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

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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 http://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: http://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 http://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

Relay Service (FIRS) at 800-877-8339.

SUPPLEMENTARY INFORMATION:

Executive Summary

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

ed 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)

tivities, 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

• 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

existing threats across the landscape.

• 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.

• 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

ja 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 be

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.

ae 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 http://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, http://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

Public Hearing

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

f 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

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)

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)

lora 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 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).

876; 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

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

rd 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

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

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

e 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.

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.)

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

fornia 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.

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) A: Nonnative, Fire; E: Fire, Climate, Genetic Low Military Value; Area Recently Closed. Horse Beach Canyon EO 3; 48 PLs Unknown Presumed Extant (Junak 2005) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate, Genetic High Military Value; Area Closed. Lower China Canyon EO 1; 9 PLs Extant; 1975 herbarium record Presumed Extant (Junak 1997, SERG 2009) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate, Genetic High Military Value; Area Closed. Upper China Canyon (including Upper Horse Beach Canyon) No EO; 4 PLs Extant; 1975 herbarium record Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate, Genetic Low Military Value. Cave Canyon (including Kinkipar Canyon) No EO; 27 PLs Unknown Extant (SERG 2010) A: Nonnative, Fire; E: Fire, Climate, Genetic Medium Military Value. Chukit Canyon 2 PLs Unknown Extant (Junak 2004) A: Nonnative, Fire; E: Fire, Climate, Genetic Low Military Value

record Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate, Genetic Low Military Value. Cave Canyon (including Kinkipar Canyon) No EO; 27 PLs Unknown Extant (SERG 2010) A: Nonnative, Fire; E: Fire, Climate, Genetic Medium Military Value. Chukit Canyon 2 PLs Unknown Extant (Junak 2004) A: Nonnative, Fire; E: Fire, Climate, Genetic Low Military Value. Lemon Tank Canyon EO 2 Extant; 1923 herbarium record Presumed Extant (CNDDB 1996) A: Land Use, Erosion, Nonnative; E: Movement, Climate, Genetic Low Military Value; Area Closed. Box Canyon EO 4; 9 PLs Unknown Extant (SERG 2009) A: Nonnative; E: Climate, Genetic Low Military Value. Norton Canyon EO 7; 27 PLs Unknown Extant—(SERG 2011) A: Nonnative; E: Climate, Genetic Low Military Value. Middle Ranch Canyon EO 5; 5 PLs Unknown Extant (SERG 2008) A: Erosion, Nonnative; E: Climate, Genetic Low Military Value. Waymuck Canyon EO 6; 1 PL Unknown Presumed Extant (CNDDB 1985) A: Erosion, Nonnative; E: Climate, Genetic High Military Value. Acmispon dendroideus var. traskiae Eagle Canyon EO 1, 9 PLs Extant; 1980 CNDDB Extant (Junak 2006, SERG 2008) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Recently Closed. Bryce Canyon No EO, 14 PLs Unknown Extant (SERG 2009) A: Nonnative, Fire; : Fire, Climate Low Military Value; Area Recently Closed. North Mosquito Cove EO 8, 14 PLs Extant; 1939 herbarium record Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Recently Closed. Canchalagua Canyon (including south Mosquito Cove) EO 4, 21 PLs Unknown Extant (SERG 2011) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Recently Closed. Thirst Canyon (including Vista Canyon) No EO, 8 PLs Unknown Extant (SERG 2009) A: Nonnative, Fire; E: Fire, Climate Medium Military Value. Cave Canyon No EO, 3 PLs Unknown Presumed Extant (Junak 1997) A: Nonnative, Fire; E: Fire, Climate Medium Military Value

1 PLs Unknown Extant (SERG 2011) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Recently Closed. Thirst Canyon (including Vista Canyon) No EO, 8 PLs Unknown Extant (SERG 2009) A: Nonnative, Fire; E: Fire, Climate Medium Military Value. Cave Canyon No EO, 3 PLs Unknown Presumed Extant (Junak 1997) A: Nonnative, Fire; E: Fire, Climate Medium Military Value. Horse Canyon No EO, 2 PLs Unknown Presumed Extant (Junak 1997) A: Nonnative, Fire; E: Fire, Climate Medium Military Value. Pyramid Head EO 5, 1 PL Extant; 1979 CNDDB Presumed Extant (Junak 1997) A: Nonnative, Fire; E: Fire, Climate High Military Value; Area Closed. SHOBA Boundary (north to Twin Dams Canyon) No EO, 8 PLs Unknown Presumed Extant (Junak 1996) A: Nonnative; E: Climate Medium Military Value. Twin Dams Canyon No EO, 2 PLs Unknown Extant (Junak 2006) A: Nonnative; E: Climate Medium Military Value. Horton Canyon (including Stone, Burn's, and Horton Canyons) EO 13, 27 PLs Unknown Extant (SERG 2010) A: Erosion, Nonnative; E: Climate Medium Military Value. Tota Canyon No EO, 7 PLs Unknown Presumed Extant (SERG 2010) A: Erosion, Nonnative; E: Climate Low Military Value. Lemon Tank Canyon (including Nanny Canyon) No EO, 19 PLs Unknown Extant (Junak 2004) A: Erosion, Nonnative; E: Movement, Climate Low Military Value; Area Partially Closed. Larkspur Canyon EO 16, 2 PLs Unknown Extant (SERG 2011) A: Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value. Chamish Canyon EO 3, 1 PL Extant; 1980 CNDDB Presumed Extant (Junak 1997) A: Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value. Box Canyon No EO, 2 PLs Unknown Presumed Extant (Junak 1997) A: Nonnative; E: Climate Low Military Value. Norton Canyon No EO, 1 PL Unknown Extant (Junak 2004) A: Nonnative; E: Climate, Hybridization Low Military Value. Upper Middle Ranch Canyon EO 10, 5 PLs Unknown Extant (Junak 2004) A: Erosion, Nonnative; E: Climate Low Military Value

native, Fire; E: Movement, Fire, Climate Low Military Value. Box Canyon No EO, 2 PLs Unknown Presumed Extant (Junak 1997) A: Nonnative; E: Climate Low Military Value. Norton Canyon No EO, 1 PL Unknown Extant (Junak 2004) A: Nonnative; E: Climate, Hybridization Low Military Value. Upper Middle Ranch Canyon EO 10, 5 PLs Unknown Extant (Junak 2004) A: Erosion, Nonnative; E: Climate Low Military Value. Lower Middle Ranch Canyon No EO, 3 PLs Unknown Extant (SERG 2008) A: Nonnative; E: Climate Low Military Value. Waymuck Canyon No EO, 4 PLs Unknown Extant (SERG 2011) A: Nonnative; E: Climate High Military Value. Warren Canyon EO 12, 20 PLs Unknown Extant (SERG 2011) A: Erosion, Nonnative; E: Movement, Climate High Military Value. Middle Wallrock Canyon No EO, 10 PLs Unknown Extant (Junak 2004) A: Nonnative; E: Movement, Climate High Military Value. Upper Wallrock Canyon No EO, 3 PLs Unknown Extant (Junak 2006) A: Erosion, Nonnative; E: Climate High Military Value. Seal Cove Terraces No EO, 3 PLs Unknown Extant (Junak 2004) A: Erosion, Nonnative, Fire; E: Movement, Fire, Climate High Military Value. Eel Cove Canyon (including terraces) EO 14, 6 PLs Unknown Extant (SERG 2010) A: Erosion, Nonnative, Fire; E: Movement, Fire, Climate High Military Value. Middle Island Plateau EO 7, 6 PLs Unknown Extant (Tierra Data 2007) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate High Military Value. Wilson Cove EO 11, 52 PLs Extant; 1981 CNDDB Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate, Hybridization High Military Value. North Wilson Cove EO 9, no PLs Extant; 1959 herbarium record Unknown A: Erosion, Nonnative; E: Climate High Military Value. North Island Terraces EO 15, no PLs Unknown Presumed Extant (CNDDB 1996) A: Erosion, Nonnative; E: Movement, Climate Medium Military Value. Castilleja grisea Thirst Canyon (including Vista Canyon) EO 10, 11 & 40; 21 PLs Extant; 1980 CNDDB Extant (SERG 2010) A: Nonnative, Fire; E: Climate Medium Military Value

ant; 1959 herbarium record Unknown A: Erosion, Nonnative; E: Climate High Military Value. North Island Terraces EO 15, no PLs Unknown Presumed Extant (CNDDB 1996) A: Erosion, Nonnative; E: Movement, Climate Medium Military Value. Castilleja grisea Thirst Canyon (including Vista Canyon) EO 10, 11 & 40; 21 PLs Extant; 1980 CNDDB Extant (SERG 2010) A: Nonnative, Fire; E: Climate Medium Military Value. Eagle Canyon (including Grove Canyon) EO 7 & 30; 50 PLs Extant; 1979 herbarium record Extant (Tierra Data 2006) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Climate Low Military Value; Area Recently Closed. Bryce Canyon EO 3, 8 & 47; 43 PLs Extant; 1979 GIS data Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Climate Low Military Value; Area Recently Closed. Canchalagua Canyon (including south Mosquito Cove and Matriarch Canyon) EO 4 & 27; 56 PLs Extant; 1963 herbarium record Extant (SERG 2011) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Climate Low Military Value; Area Recently Closed. Knob Canyon EO 2 & 49; 21 PLs Extant; 1979 CNDDB Extant (Tierra Data 2006, SERG 2008) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Climate Low Military Value; Area Recently Closed. Pyramid Head EO 1 & 15; 25 PLs Extant; 1965 herbarium record Extant (SERG 2011) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Climate High Military Value; Partially Recently Closed. Snake Canyon (including Sun Point) EO 23; 4 PLs Extant; 1939 CNDDB Presumed Extant (Junak 1997) A: Nonnative, Fire; E: Fire, Climate High Military Value; Area Closed. Upper Chenetti Canyon EO 34; 1 PL Unknown Extant (Junak 2004) A: Nonnative, Erosion, Fire, Fire Management; E: Fire, Climate High Military Value; Area Closed. Horse Beach Canyon EO 33 & 35; 49 PLs Extant; 1939 herbarium record Presumed Extant (Junak 2005) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate High Military Value; Area Closed

Military Value; Area Closed. Upper Chenetti Canyon EO 34; 1 PL Unknown Extant (Junak 2004) A: Nonnative, Erosion, Fire, Fire Management; E: Fire, Climate High Military Value; Area Closed. Horse Beach Canyon EO 33 & 35; 49 PLs Extant; 1939 herbarium record Presumed Extant (Junak 2005) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate High Military Value; Area Closed. China Canyon EO 25, 37 & 46; 6 PLs Extant; 1939 herbarium record Presumed Extant (Junak 1997; SERG 2009) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate High Military Value; Area Closed. Red Canyon EO 36; no PLs Extant; 1975 herbarium record Presumed Extant (CNDDB 1986) A: Land Use, Erosion, Nonnative, Fire, Fire Management; E: Movement, Fire, Climate High Military Value; Area Closed. Kinkipar Canyon No EO; 2 PLs Unknown Extant (SERG 2006) A: Nonnative, Fire; E: Climate Medium Military Value. Cave Canyon EO 17, 18 & 45; 9 PLs Extant; 1980 CNDDB Extant (SERG 2009) A: Nonnative, Fire; E: Climate Medium Military Value. Horse Canyon No EO; 6 PLs Unknown Extant (SERG 2010) A: Nonnative, Fire; E: Climate Medium Military Value. Upper Horse Canyon EO 19 & 39; 1 PL Extant; 1979 CNDDB Extant (Junak 2004) A: Erosion, Nonnative, Fire; E: Climate Medium Military Value. SHOBA Boundary (north to and including Twin Dams Canyon) EO 31; 55 PLs Extant; 1965 CNDDB Extant (Junak 2006, SERG 2011) A: Nonnative; E: Climate Medium Military Value. Horton Canyon (including Stone and Burn's Canyons) EO 12 & 44; 24 PLs Extant; 1981 CNDDB Extant (Junak 2006, SERG 2010) A: Erosion, Nonnative; E: Climate Medium Military Value. Lemon Tank Canyon (including Tota Canyon) No EO; 14 PLs Unknown Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Closed. Nanny Canyon EO 13; 3 PLs Extant; 1979 CNDDB Extant (Junak 2004) A: Nonnative; E: Movement, Climate Low Military Value; Area Partially Closed

ak 2006, SERG 2010) A: Erosion, Nonnative; E: Climate Medium Military Value. Lemon Tank Canyon (including Tota Canyon) No EO; 14 PLs Unknown Extant (SERG 2010) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value; Area Closed. Nanny Canyon EO 13; 3 PLs Extant; 1979 CNDDB Extant (Junak 2004) A: Nonnative; E: Movement, Climate Low Military Value; Area Partially Closed. Larkspur Canyon (including Chamish Canyon) EO 14 & 48; 15 PLs Extant; 1981 CNDDB Extant (SERG 2006—2011) A: Land Use, Erosion, Nonnative, Fire; E: Movement, Fire, Climate Low Military Value. Box Canyon EO 20 & 41; 22 PLs Extant; 1979 CNDDB Extant (SERG 2011) A: Nonnative; E: Climate Low Military Value. Upper Norton Canyon EO 21; 6 PLs Extant; 1979 CNDDB Extant (SERG 2011) A: Nonnative; E: Climate Low Military Value. Middle Ranch Canyon EO 24; 8 PLs Extant; 1981 CNDDB Extant (SERG 2008) A: Nonnative; E: Climate Low Military Value. Waymuck Canyon EO 22; 1 PL Unknown Extant (Junak 2004) A: Nonnative; E: Climate High Military Value. Plain northeast of Warren Canyon No EO; 4 PLs Unknown Extant (Tierra Data 2007) A: Land Use, Erosion, Nonnative; E: Movement, Climate Medium Military Value. Seal Cove Terraces EO 43; 2 PLs Unknown Extant (CNDDB 1985, SERG 2010) A: Erosion, Nonnative, Fire; E: Movement, Fire, Climate High Military Value. Eel Cove Canyon (including terraces) No EO; 3 PLs Unknown Extant (Junak 2004) A: Nonnative, Fire; E: Movement, Fire, Climate High Military Value. Terrace Canyon (south to terraces around Spray) No EO; 6 PLs Unknown Presumed Extant (SERG 2004) A: Erosion, Nonnative; E: Movement, Climate High Military Value. West Cove No EO; 3 PLs Unknown Extant (Tierra Data 2006) A: Land Use, Erosion, Nonnative; E: Movement, Climate Medium Military Value. 1 EO: element occurrence, as defined and described according to the California Natural Diversity Database. PL: point locations of plants

s around Spray) No EO; 6 PLs Unknown Presumed Extant (SERG 2004) A: Erosion, Nonnative; E: Movement, Climate High Military Value. West Cove No EO; 3 PLs Unknown Extant (Tierra Data 2006) A: Land Use, Erosion, Nonnative; E: Movement, Climate Medium Military Value. 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)

entinus 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

he 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 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 EP16MY12.002

Aerial stems of Malacothamnus clementinus can sprout from spreading underground stems (rhizomes). This makes it difficult to distinguish individual plants among groups of stems

g 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 EP16MY12.002

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 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

e 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).

EP16MY12.003

nyon, Warren Canyon, and North Island Terraces) are partially or wholly within the boundaries of a training area (IOA, TAR, or SWAT).

EP16MY12.003

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

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

ecies 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

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.

BILLING CODE 4310-55-P EP16MY12.004

grisea currently on the island; only 19 of these were known at listing.

BILLING CODE 4310-55-P EP16MY12.004

BILLING CODE 4310-55-C (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 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)

an 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

iculatus (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

e 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

Habitat— Malacothamnus clementinus

Malacothamnus clementinus occurs in a variety of habitats on San Clemente Island

ith 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

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

rt 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

and 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

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

(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 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

ing 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.

ies.

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

nize 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)

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 (F 1 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

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).

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

s 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

y 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

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

t 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

s 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 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

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

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,

nt 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

liminate 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)

onsultation 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

(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)

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

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.

roving 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

nhouse 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

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

and 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

e 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

ness 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.

h 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

eja 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

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

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;

(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

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)

ection 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

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 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

leja 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).

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

currences (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)

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

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 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)

r 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

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)

ed. 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 Mala

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