Endangered and Threatened Wildlife and Plants; 12-Month Finding on a Petition To List Castanea pumila, 37706-37716 [2011-16190]

Agencies

• Fish and Wildlife Service
• DEPARTMENT OF THE INTERIOR

[Federal Register Volume 76, Number 124 (Tuesday, June 28, 2011)]
[Proposed Rules]
[Pages 37706-37716]
From the Federal Register Online via the Government Printing Office [www.gpo.gov]
[FR Doc No: 2011-16190]


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DEPARTMENT OF THE INTERIOR

Fish and Wildlife Service

50 CFR Part 17

[Docket No. FWS-R4-ES-2009-0020; MO 92210-0-0008-B]


Endangered and Threatened Wildlife and Plants; 12-Month Finding 
on a Petition To List Castanea pumila var. ozarkensis as Threatened or 
Endangered

AGENCY: Fish and Wildlife Service, Interior.

ACTION: Notice of 12-month petition finding.

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SUMMARY: We, the U.S. Fish and Wildlife Service, announce a 12-month 
finding on a petition to list Castanea pumila var. ozarkensis (Ozark 
chinquapin), a tree, as threatened or endangered under the Endangered 
Species Act of 1973, as amended (Act). After review of all available 
scientific and commercial information, we find that listing Ozark 
chinquapin is not warranted at this time. However, we ask the public to 
submit to us any new information that becomes available concerning the 
threats to Ozark chinquapin or its habitat at any time.

DATES: The finding announced in this document was made on June 28, 
2011.

ADDRESSES: This finding is available on the Internet at https://www.regulations.gov at Docket Number [FWS-R4-ES-2009-0020]. 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, Arkansas Ecological Services Field Office, 
110 South Amity Road, Suite 300, Conway, AR 72032. Please submit any 
new information, materials, comments, or questions concerning this 
finding to the above address.

FOR FURTHER INFORMATION CONTACT: Jim Boggs, Field Supervisor, Arkansas 
Ecological Services Field Office, 110 South Amity Road, Suite 300, 
Conway, AR 72032 (see ADDRESSES); by telephone (501-513-4470) or by 
facsimile (501-

[[Page 37707]]

513-4480). If you use a telecommunications device for the deaf (TDD), 
please call the Federal Information Relay Service (FIRS) at 800-877-
8339.

SUPPLEMENTARY INFORMATION:

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 listing 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 that the petitioned action is: (1) Not warranted, (2) 
warranted, or (3) warranted, but the immediate proposal of a regulation 
implementing the petitioned action is precluded by other pending 
proposals to determine whether species are threatened or endangered, 
and expeditious progress is being made to add or remove qualified 
species from the Federal Lists of Endangered and Threatened Wildlife 
and Plants. Section 4(b)(3)(C) of the Act requires that we treat a 
petition for which the requested action is found to be warranted but 
precluded as though resubmitted on the date of such finding, that is, 
requiring a subsequent finding to be made within 12 months. We must 
publish these 12-month findings in the Federal Register.

Previous Federal Actions

    On July 1, 1975 (40 FR 27823), Castanea pumila var. ozarkensis 
(Ozark chinquapin; see Taxonomy and Species Description section) was 
included as one of the 3,000 plant species under status review. It was 
proposed or reviewed by the Service for listing as an endangered 
species under the Act in 1976 (June 16, 1976, 41 FR 24524). However, we 
did not finalize that proposed rule because of subsequent amendments to 
the Act (U.S. Fish and Wildlife Service 1988). Ozark chinquapin became 
a category 2 candidate on December 15, 1980 (45 FR 82480). It was again 
advertised as a category 2 candidate on September 27, 1985 (50 FR 
39526). The status changed on February 21, 1990 (55 FR 6184), to a 
category 1 candidate species. On September 30, 1993 (58 FR 51144), the 
status changed back to a category 2 candidate species for listing until 
the category 2 list was eliminated in 1996 (61 FR 7596). A category 2 
species was a species for which we had information indicating that a 
proposal to list as threatened or endangered under the Act may be 
appropriate but for which additional information on biological 
viability and threat was needed to support the preparation of a 
proposed rule.
    On January 6, 2004, we received a petition, dated December 28, 
2003, from Mr. Joe Glenn of Hodgen, OK, requesting that the Ozark 
chinquapin be listed under the Act as a candidate species. We 
interpreted the request to mean threatened or endangered. The petition 
clearly identified itself as such and included the requisite 
identification information for the petitioner, as required by the Code 
of Federal Regulations (CFR) at 50 CFR 424.14(a). The petition 
contained supporting information regarding the species' ecology, 
threats to the species, and survey and occurrence data for a portion of 
the Ouachita Highlands in southeastern Oklahoma. We acknowledged 
receipt of the petition in a February 2, 2004, letter to Mr. Glenn. In 
that letter, we advised the petitioner that, due to a significant 
number of court orders and settlement agreements in Fiscal Year 2004, 
we would not be able to address the petitioned request at that time.
    On June 1, 2010, we published a 90-day finding that the petition 
presented substantial information that listing the Ozark chinquapin may 
be warranted and initiated a status review of the species (75 FR 
30313). This notice constitutes the 12-month finding on the December 
28, 2003, petition to list Ozark chinquapin as threatened or 
endangered.

Species Information

Taxonomy and Species Description
    Castanea pumila var. ozarkensis (Ozark chinquapin) was first 
identified as a separate species (Castanea ozarkensis) by Ashe (1923, 
p. 60). Ashe described the range of the species as ``north of the 
Arkansas River and westward from Center Ridge, Arkansas, northward to 
southwestern Missouri and westward to the Valley of the White River'' 
(Tucker 1983, p. 2). Ashe (1923, p. 361) also described a second 
species, Castanea arkansana, in Arkansas. Ashe (1924, p. 45, in Tucker 
1983) reduced Castanea arkansana to varietal status as Castanea 
ozarkensis var. arkansana. Little (1953, p. 2, in Tucker 1983) reduced 
Castanea arkansana to synonymy with Castanea ozarkensis. Tucker (1975, 
p. 2, in Tucker 1983) reduced Castanea ozarkensis to a variety of the 
more common Castanea pumila (Castanea pumila var. ozarkensis (Ashe) 
Tucker) and concurred with Little's (1953) treatment of Castanea 
arkansana. Johnson (1988, p. 43) published a revision of the Castanea 
section (sect.) with Balanocastanion concurring as Tucker's reduction 
of Castanea ozarkensis to a variety of Castanea pumila. Tucker's 
reduction is further supported in Smith's Keys to the Flora of Arkansas 
(1994, p. 54), as well as in current scientific literature that 
references the tree.
    Ozark chinquapin is a tree in the beech family (Fagaceae). Ozark 
chinquapin has leaves 10 to 25 centimeters (cm) (4 to 10 inches (in)) 
long, broadly lanceolate (tapering to a point at the apex and sometimes 
at the base) to elliptical, with coarse teeth that are 2.5 to 9 
millimeters (mm) (0.1 to 0.35 in) long with whitish or yellowish-cream 
stellate (star-shaped) hairs on the lower surfaces. The bark is light 
brown to reddish brown or grayish, with broad flat ridges that break 
into loose plate-like scales. The fruits are subglobose (round but not 
perfectly spherical) to ovoid nuts up to approximately 20 mm (0.8 in) 
long, enclosed in a spiny burr. Burrs are solitary or in groups of two 
or three. The subspecies is distinguished from Castanea pumila var. 
pumila (Allegheny chinquapin) by the larger leaf size, larger teeth, 
and larger fruit, which also have hairs (Steyermark 1963, p. 531; Smith 
1994, p. 54).
    Ozark chinquapin was historically a medium-sized tree species that 
once grew to 20 meters (m) (65 feet (ft)), although usually much 
shorter, but now, as a result of chestnut blight, it rarely reaches 
heights of more than 9 m (30 ft). Trunks develop from stump sprouts as 
well as from seeds, but in recent years, new growth is generally from 
sprouts. Trees reaching the age to produce fruit (4 to 5 years; Paillet 
1993, p. 262) are still common (Arkansas Natural Heritage Commission 
(ANHC) 2010, personal communication (pers. comm.)). Ecologically the 
tree has taken on the character of an understory shrub similar to 
Castanea dentata (American chestnut) (Paillet 2010, pers. comm.) due to 
the fungus parasite (Cryphonectria parasitica) that is responsible for 
the chestnut blight disease, which has adversely affected many Castanea 
spp. populations in the United States (Tucker 1983, pp. 8-9; Steyermark 
1963, p. 531). However, Paillet (1991, p. 10; 1993, pp. 261-262) noted 
an area on the Ozark National Forest that was cut 4 to 5 years 
previously that was full of broad chinquapin crowns, and the ground 
littered with burrs from the summer's nut crop. Ozark chinquapin 
differs in its growth and ability to put out an earlier seed (nut) crop 
compared to Castanea dentata, and appears to allow for an

[[Page 37708]]

abundant but short-lived pulse of seed germination in the decade 
following opening of the forest canopy due to disturbance (Paillet 
2010, pers. comm.).
Habitat
    Ozark chinquapin has been described as historically common in thin 
woods, edges of woods, and mid-successional woods (Tucker 1983, pp. 8-
9). Turner (1935, p. 419) describes Ozark chinquapin as ``fairly 
common'' on north, east, and west facing slopes, ravines, gullies, or 
narrow valleys, and less frequently in the deep, narrow south-facing 
gullies or ravines in the white oak, red oak, red maple, hard maple 
hickory association of northwest Arkansas. It historically occupied 
canopy and subcanopy positions on a variety of habitats, including dry 
upland (the higher ground of a region or district; an elevated region) 
deciduous or mixed hardwood-pine communities on acid soils of ridge-
tops, upper slopes adjacent to ravines and gorges, and the tops of 
sandstone bluffs (C. McDonald 1987, pers. comm.). It is well documented 
that fire frequency had a major role in shaping landscape and regional 
vegetation patterns in the Interior Highlands (Batek et al. 1999, pp. 
407-409; Spetich 2004, pp. 21-28, 49-50, 65-69; Guyette and Spetich 
2002, pp. 466-473; Guyette and Spetich 2003, pp. 463-474; Bidwell et 
al. undated, pp. 2877-2-2877-12; Elliot and Vose 2010, pp. 49-66). 
Ozark chinquapin is fire tolerant, but sprouts may be damaged by fire 
(Kral 1983, p. 287).
    Ozark chinquapin occupy sandstone areas in Alabama, but occupy 
limestone, sandstone, chert rock, and possibly a combination in the 
Interior Highlands of Arkansas, Missouri, and Oklahoma (Johnson 1988, 
p. 43). Associated trees in these habitats include Quercus alba (white 
oak), Quercus stellata (post oak), Quercus rubra (northern red oak), 
Nyssa sylvatica (black gum), Pinus echinata (short-leaf pine), Morus 
rubra (mulberry), Carya spp. (hickories), Ulmus americana (American 
elm), and Ostrya virginiana (ironwood) (Steyermark 1963, p. 531; G. 
Tucker 1976, pers. comm.). Soil conditions typically are acid and 
sandstone-derived, and soil moisture conditions vary from mesic (drains 
well but retains water) to dry; shade is variable (G. Tucker 1976, 
pers. comm.; C. McDonald 1987, pers. comm.).
    Faber-Langendoen (2001, pp. 444, 446, and 449) describe three 
forest types that Ozark chinquapin is associated with in the Interior 
Highlands. These include: (1) Short-leaf pine, white oak, Schizachyrium 
scoparium (little bluestem) woodland, (2) Pinus echinata (shortleaf 
pine), Quercus velutina (black oak), post oak, Vaccinium spp. 
(blueberry species) forest, (3) white oak, northern red oak, Acer 
saccharum (sugar maple), Carya cordiformis (bitternut hickory), and 
Lindera benzoin (northern spicebush) forest.
    The first of these forest types is reported from Missouri and 
Arkansas, where it is known from the Ozark and Ouachita Mountains, and 
may extend into Oklahoma (this forest type is synonymous (the same or 
similar) with acid bedrock savanna in Missouri and dry mesic slope 
Woodland (Smith et al. 2000 in Faber-Langendoen 2001, p. 444)). It 
contains an open canopy (woodland), and Ozark chinquapin is reported as 
comprising a portion of the shrub and sapling strata.
    The second of these forest types white oak ranges from eastern 
Oklahoma to the southwestern corner of Illinois, but may have been 
widespread prior to excessive harvest of shortleaf pine. It is 
synonymous with the dry acid bedrock forest in Missouri (Faber-
Langendoen 2001, p. 446) and (in part) dry shortleaf pine-oak-hickory 
forest (Allard 1990 in Faber-Langendoen 2001, p. 446) and dry south 
slope woodland (Smith et al. 2000 in Faber-Langendoen 2001, p. 446). 
The tree canopy is short, spreading, open, and contains numerous 
branches; a shortleaf-pine emergent canopy often forms over a shorter 
canopy of oaks. Ozark chinquapin comprises a portion of the shrub layer 
in Arkansas, Missouri, and Oklahoma.
    The third forest type (little bluestem woodland) is known from the 
South-Central United States, particularly the Ozark and Ouachita 
Mountain regions in Arkansas, Missouri, and Oklahoma. It is synonymous 
with the mesic forest, mesic limestone-dolomite forest, acid bedrock 
forest (mesic sandstone forest and mesic igneous forest) in Missouri, 
and mesic oak-hickory forest (Tucker 1989 in Faber-Langendoen 2001, p. 
469). The canopy is dominated by oaks, sugar maple, and hickories, 
while the understory closure varies with moisture status at the site, 
being more closed under greater moisture conditions. Ozark chinquapin 
comprises a portion of the shrub layer in moderately well-drained 
soils.
Distribution
    Ozark chinquapin is located throughout the Interior Highlands in 
Arkansas, Missouri, and Oklahoma (Kartesz 1994; ANHC 2010, pers. comm.; 
USDA Forest Service (USFS) 2010, pers. comm.; Missouri Department of 
Conservation 2010, pers. comm.). In Arkansas, it is in 39 counties, 
represented by thousands of elements of occurrence (known locations of 
individual(s) based on field observation). In Missouri, it is found in 
9 counties, including but not limited to 48 elements of occurrence 
representing multiple individuals on the Mark Twain National Forest, 
Big Sugar Creek State Park, and Roaring River State Park. In Oklahoma, 
the species is in 8 counties.
    Ozark chinquapin currently is widespread and abundant within the 
Interior Highlands of Arkansas, but is less common and widespread 
within the uplands of southwestern Missouri and eastern Oklahoma. For 
example, Waterfall and Wallis (1963, p. 14) report Ozark chinquapin 
occurrence in only three of seven Oklahoma counties (Adair, Cherokee, 
and Delaware) in the Ozark uplift portion of the Interior Highlands.
    Localities with seed-producing trees are common on public and 
private lands in the Interior Highlands. Based on a detailed 
reconstruction of Ozark chinquapin in the pre-blight forests of 
northwest Arkansas, almost none of the original trees survived the 
arrival of blight circa 1957. Most Ozark chinquapin sprouts form after 
the blight infestation and represent old seedlings, which may represent 
an extreme case of a reproductive strategy based on advanced 
regeneration (Paillet 2010, pers. comm.). Ozark chinquapin populations 
still occur throughout the tree's historical core distribution in the 
Interior Highlands.
    Herbarium specimens are all that remains to support the existence 
of Ozark chinquapin in Alabama (in Bibb, Lawrence, Tuscaloosa, Walker, 
and Winston Counties in the Appalachian Mountains). Data to support the 
abundance and distribution of Ozark chinquapin in the Appalachian 
Mountains is lacking, and researchers have been unable to find extant 
populations in this region. While it is the opinion of tree experts 
that Ozark chinquapin is the best taxonomic classification (see 
Taxonomy and Species Description), the Ozark Chinquapin Foundation 
reports Ozark chinquapin co-occurrence with Castanea pumila var. pumila 
in the coastal plain of Louisiana and Mississippi (S. Bost, Ozark 
Chinquapin Foundation, pers. comm. 2010). The Service, however, has no 
documentation available to substantiate these records. For the present, 
according to the best available scientific literature, Ozark chinquapin 
is best treated as a separate species. The Interior Highlands in 
Arkansas, Missouri, and Oklahoma contain the only known extant

[[Page 37709]]

populations of Ozark chinquapin at this time (Johnson 1988, pp. 43-45).
    At present, there are thousands of element occurrences in the 
Interior Highlands. Individual site records commonly report multiple 
Ozark chinquapin sprout clumps and trees producing fruit. These vary 
from tens to hundreds of individual sprout clumps at an element 
occurrence record site (Kartesz 1994; ANHC 2010, pers. comm.; USFS 
2010, pers. comm.; Missouri Department of Conservation 2010, pers. 
comm.).

Summary of Information Pertaining to the Five Factors

    Section 4 of the Act (U.S.C. 1533 et seq.) and implementing 
regulations (50 CFR 424) set forth the procedures for adding species to 
the Federal Lists of Endangered and Threatened Wildlife and Plants. 
Under section 4(a)(1) of the Act, a species may be determined to be 
endangered or threatened based on any of the following 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.

In making this finding, information pertaining to Ozark chinquapin in 
relation to the five factors provided in section 4(a)(1) of the Act is 
discussed below.
    In considering what factors might constitute threats to the 
species, we must look beyond the exposure of the species to a factor to 
evaluate whether the species may respond to the factor in a way that 
causes actual effects to the species. If there is exposure to a factor 
and the species responds negatively, the factor may be a threat and, 
during the status review, we attempt to determine how significant a 
threat it is. The threat is significant if it drives, or contributes 
to, the risk of extinction of the species such that the species may 
warrant listing as endangered or threatened as those terms are defined 
in the Act.

Factor A. Present or Threatened Destruction, Modification, or 
Curtailment of the Species' Habitat or Range

    Under Factor A, we evaluated the following threats: Habitat loss 
and/or fragmentation; and forest composition, structure conversions, 
and forest and fire management (fire use, fire suppression, and forest 
silvicultural practices; timber harvest, salvage logging, forest 
thinning, and forest restoration projects).
Habitat Loss and Fragmentation
    Johnson (1988, pp. 41-45) recognized Ozark chinquapin records from 
the Interior Highlands and Appalachian Mountains. Herbarium specimens 
are all that remain to support the existence of Ozark chinquapin in 
Alabama (in five counties in the Appalachian Mountains; Johnson 1988, 
p. 43). Data to support the abundance and distribution of the Ozark 
chinquapin in the southern Appalachian Mountains are lacking, and 
researchers have been unable to find extant populations in this region. 
While there is support for an Appalachian-Ozarkian floristic (relating 
to flowers) relationship by other taxa such as Neviusia alabamensis 
(Moore 1956 in Johnson 1988, p. 44), floristic relationships to the 
lower Mississippi Valley and Gulf Coastal Plain (Ozark Chinquapin 
Foundation 2010, pers. comm.) can only be considered speculative at 
this time (Johnson 1988, p. 47; ANHC 2010, pers. comm.). Steyermark 
(1963, p. 531) states that Louisiana and Mississippi are sometimes 
included as part of the Ozark chinquapin range, but specimens examined 
from those States have been proven not to be Ozark chinquapin. Ozark 
chinquapin is sympatric over virtually its entire range with Castanea 
pumila var. pumila and with Castanea dentata in Alabama. Further 
compounding questions regarding taxonomy of the species, herbarium, 
laboratory, and field studies indicate that in areas of sympatry the 
two varieties of Castanea pumila may be intermediate and identification 
of the two species may not always be possible (Johnson 1988, p. 43).
    Ashe (1923) described the range of the species as ``north of the 
Arkansas River and westward from Center Ridge, Arkansas, northward to 
southwestern Missouri and westward to the Valley of the White River.'' 
Tucker (1983, p. 16) reported a large number of populations of Ozark 
chinquapin in the Interior Highlands of Arkansas, Missouri, and 
Oklahoma. Nearly 20 years later, the distribution and abundance of 
populations remain similar. The largest populations occur on public 
lands (such as the Ouachita National Forest (AR and OK), Ozark National 
Forest (AR), Mark Twain National Forest (MO), State Wildlife Management 
Areas and Parks (AR, MO, and OK), Buffalo National River (AR), Hot 
Springs National Park (AR), and Pea Ridge National Military Park (AR). 
Thousands of elements of occurrences represented by numerous 
individuals occur in the Interior Highlands (ANHC 2010, pers. comm.; 
USFS 2010, pers. comm.; Missouri Department of Conservation 2010, pers. 
comm.; and Oklahoma Natural Heritage 2010; National Park Service (NPS) 
2010 and 2011).
    The Ozark-Ouachita Highlands Assessment (OOHA) 1999 Terrestrial 
Vegetation and Wildlife Report, prepared by a collaborative team of 
natural resource specialists and research scientists, examined 
historical and existing forest conditions throughout the Interior 
Highlands of Arkansas, Missouri, and Oklahoma (USFS 1999, section 5). 
The area of analysis overlaps much of the range of Ozark chinquapin. 
The upland oak-hickory forest type provided the dominant cover within 
the region at the time of the OOHA. It covered 15 million acres (6.1 
million hectares) or about 36 percent of the area. The oak-pine forest 
type provided the second most extensive cover. It covered 4.4 million 
acres (1.8 million hectares) or 11 percent of the area. In 1999, clear-
cutting had declined by 97.5 percent over a 10-year period in National 
Forests within the planning area. Additionally, herbicide application 
in the National Forests experienced an 83 percent decline over the same 
period (USFS 1999, p. 73; UUSFS 2005a, pp. 2-5, 2-6 and 2-27; USFS 
2005b, pp. 176-178). Oak-hickory and oak-pine forest types continue to 
be common forest types in the Interior Highlands. OOHA descriptions of 
vegetation cover or silvicultural practices do not indicate significant 
reductions in suitable habitat for Castanea pumila var. ozarkensis.
    Moreover, the majority of Ozark chinquapin habitat is located on 
State and Federally managed lands. Ozark chinquapin is designated as a 
USFS sensitive species. Land and resource management plans have 
recently been revised for National Forests within the range of the 
species. Revisions of these plans include development of standards to 
protect the species while allowing normal forest management activities, 
including the use of prescribed fire, thinning, and natural gas 
development. These standards further demonstrate that management 
activities (for example, prescribed fire and thinning) on public lands 
enhance sprouting, flowering, and fruit production of this species, 
thus enhancing stewardship for the species. The general direction 
within these plans is for the National Forests to manage habitat to 
move species toward recovery and delisting and to prevent the listing 
of proposed or sensitive species (USFS 2005a, p. 2-13; USFS 2005b, p. 
76).
    Private property development and land use activities may threaten 
Ozark

[[Page 37710]]

chinquapin due to habitat conversion or loss. On the other hand, 
private landowners interested in the conservation of Ozark chinquapin 
have been able to sustain isolated, moderately sized individuals 
capable of seed production on small tracts of private land. In short, 
as the human population continues to increase in the Interior 
Highlands, we believe loss or conversion of forested habitat on private 
lands and its effect on Ozark chinquapin will be minimal, due to the 
wide distribution and vast amount of contiguous habitats afforded the 
species on State and Federal lands. While we expect some element 
occurrences to be lost on private land, we conclude that habitat loss 
and fragmentation are not current threats to Ozark chinquapin, nor do 
we believe they will be in the foreseeable future.
Forest Composition, Structure Conversions, Forest and Fire Management
    It is generally accepted that climate, topography, and substrate 
place fundamental constraints on vegetation at many different spatial 
and temporal scales, but at the landscape scale, vegetation patterns 
also may be controlled by disturbance histories (Zedler et al. 1983; 
McCune and Allen 1985; Myers 1985 in Batek et al. 1999, p. 398). Much 
of our knowledge of fire effects on trees comes from a relatively small 
collection of studies throughout the eastern United States during the 
period 1957 to 1998 (Dey and Hartman 2005, p. 38). Fire suppression is 
one of the major determinants of contemporary vegetation patterns in 
the Interior Highlands. Batek et al. (1999, pp. 407-410) concluded that 
where fire regimes are primarily anthropogenic, as in the Interior 
Highlands (specifically in the Ozarks), they exert strong constraints 
on vegetation composition and patterns. Based on their reconstruction 
analysis, the Interior Highlands vegetative community was replaced 
during the 19th century by a more homogenous landscape dominated by 
several oak species. Most of the shortleaf pine was felled from 1888 to 
1909 (Steven 1991 in Batek et al. 1999, p. 410), and fire suppression 
since 1940 has favored invasion of fire-sensitive species that were 
more restricted in distribution 150 years ago (Batek et al. 1999, p. 
410; Arthur et al. 1998, p. 225).
    Historically, the Interior Highlands landscape consisted of a 
mosaic of prairies, savannas, woodlands, and forests maintained by 
fires and adapted to disturbance. Based on Government Land Office (GLO) 
survey records interpreted by the ANHC, only 33 percent of the Ozark 
Mountains was described as closed forest (much in steep slopes). The 
remaining 67 percent at the time of the GLO surveys had average tree 
densities ranging from 38 to 76 trees per acre.
    European settlement brought changes to the ecosystem that led to 
extensive timber harvest and fire suppression. As a result, the average 
tree density per acre (ha) increased from 52 to 148 (21 to 60) trees. 
Even more staggering was the increase from 300 to 1,000 stems per acre 
(121 to 405 stems per ha) in the sapling and shrub layers. Increased 
trees per acre competing for the same amount of nutrients and water put 
the ecosystem under stress. There is nothing in the post-glacial record 
that suggests that the Interior Highlands have been previously affected 
by changes of this magnitude or rapidity (Spetich 2004, pp. 28 and 
304). Despite this forest conversion after European settlement, Ozark 
chinquapin remained a prized source of edible nuts, fence posts, and 
railroad ties in the Interior Highlands until its rapid ecological and 
socioeconomic demise in the mid-1940s from chestnut blight (Tucker 
1983, p. 7). Canopy closure in undisturbed woods did not seem to have a 
major effect on Ozark chinquapin populations (Paillet 2010, pers. 
comm.).
    Hyatt (1993, pp. 116-118) recounts the floristic history of Baxter 
County in north central Arkansas from the earliest floristic survey in 
1818 to present day. Ecologically and floristically, Baxter County was 
very different during Hyatt's 1987-1988 surveys, as compared with the 
county's surveys from the early 19th century, when many upland areas 
were once prairie. Much of this prairie had disappeared by 1880 and was 
replaced with ``upland hardwood'' and ``pine-hardwood'' forest. By the 
late 19th century, nearly all of the existing forest land was logged 
for railroad ties and lumber (Hyatt and Moren 1990 in Hyatt 1993, p. 
117). Hyatt (1993, pp. 119 and 127) describes Ozark chinquapin as 
``common, diseased, [and] rarely reproductive,'' and from only 
``Deciduous Forest.''
    Chapman et al. (2006) describe long-term dynamics from 1934 to 2002 
in oak stands within the Sylamore Experimental Forest (SEF), located in 
the Ozark National Forest in north central Arkansas. When SEF was 
established in 1934, it was representative of typical unharvested 
forests of the region that had a long history (100 plus years) of 
frequent fire. Some cutting (harvest) was conducted after establishment 
(start of growth) and a fire prevention program was implemented, but 
little management occurred after 1960. Total tree density increased 
from 899 to 2,550 trees per ac (364 to 1,032 trees per ha) and basal 
area (an area of a given section of land that is occupied by the cross-
section of tree trunks and stems at their base) from 25 to 57 m\2\/ac 
(10 to 23 m\2\/ha). Increases occurred among understory, midstory, and 
overstory trees for most species, except Ozark chinquapin, which 
decreased markedly in all three categories, and Quercus velutina (Black 
oak). Chestnut blight is the probable cause of the Ozark chinquapin 
decline, but fire suppression also may have exacerbated the decline.
    Spetich (2004, p. 49) evaluated fire-scarred trees and stumps at 
the Big Piney Ranger District (formerly Bayou and Pleasant Hill Ranger 
Districts), Ozark National Forest, north central Arkansas, for the 
three time periods 1747 to 1764, 1804 to 1906, and 1916 to 1954. From 
1747 to 1764, the fire return interval ranged from 1 to 3 years, with a 
mean return interval of 2.4 years. From 1804 to 1906, the fire interval 
ranged from 1 to 9 years, with a mean return interval of 4.4 years. 
From 1916 to 1954, the fire return interval ranged from 1 to 12 years, 
with a mean return interval of 5.3 years. This validates what other 
researchers have found to be a positive correlation between fire 
frequency and low levels of human population and a negative correlation 
between fire frequency and high levels of human population density. 
Thus, increasing human settlement and fragmentation of the landscape 
resulted in a decrease of fire return interval (Spetich 2004, pp. 49, 
463, 469-473).
    In 2003, an administrative study designed to monitor the immediate 
and short-term effects of prescribed fire on individual Ozark 
chinquapin stems was implemented north of the Crystal Mountain 
Recreation Area on the Caddo-Womble Ranger District, Ouachita National 
Forest, AR. Three areas were studied: An area thinned in previous 
years, an area with no harvest, and an area that served as a reference 
site. The monitoring was designed to capture the current stand 
conditions and health and abundance of individual Ozark chinquapin 
stems. The harvest/burn area showed the widest range of variability and 
the greatest increase in number of Ozark chinquapin sprouts; there was 
also an increase in the number of Ozark chinquapin sprouts in the 
burned area, which had no previous harvest treatments and little to no 
change in the reference area (USFS 2003, pp. 4-5).
    Historical descriptions of vegetation and flora of the Ouachita 
Mountains (a portion of the Interior Highlands) in

[[Page 37711]]

eastern Oklahoma are very similar to those previously discussed for 
this region. Nuttall (1780 to 1820) and Rice and Penfound (1953 to 
1957) accounts of an area dominated by pines and hardwoods intermixed 
with open prairies contained a mosaic of vegetation types established 
by frequent anthropogenic fire and lightning-caused fires (Thwaites 
1905, Curtis 1956, Pyne 1982, and Masters 1991 in Crandall and Tyrl 
2006, p. 65; Rice and Penfound 1959, pp. 595-596). They reported Ozark 
chinquapin from stands in eastern and central Oklahoma, but provide no 
discussion on its status, distribution, or abundance. With the 
implementation of fire suppression in the 1920s, the region changed to 
a landscape of predominately forest (Crandall and Tyrl 2006, p. 65; 
Rice and Penfound, pp. 606-607).
    Crandall and Tyrl (2006, p. 65) and Smith et al. (1997 in Hoagland 
and Buthod 2009, pp. 78-81) documented 447 and 359 species at the 
Pushmataha Wildlife Management Area and McCurtain County Wilderness 
Area, McCurtain County, Oklahoma, respectively, but no Ozark chinquapin 
were reported within these areas (collectively comprising 33,090 ac 
(13,391 ha)). Hoagland and Buthod (2008, pp. 18 and 24; 2009, pp. 61 
and 85) reported Ozark chinquapin presence at The Nature Conservancy's 
T. Nickel Family Nature and Wildlife Preserve and Cucumber Creek Nature 
Preserve, Cherokee and LeFlore Counties, Oklahoma. They reported Ozark 
chinquapin in xeric forests, predominately on south facing and exposed 
slopes at the preserve.
    In summary, the OOHA recognized Ozark chinquapin as a species of 
viability concern, the habitat description being ``woodland, fire 
maintained'' (USFS 1999, p. 137). Loss of natural fire regimes is 
recognized as a threat to the health and sustainability of oak-hickory 
and oak-pine ecosystems in which Ozark chinquapin occurs (Spetich 2004, 
pp. 49-50 and 65-66). Given the current understanding of fire as it 
relates to ecosystem health and sustainability within most of the 
habitats where Ozark chinquapin is known to occur, we cannot conclude 
that fire, whether natural or prescribed, is negatively influencing the 
species. Fire plays a vital role in the management of Ozark chinquapin 
by maintaining open habitat, encouraging both seed germination and 
vegetative regeneration. While fire may injure or kill individuals, 
long-term effects on sustaining viable populations are beneficial. It 
is well documented that fire suppression adversely effects reproduction 
of Ozark chinquapin. In contrast, prescribed fire reduces fuel 
availability in the forest, which reduces the threat of catastrophic 
wildfires that are likely a greater threat to Ozark chinquapin than 
prescribed fire.
    Scientific literature supports widespread forest composition and 
structure changes throughout the Interior Highlands beginning in the 
late 1800s and extending over one century. Tucker (1983, p. 15) stated 
that Ozark chinquapin formerly was a member of the climax (the highest 
or most intense point in the development) community, but presently is 
one of the first species to regenerate following a disturbance (for 
example, clear-cut and prescribed fire). Paillet (1991, p. 10; 1993, 
pp. 261-262) noted an area on the Ozark National Forest that was cut 4 
to 5 years previously that was full of broad chinquapin crowns, with 
the ground littered with burrs from the summer's nut crop. Despite 
these changes, Ozark chinquapin remains common throughout its 
historical distribution in the Interior Highlands. Current land 
management efforts, particularly on State and Federal lands, favor 
Ozark chinquapin persistence in this region.
Summary of Factor A
    We evaluated habitat loss, fragmentation, forest composition, 
structure conversions, forest management, and fire management as 
threats to the Ozark chinquapin. We found that habitat loss and 
fragmentation may be happening on private lands, but that its effect on 
Ozark chinquapin is minimal due to widespread distribution and vast 
amounts of contiguous habitats afforded the species on State and 
Federal lands. Forest composition and structure conversions have 
occurred throughout the species' range, but despite these changes, 
Ozark chinquapin remains common throughout its historical distribution 
in the Interior Highlands. Additionally, current forest management 
efforts, particularly on State and Federal lands, favor Ozark 
chinquapin persistence in this region. Fire management was the last 
threat we evaluated. Fire plays a vital role in the management of Ozark 
chinquapin by maintaining open habitat, encouraging both seed 
germination and vegetative regeneration. While fire may injure or kill 
individuals, long-term effects on sustaining viable populations is 
beneficial.
    Based on our review of the best available scientific and commercial 
information, we conclude that the Ozark chinquapin is not threatened by 
the present or threatened destruction, modification, or curtailment of 
its habitat or range now or in the foreseeable future. Additionally, 
for these reasons, we conclude that alterations to forest composition 
and structure and forest and fire management do not pose an imminent 
threat to Ozark chinquapin now or in the foreseeable future.

Factor B. Overutilization for Commercial, Recreational, Scientific, or 
Educational Purposes

    We do not have any evidence of risks to the Ozark chinquapin from 
overutilization for commercial, recreational, scientific, or 
educational purposes, and we have no reason to believe this factor will 
become a threat to the species in the future. Therefore, based on a 
review of the best available scientific and commercial information, we 
find that overutilization for commercial, recreational, scientific, or 
educational purposes is not a threat to Ozark chinquapin now or in the 
foreseeable future.

Factor C. Disease or Predation

    Under Factor C, we evaluated the following diseases: ink disease 
(Phytopthera cinnamomi) and chestnut blight (Cryphonectria parasitica). 
We do not have any information to indicate that any other disease or 
that predation poses a threat to Ozark chinquapin at this time.

Ink Disease

    Ink disease, caused by the fungus Phytopthora cinnamomi, is known 
to attack the root systems of all North American Castanea species. It 
has been present in the southeast United States for over a century. The 
pathogen is slow spreading. Phytopthora cinnamomi spores spread through 
groundwater, and thus are most prevalent in low-lying areas. The 
pathogen also appears to be restricted to relatively warm temperatures 
(generally south of Philadelphia, PA) and heavier soils (Paillet 2010, 
pers. comm.). The relatively coarse sandstone and chert loam upland 
soils where Ozark chinquapin thrives may be too well drained for the 
pathogen (Paillet 2010, pers. comm.). For these reasons, we conclude 
that ink disease does not pose an imminent threat to Ozark chinquapin 
now or in the foreseeable future.
Chestnut Blight
    Chestnut blight, caused by the fungal parasite Cryphonectria 
(formerly Endothia) parasitica, attacks the stems of all North American 
Castanea species, but is not directly pathogenic to the root system. 
Castanea species evolved in

[[Page 37712]]

North America with little or no resistance to chestnut blight, due to 
isolation from the Asiatic Castanea species, which evolved with this 
parasitic fungus and developed some resistance (Anagnostakis 1982 p. 
466). The chestnut blight was first found in Castanea dentata (American 
chestnut; 1904). Over a period of approximately 20 years, the blight 
spread throughout the range of the American chestnut, reducing this 
important forest tree to a shrub or small tree. The fungus enters 
wounds in the bark and grows under the bark, eventually killing the 
cambium (a layer of living cells, between the bark and hardwood, that 
each year produces additional wood and bark cells) encircling the 
infected area. This results in top-kill of the tree (above the ground). 
After top-kill, sprouts develop at the base of the tree from dormant 
buds. These sprouts grow, become infected, and die, and the process is 
repeated (Anagnostakis 2000, p. 1). Chestnut blight is widely 
recognized as the dominant threat to Ozark chinquapin. The blight's 
effect on Ozark chinquapin was first noted in the 1940s (Tucker 1983, 
p. 7). However, while there is an abundance of scientific literature 
addressing the effects of chestnut blight on the American chestnut, 
literature addressing its effects on Ozark chinquapin specifically is 
very limited. There are clearly a number of similarities in the current 
status of the two species (Paillet 2010, pers. comm.). The long-term 
threat posed to both species is that: (1) Trees survive by avoiding 
chestnut blight, so there is little selective pressure to generate 
blight resistance; and (2) chestnut blight severely restricts 
reproduction (cross pollination and seed production), which may serve 
as resistance genes through normal cross breeding species that are not 
self fertile.
    The ability of Ozark chinquapin to produce a mast crop after 4 to 5 
years of age increases the likelihood of cross pollination (fertile 
individuals) and subsequent seed production. This allows for a 
significant but short lived pulse of cross pollination and seed 
production in the decade following a release response (release of seeds 
and pollination) (Paillet 2010, pers. comm.). Although most Ozark 
chinquapin specimens now found are infertile multi-stemmed understory 
shrubs due to chestnut blight, it is not exceedingly rare to find 
fertile specimens in a variety of Arkansas habitats or to find young 
specimens with single trunks and no evidence of chestnut blight-killed 
older trunks, indicating recent seed production (ANHC 2010, pers. 
comm.). In one Arkansas locality, the sprouts produced seeds within a 
few years of release (Paillet, 1993, p. 267). This indicates there is 
some level of reproduction (cross pollination and subsequent seed 
production and germination) (ANHC 2010, pers. comm.), albeit degraded 
by chestnut blight (Tucker, 1983, pp. 9, 16).
    Ozark chinquapin, like American chestnut, also has suppressed 
sprout clumps that reside on the forest floor. Almost all sprout clumps 
represent ``old seedlings'' that never grew to tree size. Many of these 
suppressed Ozark chinquapin sprouts are small and inconspicuous, 
escaping notice by the casual observer (Paillet 2010, pers. comm.). 
Nibbs (1983 in Paillet 2002, p. 1527) showed that suppressed seedlings 
of several New England tree species are capable of sprouting and that 
sprouts from seedlings established before tree harvest were more 
successful in regenerating forests in Massachusetts than were either 
stump sprouts or new seedlings. Much of the adaptive character of 
American chestnut as an understory shrub applies as well to Ozark 
chinquapin.
    The Ozark-St. Francis National Forest, Wedington Unit, is involved 
in a detailed reconstruction of Ozark chinquapin in the pre-chestnut 
blight forests of northwest Arkansas. Although in modern forests we 
think of Ozark chinquapin growing in clumps of sprouts, most of the 
original trees had a single, upright dominant trunk. Most of these 
original trees did not survive by resprouting. Most surviving Ozark 
chinquapin sprouts, as in the case of the American chestnut, represent 
``old seedlings.'' This may represent an extreme case of a reproductive 
strategy based on advanced regeneration (Paillet 2010, pers. comm.), 
but limited information is available to support or refute this 
hypothesis.
    An understanding of adaptive genetic differentiation among 
populations is of primary importance in the conservation of Castanea 
species in North America (Dane and Hawkins 1999, p. 2). Stillwell et 
al. (2003, pp. 3-4) discuss several effects to the American chestnuts 
as a consequence of chestnut blight, including ecological changes and 
the diminished importance of cross pollination, seed production, and 
germination on the amount and distribution of genetic diversity in the 
species. First, the chestnut blight significantly alters the ecology of 
American chestnut, which may reduce the overall level of genetic 
diversity. Secondly, chestnut blight may affect the distribution of 
genetic variance within and among populations. This could occur by 
genetic drift from the reduced population size or from the vegetative 
expansion of root collars, both of which would tend to diminish genetic 
variance within patches.
    Dane and Hawkins (1999) characterize the genetic diversity within 
and between populations of the Ozark chinquapin to provide an 
understanding of overall genetic composition and its relationship to 
the vulnerability of the species to chestnut blight. The proportion of 
genetic diversity found among the studied Ozark chinquapin populations 
was slightly greater than that observed for other Castanea species, 
other long-lived perennial species, wind-outcrossing (to cross-
pollinate (reproduce) by wind dispersal) species, and late-successional 
species (Hamrick and Godt 1996 in Dane and Hawkins 1999, p. 8). ANHC 
(1996, p. 5) also found similar results in four Arkansas Ozark 
chinquapin populations, although the amount of genetic diversity found 
among the populations was very low. They reported a high level of 
heterozygosity within populations that may have been the result of tree 
recovery in clear-cut areas following the incidence of chestnut blight. 
Dane et al. (2003, p. 319) found high genetic diversity in the more 
narrowly distributed Ozark chinquapin, similar to that in regionally 
distributed Castanea pumila var. pumila (Allegheny chinquapin). While 
Fu and Dane (2003, pp. 228-229) found that genetic diversity in 
Allegheny chinquapin was much higher than that observed in the American 
chestnut, which is geographically sympatric (Johnson 1988, p. 42), and 
is similar to that of the closely related Ozark chinquapin. The greater 
level of genetic diversity in Ozark chinquapin may be related to its 
origin as it is less evolved than the more common Allegheny chinquapin 
as evidenced by its lack of stoloniferous (producing stolons; putting 
forth suckers) growth (an adaptation for survival in early successional 
stages and areas with low soil fertility), its arborescent (having the 
size, form, or characteristics of a tree) habit, and other habitat 
requirements (Dane and Hawkins 1999, p. 8).
    There are high levels of outcrossing and gene flow among Ozark 
chinquapin populations. Indirect estimates of outcrossing rates suggest 
that most populations are highly outcrossed (Dane and Hawkins 1999, p. 
9). Johnson (1988, pp. 37-40) found the Castanea species to be mainly 
wind-pollinated, and detected infrequent occurrences of self-
compatibility and apomixis (reproduction without meiosis (the process 
of cell division in sexually reproducing organisms that reduces the

[[Page 37713]]

number of chromosomes) or formation of gametes (eggs)).
    Knowles and Grant (1981, p. 4, in Stillwell et al. 2003) and Mitton 
and Grant (1980, p. 4, in Stillwell et al. 2003) present contrasting 
information on long-lived trees and the general perception that more 
heterozygous individuals are less variable and better adapted in 
fluctuating environments. Stillwell et al. (2003, pp. 9-11) suggest 
that the chestnut blight has had significant effects on the genetics of 
American chestnut populations. They found that a slight growth 
advantage for heterozygous genotypes has resulted in a profound excess 
of heterozygotes within populations. Studies of different age classes 
(seeds, seedlings, and stands of differing ages) show an increase in 
heterozygosity with increasing age within other tree species. The 
difference observed by Stillwell et al. (2003, pp. 9-11) is that all 
extant American chestnut genotypes are more than 70 years old and many 
that succumbed to the blight as mature canopy trees are much older. 
Therefore, as selection favors a population of heterozygous 
individuals, there are no new recruits to restore the population toward 
Hardy-Weinberg equilibrium (a constant state of genetic variation in a 
population from one generation to the next in the absence of 
disturbance). Prolonged absence of cross pollination and subsequent new 
recruitment from seed germination in the American chestnut has resulted 
in a change in population genetics, yet it is not well documented 
whether these same effects have resulted in similar changes to 
population genetics of the Ozark chinquapin due to its ability to 
produce mast crops before succumbing to chestnut blight.
    The high mortality of American chestnut stems in conjunction with 
near total elimination of reproduction through cross pollination could 
have resulted in the loss of some (mostly rare) alleles (one of two or 
more alternative forms of a gene that arise by mutation and are found 
at the same place on a chromosome) (Loveless and Hamrick 1984; Leberg 
1992 in Stillwell et al. 2003, pp. 207-213). It is not clear; however, 
whether this slightly lower genetic diversity is a result of the 
chestnut blight epidemic. Huang et al. (1998, pp. 1015-1019) suggested 
that the low genetic diversity of the American chestnut resulted in the 
high susceptibility to attack by blight, rather than that the low 
genetic diversity was a direct consequence of the blight pandemic, and 
that other Castanea species with more diverse allozyme variation are 
less susceptible to epidemics. In the absence of knowledge of pre-
blight genetic population structure, it is difficult to make any 
definitive statement on changes in genetic diversity due to the 
chestnut blight pandemic (Stillwell et al. 2003, p. 10).
    Grenate (1965 in Anagnostakis 1987 p. 27) isolated forms of the 
chestnut blight fungus that had a different appearance and reduced 
virulence in Castanea species infected by chestnut blight in Italy. 
Hypovirulence is a disease, or a group of diseases, that affect the 
chestnut blight, reducing the ability of the blight to kill susceptible 
Castanea tree hosts (Van Alfen et al. 1975 in Anagnostakis 1987 p. 28). 
Hypovirulence is controlled by genetic determinants in the cytoplasm of 
the fungus (Day et al. 1977 in Anagnostakis 1987 p. 28). These 
hypovirulent forms cured existing blight when they were inoculated into 
cankers of infected trees. Due to successes achieved with hypovirulent 
strains in Europe, research and conservation efforts began in the early 
1970s with the American chestnut (Anagnostakis 1987 pp. 32-33) and 
continue at present with the Ozark chinquapin. Full restoration of the 
Ozark chinquapin may prove complicated and might require establishment 
of a backcross breeding program designed to transfer the blight 
resistance of Castanea henryi (Chinese chinquapin) (Dane and Hawkins 
1999, p. 9). Similar efforts are ongoing to discover hypovirulent forms 
or founder (fall in or give way; collapse) trees with natural chestnut 
blight resistance in Ozark chinquapin, although there is preference 
towards the latter (Ozark Chinquapin Foundation 2010, pers. comm.).
    Success at bringing chestnut blight into balance in Europe (Italy 
and France) demonstrates that the fungus might be controlled in North 
America (Anagnostakis 1987 p. 33). Brewer (1995, pp. 54-55) found that 
certain ecological factors may explain differential success of 
hypovirulence in different Michigan soil types: (1) American chestnut 
has a better competitive advantage on well-drained sandy soils, (2) 
hypovirulence originates from sandy textured hypovirulence originates 
soils, and (3) sandy textured soils provide more dispersing agents for 
hypovirulent strains. While it remains unclear how important each of 
these factors is in the hypovirulence phenomenon and how chestnut 
blight, double-stranded RNA, and American chestnut interact, it should 
enable researchers, foresters, and conservationists the opportunity to 
better assess hypovirulence as a biological control that also may favor 
restoration of Ozark chinquapin populations.
    Despite the shift in reproductive strategy (seed production/
germination versus vegetative regeneration) and a shorter life span for 
the stems, chestnut blight has not affected the distribution and 
abundance of Ozark chinquapin in the Interior Highlands of Arkansas, 
Missouri, and Oklahoma (see ``Distribution''). Tucker (1983, p. 25) 
states that chestnut blight is responsible for the mortality of extant 
reproductive populations (those capable of cross pollination and seed 
production), reducing populations to primarily reproduction via 
regeneration, and that populations capable of cross pollination and 
seed production are increasingly rare. However, there are numerous 
references in the scientific literature and from personal 
communications with agencies and conservation groups actively involved 
in the conservation of Ozark chinquapin that indicate that this species 
is adapted to and capable of producing mast crops annually in areas 
with active management (such as forest management and prescribed fire) 
(Paillet 1993, p. 267; Paillet 2002, p. 1528; Paillet 2010, pers. 
comm.; ANHC 2010, pers. comm.; USFS 2010, pers. comm.; Ozark Chinquapin 
Foundation 2010, pers. comm.; Missouri Department of Natural Resources 
2010, pers. comm.). While not done as extensively as for American 
chestnut, genetic studies indicate that Ozark chinquapin has greater 
genetic diversity than American chestnut and similar genetic diversity 
to Allegheny chinquapin, both of which are more geographically 
widespread than Ozark chinquapin (Dane and Hawkins 1999, p. 2-9; 
Stillwell et al. 2003, pp. 3-11; ANHC 1996, p. 5; Dane et al. 2003, p. 
319; Fu and Dane 2003, pp. 228-229; Huang et al. 1998, pp. 1015-1019). 
The greater level of genetic diversity in Ozark chinquapin may be 
related to evolutionary adaptations for survival in early successional 
stages and areas with low soil fertility, its arborescent habit, and 
other habitat requirements (Dane and Hawkins 1999, p. 8). Thus, 
information available does not indicate that chestnut blight has 
resulted in a loss of genetic diversity for Ozark chinquapin. While the 
ecological demise of Castanea species is well documented in scientific 
literature, the seemingly endless cycle of sprouting (regeneration) and 
reinfection has continued in American chestnut, as well as Ozark 
chinquapin, unabated to present day (over 100 years in the former 
species and 70 years in the latter) (Anagnostakis and Hillman undated, 
pp. 6-7). Success at bringing chestnut blight

[[Page 37714]]

into balance in Europe (Italy and France) with hypovirulence 
demonstrates that the fungus might be controlled in North America 
(Anagnostakis 1987 p. 33). Moreover, similar hypo virulent efforts as 
those taking place in Europe are ongoing with Ozark chinquapin (Ozark 
Chinquapin Foundation, 2010 pers. comm.).
Summary of Factor C
    Ink disease does not pose an imminent threat now or in the 
foreseeable future to the continued existence of extant Ozark 
chinquapin populations; however, chestnut blight has posed a long-term, 
imminent threat to mature Ozark chinquapins for the past 70 years and 
will for the foreseeable future. However, chestnut blight does not 
threaten the continued existence of Ozark chinquapin at this time or in 
the foreseeable future. Our conclusion is based on the following: (1) 
The documented widespread distribution and abundance of Ozark 
chinquapin is more complex than the picture presented by chestnut 
blight alone and may represent combined effects of changes in 
disturbance regime, climate, and land use history that extend over a 
prolonged period (post-glacial history) in the region; (2) it is well 
documented that the Ozark chinquapin remains widespread and abundant 
within the Interior Highlands; and (3) due to the life history traits 
of Ozark Chinquapin, it appears that cross pollination and production 
of seeds, while rare, does occur, which may allow for a significant, 
albeit greatly diminished, short pulse of seed production and 
germination in the decade after a disturbance (release) response. Based 
on our review of the best available scientific and commercial 
information, we conclude that the Ozark chinquapin is not threatened by 
the disease or predation now or in the foreseeable future.

D. Inadequacy of Existing Regulatory Mechanisms

    The majority of Ozark chinquapin populations occur on public land. 
Populations that occur on these lands are protected by State and 
Federal laws and regulations.
Federal Regulations and Management
    The NPS, under its National Park Service Organic Act (16 U.S.C. 1 
et seq.), is responsible for managing the National Parks to conserve 
the scenery and the natural and historic objects and the wildlife (see 
``Distribution'' section and Factor A, for National Parks with extant 
Ozark chinquapin populations) found on the parks. The National Parks 
Omnibus Management Act of 1998 (16 U.S.C. 5934 et seq.) requires the 
NPS to inventory and monitor its natural resources. NPS has implemented 
its resource management responsibilities through its Management 
Policies, Section 4.4, which states that the NPS ``will maintain as 
parts of the natural ecosystems of parks all plants and animals native 
to park ecosystems.'' Section 207 of the Omnibus Management Act of 1998 
allows NPS to withhold from the public any information related to the 
nature and specific location of endangered, threatened, or rare species 
unless disclosure would not create an unreasonable risk of harm to the 
species.
    Hot Springs National Park (HSNP) does not specifically manage for 
Ozark chinquapin. HSNP's current General Management Plan (GMP) was 
approved in the 1980s and did not specifically address the Ozark 
chinquapin. However, HSNP does manage for the entire ecosystem that 
includes the Ozark chinquapin. For instance, in May 2005, HSNP 
abandoned its practice of total fire suppression regardless of ignition 
source and has since utilized fire as an ecosystem restoration tool on 
Sugarloaf Mountain (the only site in the park with an extant population 
of Ozark chinquapin). As a result of the new fire regime, young Ozark 
chinquapin sprouts have responded favorably at sites with suitable 
habitat. Furthermore, HSNP is currently in the process of developing a 
new GMP, which will incorporate ecosystem restoration that will prove 
valuable to Ozark chinquapin restoration at HSNP, with expertise from 
other agencies and researchers (for example, USFS Southeast Research 
Station; S. Rudd, NPS, pers. comm. 2011). Similarly, Pea Ridge National 
Military Park does not currently have a GMP that specifically addresses 
the conservation needs of Ozark chinquapin, but it actively utilizes 
fire as an ecosystem restoration tool (K. Eads, NPS, pers. comm. 2011).
    Finally, Buffalo National River (BNR) is developing a predictive 
geographic information system (map) model based on soil types and 
aspects associated with Ozark chinquapin populations at BNR. This work 
also includes a better delineation (survey) of Ozark chinquapin 
populations to aid in a better understanding of its health and spatial 
distribution, important modeling parameters. This information will be 
available in summer 2011 and will further help guide Ozark chinquapin 
habitat restoration efforts at BNR. BNR also began work in 2009 with an 
arborist to gather seeds from trees at BNR seemingly unaffected by 
chestnut blight for propagation (B. Wilson, NPS, pers. comm. 2011).
    Ozark chinquapin is currently designated as a USFS sensitive 
species (see Distribution section and Factor A for USFS lands with 
extant Ozark chinquapin populations). The National Forest Management 
Act of 1976 (16 U.S.C. 1600 et seq.) specifies guidelines for land 
management plans developed to achieve goals that include protection of 
sensitive species. USFS Manual 2670, Threatened, Endangered and 
Sensitive Plants and Animals, sections 22 and 32, requires the USFS to 
develop and implement management practices that ensure that sensitive 
species do not become threatened or endangered due to USFS actions. 
Factor A of this finding discusses some vegetative monitoring and 
management activities which include the Ozark chinquapin that are 
conducted and controlled by the USFS.
State Regulations and Management
    Additionally, the Ozark chinquapin currently receives protection on 
State park and natural heritage owned lands (see Distribution section 
and Factor A) in Arkansas, Missouri, and Oklahoma. State parks in 
Missouri, similar to Arkansas and Oklahoma, are acquired and managed to 
protect a well-balanced system of areas with outstanding scenic, 
recreational, and historic significance (10 CSR 100-1.010). Missouri 
State parks currently track resiliency and recovery of Ozark chinquapin 
with implementation of prescribed fire to manage for ecosystem health 
(such as fire-mediated woodlands that support Ozark chinquapin) and 
monitor distribution with aid from the Natural Heritage Program (A. 
Vaughn, Missouri State Parks, pers. comm. 2010). Arkansas Game and Fish 
Commission (AGFC) has no specific management strategy for Ozark 
chinquapin on Wildlife Management Areas; similar to other State 
properties throughout the species range, they maintain a species list 
for inventory purposes and elements of occurrence and have prescribed 
fire management plans that benefit Ozark chinquapin (M. Blaney, AGFC, 
pers. comm. 2011).
    The ANHC System of Natural Areas provides long-term protection to 
some of Arkansas' most ecologically significant lands. ANHC rules and 
regulations prohibit the collection and/or removal of plants (including 
fruits, nuts, or edible plant parts), animals, fungi, rocks, minerals, 
fossils, archaeological artifacts, soil, downed wood, or any other 
natural material, alive or dead. Natural areas are managed according to 
an established management

[[Page 37715]]

plan and a conservation vision aimed at protecting, enhancing, 
interpreting, and sometimes even restoring the significant ecological 
values present at the site (for example, natural ecosystem health). To 
do this, management plans for areas within the system are prepared and 
updated regularly to set the frameworks for future management 
activities. ANHC no longer tracks Ozark chinquapin as a State species 
of concern, due to its widespread distribution and local abundance in 
Arkansas (C. Colclasure, ANHC, pers. comm. 2010 and T. Witsell, ANHC, 
pers. comm. 2011).
Summary of Factor D
    In summary, we do not consider the inadequacy of existing 
regulatory mechanisms to be a threat to the populations of Ozark 
Chinquapin in the national forests and parks and State parks and 
natural areas in Arkansas, Missouri, and Oklahoma. The regulatory 
mechanisms discussed above allow the Federal and State agencies to 
prevent collection or take of Ozark chinquapin and implement management 
practices to ensure long-term population viability and promote natural 
ecosystem restoration and health on public property. Furthermore, we do 
not consider development outside these Federal and State lands to be a 
threat to Ozark chinquapin populations within these Federal lands. 
Therefore, based on a review of the available information, we find that 
inadequacy of existing regulatory mechanisms is not a threat to Ozark 
chinquapin now or in the foreseeable future.

E. Other Natural or Manmade Factors Affecting the Species' Continued 
Existence

Climate Change
    Habitat is dynamic, and species may move from one area to another 
over time. Climate change will be a particular challenge for 
biodiversity, because the interaction of additional stressors 
associated with climate change and current stressors may push species 
beyond their ability to survive (Lovejoy 2005, pp. 325-326). The 
synergistic (combined or cooperative action or force) implications of 
climate change and habitat fragmentation are the most threatening facet 
of climate change for biodiversity (Hannah et al. 2005, p. 4). Current 
climate change predictions for terrestrial areas in the Northern 
Hemisphere indicate warmer air temperatures, more intense precipitation 
events, and increased summer continental drying (Field et al. 1999, pp. 
1-3; Hayhoe et al. 2004, p. 12422; Cayan et al. 2005, p. 6; 
Intergovernmental Panel on Climate Change (IPCC) 2007, p. 1181). 
Climate change may lead to increased frequency and duration of severe 
storms and droughts (Golladay et al. 2004, p. 504; McLaughlin et al. 
2002, p. 6074; Cook et al. 2004, p. 1015). According to the Arkansas 
Statewide Forest Resource Assessment (2010, p. 68), the U.S. Department 
of Agriculture concluded that specie