat modification. Ten of
the 29 occurrences (34 percent; plain northeast of Warren Canyon,
Larkspur Canyon, Lemon Tank Canyon, Eagle Canyon, Bryce Canyon, Horse
Beach Canyon, China Canyon, Knob Canyon, Canchalagua Canyon, and
Pyramid Head) are within or partially within the IOA and experience
direct habitat impacts, while three of 29 occurrences (10 percent;
Thirst Canyon, SHOBA Boundary Occurrence, and Upper Horse Canyon) are
near the IOA (within 1,000 ft (305 m)) and could experience diffuse or
accidental impacts to C. grisea habitat. Recent area closures due to
unexploded ordnance could make habitat impacts from training difficult
to assess for several occurrences (34 percent; Nanny Canyon, Lemon Tank
Canyon, Eel Point, Eagle Canyon, Bryce Canyon, Horse Beach Canyon,
China Canyon, Knob Canyon, Canchalagua Canyon, and Pyramid Head) in the
future. Additionally, one occurrence (West Cove) is within an Assault
Vehicle Maneuver Area (AVMA) and could be subject to habitat
disturbance from vehicles.
The southern portion of Castilleja grisea's distribution extends
through SHOBA where impacts to the habitat are likely. Certain
munitions exercises involve the use of incendiary devices, such as
illumination rounds, white phosphorous, and tracer rounds, which pose a
high risk of fire ignition (USFWS 2008, p. 11-13). Because of the
elevated risk of fire associated with training activities, live and
inert munitions fire are targeted towards Impact Areas I and II within
SHOBA where bombardments and land demolition are concentrated. Four of
29 occurrences (14 percent; China Canyon, Red Canyon, Upper Chenetti
Canyon and Horse Beach Canyon) are within or partially within Impact
Areas. Currently, the Impact Areas are closed to nonmilitary personnel,
so the plant's status at these four occurrences is unknown, as well as
the status of any conservation action that would otherwise be expected
to be implemented in these areas (USFWS 2008, p. 50).
Also within SHOBA, an occurrence of C. grisea is located in lower
Horse Beach Canyon, above Horse Beach. Horse Beach (TAR 21) is used for
special warfare training activities that include the use of live fire,
illumination rounds, and tracers. Training activities within parts of
SHOBA pose a direct threat to habitat due to associated ground
disturbance and land demolition. Sixteen of 29 C. grisea occurrences
(55 percent) are located outside of heavily impacted training areas,
and 13 occurrences (45 percent; West Cove, Plain northeast of Warren
Canyon, Larkspur Canyon, Lemon Tank Canyon, Eagle Canyon, Bryce Canyon,
China Canyon, Knob Canyon, Canchalagua Canyon, Pyramid Head, Red
Canyon, Upper Chenetti Canyon and Horse Beach Canyon) are at least
partially within the boundaries of a training area (IOA, TAR, AVMA, or
Impact Area). Although, within training areas, many of the impacts to
these 13 occurrences would be diffuse and are unlikely to have a high
impact on the species. The Navy has demonstrated their efforts to help
conserve and manage listed species on the island through amelioration
of habitat impacts by military activities through implementation of the
MOFMP and INRMP. Land use appears to pose a high-magnitude threat to
the habitat of a small number of occurrences of C. grisea on San
Clemente Island.
Erosion
Erosion and associated soil loss caused by browsing of feral goats
and rooting of feral pigs likely modified the island's habitat (Navy
2002, p. 1-14). Defoliation from overgrazing on San Clemente Island
resulted in increased erosion over much of the island, especially on
steep slopes where denuded soils can be quickly washed away during
storm events (Johnson 1980, p. 107; Navy 2002, pp. 1-14, 3-9; Tierra
Data Inc. 2007, pp. 6-7). There may be residual impacts from historical
grazing, and vegetation may be slow to recover and hold soil. In the
INRMP, erosion was identified as a threat to the canyon woodland
habitat and maritime desert scrub, which is habitat for Castilleja
grisea (Navy 2002, pp. 4-3, 4-12). The process of soil erosion can lead
to destruction of terraces, steep slopes, and canyons that support the
growth and reproduction of C. grisea. Castilleja grisea plants occur
within steep canyon areas where such concentration of water flows may
be a threat (Navy 2002, p. D-23).
Increased military activities where Castilleja grisea occurs within
training area boundaries are expected to increase erosion associated
with roadways, through soil compaction and other soil disturbances. The
impacts from erosion are anticipated along the ridgeline of the eastern
escarpment, affecting eight occurrences (Pyramid Head, Knob Canyon,
Canchalagua Canyon, Bryce Canyon, Eagle Canyon, Thirst Canyon, SHOBA
Boundary occurrence, and Horton Canyon) (Tierra Data Inc 2007, pp.12-
18; Navy 2008a, p. G-8). Closure of the eastern escarpment within SHOBA
due to unexploded ordnance could make assessing this threat and
implementing conservation measures in these eight occurrences difficult
in the future.
The Navy studied the potential for erosion from several proposed
military activities (Tierra Data Inc. 2007, pp. 1-45, Appendices).
Approximately 13 of 29 Castilleja grisea occurrences (45 percent; West
Cove, Plain northeast of Warren Canyon, Larkspur Canyon, Lemon Tank
Canyon, Eagle Canyon, Bryce Canyon, China Canyon, Knob Canyon,
Canchalagua Canyon, Pyramid Head, Red Canyon, Upper Chenetti Canyon,
and Horse Beach Canyon) fall partially or wholly within the boundaries
of a designated training area (IOA, TAR, AVMA, or Impact Area), and are
likely to be impacted by erosion. Fifteen occurrences of C. grisea are
at least partially within 500 ft (152 m) of a road (paved or unpaved)
(China Canyon, Horse Beach Canyon, Pyramid Head, Knob Canyon,
Canchalagua Canyon, Bryce Canyon, Eagle Canyon, Upper Horse Canyon,
Plain northeast of Warren Canyon, Horton Canyon, Seal Cove Terraces,
Lemon Tank Canyon, Larkspur Canyon, Terrace Canyon, and West Cove)
(Forman and Alexander
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1998, p. 217). These occurrences could be subject to diffuse
disturbance and road effects that degrade the habitat quality. Roads
can concentrate water flow, causing incised channels and erosion of
slopes (Forman and Alexander 1998, pp. 216-217). This increased erosion
near roads can degrade habitat, especially along the steep canyons and
ridges.
Along the eastern escarpment, Castilleja grisea is found in steep
canyons in proximity to roads where it may be vulnerable to runoff
during storm events (Navy 2008a, pp. G-4, G-8). At the southern end of
the species' range, one occurrence is downslope from Horse Beach Canyon
Road along a poorly maintained dirt road that is proposed to serve as
part of the Assault Vehicle Maneuver Corridor. This location is likely
to have an elevated risk from erosion (USFWS 2008, p. 99).
The Navy incorporates erosion control measures into all site
feasibility studies and project design to minimize the potential to
exacerbate existing erosion and avoid impacts to listed species (Munson
2011a, pers. comm.). The INRMP requires that all projects include
erosion conservation work (Navy 2002, p. 4-89). These conservation
actions include best management practices, choosing sites that are
capable of sustaining disturbance with minimum soil erosion, and
stabilizing disturbed sites (Navy 2002, pp. 4-89-4-91). An erosion
control plan for San Clemente Island is in the development stage, with
expectations to reduce impacts of erosion where Castilleja grisea
occurs in areas with increased and expanded military operations (Munson
2011a, pers. comm.). This erosion control plan will address military
operations associated with the IOA, AVMA and AFP; however, since the
plan is not yet finalized, it does not currently ameliorate the noted
threats from erosion.
In areas that will not be covered under the erosion control plan,
erosion control measures are already being incorporated into project
designs to minimize the potential to exacerbate existing erosion and
avoid impacts to listed species (Munson 2011a, pers. comm.).
Additionally, large-scale island-wide maneuvers with assault vehicles
have been postponed until the erosion control plan is enacted. The
processes and results of erosion are island-wide threats to C. grisea,
particularly to the occurrences in or adjacent to military training
areas or roads. Seventeen of 29 occurrences (55 percent; West Cove,
Plain northeast of Warren Canyon, Larkspur Canyon, Lemon Tank Canyon,
Eagle Canyon, Bryce Canyon, China Canyon, Knob Canyon, Canchalagua
Canyon, Pyramid Head, Red Canyon, Upper Chenetti Canyon, Horse Beach
Canyon, Upper Horse Canyon, Horton Canyon, Seal Cove Terraces, and
Terrace Canyon) of C. grisea are in areas that could be subject to, and
threatened by, erosion from training activities or road use.
Occurrences in operationally closed areas may not be afforded the
conservation measures outlined by the Navy.
Erosion can lead to overall habitat degradation and loss of
individuals or groupings of plants. However, despite existing levels of
erosion on the island, the distribution of Castilleja grisea has
increased since listing. The Navy incorporates erosion control measures
into all projects to minimize the potential to exacerbate existing
erosion and avoid impacts to habitat and listed species. Although the
Navy tries to ameliorate erosion, management efforts are not possible
in areas that are closed to natural resource personnel. The processes
and results of erosion are island-wide threats to C. grisea,
particularly to the 17 occurrences in or adjacent to military training
areas or roads. Therefore, erosion is still considered a threat to the
existence of C. grisea.
Nonnative Plants
One of the threats to Castilleja grisea identified in the final
listing rule was the spread of nonnative plants into its habitat (42 FR
40682, 40684). Nonnatives can alter habitat structure, ecological
processes such as fire regimes, nutrient cycling, hydrology, and energy
budgets, and compete for water, space, light, and nutrients (for
discussion of nonnatives on San Clemente Island, see above discussion
on Nonnative Species under Malacothamnus clementine--Factor A).
Castilleja grisea is often associated with native maritime desert scrub
vegetation types, where nonnative grasses are present but not a
dominant component of the plant community (Tierra Data Inc. 2005, pp.
29-42).
Although previous invasions of nonnative species were probably
introduced in grazing fodder, current invasions are typically
introduced and spread around the island by military activities and
training (see above discussion on Nonnative Species under Malacothamnus
clementinus--Factor A). Nonnative plants constitute a rangewide threat
to all native plants on San Clemente Island, including all occurrences
of Castilleja grisea. A total of 9 of 29 occurrences (31 percent; China
Canyon, Horse Beach Canyon, Pyramid Head, Knob Canyon, Canchalagua
Canyon, Bryce Canyon, Eagle Canyon, Plain northeast of Warren Canyon,
and Lemon Tank Canyon) are within 500 ft (152 m) of Ridge Road or China
Point Road, and may be subject to diffuse disturbance and road effects
that degrade the habitat quality along the road (Forman and Alexander
1998, p. 217). Roadsides tend to create conditions (high disturbance,
seed dispersal from vehicles, ample light and water) preferred by
nonnative species (Forman and Alexander 1998, p. 210). Nonnatives,
including Foeniculum vulgare and Mesembryanthemum crystallinum
(crystalline iceplant), have been found in the disturbed shoulders
along the road between Ridge Road and China Point in SHOBA (Braswell
2011, pers. obs.).
Potential impacts from nonnative plants are expected to be
minimized by annual implementation of the Navy's island-wide nonnative
plant control program (O'Connor 2009b, pers. comm.; Munson 2011a, pers.
comm.; see above discussion on Nonnative Species under Malacothamnus
clementine--Factor A). This program targets nonnative species for
elimination using herbicide and mechanical removal, prioritizing
species that are new to the island or are particularly destructive. The
program has been successful at isolating and limiting some species,
such as Foeniculum vulgare, to a few locations (Howe 2011b, pers.
comm.). To reduce the potential for transport of nonnative plants to
San Clemente Island, military and nonmilitary personnel inspect
tactical ground vehicles, and remove any visible plant material, dirt,
or mud prior to going onto the island (USFWS 2008, p. 63). This
precaution helps to control the movement of nonnative plants onto the
island, but once on the island nonnatives are easily spread by the
movement of vehicles from one area to another. Although nonnative
plants will continue to pose a rangewide risk to C. grisea, it is a
threat of low intensity, and the Navy has taken steps to curtail
habitat conversion from nonnative plants.
Nonnative plant species are an island-wide threat to the native
vegetative community. The Navy has taken preventative and conservation
measures through funding and implementing nonnative plant species
control on the island. Management and control of nonnative plants is
not in place at the four occurrences (14 percent; China Canyon, Red
Canyon, Upper Chenetti Canyon, and Horse Beach Canyon) that are closed
to natural resource managers. However, outside of these areas,
Castilleja grisea has persisted on the
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island. Despite the continued risk of encroachment by nonnatives,
Castilleja grisea remains on the island, and its range has continued to
expand. Impacts from nonnative plants are a persistent, but low-level,
threat to C. grisea habitat.
Fire
Fire was not considered a threat to Castilleja grisea habitat at
the time of listing (42 FR 40682; August 11, 1977). Since that time,
however, over 50 percent of the island has experienced at least one
wildfire (Navy 2002, Map 3-3, p. 3-32). The majority of fires are
concentrated in SHOBA, potentially impacting 15 of 29 occurrences (52
percent; Thirst Canyon, Eagle Canyon, Bryce Canyon, Canchalagua Canyon,
Knob Canyon, Pyramid Head, Snake Canyon, Upper Chenetti Canyon, Horse
Beach Canyon, China Canyon, Red Canyon, Kinkipar Canyon, Cave Canyon,
Horse Canyon, and Upper Horse Canyon). Seven occurrences occur within
the eastern escarpment in SHOBA (Thirst Canyon, Eagle Canyon, Bryce
Canyon, Canchalagua Canyon, Knob Canyon, Pyramid Head, and Snake
Canyon), where impacts from fire are less likely. Recent closure of
this area limits the ability to assess the status and manage habitat at
these occurrences.
Because of the elevated risk of fire associated with training
activities, live and inert munitions fire is targeted towards two
delineated Impact Areas. The risk of frequent fire is higher in Impact
Areas I and II, potentially affecting the habitat at four of 29
occurrences (14 percent; Upper Chenetti Canyon, Horse Beach Canyon,
China Canyon, and Red Canyon). The effects of fire, and the state of
plants within the Impact Areas, are currently unknown due to closure of
the area (USFWS 2008, p. 50). Fires are occasionally ignited by
activities north of SHOBA, posing a low-magnitude threat to the habitat
at 14 of the 29 occurrences (48 percent; SHOBA Boundary, Horton Canyon,
Lemon Tank Canyon, Nanny Canyon, Larkspur Canyon, Box Canyon, Upper
Norton Canyon, Middle Ranch Canyon, Waymuck Canyon, Plain northeast of
Warren Canyon, Seal Cove Terraces, Eel Cove Canyon, Terrace Canyon, and
West Cove) (Navy 2002, Map 3-4, p. 3-33).
Increased fire frequency from intensified military use could lead
to localized changes in vegetation (see above discussion on fire
frequency under Malacothamnus clementinus--Factor A). The Navy has
significantly expanded the number of locations where live fire and
demolition training will take place (USFWS 2008, pp. 21-37), including
TAR north of SHOBA (TAR 17--Eel Cove Canyon and Seal Cove Terraces, and
TAR 14 and 15--Larkspur Canyon). In addition to demolitions, certain
proposed munitions exercises involve the use of incendiary devices,
such as illumination rounds, white phosphorous, and tracer rounds,
which pose a high risk of fire ignition. Expanded live fire and
demolition training is also approved within TAR 16 (Lemon Tank Canyon)
toward the center of the island. It is likely that the fire pattern on
the island will change due to this increase in ignition sources, with
fires becoming more common within and adjoining the training areas
north of SHOBA.
At the time of listing, fire was not identified as a threat because
of lack of fire history and the low intensity of military training on
the island. Since that time, military training has significantly
increased, and we have better records of the fire frequency on the
island. Approximately 19 of 29 occurrences (65 percent) of Castilleja
grisea fall within areas that may be subject to recurrent fires
associated with military training. This includes locations that fall
within SHOBA that serve as a buffer for Impact Areas I and II, and
occurrences near live fire and demolition training areas. As described
in the Background section, occurrences of C. grisea have been
discovered within and outside of the impact areas in SHOBA (Junak and
Wilken 1998, p. 298; Navy 2002, p. D-20), indicating that the species
is tolerant of at least occasional fire. High fire frequency may be a
potential threat that could limit the distribution of C. grisea by
overwhelming its tolerance threshold (Brooks et al. 2004, p. 683;
Jacobson et al. 2004, p. 1). Frequent fire may exceed a plant taxon's
capacity to persist by depleting seed banks and reducing reproductive
output when fire occurs at higher than natural frequencies in C. grisea
habitat (Zedler et al. 1983, pp. 811-815).
Within the Impact Areas or operationally closed zones, fire
suppression and firefighting are not being implemented because of
safety hazards from the presence of unexploded ordnance. Fires that
escape designated training areas threaten other parts of the island,
though it is unlikely that one fire is capable of spreading throughout
the entire range of the species due to its broad distribution across
the island. The Navy's implementation of the MOFMP will limit the
frequency with which fires escape Impact Areas and TAR. Through the
annual review process, the Navy will identify mechanisms to reduce fire
return intervals within areas and habitats where this taxon is
concentrated (USFWS 2008, pp. 91-122). Although the threat is
ameliorated through the MOFMP, fire remains an island-wide threat to C.
grisea, particularly to the habitat at the 19 occurrences that fall
within areas that may be subject to recurrent fire associated with
military training.
Fire Management
A fire management plan within the MOFMP was developed by the Navy
to provide flexibility for the timing of military training and to
ensure that adequate fire suppression resources were present with an
increased level of training activities (see above discussion on Fire
Management under Malacothamnus clementinus--Factor A). The Navy
constructed fuelbreaks around the Impact Areas for safety purposes and
to manage the spread of fire from the Impact Areas. Maintenance of
these fuelbreaks reduces the likelihood and frequency of fires
spreading to sensitive areas and habitats, such as those occupied by
Castilleja grisea. Fuelbreaks on San Clemente Island are created using
herbicides and strip burning, and maintained using herbicides and fire
retardant (Phos-Chek D75F) (USFWS 2008, pp. 97-98) (see above
discussion on Fire Management (including fire retardant use) under
Malacothamnus clementinus--Factor A).
Four occurrences (Red Canyon, China Canyon, Horse Beach Canyon, and
Upper Chenetti Canyon) of C. grisea have been documented within the
Impact Areas, and are likely exposed to impacts from higher intensity
training, such as bombardment and fire. Some of these occurrences are
near fuelbreaks and may be impacted by a change in the vegetation
community from fuelbreak maintenance, resulting in an increase in
erosion or invasive nonnative plants. Additionally, occurrences on the
eastern escarpment near the firebreaks on Ridge Road (Canchalagua
Canyon, Knob Canyon) might be impacted by the creation and maintenance
of firebreaks (USFWS 2008, p. 57). The Navy has committed to studying
the effects of Phos-Chek on San Clemente Island vegetation, and has
avoided application of Phos-Chek within 300 ft (91.4 m) of mapped
listed species to the extent allowable with fuelbreak installation
(USFWS 2008, pp. 97-98). In the MOFMP, the Navy committed to conducting
preseason briefings for firefighting personnel on the guidelines for
fire suppression and limitations associated with the use of Phos-Chek
and saltwater drops (USFWS 2008, pp. 97-98). The impact of saltwater on
the habitat of C. grisea has not yet been
[[Page 29119]]
assessed. However, if salt persists, the composition in the plant
community could change to favor more salt-tolerant taxa.
It is anticipated that the Navy will construct additional
fuelbreaks to minimize the risk of fire spreading from areas proposed
for expansion of live fire and demolition training north of SHOBA
(USFWS 2008, p. 98). To minimize the potential for effects to listed
species, the Navy considers the documented locations of listed species
on the island as fuelbreak lines are developed. The majority of
Castilleja grisea habitat is not impacted by fire management, and only
6 of 29 occurrences (21 percent) are associated with fuelbreaks. Even
if expanded in conjunction with increased levels of training
activities, the benefits of fuelbreaks outweigh the detrimental impacts
of recurrent fire to C. grisea habitat. The threat of fire management
to C. grisea habitat is restricted mainly to occurrences within SHOBA,
and particularly to occurrences in the Impact Areas. Because of the
isolated nature of this threat and its role in prevention of fire, fire
management is a low-magnitude threat to C. grisea in the future.
Summary of Factor A
The habitat of Castilleja grisea is threatened by destruction and
modification of habitat associated with land use, erosion, the spread
of nonnatives, fire, and fire management. To help ameliorate these
threats, the Navy is implementing a MOFMP, an INRMP, and the island-
wide control of nonnative plants. (Navy 2002, pp. 1-1--8-12; USFWS
2008, pp. 1-237). The MOFMP has been helpful in informing strategic
decisions for training using live fire or incendiary devices. The Navy
has postponed major troop and assault vehicle maneuvers across the
island until an erosion control plan is completed (Navy 2008b, pp. 5-
29, 5-30; USFWS 2008, pp. 62, 87). Natural resource managers have been
successful at decreasing the prevalence of particularly destructive
nonnatives, such as Foeniculum vulgare. In recent years, access to
Impact Areas I and II within SHOBA for biological monitoring and
conservation actions has been strictly prohibited (USFWS 2008, p. 50),
so the status of four occurrences (Red Canyon, China Canyon, Horse
Beach Canyon, and Upper Chenetti Canyon) remains unknown. Recently,
closures along the eastern escarpment in SHOBA have also limited the
monitoring and management of four occurrences (Knob Canyon, Canchalagua
Canyon, Bryce Canyon, and Eagle Canyon). However, 16 of 29 occurrences
(55 percent) of C. grisea fall outside Impact Areas, IOA, AVMA, TAR,
and fuelbreaks, where the most intensive habitat disturbances are
likely to take place. While it is anticipated that military training
activities will likely increase, based on the current range of C.
grisea and conservation efforts, the threats to the habitat of C.
grisea posed by land use, erosion, nonnatives, fire and fire management
are decreasing in magnitude.
Factor B. Overutilization for Commercial, Recreational, Scientific, or
Educational Purposes
In the listing rule (42 FR 40682; August 11, 1977), the Service did
not identify any threats from overutilization, and there is no new
information to indicate that overutilization is a threat to Castilleja
grisea. Although voucher herbarium specimens of C. grisea and seeds
have been collected for research and seed banking, overutilization of
C. grisea for any purpose is not currently considered a threat nor
expected to be in the future.
Factor C. Disease or Predation
Grazing of feral goats and rooting of feral pigs were considered a
direct threat to Castilleja grisea in the final listing rule (42 FR
40682; August 11, 1977). As stated above, this threat was ameliorated
by the removal of all goats and pigs from San Clemente Island in 1992,
as recognized in our 2007 status review (USFWS 2007c, p. 11).
Currently, no other predators or diseases on San Clemente Island are
known to pose a significant threat to C. grisea, nor are they expected
to become a threat in the future.
Factor D. Inadequacy of Existing Regulatory Mechanisms
The Act requires us to examine the adequacy of existing regulatory
mechanisms with respect to those existing and foreseeable threats that
may affect Castilleja grisea. The inadequacy of existing regulatory
mechanisms was not indicated as a threat to C. grisea at listing (42 FR
40682; August 11, 1977). Since it was listed as endangered, the Act has
been and continues to be the primary Federal law that affords
protection to C. grisea. The Service's responsibilities in
administering the Act include sections 7, 9, and 10 (for more
information on the Service's responsibilities, see above discussion
under Malacothamnus clementinus--Factor D). Critical habitat has not
been designated or proposed for this taxon. Listing C. grisea provided
a variety of protections, including the prohibitions against removing
or destroying plants within areas under Federal jurisdiction and the
conservation mandates of section 7 for all Federal agencies. If C.
grisea were not listed, these protections would not be provided. Thus,
we must evaluate whether other regulatory mechanisms would provide
adequate protections absent the protections of the Act.
Other Federal Protections
National Environmental Policy Act (NEPA)
All Federal agencies are required to adhere to the National
Environmental Policy Act (NEPA) of 1970 (42 U.S.C. 4321 et seq.) for
projects they fund, authorize, or carry out. The Council on
Environmental Quality's regulations for implementing NEPA (40 CFR parts
1500-1518) state that agencies shall include a discussion on the
environmental impacts of the various project alternatives (including
the proposed action), any adverse environmental effects that cannot be
avoided, and any irreversible or irretrievable commitments of resources
involved (40 CFR part 1502). The NEPA itself is a disclosure law, and
does not require subsequent minimization or mitigation measures by the
Federal agency involved. Although Federal agencies may include
conservation measures for Castilleja grisea as a result of the NEPA
process, any such measures are typically voluntary in nature and are
not required by the statute. NEPA does not itself regulate activities
that might affect C. grisea, but it does require full evaluation and
disclosure of information regarding the effects of contemplated Federal
actions on sensitive species and their habitats.
On San Clemente Island, the Navy must meet the NEPA requirements
for actions significantly affecting the quality of the human
environment. Typically, the Navy prepares Environmental Assessments and
Environmental Impact Statement on operational plans and new or
expanding training actions. Absent the listing of Castilleja grisea, we
would expect the Navy to continue to meet the procedural requirements
of NEPA for its actions, including evaluating the environmental impacts
to rare plant species and other natural resources. However, as
explained above, NEPA does not itself regulate activities that might
affect C. grisea.
Sikes Act Improvement Act (Sikes Act)
The Sikes Act (16 U.S.C. 670) authorizes the Secretary of Defense
to develop cooperative plans with the
[[Page 29120]]
Secretaries of Agriculture and the Interior for natural resources on
public lands. The Sikes Act Improvement Act of 1997 requires Department
of Defense installations to prepare INRMPs that provide for the
conservation and rehabilitation of natural resources on military lands
consistent with the use of military installations to ensure the
readiness of the Armed Forces. An INRMP is a plan intended ``* * * to
guide installation commanders in managing their natural resources in a
manner that is consistent with the sustainability of those resources
while ensuring continued support of the military mission'' (Navy 2002,
p. 1-1). INRMPs are developed in coordination with the State and the
Service, and are generally updated every 5 years. Although an INRMP is
technically not a regulatory mechanism because its implementation is
subject to funding availability, it is an important guiding document
that helps to integrate the military's mission with natural resource
protection.
San Clemente Island Integrated Natural Resources Management Plan
(INRMP)
Pursuant to the Sikes Act, the Navy adopted an INRMP for San
Clemente Island that identifies multiple objectives for protecting
Castilleja grisea and its habitat to help reduce threats to this taxon
(Navy 2002). The INRMP also disclosed actions through the NEPA process,
and to comply with such legislation and regulations as the Endangered
Species Act, the Federal Noxious Weed Act of 1974 (7 U.S.C. 2801), the
Comprehensive Environmental Response, Compensation, and Liability Act
(42 U.S.C. 9601), the Resources Conservation and Recovery Act (42
U.S.C. 6901), and the Soil Conservation Act (16 U.S.C. 3B) (see INRMP
section above under Malacothamnus clementinus--Factor D). Natural
resource objectives of relevance to the protection of C. grisea in the
INRMP include an objective to: ``Protect, monitor, and restore plants
and cryptograms in order to manage for their long-term sustainability
on the island'' (Navy 2002, p. 4-39). The INRMP specifically includes
the following objectives for C. grisea management: recovery of native
shrub communities that are host plants for the species, the removal of
nonnatives, monitoring of the species, studies of preferred host
plants, study of plant's response to fire, and studies and inventory of
insect pollinators (Navy 2002, pp. D-20, D-21). Multiple INRMP
management strategies have been implemented for the conservation of C.
grisea. Other INRMP strategies that target the plant communities within
which this species occurs include: Controlling erosion, with priority
given to locations where erosion may be affecting listed species;
producing a new vegetation map; reducing nonnative plant cover from
1992-1993 baseline levels; managing the size and intervals of fires;
experimenting with fire management to improve native plant dominance
while protecting sensitive plant occurrences; and conducting genetic
and biological studies of C. grisea across the island.
The MOFMP, Erosion Control Plan, and nonnative plant species
control conducted on the island are discussed above under Castilleja
grisea--Factor A. The Present or Threatened Destruction, Modification,
or Curtailment of Its Habitat or Range. Absent listing under the Act,
the Navy would still be required to develop and implement INRMPs under
the Sikes Act. However, as noted under the other factors, while the
INRMP helps to ameliorate threats and provides some protection for C.
grisea occurrences, those occurrences within Impact Areas or
operationally closed areas may not benefit from the conservation
measures. While the INRMP has reduced the severity of threats and
contributed to conservation of the species, it still allows for land
use consistent with military readiness and training. Thus, Navy
activities will continue to impact C. grisea as described under Factor
A and E.
State Protections
Since the time of listing, Castilleja grisea has benefited from
additional State protections under the Native Plant Protection Act
(NPPA) and California Endangered Species Act (CESA; listed 1982).
However, the range of C. grisea is restricted to a Federal military
installation, so listing under NPPA and CESA may only afford protection
to this species in rare instances when the lead agency is a non-Federal
agency or when proposed activities fall under other State laws.
Summary of Factor D
The regulatory mechanisms outlined above provide for adequate
conservation of Castilleja grisea. In continuance of a long history of
cooperative conservation efforts, the Navy also implemented several
conservation actions that benefit this plant taxon. The Navy has
implemented an MOFMP to reduce the risk of fire on the island and a
nonnative plant species control program. In response to the
conservation actions proposed and the current status of the listed
taxon, we issued a non-jeopardy biological opinion on the Navy's MOFMP.
The provisions included in the San Clemente Island INRMP provide
protection to all C. grisea occurrences and adaptive management of its
habitat in order to help address threats to the plant from military
activities and nonnative plants. However, as indicated in the
discussion under Factor A, not all management tools described in the
INRMP are in place, and conservation management may not be implemented
at several of the known occurrences that have been closed to natural
resource managers. Castilleja grisea occurrences are afforded
protection through Federal and military mechanisms, and thus the
inadequacy of existing regulatory mechanisms is not considered a threat
to the species now or in the future. However, in the absence of the
Act, the existing regulatory mechanisms are not adequate to conserve C.
grisea throughout its range both now and in the future.
Factor E. Other Natural or Manmade Factors Affecting Their Continued
Existence
The 1977 listing rule identified nonnatives as a threat to
Castilleja grisea under Factor E: competition from nonnative plants (42
FR 40682; August 11, 1977). In this 5-factor analysis, impacts from
nonnative plants are discussed above under Factor A as a threat to
habitat. Other Factor E threats identified since listing that currently
impact C. grisea plants include: (1) Movement of vehicles and troops,
(2) fire, and (3) climate change. Factor E addresses threats to
individuals of the species, rather than the habitat modification
threats that are discussed in Factor A. Therefore, while some threats
are discussed in both sections, in this section we are focusing on the
direct impacts to individuals of C. grisea.
Movement of Vehicles and Troops
Military training activities within training areas often entail the
movement of vehicles and troops over the landscape with the potential
of trampling or crushing individual plants (for discussion of SWAT,
TAR, and IOA, see above discussion for Malacothamnus clementinus--
Factor E). Based on the distribution of Castilleja grisea occurrences
and type of troop movements likely to occur, impacts due to trampling
and crushing are likely to occur within the IOA or AVMA, along roads,
and in the Impact Areas. Specifically, major troop movements and
vehicle landings are planned through Horse Beach and the Horse Beach
Canyon occurrence, with troops and assault vehicles moving
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north along Horse Beach Road from the beach (USFWS 2008, pp. 30, 41).
These operations could affect the Horse Beach Canyon and China Canyon
occurrences (USFWS 2008, pp. 85-86). The status of these plants is
currently unknown because of closure of the Impact Areas (USFWS 2008,
p. 50).
Sixteen of 29 occurrences (approximately 55 percent; West Cove,
Terrace Canyon, Larkspur Canyon, Nanny Canyon, Lemon Tank Canyon, Seal
Cove Canyon, Eel Cove Canyon, Plain northeast of Warren Canyon, Eagle
Canyon, Bryce Canyon, Horse Beach Canyon, China Canyon, Red Canyon,
Knob Canyon, Canchalagua Canyon, and Pyramid Head) are partially or
wholly within the boundaries of a training area (IOA, TAR, AVMA, SWAT,
or Impact Area), and may be impacted by trampling. Recent documentation
of C. grisea within these training areas suggests that, while the
individual plants have the potential to be impacted by the activities
described above, they are able to sustain themselves under the recent
levels of traffic from vehicles and troops associated with training
activities (SERG 2009-2011, GIS data). Steep slopes along the eastern
escarpment may also afford the eight C. grisea occurrences there some
topographic protection from vehicle and troop movements. The
anticipated loss of individual plants from proposed increases in troop
and vehicle movement is likely to increase, though this will likely be
a low-level impact to the survival and recovery of C. grisea because it
is diffuse and managed by the Navy (USFWS 2008, pp. 91-102).
Fire
Although not specifically mentioned in the listing rule, intense or
frequent fires could threaten Castilleja grisea. In the Factor A
discussion above, we addressed impacts of fire on the habitat; this
section covers the discrete threats to individuals of C. grisea. As
discussed in the Background section, it is unknown if C. grisea is
adapted to periodic fires, though it is likely that this taxon is
resilient to occasional fires (Navy 2002, p. D-10; Tierra Data Inc.
2005, p. 80). Castilleja grisea has recently been documented in
portions of Horse Beach Canyon that burned up to three times since
1979, and a large occurrence was discovered in Pyramid Cove the year
following a fire (Navy 1996, p. 5-2). The mechanisms and conditions
under which C. grisea can tolerate fire, and at what frequency, are
unknown. At higher than natural fire frequencies, fire has the
potential to exceed a plant's capacity to persist by depleting seed
banks and reducing reproductive output (Zedler et al. 1983, pp. 811-
815). The response of C. grisea to fire may also be governed by the
response of its host species to fire.
Castilleja grisea occurs in some areas of the island that may
experience elevated fire frequency, such as SHOBA and especially the
Impact Areas (Red Canyon, China Canyon, Horse Beach Canyon, Upper
Chenetti Canyon) (discussed in Factor A above). The potential for
frequent fire at many of the occurrences within SHOBA is reduced by
their location on the eastern side of the island, away from Impact
Areas I and II. In conjunction with its expansion of training
activities, the Navy implemented a fire management plan within the
MOFMP that is focused on fire prevention, fuels management, and fire
suppression. These measures should minimize the frequency and spread of
fires that could result in loss of C. grisea individuals.
Cu astilleja grisea is likely to withstand occasional fires, as
demonstrated through its stability on the island since listing.
Although fire ignition points are concentrated in the military training
areas, fires that escape these areas can spread to most other areas of
the island. However, fires that escape from training areas are not
likely to disturb the entire distribution of C. grisea at one time
because this taxon is widely distributed across San Clemente Island,
and associated with steep canyon areas where fires are less likely to
impact the plant. Nine of 29 C. grisea occurrences (31 percent; Eel
Cove Canyon, Seal Cove Terraces, Red Canyon, China Canyon, Horse Beach
Canyon, Upper Chenetti Canyon, Larkspur Canyon, Lemon Tank Canyon, and
Snake Canyon) are more vulnerable to the spread of fire associated with
military training. These occurrences include locations that fall within
0.5 mi (805 m) of TAR, or within Impact Areas where live fire and
demolition training will be performed.
The Navy's fire management practices minimize ignitions as well as
the spread of fires (as described above in Factor A). The Navy is
conducting annual reviews of fire management and fire occurrences that
will allow for adaptive management. These measures should minimize the
frequency and spread of fires that could result in loss of individuals
of C. grisea. Although, in areas operationally closed to natural
resource managers, conservation actions may not be implemented, and the
plant's status remains unknown. We anticipate that the Navy's
implementation of the MOFMP will limit the frequency with which fires
escape Impact Areas and TAR and that, through the annual review
process, the Navy will identify mechanisms to reduce fire return
intervals in areas not designated for incendiary use (USFWS 2008, pp.
91-122). Therefore, the impact of fire on individual C. grisea plants
is likely a low-level threat to long-term persistence of this taxon.
Climate Change
For general information regarding climate change impacts, see above
discussion on climate change under Malacothamnus clementinus--Factor E.
Since listing of Castilleja grisea (USFWS 1977, p. 40684), the
potential impacts of ongoing, accelerated climate change have become a
recognized threat to the flora and fauna of the United States (IPCC
2007a, pp. 1-52; PRBO 2011, pp. 1-68) (for discussion of climate change
scenarios in California, see Malacothamnus clementinus--Factor E
above). San Clemente is located within a Mediterranean climatic regime,
but with a significant maritime influence. Climate change models
predict an increase in average temperature for southern California.
There is substantial uncertainty in precipitation projections, and
relatively little consensus concerning precipitation patterns and
projections for southwestern California (PRBO 2011, p. 40). Less
rainfall and warmer air temperatures could limit the range of C.
grisea, although there is no direct research on the effects of climate
change on the species. Castilleja grisea occurs in great numbers on the
eastern side of the island, where fog contributes to a wetter climate.
This area could become drier if fog is less frequent, possibly
affecting moisture availability for C. grisea. The impacts of predicted
future climate change to C. grisea remain unclear. While we recognize
that climate change is an important issue with potential effects to
listed species and their habitats, information is not available to make
accurate predictions regarding its effects to C. grisea at this time.
Summary of Factor E
Castilleja grisea continues to be impacted by military activities
and fire at 17 of the 29 (59 percent) occurrences on San Clemente
Island. Military training activities have the potential to ignite fires
within C. grisea habitat, though the majority of occurrences are
outside of the Impact Areas and TAR where the highest impacts are
recognized. The threat from fire is reduced by implementation of the
Navy's MOFMP, which should limit the frequency of fires escaping from
the Impact Areas, although suppression will not likely occur within the
boundaries of the Impact Areas. Threats from
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trampling and crushing of individual plants are likely to increase due
to increases in training on the island. However, C. grisea has expanded
its distribution on the island, and the Navy is implementing
conservation measures that will continue to improve conditions for this
taxon. Finally, climate change may likely influence this taxon, though
the magnitude of this rangewide threat or how it may affect this taxon
is unknown at this time. Given the distribution of the species and the
conservation measures that will be implemented by the Navy, the threats
described here currently and in the future are either of limited extent
or adequately managed to reduce and minimize impacts to the species,
while the potential overall threat of climate change remains unknown
across this taxon's range.
Combination of Factors--Castilleja grisea
A species may be affected by more than one threat in combination.
Within the preceding review of the five listing factors, we have
identified multiple threats that may have interrelated impacts on the
species (see above discussion on Combination of Factors under
Malacothamnus clementinus--Factor E). The species' productivity may be
reduced because of these threats, either singularly or in combination.
However, it is not necessarily easy to determine (nor is it necessarily
determinable) whether a particular threat is the primary threat having
the greatest effect on the viability of the species, or whether it is
exacerbated by or working in combination with other potential threats
to have cumulative or synergistic effects on the species. While the
combination of factors is a threat to the existence of Castilleja
grisea, we are unable to determine the magnitude or extent of
cumulative or synergistic effects of the combination of factors on the
viability of the species at this time.
Finding
An assessment of the need for a species' protection under the Act
is based on threats to that species and the regulatory mechanisms in
place to ameliorate impacts from these threats. As required by section
4(a)(1) of the Act, we conducted a review of the status of these taxa
and assessed the five factors in consideration of whether Malacothamnus
clementinus, Acmispon dendroideus var. traskiae, and Castilleja grisea
are threatened or endangered throughout all of their range. We examined
the best scientific and commercial information available regarding the
past, present, and future threats faced by the species. We reviewed
information presented in the May 18, 2010, petition, information
available in our files, and through our 90-day finding in response to
this petition, and other available published and unpublished
information. We also consulted with species experts and Navy staff, who
are actively managing for the conservation of M. clementinus, A. d.
var. traskiae, and C. grisea on San Clemente Island.
In considering what factors might constitute threats, we must look
beyond the mere exposure of the species to the factor to determine
whether the exposure causes actual impacts to the species. If there is
exposure to a factor, but no response, or only a positive response,
that factor is not a threat. If there is exposure and the species
responds negatively, the factor may be a threat and we then attempt to
determine how significant the threat is. If the threat is significant,
it may drive, or contribute to, the risk of extinction of the species
such that the species warrants listing as threatened or endangered as
those terms are defined by the Act. This does not necessarily require
empirical proof of a threat. The combination of exposure and some
corroborating evidence of how the species is likely impacted could
suffice. The mere identification of factors that could impact a species
negatively is not sufficient to compel a finding that listing is
appropriate; we require evidence that these factors are operative
threats that act on the species to the point that the species meets the
definition of threatened or endangered under the Act.
A direct threat identified in the listing rule (42 FR 40682),
grazing from feral herbivores, was eliminated by 1992 through the
complete removal of goats and pigs from the island (Factors A and C).
This action also fulfilled one of the primary goals of the Recovery
Plan under Objective 2 (USFWS 1984, p. 107). However, as a result of
years of grazing, impacts from nonnative plants and erosion have
continued to increase on the island. Our review of the status of
Malacothamnus clementinus, Acmispon dendroideus var. traskiae, and
Castilleja grisea determined that threats to these species under
Factors A, D, and E are present. The Navy's natural resource management
and INRMP for the island have helped to ameliorate many of the threats
to these species. The Navy implements natural resource management
through the control of nonnative species, execution of the fire
management plan, and avoidance of federally listed species. Despite
current impacts from these threats to the habitat and individuals of
these taxa, surveys indicate that the range of each taxon has increased
since the time of listing. Increased survey efforts and survey accuracy
have also shown that these taxa occupy significantly more sites than
were known at listing. The extent to which this represents the
detection of previously unknown occurrences, recruitment from the
existing seed bank, or recolonization associated with dispersal events,
or positive response to management and conservation efforts is not
known. Regardless, the increase of both the range and number of
occurrences for all species indicates an overall improved status for
these species since listing.
The surveys and discoveries of new occurrences also contribute to
the achievement of objectives in the Recovery Plan (Objective 6; USFWS
1984, p. 107). The Navy has taken measures to locate the heaviest
impacts of military operations away from the species to the extent
feasible while meeting operational needs, which will minimize, but not
fully eliminate, the damage or destruction of individuals or
occurrences of M. clementinus, A. d. var. traskiae, and C. grisea,
partially fulfilling Objective 1 of the Recovery Plan (USFWS 1984, p.
107; USFWS 2008, pp. 90, 101, 121). However, the largest and most
diverse occurrences of Malacothamnus clementinus are closed to natural
resource monitoring and management, and their status remains unknown.
Malacothamnus clementinus
Since the removal of feral goats and pigs, the distribution of
Malacothamnus clementinus has expanded from 3 to 11 occurrences on San
Clemente Island. However, there are still significant threats to the
species, including threats to habitat from military training activities
directly related to land use, erosion, nonnative plants, fire, and fire
management (see Malacothamnus clementinus--Factor A). Habitat impacts
are caused by the movement of troops and vehicles over the landscape,
as well as by the use of live fire, demolitions, and bombardments. Six
of the 11 known occurrences of M. clementinus are within SHOBA, much of
which serves as a buffer from military training impacts for the rest of
the island. Three M. clementinus occurrences are directly within the
Impact Areas, where frequent fire, habitat disturbance (bombardment),
and troop and vehicle movement occur. This includes the occurrence at
Horse Beach Canyon that comprises the greatest number of point
localities and one of the two occurrences with the greatest genetic
variability (Helenurm
[[Page 29123]]
1999, p. 39). Through implementation of the INRMP, the Navy developed
an MOFMP and a nonnative plant management plan to help minimize or
ameliorate these threats to the species. However, the status of M.
clementinus at Lemon Tank Canyon and the three occurrences in Impact
Areas within SHOBA remains unknown at this time, because these areas
are closed to natural resource personnel (USFWS 2008, p. 50).
Threats to individual Malacothamnus clementinus plants also affect
the species and include: Movement of vehicles and troops, fire, climate
change, and low genetic diversity (see Malacothamnus clementinus--
Factor E). The steps that the Navy has taken to minimize impacts and
avoid endangered species to the extent practicable have helped
ameliorate the threats caused by training to the individual M.
clementinus plants. Climate change may impact M. clementinus, though
the effect is largely unknown. The genetic makeup of the species has
been studied (fulfilling Objective 4 of the Recovery Plan), revealing
that genetic variation within the species is low. Combined with a low
seed production rate and vegetative reproduction, low genetic diversity
puts the species at risk of low genetic fitness and extinction by
stochastic events.
The Navy implemented an INRMP to coordinate the management of
natural resources on the island. Providing a framework for military
operations, this plan helps to ameliorate threats to the endangered
species on the island, and provides for long-term conservation planning
within the scope of military readiness. Provisions included in the
INRMP provide some protection for Malacothamnus clementinus occurrences
(including Acmispon dendroideus var. traskiae, and Castilleja grisea),
and allows adaptive management of the habitat in order to help address
threats from military activities and nonnative plants. Occurrences
within Impact Areas or operationally closed areas may not benefit from
the conservation measures associated with the MOFMP due to lack of
access for natural resources personnel. Existing regulatory mechanisms,
absent the protections of the Act, provide insufficient certainty that
efforts needed to address long-term conservation of the species will be
implemented, or that they will be effective in reducing the level of
threats to M. clementinus throughout its range. Under the INRMP,
occurrences of M. clementinus, including the largest and most
genetically diverse occurrences, will continue to be impacted by
military activities necessary for military readiness and training, and
the closure of some areas creates uncertainty as to the status of the
occurrences within those areas and whether those occurrences will
benefit from conservation measures.
As discussed in the Factor Analysis, a species may be affected by
more than one threat in combination. For example, fires (Factors A and
E) may be more intense or frequent in the habitat if there are greater
amounts of nonnative grasses (Factor A) present in the vegetative
community. Additionally, military activities or erosion may lead to
increased nonnatives in an area. Thus, the species' viability may be
reduced because of synergistic effects when multiple threats are
present at one time. Therefore, the combination of factors is a threat
to the existence of Malacothamnus clementinus, but we are unable to
determine the magnitude or extent of any synergistic effects of the
various factors and their impact at this time.
In conclusion, we have carefully assessed the best scientific and
commercial information available regarding the past, present, and
future threats faced by this species. Our review of the information
pertaining to the five threat factors does not support a conclusion
that the threats have been sufficiently removed, or that their
imminence, intensity, or magnitude have been reduced to the extent that
the species no longer requires the protections of the Act. Four of the
11 known occurrences of the species have been closed to nonmilitary
personnel, such that we are unable to assess the impacts of the threats
described under the five listing factors above, nor are we able to
document the status of a substantial portion of the occurrences of
Malacothamnus clementinus. This includes one occurrence with the
highest number of point localities and the greatest genetic
variability. Under provision of section 4(a)(1) of the Act, we must
assess the status in order to list or change the status of a species
from endangered to threatened.
The 2007 status review listed land use, fire, nonnative species,
erosion, natural factors, fire management, and access to SHOBA as
threats to the species (USFWS 2007, p. 1-23). Although we recommended
downlisting in our 2007 status review, at this time we conclude that
Malacothamnus clementinus continues to be in danger of extinction
throughout its range because of the change in intensity of training and
associated impacts enacted in the 2008 MOFMP. These changes include the
escalation in frequency and intensity of bombardments in Impact Areas I
and II and the movement of large groups of troops and vehicles through
M. clementinus habitat. The threats to M. clementinus, coupled with low
genetic fitness, place this taxon at risk of extinction throughout all
of its range, and reclassification from endangered to threatened is not
warranted at this time.
Acmispon dendroideus var. traskiae
Since listing and the removal of feral goats and pigs on San
Clemente Island, the distribution of Acmispon dendroideus var. traskiae
has expanded from 6 to 29 occurrences, mainly along the western
terraces and eastern escarpment. These significant gains demonstrate
alleviation of threats from feral ungulates and that the species is
persisting despite existing and remaining threats across the landscape.
The taxon faces impacts from military training activities and land use,
erosion, nonnative plants, and fire (see Acmispon dendroideus var.
traskiae--Factor A). Impacts from land use include movement of troops
and vehicles over the landscape, as well as the use of live fire,
demolitions, and bombardments. Much of this activity is concentrated in
training areas within the range of A. d. var. traskiae. However, many
of these occurrences are along the eastern escarpment that is more
protected from fire and military activity. Additionally, the majority
of locations occupied by A. d. var. traskiae (24 of 29 occurrences, or
83 percent) fall outside of training areas, and thus do not receive
intensive habitat disturbance. Access to the eastern escarpment, within
SHOBA and east of Ridge Road, was recently closed for safety concerns.
As a result, the status of 4 of 29 occurrences (14 percent) could be
difficult to monitor in the future.
The Navy implemented a nonnative plant management plan and an MOFMP
to ameliorate habitat threats to the species. Erosion control measures
are incorporated into all project designs to minimize the potential to
exacerbate existing erosion and avoid impacts to listed species (Munson
2011a, pers. comm.). Additionally, large-scale island-wide maneuvers
with assault vehicles have been postponed until an erosion control plan
is drafted and implemented. While it is anticipated that military
training activities, erosion, nonnatives, and fire will have ongoing
impacts to the taxon's habitat, based on the current distribution of
this taxon and existing conservation efforts, impacts from these
threats are reduced and minimized for Acmispon dendroideus var.
traskiae.
[[Page 29124]]
Under the Sikes Act, the Navy has implemented an INRMP to organize
the management of natural resources on the island (also see above
discussion in the Finding section for Malacothamnus clementinus).
Existing regulatory mechanisms, absent the protections of the Act,
provide insufficient certainty that efforts needed to address long-term
conservation of the species will be implemented, or that they will be
effective in reducing the level of threats to Acmispon dendroideus var.
traskiae throughout its range. Under the INRMP, occurrences of A. d.
var. traskiae will continue to be impacted by military activities
necessary for military readiness and training.
Individual Acmispon dendroideus var. traskiae plants also face
threats on the island. Movement of vehicles and troops, fire, climate
change, and hybridization with related species all impact the status of
the species (see Acmispon dendroideus var. traskiae--Factor E). The
steps that the Navy has taken to minimize impacts and avoid endangered
species to the extent practicable are ameliorating the threat of
trampling individual A. d. var. traskiae plants caused by training.
Hybridization has also been studied (fulfilling Objective 4 of the
Recovery Plan), with confirmed hybrids occurring in Wilson Cove (Wilson
Cove). The genetic integrity of A. d. var. traskiae may be threatened
by hybridization with A. argophyllus var. argenteus at one of the
largest occurrences, and requires further investigation. The threats
described here (Factor E) are either of limited or undetermined
magnitude, or reduced to the extent that we anticipate they will not
impede the recovery of A. d. var. traskiae.
As discussed above in the Factor Analysis, a species may be
affected by more than one threat in combination. For example, fires
(Factors A and E) may be more intense or frequent in the habitat if
there are greater amounts of nonnative grasses (Factor A) present in
the vegetative community. Thus, the species' viability may be reduced
because of threats in combination. Therefore, the combination of
factors is a threat to the existence of Acmispon dendroideus var.
traskiae, but we are unable to determine the magnitude or extent of any
synergistic effects of the various factors and their impact at this
time.
In conclusion, we have carefully assessed the best scientific and
commercial information available regarding the past, present, and
future threats faced by this species. After review of the information
pertaining to the five threat factors, we find that the ongoing threats
are not of sufficient imminence, intensity, or magnitude to indicate
that Acmispon dendroideus var. traskiae is presently in danger of
extinction throughout its range and does not, therefore, meet the
definition of an endangered species. While A. d. var. traskiae will
continue to be impacted by military training activities and land use,
erosion, nonnative plants, and fire, the expanded number of occurrences
reduces the severity and magnitude of threats and the likelihood that
any one event would affect all occurrences of the species. The extent
of hybridization within the species is also not known and could affect
the genetic integrity of the plant. Additionally, the plant occurs in
recently closed areas, and these occurrences will not be able to be
accessed or managed in the future with these closures.
Though these threats to Acmispon dendroideus var. traskiae still
exist and will continue into the foreseeable future, the range of this
taxon has substantially increased since listing, and the Navy is
implementing conservation actions through their INRMP to reduce threats
impacting A. d. var. traskiae. Therefore, we find that the petitioned
action to downlist A. d. var. traskiae to threatened is warranted.
Please see the Significant Portion of the Range Analysis section below
for our evaluation as to whether this species may or may not be in
danger of extinction in a significant portion of its range.
Castilleja grisea
The known distribution of Castilleja grisea has expanded from 19 to
29 known occurrences since listing, likely due to the removal of feral
goats and pigs from the island in 1992. These significant gains
demonstrate some alleviation of threats from feral ungulates and that
the species is persisting despite existing and remaining threats across
the landscape. Castilleja grisea faces impacts from military training
activities and land use, erosion, nonnative plants, fire, and fire
management (see Castilleja grisea--Factor A). The movement of troops
and vehicles over the landscape, as well as use of live fire,
demolitions, and bombardments, results in destruction and degradation
of habitat occupied by C. grisea. Much of this activity is concentrated
in SHOBA within training areas and Impact Areas. Four occurrences are
within the Impact Areas, where frequent fire, habitat disturbance
(bombardment), and troop and vehicle movement take place in the heavily
used ranges. Access to parts of SHOBA, including the eastern escarpment
and east of Ridge Road, was recently closed for safety concerns. The
status of the four occurrences may be difficult to assess in the
future, although these areas may be more protected from fire and
military activity and are likely less impacted by habitat threats. A
large proportion of C. grisea occurrences fall outside Impact Areas,
TAR, and fuelbreaks, where the most intensive habitat disturbances are
likely to take place.
Threats impacting individual plants of Castilleja grisea on the
island include: movement of vehicles and troops, fire, and potentially
climate change (see Castilleja grisea--Factor E). The Navy has
ameliorated the threats to individual plants by taking steps to
minimize training impacts and measures to avoid endangered species to
the extent practicable. The threats described under Factor E are either
of limited extent or adequately managed and are not likely to impede
the recovery of C. grisea.
Under the Sikes Act, the Navy has implemented an INRMP to organize
the management of natural resources on the island (also see above
discussion in the Finding section for Malacothamnus clementinus).
Existing regulatory mechanisms, absent the protections of the Act,
provide insufficient certainty that efforts needed to address long-term
conservation of the species will be implemented, or that they will be
effective in reducing the level of threats to Castilleja grisea
throughout its range. Under the INRMP, occurrences of C. grisea will
continue to be impacted by military activities necessary for military
readiness and training.
As discussed above in the Factor Analysis, a species may be
affected by more than one threat in combination. For example, fires
(Factors A and E) may be more intense or frequent in the habitat if
there are greater amounts of nonnative grasses (Factor A) present in
the vegetative community. Thus, the species' viability may be reduced
because of threats in combination. Therefore, the combination of
factors is a threat to the existence of Castilleja grisea, but we are
unable to determine the magnitude or extent of any synergistic effects
of the various factors and their impact at this time.
In conclusion, we have carefully assessed the best scientific and
commercial information available regarding the past, present, and
future threats faced by this species. After review of the information
pertaining to the five threat factors, we find the ongoing threats are
not of sufficient imminence, intensity, or magnitude to indicate that
Castilleja grisea is
[[Page 29125]]
presently in danger of extinction across its range. While C. grisea
will continue to be impacted by military training activities and land
use, erosion, nonnative plants, and fire, the expanded number of
occurrences reduces the severity and magnitude of threats and the
likelihood that any one event would affect all occurrences of the
species. Additionally, the plant occurs in operationally closed areas,
such as the Impact Areas, where threats are concentrated and
occurrences cannot be accessed or managed with these closures.
Though threats to Castilleja grisea still exist and will continue
into the foreseeable future, the range of this taxon has substantially
increased since listing, and the Navy is implementing conservation
actions through their INRMP to reduce threats impacting C. grisea.
Therefore, we find that the petitioned action to downlist C. grisea to
threatened is warranted at this time. Please see the Significant
Portion of the Range Analysis section below for our evaluation as to
whether this species may or may not be in danger of extinction in a
significant portion of its range.
Significant Portion of the Range Analysis
The Act defines ``endangered species'' as any species which is ``in
danger of extinction throughout all or a significant portion of its
range,'' and ``threatened species'' as any species which is ``likely to
become an endangered species within the foreseeable future throughout
all or a significant portion of its range.'' The definition of
``species'' is also relevant to this discussion. The Act defines the
term ``species'' as follows: ``The term `species' includes any
subspecies of fish or wildlife or plants, and any distinct population
segment [DPS] of any species of vertebrate fish or wildlife which
interbreeds when mature.'' The phrase ``significant portion of its
range'' (SPR) is not defined by the statute, and we have never
addressed in our regulations: (1) The consequences of a determination
that a species is either endangered or likely to become so throughout a
significant portion of its range, but not throughout all of its range;
or (2) what qualifies a portion of a range as ``significant.''
Two recent district court decisions have addressed whether the SPR
language allows the Service to list or protect less than all members of
a defined ``species'': Defenders of Wildlife v. Salazar, 729 F. Supp.
2d 1207 (D. Mont. 2010), concerning the Service's delisting of the
Northern Rocky Mountain gray wolf (74 FR 15123, Apr. 12, 2009); and
WildEarth Guardians v. Salazar, 2010 U.S. Dist. LEXIS 105253 (D. Ariz.
Sept. 30, 2010), concerning the Service's 2008 finding on a petition to
list the Gunnison's prairie dog (73 FR 6660, Feb. 5, 2008). The Service
had asserted in both of these determinations that it had authority, in
effect, to protect only some members of a ``species,'' as defined by
the Act (i.e., species, subspecies, or DPS), under the Act. Both courts
ruled that the determinations were arbitrary and capricious on the
grounds that this approach violated the plain and unambiguous language
of the Act. The courts concluded that reading the SPR language to allow
protecting only a portion of a species' range is inconsistent with the
Act's definition of ``species.'' The courts concluded that once a
determination is made that a species (i.e., species, subspecies, or
DPS) meets the definition of ``endangered species'' or ``threatened
species,'' it must be placed on the list in its entirety and the Act's
protections applied consistently to all members of that species
(subject to modification of protections through special rules under
sections 4(d) and 10(j) of the Act).
Consistent with that interpretation, and for the purposes of this
finding, we interpret the phrase ``significant portion of its range''
in the Act's definitions of ``endangered species'' and ``threatened
species'' to provide an independent basis for listing; thus there are
two situations (or factual bases) under which a species would qualify
for listing: A species may be endangered or threatened throughout all
of its range; or a species may be endangered or threatened in only a
significant portion of its range. If a species is in danger of
extinction throughout an SPR, it, the species, is an ``endangered
species.'' The same analysis applies to ``threatened species.''
Therefore, the consequence of finding that a species is endangered or
threatened in only a significant portion of its range is that the
entire species shall be listed as endangered or threatened,
respectively, and the Act's protections shall be applied across the
species' entire range.
We conclude, for the purposes of this finding, that interpreting
the SPR phrase as providing an independent basis for listing is the
best interpretation of the Act because it is consistent with the
purposes and the plain meaning of the key definitions of the Act; it
does not conflict with established past agency practice (i.e., prior to
the 2007 Solicitor's Opinion), as no consistent, long-term agency
practice has been established; and it is consistent with the judicial
opinions that have most closely examined this issue. Having concluded
that the phrase ``significant portion of its range'' provides an
independent basis for listing and protecting the entire species, we
next turn to the meaning of ``significant'' to determine the threshold
for when such an independent basis for listing exists.
Although there are potentially many ways to determine whether a
portion of a species' range is ``significant,'' we conclude, for the
purposes of this finding, that the significance of the portion of the
range should be determined based on its biological contribution to the
conservation of the species. For this reason, we describe the threshold
for ``significant'' in terms of an increase in the risk of extinction
for the species. We conclude that a biologically based definition of
``significant'' best conforms to the purposes of the Act, is consistent
with judicial interpretations, and best ensures species' conservation.
Thus, for the purposes of this finding, a portion of the range of a
species is ``significant'' if its contribution to the viability of the
species is so important that, without that portion, the species would
be in danger of extinction.
We evaluate biological significance based on the principles of
conservation biology using the concepts of redundancy, resiliency, and
representation. Resiliency describes the characteristics of a species
that allow it to recover from periodic disturbance. Redundancy (having
multiple populations distributed across the landscape) may be needed to
provide a margin of safety for the species to withstand catastrophic
events. Representation (the range of variation found in a species)
ensures that the species' adaptive capabilities are conserved.
Redundancy, resiliency, and representation are not independent of each
other, and some characteristic of a species or area may contribute to
all three. For example, distribution across a wide variety of habitats
is an indicator of representation, but it may also indicate a broad
geographic distribution contributing to redundancy (decreasing the
chance that any one event affects the entire species), and the
likelihood that some habitat types are less susceptible to certain
threats, contributing to resiliency (the ability of the species to
recover from disturbance). None of these concepts is intended to be
mutually exclusive, and a portion of a species' range may be determined
to be ``significant'' due to its contributions under any one of these
concepts.
For the purposes of this finding, we determine if a portion's
biological contribution is so important that the portion qualifies as
``significant'' by
[[Page 29126]]
asking whether, without that portion, the representation, redundancy,
or resiliency of the species would be so impaired that the species
would have an increased vulnerability to threats to the point that the
overall species would be in danger of extinction (i.e., would be
``endangered''). Conversely, we would not consider the portion of the
range at issue to be ``significant'' if there is sufficient resiliency,
redundancy, and representation elsewhere in the species' range that the
species would not be in danger of extinction throughout its range if
the population in that portion of the range in question became
extirpated (extinct locally).
We recognize that this definition of ``significant'' establishes a
threshold that is relatively high. On the one hand, given that the
consequences of finding a species to be endangered or threatened in an
SPR would be listing the species throughout its entire range, it is
important to use a threshold for ``significant'' that is robust. It
would not be meaningful or appropriate to establish a very low
threshold whereby a portion of the range can be considered
``significant'' even if only a negligible increase in extinction risk
would result from its loss. Because nearly any portion of a species'
range can be said to contribute some increment to a species' viability,
use of such a low threshold would require us to impose restrictions and
expend conservation resources disproportionately to conservation
benefit: listing would be rangewide, even if only a portion of the
range of minor conservation importance to the species is imperiled. On
the other hand, it would be inappropriate to establish a threshold for
``significant'' that is too high. This would be the case if the
standard were, for example, that a portion of the range can be
considered ``significant'' only if threats in that portion result in
the entire species' being currently endangered or threatened. Such a
high bar would not give the SPR phrase independent meaning, as the
Ninth Circuit held in Defenders of Wildlife v. Norton, 258 F.3d 1136
(9th Cir. 2001).
The definition of ``significant'' used in this finding carefully
balances these concerns. By setting a relatively high threshold, we
minimize the degree to which restrictions will be imposed or resources
expended that do not contribute substantially to species conservation.
But we have not set the threshold so high that the phrase ``in a
significant portion of its range'' loses independent meaning.
Specifically, we have not set the threshold as high as it was under the
interpretation presented by the Service in the Defenders litigation.
Under that interpretation, the portion of the range would have to be so
important that current imperilment there would mean that the species
would be currently imperiled everywhere. Under the definition of
``significant'' used in this finding, the portion of the range need not
rise to such an exceptionally high level of biological significance.
(We recognize that if the species is imperiled in a portion that rises
to that level of biological significance, then we should conclude that
the species is in fact imperiled throughout all of its range, and that
we would not need to rely on the SPR language for such a listing.)
Rather, under this interpretation we ask whether the species would be
endangered everywhere without that portion, i.e., if that portion were
completely extirpated. In other words, the portion of the range need
not be so important that even being in danger of extinction in that
portion would be sufficient to cause the remainder of the range to be
endangered; rather, the complete extirpation (in a hypothetical future)
of the species in that portion would be required to cause the remainder
of the range to be endangered.
The range of a species can theoretically be divided into portions
in an infinite number of ways. However, there is no purpose to
analyzing portions of the range that have no reasonable potential to be
significant and threatened or endangered. To identify only those
portions that warrant further consideration, we determine whether there
is substantial information indicating that: (1) The portions may be
``significant,'' and (2) the species may be in danger of extinction
there or likely to become so within the foreseeable future. Depending
on the biology of the species, its range, and the threats it faces, it
might be more efficient for us to address the significance question
first or the status question first. Thus, if we determine that a
portion of the range is not ``significant,'' we do not need to
determine whether the species is endangered or threatened there; if we
determine that the species is not endangered or threatened in a portion
of its range, we do not need to determine if that portion is
``significant.'' In practice, a key part of the portion status analysis
is whether the threats are geographically concentrated in some way. If
the threats to the species are essentially uniform throughout its
range, no portion is likely to warrant further consideration. Moreover,
if any concentration of threats applies only to portions of the
species' range that clearly would not meet the biologically based
definition of ``significant,'' such portions will not warrant further
consideration.
Having determined that Acmispon dendroideus var. traskiae and
Castilleja grisea are no longer endangered throughout their ranges as a
consequence of the threats evaluated under the five factors in the Act,
we must next consider whether there are any significant portions of
these two species' ranges where they are currently endangered. A
portion of a species' range is significant if it is part of the current
range of the species and is important to the conservation of the
species as evaluated based upon its representation, resiliency, or
redundancy.
Acmispon dendroideus var. traskiae
Applying the process described above, we evaluated the range of
Acmispon dendroideus var. traskiae to determine if any units could be
considered a significant portion of its range. This taxon is an island
endemic restricted to a single, small island, with no natural division
in its range. Because of its limited range and number of occurrences in
close proximity to one another, no portion is likely to have a greater
contribution to representation, resiliency, or redundancy than other
portions. Furthermore, the existing and potential primary direct and
indirect threats from military training activities, nonnative plant
species, fire, and erosion are relatively uniform across San Clemente
Island, indicating that no portions of its range are experiencing a
greater severity or magnitude of threats. We conclude that there are no
portions that warrant further consideration under this analysis.
In summary, the primary threats to Acmispon dendroideus var.
traskiae are relatively uniform throughout its range. We determined
that none of the existing or potential threats, either alone or in
combination with others, currently place A. d. var. traskiae in danger
of extinction throughout all or a significant portion of its range.
However, without the continued protections of the Act, this taxon is
likely to become endangered throughout its range in the foreseeable
future. Threatened status is therefore appropriate for A. d. var.
traskiae throughout its entire range.
Castilleja grisea
Applying the process described above, we evaluated the range of
Castilleja grisea to determine if any units could be considered a
significant portion of its range (also see the Significant Portion of
the Range
[[Page 29127]]
Analysis section above for Acmispon dendroideus var. traskiae). This
island endemic is restricted to a single, small island with no natural
division in its range. Because of its limited range and number of
occurrences in close proximity to one another, no portion is likely to
have a greater contribution to its representation, resiliency, or
redundancy than other portions. The primary threats to C. grisea,
military training activities, nonnative plant species, fire, and
erosion, are relatively uniform throughout its range (San Clemente
Island), indicating that no portion is experiencing a greater severity
or magnitude of threats. We conclude that there are no portions that
warrant further consideration under this analysis. We determined that
none of the existing or potential threats, either alone or in
combination with others, currently place C. grisea in danger of
extinction throughout all of its range. However, without the continued
protections of the Act, this taxon is likely to become endangered
throughout its range in the foreseeable future. Threatened status is
therefore appropriate for C. grisea throughout its entire range.
Effects of This Rule
If this proposed rule is made final, it would revise 50 CFR
17.12(h) to reclassify Acmispon dendroideus var. traskiae and
Castilleja grisea from endangered to threatened on the List of
Endangered and Threatened Plants and to correct the scientific and
common names for Acmispon dendroideus var. traskiae. However, this
reclassification does not significantly change the protections afforded
these species under the Act. The regulatory protections of section 9
and section 7 of the Act (see Factor D, above) would remain in place.
Pursuant to section 7 of the Act, all Federal agencies must ensure that
any actions they authorize, fund, or carry out are not likely to
jeopardize the continued existence of A. d. var. traskiae and C.
grisea. Whenever a species is listed as threatened, the Act allows
promulgation of special rules under section 4(d) that modify the
standard protections for threatened species found under section 9 of
the Act and Service regulations at 50 CFR 17.31 and 17.71, when it is
deemed necessary and advisable to provide for the conservation of the
species. There are no 4(d) rules in place or proposed for A. d. var.
traskiae and C. grisea, because there is currently no conservation need
to do so for these species.
Recovery actions directed at Acmispon dendroideus var. traskiae and
Castilleja grisea will continue to be implemented as outlined in the
Recovery Plan for the Endangered and Threatened Species of the
California Channel Islands (USFWS 1984). This recovery plan addresses
10 plants (including Malacothamnus clementinus, A. d. var. traskiae,
and C. grisea) and animals distributed among three of the Channel
Islands (USFWS 1984).
Peer Review
In accordance with our joint policy on peer review published in the
Federal Register on July 1, 1994 (59 FR 34270), we will seek the expert
opinions of at least three appropriate and independent specialists
regarding this proposed rule to reclassify Acmispon dendroideus var.
traskiae and Castilleja grisea from endangered to threatened. The
purpose of peer review is to ensure that our proposed rule is based on
scientifically sound data, assumptions, and analyses. We have invited
these peer reviewers to comment during this public comment period on
our proposed downlisting.
We will consider all comments and information we receive during
this comment period on this proposed rule during our preparation of the
final determination. Accordingly, the final decision may differ from
this proposal.
Public Hearings
Section 4(b)(5) of the Act provides for one or more public hearings
on this proposal, if requested. We must receive your request within 45
days after the date of this Federal Register publication. Send your
request to the address shown in the FOR FURTHER INFORMATION CONTACT
section. We will schedule public hearings on this proposal, if any are
requested, and announce the dates, times, and places of those hearings,
as well as how to obtain reasonable accommodations, in the Federal
Register and local newspapers at least 15 days before the hearing.
Required Determinations
Clarity of the Rule
We are required by Executive Orders 12866 and 12988 and by the
Presidential Memorandum of June 1, 1998, to write all rules in plain
language. This means that each rule we publish must:
(a) Be logically organized;
(b) Use the active voice to address readers directly;
(c) Use clear language rather than jargon;
(d) Be divided into short sections and sentences; and
(e) Use lists and tables wherever possible.
If you feel that we have not met these requirements, send us
comments by one of the methods listed in the ADDRESSES section. To
better help us revise the rule, your comments should be as specific as
possible. For example, you should tell us the names of the sections or
paragraphs that are unclearly written, which sections or sentences are
too long, the sections where you feel lists or tables would be useful,
etc.
Executive Order 13211
Executive Order 13211 requires agencies to prepare Statements of
Energy Effects when undertaking certain actions. This rule is not
expected to significantly affect energy supplies, distribution, or use.
Therefore, this action is not a significant energy action and no
Statement of Energy Effects is required.
Paperwork Reduction Act of 1995
Office of Management and Budget (OMB) regulations at 5 CFR part
1320, which implement provisions of the Paperwork Reduction Act (44
U.S.C. 3501 et seq.), require that Federal agencies obtain approval
from OMB before collecting information from the public. This rule does
not contain any new collections of information that require approval by
OMB under the Paperwork Reduction Act. This rule will not impose
recordkeeping or reporting requirements on State or local governments,
individuals, businesses, or organizations. An agency may not conduct or
sponsor, and a person is not required to respond to, a collection of
information unless it displays a currently valid OMB control number.
National Environmental Policy Act
We determined we do not need to prepare an Environmental Assessment
or an Environmental Impact Statement, as defined under the authority of
the National Environmental Policy Act of 1969 (42 U.S.C. 4321 et seq.),
in connection with regulations adopted pursuant to section 4(a) of the
Act. We published a notice outlining our reasons for this determination
in the Federal Register on October 25, 1983 (48 FR 49244).
References Cited
A complete list of references cited in this rulemaking is available
on the Internet at https://www.regulations.gov and upon request from the
Carlsbad Fish and Wildlife Office (see FOR FURTHER INFORMATION
CONTACT).
Author(s)
The primary authors of this package are the staff members of the
Carlsbad Fish and Wildlife Office.
[[Page 29128]]
List of Subjects in 50 CFR Part 17
Endangered and threatened species, Exports, Imports, Reporting and
recordkeeping requirements, Transportation.
Proposed Regulation Promulgation
Accordingly, we propose to amend part 17, subchapter B of chapter
I, title 50 of the Code of Federal Regulations, as set forth below:
PART 17--ENDANGERED AND THREATENED WILDLIFE AND PLANTS
1. The authority citation for part 17 continues to read as follows:
Authority: 16 U.S.C. 1361-1407; 16 U.S.C. 1531-1544; 16 U.S.C.
4201-4245; Pub. L. 99-625, 100 Stat. 3500; unless otherwise noted.
2. Amend Sec. 17.12(h) under ``Flowering Plants'' by removing the
entry for ``Lotus dendroideus var. traskiae'' and adding an entry for
``Acmispon dendroideus var. traskiae'' and revising the entry for
``Castilleja grisea'' to read as follows:
Sec. 17.12 Endangered and threatened plants.
* * * * *
(h) * * *
--------------------------------------------------------------------------------------------------------------------------------------------------------
Species
-------------------------------------------------------- Historic range Family Status When Critical Special
Scientific name Common name listed habitat rules
--------------------------------------------------------------------------------------------------------------------------------------------------------
Flowering Plants
* * * * * * *
Acmispon dendroideus var. San Clemente Island U.S.A. (CA)......... Fabaceae............ T 26 NA NA
traskiae. lotus.
* * * * * * *
Castilleja grisea................ San Clemente Island U.S.A. (CA)......... Orobanchaceae....... T 26 NA NA
Paintbrush.
* * * * * * *
--------------------------------------------------------------------------------------------------------------------------------------------------------
Authority
The authority for this action is section 4 of the Endangered
Species Act of 1973, as amended (16 U.S.C. 1531 et seq.).
Dated: May 1, 2012.
David L. Cottingham,
Acting Director, Fish and Wildlife Service.
[FR Doc. 2012-11339 Filed 5-15-12; 8:45 am]
BILLING CODE 4310-55-P
