Endangered and Threatened Wildlife and Plants: Proposed Endangered, Threatened, and Not Warranted Status for Distinct Population Segments of Rockfish in Puget Sound

DEPARTMENT OF COMMERCE National Oceanic and Atmospheric Administration 50 CFR Parts 223 and 224 [Docket No. 080229341-9330-02] RIN 0648-XF89 Endangered and Threatened Wildlife and Plants: Proposed Endangered, Threatened, and Not Warranted Status for Distinct Population Segments of Rockfish in Puget Sound AGENCY:

National Marine Fisheries Service (NMFS), National Oceanic and Atmospheric Administration (NOAA), Commerce.

ACTION:

Proposed rule; 12-month petition finding; request for comments.

SUMMARY:

We, the NMFS, have completed Endangered Species Act (ESA) status reviews for five species of rockfish ( Sebastes spp.) occurring in Puget Sound, Washington, in response to a petition submitted by Mr. Sam Wright of Olympia, Washington, to list these species in Puget Sound as threatened or endangered species. We reviewed best available scientific and commercial information on the status of these five stocks and considered whether they are in danger of extinction throughout all or a significant portion of their ranges, or are likely to become endangered within the foreseeable future throughout all or a significant portion of their ranges. For bocaccio ( S. paucispinis ), we have determined that the members of this species in the Georgia Basin are a distinct population segment (DPS) and are endangered throughout all of their range. We propose to list this bocaccio DPS as endangered. We have determined that yelloweye rockfish ( S. ruberrimus ) and canary rockfish ( S. pinnige r) in the Georgia Basin are DPSs and are likely to become endangered within the foreseeable future throughout all of their range. We propose to list the Georgia Basin DPSs of yelloweye and canary rockfish as threatened. We determined that populations of greenstriped rockfish (S. elongatus) and redstripe rockfish ( S. proriger ) occurring in Puget Sound Proper are DPSs but are not in danger of extinction throughout all or a significant portion of their ranges or likely to become so in the foreseeable future

ll of their range. We propose to list the Georgia Basin DPSs of yelloweye and canary rockfish as threatened. We determined that populations of greenstriped rockfish (S. elongatus) and redstripe rockfish ( S. proriger ) occurring in Puget Sound Proper are DPSs but are not in danger of extinction throughout all or a significant portion of their ranges or likely to become so in the foreseeable future. We find that listing the greenstriped rockfish Puget Sound Proper DPS and the redstripe rockfish Puget Sound Proper DPS is not warranted at this time.

Any protective regulations determined to be necessary and Federal Register notice. We solicit information to inform these listing determinations and the development of proposed protective regulations and designation of critical habitat in the event these species are listed.

DATES:

Comments on this proposal must be received by June 22, 2009. A public hearing will be held promptly if any person so requests by June 8, 2009. Notice of the location and time of any such hearing will be published in the Federal Register not less than 15 days before the hearing is held.

ADDRESSES:

You may submit comments by any of the following methods:

• Federal e-Rulemaking Portal: http://www.regulations.gov . Follow the instructions for submitting comments.

• Mail: Submit written comments to Chief, Protected Resources Division, Northwest Region, National Marine Fisheries Service, 1201 NE Lloyd Blvd., Suite 1100, Portland, OR 97232.

INSTRUCTIONS: All comments received are a part of the public record and will generally be posted to http://www.regulations.gov without change. All Personal Identifying Information (for example, name, address, etc.) voluntarily submitted by the commenter may be publicly accessible. Do not submit Confidential Business Information or otherwise sensitive or protected information. We will accept anonymous comments (enter N/A in the required fields, if you wish to remain anonymous)

erally be posted to http://www.regulations.gov without change. All Personal Identifying Information (for example, name, address, etc.) voluntarily submitted by the commenter may be publicly accessible. Do not submit Confidential Business Information or otherwise sensitive or protected information. We will accept anonymous comments (enter N/A in the required fields, if you wish to remain anonymous). Attachments to electronic comments will be accepted in Microsoft Word, Excel, WordPerfect, or Adobe PDF file formats only. The rockfish petition, draft status report, and other reference materials regarding this determination can be obtained via the Internet at: http://www.nwr.noaa.gov/ or by submitting a request to the Assistant Regional Administrator, Protected Resources Division, Northwest Region, NMFS, 1201 NE Lloyd Blvd., Suite 1100, Portland, OR 97232.

FOR FURTHER INFORMATION CONTACT:

Eric Murray, NMFS, Northwest Region (503) 231-2378; or Dwayne Meadows, NMFS, Office of Protected Resources (301) 713-1401.

SUPPLEMENTARY INFORMATION:

Background

On April 9, 2007, we received a petition from Mr. Sam Wright of Olympia, Washington, to list stocks of bocaccio, canary rockfish, yelloweye rockfish, greenstriped rockfish, and redstripe rockfish in Puget Sound as endangered or threatened species under the ESA and to designate critical habitat. We declined to initiate a review of the species' status under the ESA, finding that the petition failed to present substantial scientific or commercial information to suggest that the petitioned actions may be warranted (72 FR 56986; October 5, 2007). On October 29, 2007, we received a letter from Sam Wright presenting information that was not included in the April 2007 petition, and requesting that we reconsider our October 5, 2007, decision not to initiate a review of the species' status

on failed to present substantial scientific or commercial information to suggest that the petitioned actions may be warranted (72 FR 56986; October 5, 2007). On October 29, 2007, we received a letter from Sam Wright presenting information that was not included in the April 2007 petition, and requesting that we reconsider our October 5, 2007, decision not to initiate a review of the species' status. We considered the supplemental information provided in the letter and the information submitted previously in the April 2007 petition as a new petition to list these species and to designate critical habitat. The supplemental information included additional details on the life histories of bocaccio and greenstriped rockfish supporting the case that individuals of these species occurring in Puget Sound may be unique. There was also additional information on recreational harvest indicating significant declines of rockfish abundance. On March 17, 2008, we provided notice of our determination that the petition presented substantial scientific information indicating that the petitioned action may be warranted and requested information to assist with a status review to determine if these five species of rockfish in Puget Sound warranted listing under the ESA (73 FR 14195). Copies of the April and October 2007 petitions and our October 2007 and March 2008 petition findings are available from NMFS (see ADDRESSES , above).

ESA Statutory, Regulatory, and Policy Provisions

The ESA defines species to include subspecies or a DPS of any vertebrate species which interbreeds when mature (16 U.S.C. 1532(16); 50 CFR 424.02 (k)). The U.S. Fish and Wildlife Service and NMFS have adopted a joint policy describing what constitutes a DPS of a taxonomic species (61 FR 4722; February 7, 1996)

from NMFS (see ADDRESSES , above).

ESA Statutory, Regulatory, and Policy Provisions

The ESA defines species to include subspecies or a DPS of any vertebrate species which interbreeds when mature (16 U.S.C. 1532(16); 50 CFR 424.02 (k)). The U.S. Fish and Wildlife Service and NMFS have adopted a joint policy describing what constitutes a DPS of a taxonomic species (61 FR 4722; February 7, 1996). The joint DPS policy identifies two criteria for making DPS determinations: (1) The population must be discrete in relation to the remainder of the taxon (species or subspecies) to which it belongs; and (2) the population must be significant to the remainder of the taxon to which it belongs.

A population segment of a vertebrate species may be considered discrete if it satisfies either one of the following conditions: (1) “It is markedly separated from other populations of the same taxon as a consequence of physical, physiological, ecological, or behavioral factors. Quantitative measures of genetic or morphological discontinuity may provide evidence of this separation"; or (2) “it is delimited by international governmental boundaries within which differences in control of exploitation, management of habitat, conservation status, or regulatory mechanisms exist that are significant in light of section 4(a)(1)(D)” of the ESA.

If a population segment is found to be discrete under one or both of the above conditions, its biological and ecological significance to the taxon to which it belongs is evaluated

l governmental boundaries within which differences in control of exploitation, management of habitat, conservation status, or regulatory mechanisms exist that are significant in light of section 4(a)(1)(D)” of the ESA.

If a population segment is found to be discrete under one or both of the above conditions, its biological and ecological significance to the taxon to which it belongs is evaluated. This consideration may include, but is not limited to: (1) “persistence of the discrete population segment in an ecological setting unusual or unique for the taxon; (2) evidence that the loss of the discrete population segment would result in a significant gap in the range of a taxon; (3) evidence that the discrete population segment represents the only surviving natural occurrence of a taxon that may be more abundant elsewhere as an introduced population outside its historic range; and (4) evidence that the discrete population segment differs markedly from other populations of the species in its genetic characteristics.”

The ESA defines an endangered species as one that is in danger of extinction throughout all or a significant portion of its range, and a threatened species as one that is likely to become an endangered species in the foreseeable future throughout all or a significant portion of its range (16 U.S.C. 1532 (6) and (20)). The statute requires us to determine whether any species is endangered or threatened because of any of the following factors: the present or threatened destruction of its habitat, overexploitation, disease or predation, the inadequacy of existing regulatory mechanisms, or any other natural or manmade factors (16 U.S.C. 1533). We are to make this determination based solely on the best available scientific information after conducting a review of the status of the species and taking into account any efforts being made by states or foreign governments to protect the species

t, overexploitation, disease or predation, the inadequacy of existing regulatory mechanisms, or any other natural or manmade factors (16 U.S.C. 1533). We are to make this determination based solely on the best available scientific information after conducting a review of the status of the species and taking into account any efforts being made by states or foreign governments to protect the species. The steps we follow in implementing this statutory scheme are to review the status of the species, analyze the threats facing the species, assess whether certain protective efforts mitigate these threats, and then make our best determination about the species' future persistence.

Status Review

To assist in the status review, we formed a Biological Review Team (BRT) comprised of Federal scientists from our Northwest and Southwest Fisheries Science Centers. We also requested

The BRT used structured decision making to guide its consideration of the questions presented. To allow for expressions of the level of uncertainty, the BRT adopted a “likelihood point” method. Each BRT member distributed 10 “likelihood points” among DPS scenarios and risk categories. This approach has been widely used by NMFS BRTs in previous DPS determinations (e.g., Pacific Salmon, Southern Resident Killer Whale). The BRT presented its findings in a draft status review report (hereafter “draft status report”) for the five species of rockfish (Drake et al. , 2008). Information from the draft status report and findings of the BRT inform our proposed determinations.

Distribution and Life-History Traits of Rockfishes

Rockfishes are a diverse group of marine fishes (about 102 species worldwide and at least 72 species in the northeastern Pacific (Kendall, 1991)) and as a group are among the most common of bottom and mid-water dwelling fish on the Pacific coast of North America (Love et al. , 2002)

t and findings of the BRT inform our proposed determinations.

Distribution and Life-History Traits of Rockfishes

Rockfishes are a diverse group of marine fishes (about 102 species worldwide and at least 72 species in the northeastern Pacific (Kendall, 1991)) and as a group are among the most common of bottom and mid-water dwelling fish on the Pacific coast of North America (Love et al. , 2002). Adult rockfish can be the most abundant fish in various coastal benthic habitats, such as kelp forests, rocky reefs, and rocky outcrops in submarine canyons at depths greater than 300 m (980 feet) (Yoklavich, 1998). The life history of rockfishes is different than that of most other bony fishes. Whereas most bony fishes fertilize their eggs externally, fertilization and embryo development in rockfishes is internal, and female rockfish give birth to live larval young. Larvae are found in surface waters and may be distributed over a wide area extending several hundred miles offshore (Love et al. , 2002). Larvae and small juvenile rockfish may remain in open waters for several months. The dispersal potential for larvae varies by species depending on the length of time larvae remain in the pelagic environment (i.e., ''pelagic larval duration'') and the fecundity of females (i.e., the more larval propagules a species produces, the greater the potential that some larvae will be transported long distances). Dispersal potential may also be influenced by the behavior of pre-settlement fish. For example, diel, tidal, or vertical migration can affect dispersal.

Larval rockfish feed on diatoms, dinoflagellates, tintinnids, and cladocerans, and juveniles consume copepods and euphausiids of all life stages (Sumida and Moster, 1984). Survival and subsequent recruitment of young rockfishes exhibit considerable interannual variability (Ralston and Howard, 1995)

vior of pre-settlement fish. For example, diel, tidal, or vertical migration can affect dispersal.

Larval rockfish feed on diatoms, dinoflagellates, tintinnids, and cladocerans, and juveniles consume copepods and euphausiids of all life stages (Sumida and Moster, 1984). Survival and subsequent recruitment of young rockfishes exhibit considerable interannual variability (Ralston and Howard, 1995). Juveniles and subadults may be more common than adults in shallow water and are associated with rocky reefs, kelp canopies, and artificial structures such as piers and oil platforms (Love et al. , 2002). Adults generally move into deeper water as they increase in size and age (Garrison and Miller, 1982; Love, 1996), and many species exhibit strong site fidelity to rocky bottoms and outcrops (Yoklavich et al. , 2000).

Adults eat bottom and mid-water dwelling invertebrates and small fishes, including other species of rockfish associated with kelp beds, rocky reefs, pinnacles, and sharp drop-offs (Love, 1996; Sumida and Moser, 1984). Many species of rockfishes are slow-growing, long-lived (50 140 years; Archibald et al. , 1981), and late maturing (6 12 yrs; Wyllie-Echeverria, 1987).

Environmental History and Features of Puget Sound

Puget Sound is a fjord-like estuary located in northwest Washington State and covers an area of about 2,330 km 2 (900 sq miles), including 4,000 km (2500 miles) of shoreline. Puget Sound is part of a larger inland system, the Georgia Basin, situated between southern Vancouver Island and the mainland coasts of Washington State and British Columbia. This extensive system is a series of interconnected basins separated by shallow sills. Puget Sound can be subdivided into five major basins: (1) North Puget Sound, (2) Main Basin, (3) Whidbey Basin, (4) South Puget Sound, and (5) Hood Canal. In this Notice, we use the term “Puget Sound” or “greater Puget Sound” to refer to these five basins

mainland coasts of Washington State and British Columbia. This extensive system is a series of interconnected basins separated by shallow sills. Puget Sound can be subdivided into five major basins: (1) North Puget Sound, (2) Main Basin, (3) Whidbey Basin, (4) South Puget Sound, and (5) Hood Canal. In this Notice, we use the term “Puget Sound” or “greater Puget Sound” to refer to these five basins. Each of the basins differs in features such as temperature regimes, water residence and circulation, biological conditions, depth profiles and contours, processes, species, and habitats (Drake et al. , 2008). We use the term “Puget Sound Proper” in this Notice to refer to all of these basins except North Puget Sound (Figure 1).

EP23AP09.000

In the Puget Sound system, net seaward outflow in the upper portion of the water column is driven by winter rainfall and summer snowmelt, and net landward inflow of high salinity ocean water occurs in the deeper portion of the water column (Masson, 2002; Thomson, 1994). Shallow sills within Puget Sound substantially reduce the flushing rate of freshwater, sediments, nutrients, contaminants, and many organisms. Concentrations of nutrients (i.e., nitrates and phosphates) are consistently high throughout most of the greater Puget Sound, largely due to the flux of oceanic water into the basin (Harrison et al. , 1994) and input of nutrients from freshwater runoff (Embrey and Inkpen, 1998).

Coastal areas within Puget Sound generally are characterized by high levels of rainfall and river discharge in the winter, while inland mountains are characterized by heavy snowfall in the winter and high snowmelt in late spring and early summer. Puget Sound's shorelines range from rocky sea cliffs to coastal bluffs and river deltas. Most of Puget Sound's shorelines are coastal bluffs, which are composed of erodable gravel, sand, and clay deposited by glaciers over 15,000 years ago (Downing, 1983; Shipman, 2004)

nter, while inland mountains are characterized by heavy snowfall in the winter and high snowmelt in late spring and early summer. Puget Sound's shorelines range from rocky sea cliffs to coastal bluffs and river deltas. Most of Puget Sound's shorelines are coastal bluffs, which are composed of erodable gravel, sand, and clay deposited by glaciers over 15,000 years ago (Downing, 1983; Shipman, 2004). Extensive development of coastal bluffs along the Sound has led to the widespread use of engineered structures designed to protect upland properties, railroads, and roads. These modifications have increased rapidly since the 1970s, with demonstrated negative impacts on the health of the ecosystem (Thom et al. , 1994).

Characteristics of the physical habitat such as depth, substrate, wave exposure, salinity, and gradient largely determine the plants and animals that can use particular areas of Puget Sound and the entire Georgia Basin. Eight major nearshore habitats have been characterized and quantified: rocky reefs, kelp beds, mixed sediment intertidal beaches, saltmarsh, tide flats, subtidal soft sediments, eelgrass beds, and open water/pelagic habitats (Dethier, 1990; Levings and Thom, 1994; NMFS, 2007). The shallow nearshore areas of Puget Sound contain eelgrass and seaweed habitats that support many marine fish and invertebrate populations at some time during their life cycle. Kelp beds and eelgrass meadows cover the largest area; floating kelps are found primarily over hard substrate along the Strait of Juan de Fuca and San Juan Islands, whereas eelgrass beds are estimated to cover 200 km 2 (77 mi 2 ) throughout Puget Sound, with the exception of South Sound (Nearshore Habitat Program, 2001; Mumford, 2007). Other major habitats include subaerial and intertidal wetlands (176 km 2 )(68 mi 2 ), and mudflats and sandflats (246 km 2 )(95 mi 2 )

e found primarily over hard substrate along the Strait of Juan de Fuca and San Juan Islands, whereas eelgrass beds are estimated to cover 200 km 2 (77 mi 2 ) throughout Puget Sound, with the exception of South Sound (Nearshore Habitat Program, 2001; Mumford, 2007). Other major habitats include subaerial and intertidal wetlands (176 km 2 )(68 mi 2 ), and mudflats and sandflats (246 km 2 )(95 mi 2 ). In pelagic areas, the euphotic zone (zone that receives enough light for photosynthesis) extends to about 20 m (66 feet) depth in the relatively clear regions of North Puget Sound, and to 10 m (33 feet) depth in the more turbid waters of the South Sound basin. Most of the bottom of Puget Sound is comprised of soft sediments, ranging from coarse sands to fine silts and clays. Rocky reefs, composed of bedrock or a et al. , 2008).

The human population in the greater Puget Sound region has increased rapidly over the last 2 decades. In 2005, the area housed approximately 4.4 million people, a 25 percent increase from 1991. According to the State Office of Management, the population is expected to grow to 4.7 to 6.1 million residents by 2025 (OFM, 2005).

Freshwater, marine, nearshore, and upland habitats throughout the greater Puget Sound region have been affected by a variety of human activities, including agriculture, heavy industry, timber harvest, and the development of sea ports and residential property (Sound Science, 2007).

Environmental History and Features of the Strait of Georgia

The Strait of Georgia is that portion of the Georgia Basin that lies in Canada (Figure 1). The coastal drainage of the Strait of Georgia is bounded to the west and south by the Olympic and Vancouver Island mountains and to the north and east by the Cascade and Coast mountains. At sea level, the Strait has a mild maritime climate and is dryer than other parts of the coast because of the rain shadow effect of the Olympic and Vancouver Island mountains

Basin that lies in Canada (Figure 1). The coastal drainage of the Strait of Georgia is bounded to the west and south by the Olympic and Vancouver Island mountains and to the north and east by the Cascade and Coast mountains. At sea level, the Strait has a mild maritime climate and is dryer than other parts of the coast because of the rain shadow effect of the Olympic and Vancouver Island mountains.

The Strait of Georgia has a mean depth of 156 m (420 m maximum) and is bounded by narrow passages (Johnstone Strait and Cordero Channel to the north and Haro and Rosario straits to the south) and shallow submerged sills (minimum depth of 68 m (223 feet) to the north and 90 m (295 feet) to the south). The Strait of Georgia covers an area of approximately 6,800 km 2 (2625 sq miles)(Thomson, 1994), is approximately 220 km (137 miles) long, and varies from 18.5 to 55 km (12 to 34 miles) in width (Tully and Dodimead, 1957; Waldichuck, 1957). Both southern and northern approaches to the Strait of Georgia are through a maze of islands and channels, the San Juan and Gulf islands to the south and a series of islands to the north that extend for 240 km (149 miles) to Queen Charlotte Strait (Tully and Dodimead, 1957). Both northern channels (Johnstone Strait and Cordero Channel) are from 1.5 to 3 km (0.9 to 1.9 miles) wide and are effectively two-way tidal falls, in which currents of 22-28 km/hr (12-15 knots) occur at peak flood (Tully and Dodimead, 1957).

Freshwater inflows are dominated by the Fraser River, which accounts for roughly 80 percent of the freshwater entering the Strait of Georgia. Fraser River run-off and that of other large rivers on the mainland side of the Strait are driven by snow and glacier melt, and their peak discharge period is generally in June and July. Discharges from rivers that drain into the Strait of Georgia off Vancouver Island (such as the Chemainus, Cowichan, Campbell, and Puntledge rivers) peak during periods of intense precipitation, generally in November (Waldichuck, 1957)

and that of other large rivers on the mainland side of the Strait are driven by snow and glacier melt, and their peak discharge period is generally in June and July. Discharges from rivers that drain into the Strait of Georgia off Vancouver Island (such as the Chemainus, Cowichan, Campbell, and Puntledge rivers) peak during periods of intense precipitation, generally in November (Waldichuck, 1957).

Circulation in the Strait of Georgia occurs in a general counter-clockwise direction (Waldichuck, 1957). Tides, winds, and freshwater run-off are the primary forces for mixing, water exchange, and circulation. Tidal flow enters the Strait of Georgia predominantly from the south, creating vigorous mixing in the narrow, shallow straits and passes of the Strait of Georgia. The upper, brackish water layer in the Strait of Georgia is influenced by large freshwater run-off, and salinity in this layer varies from 5 to 25 practical salinity units (psu). Deep, high-salinity (33.5 to 34 psu), oceanic water enters the Strait of Georgia from the Strait of Juan de Fuca. The surface outflowing and deep inflowing water layers mix in the vicinity of the sills, creating the deep bottom layer in the Strait of Georgia. The basic circulation pattern in the southern Strait of Georgia is a southerly outflow of low-salinity surface water through the Rosario and Haro Straits (Crean et al. , 1988), with the northerly inflow of high salinity oceanic water from the Strait of Juan de Fuca at the lowest depths.

Marine habitat present in the Strait of Georgia includes two of the same types present in Puget Sound (kelp beds and eel grass beds) and five new habitat types. Total area of each habitat type is: estuarine marshes (3.82 km 2 (1.47 mi 2 )), sandflats (90.4 km 2 (34.9 mi 2 )), mudflats (155.1 km 2 (59.9 mi 2 ), rock-gravel 93.4 km 2 (36.1 mi 2 )), kelp beds (313.8 km 2 (121.2 mi 2 ), eel grass beds (659 km 2 (254 mi 2 )), and intertidal algae (93.4 km 2 (36.1 mi 2 )) (Levings and Thom, 1994)

Sound (kelp beds and eel grass beds) and five new habitat types. Total area of each habitat type is: estuarine marshes (3.82 km 2 (1.47 mi 2 )), sandflats (90.4 km 2 (34.9 mi 2 )), mudflats (155.1 km 2 (59.9 mi 2 ), rock-gravel 93.4 km 2 (36.1 mi 2 )), kelp beds (313.8 km 2 (121.2 mi 2 ), eel grass beds (659 km 2 (254 mi 2 )), and intertidal algae (93.4 km 2 (36.1 mi 2 )) (Levings and Thom, 1994).

Although much of the land draining into the Strait of Georgia is sparsely populated, the densely populated cities of Vancouver and Victoria are located here. Environment Canada (2005) reports that the population of the Georgia Basin has doubled between 1970 and 2005. As in Puget Sound, human development of the area has caused ecosystem stress, including degraded water quality and loss of marsh and eel grass habitat (Transboundary Georgia Basin-Puget Sound Environmental Indicators Working Group, 2002). Filling, diking, water quality changes, and watershed modification have led to decreases in the amount of all habitat types (Levings and Thom, 1994).

Life History, Biology, and Status of the Petitioned Species

The life history, biology, and status of the petitioned species, summarized below, are described in detail in the draft status report (Drake et al. , 2008) and Palsson et al. (2008).

Bocaccio

Bocaccio range from Punta Blanca, Baja California, to the Gulf of Alaska off Krozoff and Kodiak Islands, Alaska (Chen, 1971; Miller and Lea, 1972). Within this range, they are most common from Oregon to northern Baja California (Love et al. , 2002). Bocaccio are elongate, laterally compressed fish with very large mouths (Love et al. , 2002). Their appearance often varies among individuals, with several common color variations. They are most frequently found between 50 and 250 m (160 and 820 feet) depth, but may be found as deep as 475 m (1,560 feet) (Orr et al. , 2000).

Copulation and fertilization occur in the fall, generally between August and November

longate, laterally compressed fish with very large mouths (Love et al. , 2002). Their appearance often varies among individuals, with several common color variations. They are most frequently found between 50 and 250 m (160 and 820 feet) depth, but may be found as deep as 475 m (1,560 feet) (Orr et al. , 2000).

Copulation and fertilization occur in the fall, generally between August and November. Bocaccio larvae have relatively high dispersal potential, with a pelagic larval duration of approximately 155 days (Shanks and Eckert, 2005) and fecundity ranging from 20,000 to over 2 million eggs, considerably more than many other rockfish species (Love et al. , 2002). Larvae and pelagic juveniles tend to be found close to the surface, occasionally associated with drifting kelp mats. Most bocaccio remain pelagic for 3.5 months prior to settling to shallow areas, although some may remain pelagic as long as 5.5 months. Several weeks after settlement, fish move to deeper waters in the range of 18 30 m (60 100 feet) where they are found on rocky reefs (Carr, 1983; Feder, 1974; Johnson, 2006; Love, 2008). Adults inhabit waters from 12 478 m (40 1570 feet) depth but are most common at depths of 50-250 m (Feder, 1974; Love, 2002). While generally associated with hard substrata, adults do wander into mud flats. Bocaccio are also typically found well off the bottom (as much as 30 m (98 feet)) (Love et al. , 2002). Approximately 50 percent of adults mature in 4 to 6 years (MBC, 1987).

Large adult bocaccio have more movement potential than smaller, more et al. , 2008), with the majority of fish caught in the areas around Point Defiance and the Tacoma Narrows in the South basin. Bocaccio have always been rare in the North Puget Sound surveys of the recreational shery (Drake et al. , 2008). In the Strait of Georgia, bocaccio have been documented in some inlets, but records are sparse, isolated, and often based on anecdotal reports (COSEWIC, 2002)

e et al. , 2008), with the majority of fish caught in the areas around Point Defiance and the Tacoma Narrows in the South basin. Bocaccio have always been rare in the North Puget Sound surveys of the recreational shery (Drake et al. , 2008). In the Strait of Georgia, bocaccio have been documented in some inlets, but records are sparse, isolated, and often based on anecdotal reports (COSEWIC, 2002). Although the relationship between bocaccio habitat preference and distribution in the Georgia Basin is not fully understood, the available information indicates that they are frequently found in areas lacking hard substrate. This may be due to their pelagic behavior (willingness to occupy areas higher in the water column) or availability of prey items.

Adults are difficult to age, but are suspected to live as long as 54 years (Drake et al. , 2008). Bocaccio have low productivity because successful recruitment requires rare climatic and oceanic conditions. Tolimeri and Levin (2005) estimate that these conditions occur only about 15 percent of the time.

Bocaccio larvae are planktivores that feed on larval krill, diatoms, and dinoflagellates. Pelagic juveniles are opportunistic feeders, taking fish larvae, copepods, krill, and other prey. Larger juveniles and adults are primarily piscivores, eating other rockfishes, hake, sablefish, anchovies, lanternfishes, and squid. Chinook salmon, terns, and harbor seals are known predators of smaller bocaccio (Love et al. 2002). The main predators of adult bocaccio are marine mammals (COSEWIC, 2002).

Yelloweye Rockfish

Yelloweye rockfish range from northern Baja California to the Aleutian Islands, Alaska, but are most common from central California northward to the Gulf of Alaska (Clemens and Wilby, 1961; Eschmeyer et al. , 1983; Hart, 1973; Love, 1996). They are among the largest of the rockfishes, up to 11 kg (25 pounds), and easily recognizable by their bright yellow eyes and red-orange color (Love et al. , 2002)

oweye rockfish range from northern Baja California to the Aleutian Islands, Alaska, but are most common from central California northward to the Gulf of Alaska (Clemens and Wilby, 1961; Eschmeyer et al. , 1983; Hart, 1973; Love, 1996). They are among the largest of the rockfishes, up to 11 kg (25 pounds), and easily recognizable by their bright yellow eyes and red-orange color (Love et al. , 2002). Yelloweye rockfish occur in waters 25 to 475 m (80 to 1,560 feet) deep (Orr et al. , 2000), but are most commonly found between 91 to 180 m (300 to 590 feet) depth (Love et al. , 2002). Yelloweye rockfish are among the longest lived of rockfishes, living up to at least 118 years (Love, 1996; Love et al. , 2002; O'Connell and Funk, 1987). Yelloweye rockfish juveniles settle primarily in shallow, high relief zones, crevices, and sponge gardens (Love et al. , 1991; Richards et al. , 1985). As they grow and move to deeper waters, adults continue to associate with rocky, high relief areas (Carlson and Straty, 1981; Love et al. , 1991; O'Connell and Carlisle, 1993; Richards et al. , 1985). Yelloweye rockfish can be found infrequently in aggregations, but are generally solitary, demersal residents with small home ranges (Coombs 1979; DeMott, 1983; Love et al. , 2002).

Yelloweye rockfish are less frequently observed in South Puget Sound than North Puget Sound (Miller and Borton, 1980), likely due to the larger amount of rocky habitat in North Puget Sound. Yelloweye rockfish are distributed throughout the Strait of Georgia in northern Georgia Basin including areas around the Canadian Gulf Islands and the numerous inlets along the British Columbia coast (Yamanaka et al. , 2006). Their distribution in these areas most frequently coincides with high relief, complex rocky habitats (Yamanaka et al. 2006).

Approximately 50 percent of adults are mature by 41 cm (16 inches) total length (about 6 years) (Love, 1996)

eorgia in northern Georgia Basin including areas around the Canadian Gulf Islands and the numerous inlets along the British Columbia coast (Yamanaka et al. , 2006). Their distribution in these areas most frequently coincides with high relief, complex rocky habitats (Yamanaka et al. 2006).

Approximately 50 percent of adults are mature by 41 cm (16 inches) total length (about 6 years) (Love, 1996). Yelloweye rockfish store sperm for several months until fertilization occurs, commonly between the months of September and April, though fertilized individuals may be found in most months of the year, depending on where they are observed (Wyllie- Echeverria, 1987). Fertilization periods tend to get later as one moves from south to north in their range (DeLacy et al. , 1964; Hitz, 1962; Lea et al. , 1999; O'Connell 1987; Westrheim, 1975). Estimates of pelagic larval duration are not available for yelloweye rockfish, though we expect that it would be similar to or lower than that for bocaccio or canary rockfish (116 155 days; Varanasi, 2007). Fecundity ranges from 1.2 to 2.7 million eggs, considerably more than many other rockfish species (Love et al. , 2002). In Puget Sound, yelloweye rockfish are believed to fertilize eggs during the winter to summer months, giving birth early spring to late summer (Washington et al. , 1978). Although yelloweye rockfish are generally thought to spawn once a year (MacGregor, 1970), a study in Puget Sound offered evidence of at least two spawning periods per year (Washington et al. , 1978).

Yelloweye rockfish are opportunistic feeders, targeting different food sources during different phases of their life history, with the early life stages having typical rockfish diets as described for bocaccio above. Because adult yelloweye attain such large sizes, they are able to handle much larger prey, including smaller yelloweye, and are preyed upon less frequently (Rosenthal et al. , 1982)

Yelloweye rockfish are opportunistic feeders, targeting different food sources during different phases of their life history, with the early life stages having typical rockfish diets as described for bocaccio above. Because adult yelloweye attain such large sizes, they are able to handle much larger prey, including smaller yelloweye, and are preyed upon less frequently (Rosenthal et al. , 1982). Typical prey of adult yelloweye rockfishes include sand lance, gadids, flatfishes, shrimps, crabs, and gastropods (Love et al. , 2002; Yamanaka et al. , 2006). Predators of yelloweye rockfish include salmon and orcas (Ford et al. , 1998; Love et al. , 2002).

Canary Rockfish

Canary rockfish range between Punta Colnett, Baja California, and the Western Gulf of Alaska (Boehlert, 1980; Mecklenburg et al. , 2002). Within this range, canary rockfish are most common off the coast of central Oregon (Richardson and Laroche, 1979). Adults are primarily orange with a pale grey or white background (Love et al. , 2002). Canary rockfish primarily inhabit waters 50 to 250 m (160 to 820 feet) deep (Orr et al. , 2000), but may be found up to 425 m (1,400 feet) depth (Boehlert, 1980). They can live to be 84 years old (Drake et al. , 2008). Canary rockfish were once considered fairly common in the greater Puget Sound area (Holmberg, 1967).

Female canary rockfish produce between 260,000 and 1.9 million eggs per year with larger females producing more eggs. Along the Pacific Coast, the relationship between egg production and female size does not seem to vary with geography (Gunderson, 1980; Love, 2002). Canary rockfish larvae have relatively high dispersal potential, with a pelagic larval duration of approximately 116 days (Shanks and Eckert, 2005). Fertilization occurs as early as September off central California (Lea, 1999) but peaks in December (Phillips, 1960; Wyllie-Echeverria, 1987), and parturition (birth) occurs between January and April and peaks in April (Phillips, 1960)

0; Love, 2002). Canary rockfish larvae have relatively high dispersal potential, with a pelagic larval duration of approximately 116 days (Shanks and Eckert, 2005). Fertilization occurs as early as September off central California (Lea, 1999) but peaks in December (Phillips, 1960; Wyllie-Echeverria, 1987), and parturition (birth) occurs between January and April and peaks in April (Phillips, 1960). Off the Oregon and Washington coasts, parturition occurs between September and March, with peaks in December and January (Barss, 1989; Wyllie Echeverria, 1987). In British Columbia, parturition occurs slightly later with the peak in February (Hart, 1973; Westrheim, 1975). Canary rockfish spawn once per year (Guillemot, 1985).

Female canary rockfish grow larger and more quickly than do males (Lenarz, 1991; STAT, 1999), and growth does not vary with latitude (Boehlert, 1980). A 58-cm (23-inch) long female is approximately 20 years of age; a male of the same age is about 53 cm (21 inches). Fish tend to move to deeper water as they grow larger (Vetter, 1997). While canary rockfish appear to be generally sedentary (Miller, 1973), tagging studies have shown that some individuals move up to 700 km (435 miles) over several

Miller and Borton (1980) describe canary rockfish as being associated with the various rocky and coarse habitats that occur throughout the basins of Puget Sound. The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) (2007) reports that canary rockfish are broadly distributed throughout the Strait of Georgia.

Greenstriped Rockfish

Greenstriped rockfish range from Cedros Island, Baja California, to Green Island in the Gulf of Alaska. Within this range, greenstriped rockfish are common between British Columbia and Punta Colnett in northern Baja California (Eschmeyer et al. , 1983; Hart, 1973; Love et al. , 2002). They are slim fish, with a distinctive color, and are unlikely to be mistaken for other rockfishes (Love et al. , 2002)

striped rockfish range from Cedros Island, Baja California, to Green Island in the Gulf of Alaska. Within this range, greenstriped rockfish are common between British Columbia and Punta Colnett in northern Baja California (Eschmeyer et al. , 1983; Hart, 1973; Love et al. , 2002). They are slim fish, with a distinctive color, and are unlikely to be mistaken for other rockfishes (Love et al. , 2002). Greenstriped rockfish is a deep-water species that can inhabit waters from 52 to 828 m (170 to 2,715 feet) in depth, but is most common between 100 and 250 m (330 and 820 feet) depth (Orr et al. , 2000). They are solitary fish, most often found resting on the bottom (Love et al. , 2002). Male greenstriped rockfish can live to approximately 37 years of age, and females to approximately 28 years of age (Love et al. , 1990).

Greenstriped rockfish females store sperm for several months until fertilization occurs, commonly between the months of February and May in areas north of California (O'Connell and Carlisle, 1993). Fertilized individuals are found earlier in more southerly areas (Lea et al. , 1999). Greenstriped rockfish are generally believed to spawn once a year (Shaw and Gunderson, 2006), but some evidence of multiple spawnings has been reported (Love et al. , 1990). Larvae are extruded at about 5 mm (0.2 inch) length (Matarese et al. , 1989) and remain pelagic for up to 2 months (Moser and Boehlert, 1991); settling at around 30 mm (1.2 inches) length (Johnson et al. , 1997). Individual greenstriped rockfish of both sexes start to mature at 150 mm (6 inches) length and 5 years of age, with 50 percent maturity occurring at 230 mm (9 inches) and 7-10 years (Shaw and Gunderson, 2006; Wyllie Echeverria, 1987). Females produce 11,000 to 300,000 eggs annually.

Greenstriped rockfish are active and opportunistic feeders, targeting different food sources during different phases of their life history

rockfish of both sexes start to mature at 150 mm (6 inches) length and 5 years of age, with 50 percent maturity occurring at 230 mm (9 inches) and 7-10 years (Shaw and Gunderson, 2006; Wyllie Echeverria, 1987). Females produce 11,000 to 300,000 eggs annually.

Greenstriped rockfish are active and opportunistic feeders, targeting different food sources during different phases of their life history. Larvae are diurnal, with nauplii, eggs, and copepods representing important food sources (Moser and Boehlert, 1991; Sumida et al. , 1985). Greenstriped rockfish adults are generally considered to be residential and may feed nocturnally, consuming bigger crustaceans, fishes, and cephalopods during those times (Allen, 1982). Juveniles are preyed upon by birds, nearshore fishes, salmon, and porpoises (Ainley et al. , 1993; Love et al. , 1991; Morejohn et al. , 1978). Adults have been recovered in the stomachs of sharks, porpoises, salmon, seals, and possibly river otters (Antonelis Jr. and Fiscus, 1980; Merkel, 1957; Morejohn et al. , 1978).

Greenstriped rockfish are distributed throughout Puget Sound, often associated with sand and coarse substrate (Miller and Borton, 1980; Palsson et al. , 2008). Palsson et al. (2008) report that greenstriped rockfish are occasionally caught in the western Strait of Juan de Fuca. Greenstriped rockfish are occasionally reported from North Puget Sound, but the low occurrence of reports may be due to the difficulty in surveying the rocky habitats of this area by conventional trawl sampling. COSEWIC has not undertaken a greenstriped rockfish status review in Canada.

Redstripe Rockfish

Redstripe rockfish occur from southern Baja California to the Bering Sea, Alaska (Hart, 1973; Love et al. , 2002). They are a streamlined fish with a red, pink, or tan color (Love et al. , 2002). Redstripe rockfish have been reported between 12 and 425 m (39 and 1,400 feet) in depth, but 95 percent occur between 150 and 275 m (490 and 900 feet) (Love et al. , 2002)

n Canada.

Redstripe Rockfish

Redstripe rockfish occur from southern Baja California to the Bering Sea, Alaska (Hart, 1973; Love et al. , 2002). They are a streamlined fish with a red, pink, or tan color (Love et al. , 2002). Redstripe rockfish have been reported between 12 and 425 m (39 and 1,400 feet) in depth, but 95 percent occur between 150 and 275 m (490 and 900 feet) (Love et al. , 2002).

Redstripe rockfish may reach 55 years of age (Munk, 2001). They are most commonly found on a variety of substrates, from hard, high-relief reefs to sand-cobble interfaces. Juveniles settle to the bottom of sand-cobble substrates (Moser and Boehlert, 1991) and move as adults onto deeper rocky reefs and low-relief rubble bottoms. Redstripe rockfish can be found alone or in aggregations, usually near the sea-floor bottom (Love et al. , 2002b).

Estimates of pelagic larval duration and fecundity with which to infer dispersal potential are not available for redstripe rockfish, though we expect that larval duration would be similar to or slightly lower than that for bocaccio or canary rockfish (116 155 days; Varanasi, 2007). Approximately 50 percent of adults mature at 28 to 29 cm (11 to 11.5 inches) total length (Garrison and Miller, 1982). Redstripe rockfish females store sperm for several months until fertilization. Fertilization occurs between the months of April and May in areas north of California (O'Connell, 1987; Shaw, 1999; Wyllie-Echeverria, 1987). Larvae are extruded after a typical gestation period of a couple of months, peaking in July for British Columbia (Westrheim, 1975) and in June for Oregon (Shaw, 1999; Wyllie-Echeverria, 1987). Redstripe rockfish spawn once per year (Shaw, 1999). Larvae are extruded at about 5.4 mm length (0.2 inches) (Matarese et al. , 1989) and remain pelagic for up to 2 months (Moser and Boehlert, 1991). Recorded size at first maturity for redstripe rockfish is 210 to 220 mm (8.2 to 8.6 inches) length (Shaw, 1999)

Columbia (Westrheim, 1975) and in June for Oregon (Shaw, 1999; Wyllie-Echeverria, 1987). Redstripe rockfish spawn once per year (Shaw, 1999). Larvae are extruded at about 5.4 mm length (0.2 inches) (Matarese et al. , 1989) and remain pelagic for up to 2 months (Moser and Boehlert, 1991). Recorded size at first maturity for redstripe rockfish is 210 to 220 mm (8.2 to 8.6 inches) length (Shaw, 1999). Size at 50 percent maturity was recorded in the 1970s to be 280 and 290 mm (11.0 and 11.4 inches) (Westrheim, 1975) for males and females, respectively, differing from samples collected in the 1990s (243 and 262 mm (9.5 and 10.0 inches)) for males and females (about 7 years old), respectively (Shaw, 1999). It is not known whether this represents changes in size at maturity over time or differential representation of individuals that geographically mature at larger sizes.

Redstripe rockfish are active and opportunistic feeders, and show feeding habits similar to the greenstriped rockfish. Larvae are diurnal, with nauplii, eggs, and copepods representing important food sources (Moser and Boehlert, 1991; Sumida et al. , 1985). Juveniles are diurnal zooplanktivores and feed mainly on calanoid copepods and barnacle cyprids (Allen, 1982; Gaines and Roughgarden, 1987; Love et al. , 1991). Adults may also feed nocturnally, consuming bigger crustaceans, fishes, and cephalopods (Allen, 1982). Juvenile redstripe rockfish are preyed upon by birds, nearshore fishes, salmon, and porpoises (Ainley et al. , 1993; Love et al. , 1991; Morejohn et al. 1978). Redstripe et al. , 1978).

Redstripe rockfish are associated with a wide range of rocky and coarse habitats in a broad range of depths throughout most basins of Puget Sound (Palsson et al. , 2008). Palsson et al. (2008) report that redstripe rockfish are commonly caught during trawl surveys in the central Strait of Juan de Fuca, channels of the San Juan Archipelago, in the central Strait of Georgia, and in Admiralty Inlet

Redstripe rockfish are associated with a wide range of rocky and coarse habitats in a broad range of depths throughout most basins of Puget Sound (Palsson et al. , 2008). Palsson et al. (2008) report that redstripe rockfish are commonly caught during trawl surveys in the central Strait of Juan de Fuca, channels of the San Juan Archipelago, in the central Strait of Georgia, and in Admiralty Inlet. COSEWIC has not undertaken a redstripe rockfish status review in Canada.

DPS Consideration

As described above, under the DPS policy a population segment is considered a DPS if it is both discrete from other populations within its taxon and significant to its taxon. The population segment may be considered discrete if it is markedly separated from other populations of the same taxon as a consequence of physical, physiological, ecological, or behavioral factors. Quantitative measures of genetic differences may provide powerful direct evidence of this separation, because the presence of distinct genetic traits indicates that a population segment may be reproductively isolated. In addition to genetic information, various aspects of a population segment's biology, life history, and habitat may provide evidence of discreteness. For example, populations of a sedentary species may have limited reproductive exchange with other populations, and populations occupying habitat that is physically isolating may have little reproductive exchange with other isolated populations. This reproductive isolation over time may result in discreteness. For example, Yamanaka et al. (2006) concluded that for yelloweye rockfish, there are at least two distinct populations with limited genetic exchange occupying coastal North American waters between southeast Alaska and Oregon. The authors identified one population occupying the entire Pacific Coast and an inland population occupying the Strait of Georgia and possibly other inland marine waters including the Queen Charlotte Strait and Puget Sound

at for yelloweye rockfish, there are at least two distinct populations with limited genetic exchange occupying coastal North American waters between southeast Alaska and Oregon. The authors identified one population occupying the entire Pacific Coast and an inland population occupying the Strait of Georgia and possibly other inland marine waters including the Queen Charlotte Strait and Puget Sound.

There is limited direct genetic information comparing coastal populations of the petitioned rockfish species to populations within the Georgia Basin. In addition to that limited information, where available, we considered several lines of evidence to inform the consideration of discreteness of population segments within the Georgia Basin. These included genetic information from coastal populations of the petitioned species and the degree to which such information indicates stock structure among coastal populations; genetic information comparing Georgia Basin and coastal populations of other west coast rockfish species with life histories similar to the petitioned species; life-history traits of the petitioned species that could lead to reproductive isolation, and thus discreteness, of Georgia Basin populations (such as live-bearing of young, internal fertilization, short-pelagic larval stages, and fidelity to habitat); and characteristics of the species' habitat that could lead to physical isolation and thus discreteness of Georgia Basin populations (such as discontinuity of rocky habitats, bathymetric barriers, and current patterns and physical barriers that limit exchange of coastal and inland waters). The discussion below describes evidence of discreteness that may be relevant to any of the five rockfish species. The later discussion of individual species describes the considerations relevant to the discreteness of each individual species.

As described above under the DPS policy, in addition to being discrete, a population segment must also be significant to qualify as a DPS

d inland waters). The discussion below describes evidence of discreteness that may be relevant to any of the five rockfish species. The later discussion of individual species describes the considerations relevant to the discreteness of each individual species.

As described above under the DPS policy, in addition to being discrete, a population segment must also be significant to qualify as a DPS. The discussion of the policy above describes four characteristics that may make a discrete population segment significant. In the case of the petitioned rockfish species, the most relevant of these characteristics is the persistence of the discrete population segment in a unique ecological setting. The discussion below describes evidence of significance that may be relevant to any of the five rockfish species. The later discussion of individual species describes any additional considerations relevant to the significance of each individual species.

DPS Considerations Relevant to Discreteness of All Petitioned Species

Because there is little direct genetic information on the discreteness of most of the petitioned species in Puget Sound or the Georgia Basin, we considered genetic information on other rockfish species in Puget Sound and Georgia Basin with life histories similar to the petitioned species. In particular, NMFS' 2001 status review of copper, quillback, and brown rockfish (Stout et al. , 2001) concluded that there were DPSs of these rockfish in Puget Sound Proper based on genetic information. For copper rockfish, allozyme and DNA data from Seeb (1998) showed no particular genetic divergence for Puget Sound Proper specimens, but microsatellite data from Wimberger (in prep.) and Buonaccorsi et al. (2002) showed large differences between populations from within Puget Sound Proper and populations found outside Puget Sound Proper

rockfish in Puget Sound Proper based on genetic information. For copper rockfish, allozyme and DNA data from Seeb (1998) showed no particular genetic divergence for Puget Sound Proper specimens, but microsatellite data from Wimberger (in prep.) and Buonaccorsi et al. (2002) showed large differences between populations from within Puget Sound Proper and populations found outside Puget Sound Proper. Wimberger sampled copper rockfish from California, British Columbia, the San Juan Islands, the Canadian Gulf Islands, Admiralty Inlet, Central Puget Sound, and Hood Canal (the latter three populations are found within Puget Sound Proper). Wimberger found significant divergence between both Central Puget Sound and Admiralty Inlet populations, and all populations found outside of Puget Sound Proper. Equal divergence was found among Puget Sound Proper populations compared with San Juan, Gulf Island, and coastal populations as well.

Buonaccorsi et al. (2002) used a different set of microsatellite loci to compare populations of copper rockfish from Puget Sound Proper, Canadian Gulf Islands, Queen Charlotte Islands, and coastal California. They also found highly significant divergence among all sampling sites, indicating a clear divergence between populations within Puget Sound Proper and the Canadian Gulf Islands (in the Strait of Georgia). Buonaccorsi et al. (2002) also identified unique alleles in Puget Sound Proper, further evidence for isolation of Puget Sound Proper populations from other neighboring regions.

In addition to genetic information, Stout et al. (2001) pointed out that copper rockfish are live-bearing and have internal fertilization, a short pelagic larval stage, and high habitat fidelity. Copper rockfish are also considered to be non-migratory (Buonaccorsi et al. , 2002). All of these traits, combined with the physical isolation of Puget Sound Proper, could lead to reproductive isolation of copper rockfish in Puget Sound Proper

ut et al. (2001) pointed out that copper rockfish are live-bearing and have internal fertilization, a short pelagic larval stage, and high habitat fidelity. Copper rockfish are also considered to be non-migratory (Buonaccorsi et al. , 2002). All of these traits, combined with the physical isolation of Puget Sound Proper, could lead to reproductive isolation of copper rockfish in Puget Sound Proper.

For quillback rockfish, Seeb (1998) sampled four sites within Puget Sound Proper, one in the San Juan Islands (in the North Basin of Puget Sound), and coastal sites from California, Washington, and Alaska. Like copper rockfish, quillback rockfish are sedentary and show high fidelity to their home sites (Love et al. , 2002). Both allozyme and RFLP analyses indicated large differences in allele frequencies between Puget Sound Proper and the San Juan Islands. When the Puget Sound Proper samples were removed from the analysis, however, no significant divergence was found among the remaining populations (suggesting reproductive exchange among populations in California, Washington,

Brown rockfish have a distribution that is very different from copper and quillback rockfishes, as they are found in Puget Sound Proper but only rarely occur in North Puget Sound, Georgia Basin, or the Washington and Oregon coastline (Stout et al. , 2001). Genetic data support a divergence between Puget Sound Proper and California populations (Seeb, 1998). Buonaccorsi et al. (2002) sampled three sites within Puget Sound Proper, and compared them to coastal populations ranging from California to Mexico. They found significant divergence among the populations, and even between two of the Puget Sound Proper populations. Tagging studies indicate that juveniles and subadults may have relatively small home ranges (Love et al. , 2002)

lations (Seeb, 1998). Buonaccorsi et al. (2002) sampled three sites within Puget Sound Proper, and compared them to coastal populations ranging from California to Mexico. They found significant divergence among the populations, and even between two of the Puget Sound Proper populations. Tagging studies indicate that juveniles and subadults may have relatively small home ranges (Love et al. , 2002). Puget Sound Proper populations exhibited extremely low genetic divergence compared to coastal samples, which suggested to the authors a potential founder effect combined with reproductive isolation, and/or a low effective population size.

In addition to genetic information for copper, quillback, and brown rockfish, there is genetic information available regarding some of the petitioned species that can help inform consideration of DPS structure of the other petitioned species. For the petitioned species, there is genetic information for yelloweye rockfish (Yamanaka et al. , 2006 and R. Withler (unpublished data as cited in Drake et al. , 2008)) indicating genetic differences between fish from inland marine waters (Queen Charlotte Strait and Georgia Basin) and the outer coast.

In addition to genetic information that is available for some rockfish species in the Georgia Basin, there are physical features of the Georgia Basin that affect all rockfish species in similar ways, potentially contributing to reproductive isolation and thus discreteness. The waters of the Georgia Basin are isolated from coastal waters by land masses (the Olympic Peninsula and Vancouver Island); underwater sills limit the movement of water, sediment, and bottom-dwelling species such as rockfish; and internal currents limit the exchange of water between the Basin and coastal areas. These geographic features tend to contain the dispersal of larval fish and the migration of adult fish within the Basin, and even within smaller areas within the Basin, such as Puget Sound Proper

couver Island); underwater sills limit the movement of water, sediment, and bottom-dwelling species such as rockfish; and internal currents limit the exchange of water between the Basin and coastal areas. These geographic features tend to contain the dispersal of larval fish and the migration of adult fish within the Basin, and even within smaller areas within the Basin, such as Puget Sound Proper.

When the available genetic information was considered in concert with the ecological features of Puget Sound and the Georgia Basin and the life histories of the petitioned rockfishes, the BRT drew two general conclusions. First, the petitioned rockfishes in the inland marine waters (Puget Sound and the greater Georgia Basin) are likely to be reproductively isolated and genetically distinct from rockfish from the rest of the Pacific Coast. Second, and consistent with the findings of Stout et al. (2001), the more sedentary rockfishes are likely to be further reproductively isolated within Puget Sound Proper (the area that was the focus of the original listing petition). The more mobile rockfish are likely to be reproductively isolated within the Georgia Basin, but are not likely to be reproductively isolated within Puget Sound Proper.

DPS Considerations Relevant to Significance of All Petitioned Species

As described above in more detail, all five of the petitioned rockfish species occupy marine waters from California to Alaska, including coastal waters and the inland waters of the Georgia Basin. Throughout this range, the Georgia Basin is unique, for several reasons. The waters of the Georgia Basin are less saline than coastal waters because of the quantity of fresh water flowing into the Basin, particularly from the Fraser River. The greater amount of fresh water also results in stratification of water by salinity in the Georgia Basin to a greater extent than in coastal waters

gia Basin. Throughout this range, the Georgia Basin is unique, for several reasons. The waters of the Georgia Basin are less saline than coastal waters because of the quantity of fresh water flowing into the Basin, particularly from the Fraser River. The greater amount of fresh water also results in stratification of water by salinity in the Georgia Basin to a greater extent than in coastal waters. Land masses and shallow sills limit the movement of deep-dwelling fish among subbasins within the Georgia Basin, as well as the movement of sediments and nutrients to a much greater extent than in coastal waters. In addition, the inland waters of the Georgia Basin are protected by the land features of the Olympic Peninsula and Vancouver Island, and by numerous islands within the Basin, which interrupts waves and currents and results in a less energetic environment than the coast. These features make the ecological setting of the Georgia Basin region substantially different than other regions in the range of these rockfish species.

While the Straits of Georgia and Juan de Fuca and North Puget Sound are relatively wide bodies of water with numerous islands, Puget Sound Proper is composed of narrow basins separated by shallow sills. The geographic and bathymetric features that constrain rockfish movement in the Georgia Basin are even more pronounced in Puget Sound Proper. The presence of rocky habitat is very limited in Puget Sound Proper, with most bottom substrates comprised of soft sediments, ranging from coarse sands to fine silts and clay. Rockfish in Puget Sound Proper are either limited to the small amount of rocky habitat or, like bocaccio, greenstriped rockfish, and redstripe rockfish, make use of habitat with softer bottom substrates

n Puget Sound Proper. The presence of rocky habitat is very limited in Puget Sound Proper, with most bottom substrates comprised of soft sediments, ranging from coarse sands to fine silts and clay. Rockfish in Puget Sound Proper are either limited to the small amount of rocky habitat or, like bocaccio, greenstriped rockfish, and redstripe rockfish, make use of habitat with softer bottom substrates.

DPS Conclusions by Species

Bocaccio

In 2002, our Southwest Fisheries Science Center conducted a status review for bocaccio (MacCall and He, 2002), focusing on a Southern DPS occupying the coastal area from the Oregon/California border to approximately 322 km (200 miles) south of the Mexico/U.S. border. The status review concluded that at least two DPSs of bocaccio were present off the coast of the Western United States and Mexico, the Southern DPS and at least one additional DPS (the Northern) to the north. The authors (MacCall and He, 2002) did not consider whether inland stocks of bocaccio in the northern portion of this species range might be separate DPSs or what their extinction risk might be, because only the southern DPS was the subject of an ESA petition at that time. That review resulted in a determination that listing of the southern DPS of bocaccio was not warranted.

No published studies have compared genetic characteristics of bocaccio from Puget Sound and outer coastal areas, but there have been several studies of genetic variation in bocaccio along the outer coast. Wishard et al. (1980) examined allozyme variation in nine coastal sampling locations ranging from Baja California to southern Oregon, with sample sizes ranging from 12 to over 100 individuals per locality. They found two highly polymorphic loci and three others with low levels of variation. They found overlapping confidence intervals for allele frequencies across sampling locations and no evidence for population differentiation. More recently, Matala et al

astal sampling locations ranging from Baja California to southern Oregon, with sample sizes ranging from 12 to over 100 individuals per locality. They found two highly polymorphic loci and three others with low levels of variation. They found overlapping confidence intervals for allele frequencies across sampling locations and no evidence for population differentiation. More recently, Matala et al. (2004) examined genetic variation in bocaccio at seven microsatellite loci in samples from eight locations from Baja California to British Columbia, including both sides of Point Conception. Samples were adults, except in the Santa Barbara channel where age-0 fish were taken. The results indicate that coastal bocaccio are not a single breeding population. A large-scale pattern of isolation by distance was not observed in the data. However,

Some aspects of bocaccio life history indicate that populations in the Georgia Basin might not be discrete from coastal populations, in particular the ability of adult bocaccio to move over long distances and the modest levels of differentiation among coastal populations described above. For this reason, and because of the lack of direct genetic information comparing inland and coastal populations, the BRT considered it possible that Georgia Basin populations are not discrete from coastal populations, that their presence in the Georgia Basin might be the result of a rare recruitment/migration event from coastal stocks. If that were the case, bocaccio age structure in the Basin would be dominated by a single year class. However, available size frequency data provide evidence that there are multiple year classes spread out over the available time series (MacCall, 2008). In addition, coastal bocaccio are dominated by a strong 1999 year class, but bocaccio in the Georgia Basin are not, providing further evidence against a hypothesis of a single population with frequent reproductive exchange

d by a single year class. However, available size frequency data provide evidence that there are multiple year classes spread out over the available time series (MacCall, 2008). In addition, coastal bocaccio are dominated by a strong 1999 year class, but bocaccio in the Georgia Basin are not, providing further evidence against a hypothesis of a single population with frequent reproductive exchange.

The BRT concluded that the best available scientific information instead suggests that bocaccio populations in the Georgia Basin are discrete from coastal populations. Information supporting this conclusion includes the presence of multiple year classes within the Georgia Basin (indicating that bocaccio in the Basin are an independently reproducing entity and not the result of a rare recruitment/migration event from coastal stocks); the lack of a strong 1999 year class in the Georgia Basin, compared to coastal populations which do have a strong 1999 year class (suggesting separate recruitment regimes acting on Georgia Basin populations compared to coastal populations and also suggesting demographic independence); and the presence of large sexually mature individuals (suggesting the capacity for independent reproduction).

Inferences from the genetic evidence for discreteness of copper, quillback, brown, and yelloweye rockfish in the Georgia Basin also supports a conclusion that bocaccio in the Georgia Basin are discrete from coastal populations. Similarities in life histories between bocaccio and the four species for which we do have genetic information include: live-bearing of young, pelagic larval and juvenile stages, and eventual settlement to benthic habitats as fish reach adulthood. All of these species also consume similar prey items and spend at least some time in association with coarse substrates

uillback, and brown rockfishes discussed above was relevant to bocaccio.

Under the DPS policy, having concluded that there is likely a discrete population segment of Georgia Basin bocaccio we must next consider whether the discrete population segment is significant to the species to which it belongs. As described above, the Georgia Basin is a unique ecological setting for all west coast rockfish. In addition, unlike coastal bocaccio, which are most frequently found in association with rocks and boulder fields, bocaccio in the Georgia Basin have been frequently found in areas with sand and mud substrate. We therefore conclude that the discrete population segment of boccacio in the Georgia Basin is also significant and thus a DPS (Figure 1).

In its previous status review, described above, NMFS identified two DPSs of coastal bocaccio (MacCall and He, 2002). The Georgia Basin bocaccio DPS identified in this draft status review would represent a third bocaccio DPS, distinct from both the southern and northern coastal DPSs identified in the previous review.

Yelloweye Rockfish

No published studies have compared genetic characteristics of yelloweye rockfish from Puget Sound and outer coastal areas. A Canadian study (Yamanaka et al. , 2006) using nine microsatellite loci in yelloweye rockfish collected from Oregon to southeast Alaska found small allele frequency differences among all the coastal samples; however, three samples from the inside waters of the Strait of Georgia and Queen Charlotte Strait had significantly reduced levels of genetic variability and formed a distinctive genetic cluster. The authors suggested that these results imply restricted gene flow between inland and coastal populations and a lower effective size for populations within the Strait of Georgia. Subsequently, samples taken in 2005 2007 from waters between Vancouver Island and Mainland British Columbia have been screened at the same nine polymorphic microsatellite loci (R. Withler, personal communication, July 2008)

authors suggested that these results imply restricted gene flow between inland and coastal populations and a lower effective size for populations within the Strait of Georgia. Subsequently, samples taken in 2005 2007 from waters between Vancouver Island and Mainland British Columbia have been screened at the same nine polymorphic microsatellite loci (R. Withler, personal communication, July 2008). Preliminary analysis of these new samples shows that these patterns remain consistent: all the samples from inland waters form a coherent genetic cluster, and inside-outside comparisons typically yield much higher values of genetic differentiation than do comparisons of two coastal samples or two inland samples. In the north, there appears to be a fairly sharp transition between inland and coastal forms in the vicinity of the Gordon Channel. Whether a similar pattern occurs in the south is not known, as no samples from Puget Sound have been analyzed and only a single fish was collected from the Strait of Juan de Fuca. Nevertheless, these results suggest that yelloweye rockfish from the rest of the Georgia Basin are also likely to be genetically differentiated from the coastal population.

Several other lines of evidence support a conclusion that yelloweye rockfish in the Georgia Basin are discrete from coastal populations of yelloweye rockfish. Two aspects of the life history of yelloweye rockfish discussed earlier favor genetic and potentially demographic isolation from coastal populations. First, as both adults and juveniles, yelloweye rockfish are tightly associated with rocky substrata (or invertebrate prey associated with hard substrate). Such substrata are infrequent and patchy in distribution in North Puget Sound and the Georgia Strait, and are very rare in Puget Sound

Inferences from the genetic evidence for discreteness of copper, quillback, and brown rockfish in the Georgia Basin also support a conclusion that yelloweye rockfish in the Georgia Basin are discrete from coastal populations

prey associated with hard substrate). Such substrata are infrequent and patchy in distribution in North Puget Sound and the Georgia Strait, and are very rare in Puget Sound

Inferences from the genetic evidence for discreteness of copper, quillback, and brown rockfish in the Georgia Basin also support a conclusion that yelloweye rockfish in the Georgia Basin are discrete from coastal populations. Similarities in life histories between yelloweye and the three species for which we do have genetic information include: live-bearing of young, pelagic larval and juvenile stages, and eventual settlement to benthic habitats as fish reach adulthood. All of these species also consume similar prey items and spend at least some time in association with coarse substrates.

For the above reasons, the BRT concluded that the weight of the evidence supports the existence of a discrete population segment of yelloweye in the Georgia Basin more than it supports the existence of a single coastal/Georgia Basin population.

The BRT concluded there was no available information to support a conclusion that population segments of yelloweye within the Georgia Basin are discrete from one another. The BRT also concluded that it was unlikely that the small amount of rocky habitat within in Puget Sound Proper would be able to support a self sustaining population of yelloweye rockfish. Since the majority of yelloweye habitat occurs in North Puget Sound and in the Strait of Georgia , the BRT did not feel that the evidence of within Georgia Basin genetic differences for copper, quillback, and brown rockfishes discussed above was relevant to yelloweye rockfish.

Under the DPS policy, having concluded that there is likely a discrete population segment of Georgia Basin yelloweye, we must next consider whether the discrete population segment is significant to the species to which it belongs

d not feel that the evidence of within Georgia Basin genetic differences for copper, quillback, and brown rockfishes discussed above was relevant to yelloweye rockfish.

Under the DPS policy, having concluded that there is likely a discrete population segment of Georgia Basin yelloweye, we must next consider whether the discrete population segment is significant to the species to which it belongs. As described above, the Georgia Basin is a unique ecological setting for all west coast rockfish, satisfying the significance criterion of the DPS policy and supporting a conclusion that the discrete population segment of yelloweye in the Georgia Basin is also significant and thus a DPS.

Although the BRT did not examine additional DPS delineations among coastal populations of yelloweye rockfish, the BRT findings support a conclusion that the coastal populations constitute at least one additional DPS. As the BRT concluded, coastal populations are discrete from Georgia Basin populations. Because coastal populations occupy the majority of the species' range (as described above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional yelloweye rockfish DPS.

Canary Rockfish

No published studies have compared genetic characteristics of canary rockfish from Puget Sound and outer coastal areas. The allozyme study mentioned above (Wishard et al. , 1980), which examined large samples from 8 eight coastal locations in northern California, Oregon, and Washington, found low levels of heterozygosity in this species and some evidence for stock structure. In particular, samples taken south of Cape Blanco (southern Oregon) lack an allele that occurs at low frequency in populations to the north

s. The allozyme study mentioned above (Wishard et al. , 1980), which examined large samples from 8 eight coastal locations in northern California, Oregon, and Washington, found low levels of heterozygosity in this species and some evidence for stock structure. In particular, samples taken south of Cape Blanco (southern Oregon) lack an allele that occurs at low frequency in populations to the north.

The BRT concluded that the best available scientific information suggests that canary rockfish populations in the Georgia Basin are discrete from coastal populations. Canary rockfish populations were historically most abundant in South Puget Sound, which is the basin in Puget Sound furthest from coastal waters, and is separated from coastal waters by three sills, which can present barriers to migration. Inferences from the genetic evidence for discreteness of copper, quillback, brown, and yelloweye rockfish in the Georgia Basin also support a conclusion that canary rockfish in the Georgia Basin are discrete from coastal populations. Similarities in life histories between canary rockfish and the four species for which we do have genetic information include: live-bearing of young, pelagic larval and juvenile stages, and eventual settlement to benthic habitats as fish reach adulthood. All of these species also consume similar prey items and spend at least some time in association with coarse substrates.

For the above reasons, the BRT concluded that the weight of the evidence supports the existence of a discrete population segment of canary rockfish in the Georgia Basin more than it supports the existence of a single coastal/Georgia Basin population.

The BRT concluded there was no available information to support a conclusion that population segments of canary rockfish within the Georgia Basin are discrete from one another

RT concluded that the weight of the evidence supports the existence of a discrete population segment of canary rockfish in the Georgia Basin more than it supports the existence of a single coastal/Georgia Basin population.

The BRT concluded there was no available information to support a conclusion that population segments of canary rockfish within the Georgia Basin are discrete from one another. Because of this species potential for movement, the BRT did not feel that the evidence of within Georgia Basin genetic differences for copper, quillback, and brown rockfishes discussed above was relevant to canary rockfish.

Under the DPS policy, having concluded that there is likely a discrete population segment of Georgia Basin canary rockfish we must next consider whether it is significant to the species to which it belongs. As described above, the Georgia Basin is a unique ecological setting for all west coast rockfish, satisfying the significance criterion of the DPS policy and supporting a conclusion that the discrete population segment of canary rockfish in the Georgia Basin is also significant and thus a DPS.

Although the BRT did not examine additional DPS delineations among coastal populations of canary rockfish, the BRT findings support a conclusion that the coastal populations constitute at least one additional DPS. As the BRT concluded, coastal populations are discrete from Georgia Basin populations. Because coastal populations occupy the majority of the species' range (as described above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional canary rockfish DPS.

Redstripe Rockfish

No published studies have examined population genetic structure of redstripe rockfish in the Northeast Pacific

ed above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional canary rockfish DPS.

Redstripe Rockfish

No published studies have examined population genetic structure of redstripe rockfish in the Northeast Pacific. The BRT concluded that the best available scientific information supported a conclusion that the redstripe rockfish population segment in Puget Sound Proper is discrete from other redstripe rockfish populations in the rest of Georgia Basin and in coastal waters. Compared to other rockfish species, redstripe rockfish tend to occur in the mud/sand habitat that characterizes much of Puget Sound Proper. Due to the relatively deep habitat occupied by adult redstripe rockfish, the shallow sills of Puget Sound Proper would present an obstacle to northward migration of this species. Inferences from the genetic evidence for discreteness of copper, quillback, and brown rockfish in the Georgia Basin also support a conclusion that redstripe rockfish in Puget Sound Proper are discrete from other populations in the Georgia Basin. Similarities in life histories between redstripe rockfish and those three species, for which we do have genetic information include: live-bearing of young, pelagic larval and

Under the DPS policy, having concluded that there is likely a discrete population segment of Puget Sound Proper redstripe rockfish we must next consider whether the discrete population segment is significant to the species to which it belongs. As described above, Puget Sound Proper is a unique ecological setting for all west coast rockfish. In addition, the BRT noted that historical records indicated a long-standing presence of this species in Puget Sound Proper, lending further support to the conclusion that the Puget Sound Proper population segment is significant to the redstripe rockfish species

nt to the species to which it belongs. As described above, Puget Sound Proper is a unique ecological setting for all west coast rockfish. In addition, the BRT noted that historical records indicated a long-standing presence of this species in Puget Sound Proper, lending further support to the conclusion that the Puget Sound Proper population segment is significant to the redstripe rockfish species. We therefore conclude that restripe rockfish in Puget Sound Proper satisfy the significance criterion of the DPS policy and should thus be considered a DPS (Figure 1).

Although the BRT did not examine additional DPS delineations among coastal populations of redstripe rockfish, the BRT findings support a conclusion that the coastal populations constitute at least one additional DPS. As the BRT concluded, coastal populations are discrete from Georgia Basin populations. Because coastal populations occupy the majority of the species' range (as described above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional redstripe rockfish DPS.

Greenstriped Rockfish

Very little genetic information is available for greenstriped rockfish. A preliminary study of mitochondrial DNA control region sequences (J. Hess, unpublished data) compared data from coastal samples (British Columbia, Washington, and California) and samples collected from the Strait of Juan de Fuca. Preliminary results are consistent with those for coastal populations of other rockfish species: most haplotypes shared by more than one individual were found in all populations sampled, and the only significant pair wise comparison was Washington coast vs. California. However, sample sizes were low (12-40 individuals), so power to detect differences was also low

d from the Strait of Juan de Fuca. Preliminary results are consistent with those for coastal populations of other rockfish species: most haplotypes shared by more than one individual were found in all populations sampled, and the only significant pair wise comparison was Washington coast vs. California. However, sample sizes were low (12-40 individuals), so power to detect differences was also low. Furthermore, because no samples were available from Puget Sound Proper, this preliminary study provided no information about the relationship between greenstriped rockfish in Puget Sound and the Pacific coast.

Like redstripe rockfish, greenstriped rockfish tend to occur in the mud/sand habitat that characterizes much of Puget Sound Proper. Also similar to redstripe rockfish, the BRT felt that the shallow sills of Puget Sound Proper might present a migration obstacle to greenstriped rockfish. Some available information supports this conclusion, while other information suggests the sills might not present a migration obstacle to this species. Other information supporting a Puget Sound Proper DPS includes the fact that this species does not appear to occur in a large area north of Admiralty Inlet and south of the San Juan Islands, suggesting a distribution gap between the Puget Sound Proper area and the rest of the Georgia Basin and the coast. The BRT also found no compelling information to suggest that populations of greenstriped rockfish in Puget Sound Proper would be any less discrete from other Georgia Basin populations than was the case for the previously reviewed species (Stout et al. , 2001). The only information that was contrary to a Puget Sound Proper DPS was the possibility that the large intra-annual variation in the apparent abundance of the species in Puget Sound Proper could reflect periodic immigration from other areas. Ultimately, the BRT largely relied on the information from the other rockfish species, particularly the previous status review of copper, quillback, and brown rockfish (Stout et al

that was contrary to a Puget Sound Proper DPS was the possibility that the large intra-annual variation in the apparent abundance of the species in Puget Sound Proper could reflect periodic immigration from other areas. Ultimately, the BRT largely relied on the information from the other rockfish species, particularly the previous status review of copper, quillback, and brown rockfish (Stout et al. , 2001), to conclude there is likely a Puget Sound Proper DPS of greenstriped rockfish. Similarities in life histories between greenstriped rockfish and those three species, for which we do have genetic information include: live-bearing of young, pelagic larval and juvenile stages, and eventual settlement to benthic habitats as fish reach adulthood. All of these species also consume similar prey items and spend at least some time in association with coarse substrates. Thus for greenstriped rockfish, Puget Sound Proper is discrete from other greenstriped rockfish populations in the rest of Georgia Basin and in coastal waters.

Consistent with the earlier conclusions of Stout et al. (2001), Puget Sound Proper is an ecologically unique environment that differs from other parts of Georgia Basin, thus satisfying the significance criterion of the DPS policy and should thus be considered a DPS.

Although the BRT did not examine additional DPS delineations among coastal populations of greenstriped rockfish, the BRT findings support a conclusion that the coastal populations constitute at least one additional DPS. As the BRT concluded, coastal populations are discrete from Georgia Basin populations. Because coastal populations occupy the majority of the species' range (as described above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional greenstriped rockfish DPS

ns are discrete from Georgia Basin populations. Because coastal populations occupy the majority of the species' range (as described above under Life History, Biology, and Status of the Petitioned Species), they would also certainly meet the DPS requirement of being significant to the taxon. Therefore, we conclude that coastal populations constitute at least one additional greenstriped rockfish DPS.

Western Boundary of the Georgia Basin DPS

The BRT noted that the Strait of Juan de Fuca is a transition zone between the oceanic waters of the California Current and inland waters of Georgia Basin. There was general agreement among BRT members that there is unlikely to be a sharp boundary that separates populations residing in these two systems (Drake et al. , 2008). The BRT considered two possible western boundaries, the mouth of the Sekiu River and the Victoria Sill. The Sekiu River is used as the western boundary in the Washington Department of Fish and Wildlife (WDFW) assessment of rockfishes (Palsson et al. , 2008). The BRT considered the Sekiu River a precautionary boundary in that it is very unlikely that any biologically relevant divisions would occur west of that point. The Victoria Sill bisects the Strait of Juan de Fuca and runs from east of Port Angeles north to Victoria. This sill is a significant oceanographic feature in the Strait of Juan de Fuca. The deep oceanic water in the Juan de Fuca Strait extends up to a depth of about 100 m (328 feet) at the Pacific end of the strait, and its thickness diminishes along the strait to just a few meters at the Victoria Sill (Masson, 2002). Patterns of circulation created by the sill create discontinuities in temperature, salinity (Masson and Cummins, 2000), nitrogen (Mackas and Harrison, 1997), primary production (Foreman et al. , 2008), and water column organic carbon (Johannessen et al. , 2008). The Victoria Sill also appears to have the potential to restrict larval dispersal (Engie and Klinger, 2007; Paul Chittaro, NWFSC, unpublished data)

f circulation created by the sill create discontinuities in temperature, salinity (Masson and Cummins, 2000), nitrogen (Mackas and Harrison, 1997), primary production (Foreman et al. , 2008), and water column organic carbon (Johannessen et al. , 2008). The Victoria Sill also appears to have the potential to restrict larval dispersal (Engie and Klinger, 2007; Paul Chittaro, NWFSC, unpublished data). Using the FEMAT voting procedure described previously, BRT members distributed their votes among the two western boundary options. Victoria Sill received 72 percent of the votes. Thus, the BRT concluded that the Victoria Sill likely represents the western boundary in this DPS scenario. We concur.

Extinction Risk Assessment

The ESA (Section 3) defines “endangered species” as “any species which is in danger of extinction throughout all or a significant portion of its range.” “Threatened species” is defined as “any species which is likely to become an endangered species within the foreseeable future throughout all or a significant portion of its range.” We consider a variety of factors in evaluating the level of risk faced by a DPS, including: (1) absolute numbers of fish and their spatial and temporal distributions, (2) current abundance and carrying capacity of the habitat in relation to historical abundance and carrying capacity, (3) trends in abundance, based on indices such as catch statistics, catch per unit effort (CPUE), and spawner-recruit ratios, (4) climate variability, and (5) size distribution of adult fish. Additional risk factors, such as disease prevalence or evolution in life-history traits, also may be considered in the evaluation of risk to a population. The discussion that follows describes each of these considerations, which we then incorporate in the risk discussion below for each species, as relevant.

Absolute Numbers

The absolute number of individuals in a population is important in assessing two aspects of extinction risk

ase prevalence or evolution in life-history traits, also may be considered in the evaluation of risk to a population. The discussion that follows describes each of these considerations, which we then incorporate in the risk discussion below for each species, as relevant.

Absolute Numbers

The absolute number of individuals in a population is important in assessing two aspects of extinction risk. First, small populations may not be sustainable in the face of environmental fluctuations and small-population stochasticity, even if the population currently is stable or increasing (Gilpin and Soule, 1986; Thompson, 1991). Second, present abundance in a declining population is an indicator of the time expected until the population reaches critically low numbers (Caughley and Sinclair, 1994). In addition to absolute numbers, the spatial and temporal distributions of adult population sizes are important in assessing risk to a DPS.

Assessments of marine fish populations have focused on determining abundance and trends from models fit to catch, survey, and biological data. Catch records, fishery and survey catch per unit effort (CPUE), and biomass estimates from research cruises constitute most of the data available to estimate population abundance. The estimated numbers of reproductive adults is the most important measure of abundance in assessing the status of a population. Data on other life-history stages can be used as a supplemental indicator of abundance. In the case of the five petitioned species, very little information is available on their absolute abundance in the Georgia Basin and Puget Sound. Though the BRT did estimate the size of the five petitioned rockfish species using estimates of total rockfish abundance presented in Palsson et al. (2008), the BRT focused largely on trends in various abundance indices.

Historical Abundance and Carrying Capacity

An understanding of historical abundance and carrying capacity can provide insights into a population's sustainability under current conditions

BRT did estimate the size of the five petitioned rockfish species using estimates of total rockfish abundance presented in Palsson et al. (2008), the BRT focused largely on trends in various abundance indices.

Historical Abundance and Carrying Capacity

An understanding of historical abundance and carrying capacity can provide insights into a population's sustainability under current conditions. For example, estimates of historical abundance provide the basis for establishing long-term abundance trends and also provide a benchmark for an abundance that was presumably sustainable. A comparison of past and present habitat capacity can also indicate long-term population trends from habitat loss, as well as potential habitat fragmentation, which can affect population viability. For a species that is at low abundance or has experienced declines in abundance, a comparison of current abundance to current carrying capacity may provide insight into the causes for decline and the potential for recovery.

Trends in Abundance

Short- and long-term trends in abundance serve as primary indicators of risk in natural populations. Trends may be calculated with a variety of quantitative data, including catch, CPUE, and survey data. Trend analyses for the five species considered in this status review are limited by the lack of long time series of abundances in greater Puget Sound for these species. In addition, although abundance time series are available for other, more common, Puget Sound rockfish species, these time series are characterized by a lack of regular sampling, by use of different survey methods for each species, and, for harvest data, by the effect of frequently revised harvest regulations. The BRT took several approaches to utilize the best available data in order to estimate the abundance trends, and these are discussed in greater detail below

more common, Puget Sound rockfish species, these time series are characterized by a lack of regular sampling, by use of different survey methods for each species, and, for harvest data, by the effect of frequently revised harvest regulations. The BRT took several approaches to utilize the best available data in order to estimate the abundance trends, and these are discussed in greater detail below.

Climate Variability

Coupled changes in atmospheric and ocean conditions have occurred on several different time scales and have influenced the geographical distributions, and hence local abundances, of marine fishes. On time scales of hundreds of millennia, periodic cooling produced several glaciations in the Pleistocene Epoch (Imbrie et al. , 1984; Bond et al. , 1993). The central part of greater Puget Sound was covered with ice about 1 km (0.6 miles) thick during the last glacial maximum about 14,000 years ago (Thorson, 1980). Since the end of this major period of cooling, several population oscillations of pelagic fishes, such as anchovies and sardines, have been noted on the West Coast of North America (Baumgartner et al. , 1992). These oscillations, with periods of about 100 years, have presumably occurred in response to climatic variability. On decadal time scales, climatic variability in the North Pacific and North Atlantic Oceans has influenced the abundances and distributions of widespread species, including several species of Pacific salmon (Francis et al. , 1998, Mantua et al. , 1997) in the North Pacific, and Atlantic herring (Alheit and Hagen, 1997) and Atlantic cod (Swain, 1999) in the North Atlantic. Recent declines in marine fish populations in greater Puget Sound may reflect recent climatic shifts. However, we do not know whether these climatic shifts represent long-term changes or short-term fluctuations that may reverse in the near future

. , 1998, Mantua et al. , 1997) in the North Pacific, and Atlantic herring (Alheit and Hagen, 1997) and Atlantic cod (Swain, 1999) in the North Atlantic. Recent declines in marine fish populations in greater Puget Sound may reflect recent climatic shifts. However, we do not know whether these climatic shifts represent long-term changes or short-term fluctuations that may reverse in the near future. Although recent climatic conditions appear to be within the range of historical conditions, the risks associated with climatic changes may be exacerbated by human activities (Lawson, 1993).

Size Distributions

Fisheries often target larger, older, more mature fish, resulting in a population with fewer such individuals than an unfished population would have. Older females generally produce more larvae, and their larvae survive at higher rates, than those of younger females. Thus their removal can decrease the productivity of the overall population, particularly for slow-growing, long-lived species such as rockfish.

The BRT reported that size-frequency distributions for bocaccio in the 1970s included a wide range of sizes, with recreationally caught individuals from 25 to 85 cm (10 to 33 inches) in length. This broad size distribution suggests a spread of ages, with some successful recruitment over multiple years. A similar range of sizes is also evident in data from the 1980s. These patterns are more likely to result from a self-sustaining population within the Georgia Basin rather than sporadic immigration or recruitment from coastal populations. The temporal trend in size distributions for bocaccio also suggests size truncation of the population, with larger fish becoming less common over time until the 1990s. By the decade of the 2000s, no bocaccio data were

The BRT reported that canary rockfish exhibited a broad spread of sizes in the 1970s. However, by the 2000s, there were far fewer size classes represented and no fish greater than 55 cm (22 inches) were recorded in the recreational data

so suggests size truncation of the population, with larger fish becoming less common over time until the 1990s. By the decade of the 2000s, no bocaccio data were

The BRT reported that canary rockfish exhibited a broad spread of sizes in the 1970s. However, by the 2000s, there were far fewer size classes represented and no fish greater than 55 cm (22 inches) were recorded in the recreational data. Although some of this truncation may be a function of the overall lower number of sampled fish, the data in general suggest few older fish remain in the population.

For yelloweye rockfish, the BRT reported that recreationally caught fish in the 1970s spanned a broad range of sizes. By the decade of the 2000s, there was some evidence of fewer older fish in the population. However, overall numbers of fish in the database were also much lower, making it difficult to determine if size truncation occurred.

For greenstriped and redstripe rockfish, the BRT noted that these species have a small maximum size. Although common in the recreational catch data for the 1970s and 1980s, greenstriped rockfish are represented by few individuals in catch data from the 1990s and 2000s. Size distributions do not suggest any size truncation over this time period. Low numbers reported in the catch may be a function of decreasing bag limits over time, and the likelihood of discarding of this less desired species by recreational fishermen. Large numbers of redstripe were retained by fishermen in the 1980s, but very few were available in the database for the 1990s and 2000s. There was no evidence of size truncation in this species over time, but too few fish were measured in the later decades to provide a meaningful analysis.

Risk Assessment Methods

In assessing risk, NMFS BRTs consider the best scientific information available, which often includes both qualitative and quantitative information

, but very few were available in the database for the 1990s and 2000s. There was no evidence of size truncation in this species over time, but too few fish were measured in the later decades to provide a meaningful analysis.

Risk Assessment Methods

In assessing risk, NMFS BRTs consider the best scientific information available, which often includes both qualitative and quantitative information. In previous NMFS status reviews, BRTs have used a “risk matrix” method to organize and summarize the professional judgment of a panel of professional scientists regarding the degree of risk facing a species based on the available information. This approach is described in detail by Wainright and Kope (1999) and has been used for over 10 years in Pacific salmonid status reviews (e.g., Good et al. , 2005; Hard et al. , 2007), as well as in reviews of Pacific hake, walleye pollock, Pacific cod (Gustafson et al. , 2000), Puget Sound rockfishes (Stout et al. , 2001b), Pacific herring (Stout et al. 2001a; Gustafson et al. , 2006), and black abalone (Butler et al. , 2008). In this risk matrix approach, the collective condition of individual populations is summarized at the DPS level according to four demographic risk criteria: abundance, growth rate/productivity, spatial structure/connectivity, and diversity. These viability criteria, outlined in McElhany et al. (2000), reflect concepts that are well founded in conservation biology and are generally applicable to a wide variety of species. These criteria describe demographic risks that individually and collectively provide strong indicators of extinction risk. The summary of demographic risks and other pertinent information obtained by this approach is then considered by the BRT in determining the species' overall level of extinction risk.

After reviewing all relevant biological information for the species, each BRT member assigns a risk score to each of the four demographic criteria

ually and collectively provide strong indicators of extinction risk. The summary of demographic risks and other pertinent information obtained by this approach is then considered by the BRT in determining the species' overall level of extinction risk.

After reviewing all relevant biological information for the species, each BRT member assigns a risk score to each of the four demographic criteria. The scoring for the risk criteria correspond to the following values: 1-very low risk, 2-low risk, 3-moderate risk, 4-high risk, 5-very high risk. The scores were tallied (means, modes, and range of scores), reviewed, and the range of perspectives discussed by the BRT before making its overall risk determination. Although this process helps to integrate and summarize a large amount of diverse information, the risk matrix scores do not always translate directly into a determination of overall extinction risk. Other factors must be considered. For example, a DPS with a single extant sub-population might be at a high level of extinction risk because of high risk to spatial structure/connectivity, even if it exhibited low risk for the other demographic criteria. Another species might be at risk of extinction because of moderate risks to several demographic criteria.

After completing the risk matrix approach for each DPS, the BRT evaluated their overall extinction risk. The BRT was asked to use three categories of risk to describe the species' status “high risk” of extinction; “moderate risk” of extinction; or “not at risk” of extinction. To allow individuals to express uncertainty in determining the overall level of extinction risk facing the species, the BRT adopted the “likelihood point” method referred to previously.

Abundance Trends Data Reviewed by the BRT

The main data available on Puget Sound rock sh trends are from surveys of recreational anglers conducted by WDFW. These data are collected from punch cards sent in by licensed anglers and from dockside surveys

ty in determining the overall level of extinction risk facing the species, the BRT adopted the “likelihood point” method referred to previously.

Abundance Trends Data Reviewed by the BRT

The main data available on Puget Sound rock sh trends are from surveys of recreational anglers conducted by WDFW. These data are collected from punch cards sent in by licensed anglers and from dockside surveys. WDFW extrapolates the rock sh per angler data up to total catch using an estimate of number of trips derived from the salmon recreational shery. The data are reported both for the targeted catch (targeting bottom sh) and the incidental catch (targeting salmon). For the trend analyses conducted by the BRT, only the data from the shery targeting bottomfish were used because the bottomfish information was recorded in an inconsistent fashion in the salmon catch report (Drake et al. , 2008). The BRT utilized data covering the time period from 1965-2007.

The recreational data have numerous limitations. In particular, during 1994 to 2003, the total catch was still estimated using salmon shery data, yet restrictions on the salmon shery resulted in limited information. In addition, the bag limit on rock sh was lowered from 15 sh in 1983 to 1 rock sh per trip in both the north Puget Sound and Puget Sound Proper in 2000. Reductions in bag limits both directly reduce the sh per trip by capping the maximum and may lead to changes in angler targeting leading to reductions in the number of rock sh taken per trip. To correct for the effects of bag limits and changes in angler targeting, the trend analyses conducted by the BRT treated each bag limit period as a separate dataset and a scaling parameter to adjust the mean for each period was estimated.

Data from commercial fisheries were also examined by the BRT. Commercial data with effort information is available from records on the bottom trawl shery operating until 1988. Effort data (hours trawled) are available from 1955

ing, the trend analyses conducted by the BRT treated each bag limit period as a separate dataset and a scaling parameter to adjust the mean for each period was estimated.

Data from commercial fisheries were also examined by the BRT. Commercial data with effort information is available from records on the bottom trawl shery operating until 1988. Effort data (hours trawled) are available from 1955. Due to some concerns in the sheries literature about CPUE data from commercial sheries not correlating with actual population abundances, these data were not used for the trend analyses.

Data from the WDFW trawl survey (a shery independent survey) were included in the trend analysis conducted by the BRT. The survey is described in detail by Palsson et al. (2008). These trawl surveys cover 1987 to 2000, are depth stratified, and done in twelve regions. The rocky habitat used by bocaccio, canary rockfish and yelloweye rockfish is not effectively sampled by trawl gear, while the unconsolidated habitat used by redstripe rockfish and greenstriped rockfish can be trawled effectively. As a result, the BRT used the WDFW trawl survey data primarily with respect to the latter two species.

Another data source included in the BRT analysis is sightings of rock sh by recreational SCUBA divers throughout the Puget Sound as part of a program by

In addition to the data sources described above, the BRT reviewed numerous historical documents, short-term research projects, and graduate theses from regional universities. In general, historical reports confirm that the five petitioned species have consistently been part of the Puget Sound fish fauna

gs of rock sh by recreational SCUBA divers throughout the Puget Sound as part of a program by

In addition to the data sources described above, the BRT reviewed numerous historical documents, short-term research projects, and graduate theses from regional universities. In general, historical reports confirm that the five petitioned species have consistently been part of the Puget Sound fish fauna. For example, Kincaid (1919) noted that the family Scorpaenidae (which includes rockfishes) constituted “one of the most important and valuable groups of fishes found on the Pacific Coast.” He produced an annotated list of Puget Sound fishes that documented 13 species of rockfish that were known to inhabit Puget Sound, including two of the petitioned species reported with different common nanmes: the “orange rockfish” (S. pinniger) that was “abundant in deep water”, and the “red rockfish or red snapper” (S. ruberrimus), the largest of this group, “common in deep water” and “brought to market in considerable quantities.” Smith (1936) provided one of the first scientific reports on Puget Sound commercial fisheries focused on the fleet of otter trawlers which targeted flatfish landed for market in Seattle. The fishery occurred primarily over relatively soft-bottom areas. Seven rockfish species were indicated as being taken by this fishery, including three of the petitioned species “orange rockfish” (S. pinniger), “red snapper” (S. ruberrimus), and “olive-banded rock cod” (S. elongatus). Haw and Buckley's (1971) text on saltwater fishing in Washington marine waters, including Puget Sound, was designed to popularize recreational sport (hook and line) fishing in the region to the general public. Fishing locations and habitat preferences were indicated for three species of rockfish: canary, yelloweye, and bocaccio. Canary rockfish were found at depths over 150 feet (46 m) and were not restricted to rocky bottom areas

altwater fishing in Washington marine waters, including Puget Sound, was designed to popularize recreational sport (hook and line) fishing in the region to the general public. Fishing locations and habitat preferences were indicated for three species of rockfish: canary, yelloweye, and bocaccio. Canary rockfish were found at depths over 150 feet (46 m) and were not restricted to rocky bottom areas. This species occurred in certain locations as far south as Point Defiance and was taken in large numbers at Tacoma Narrows, but was considered more abundant in the San Juan Islands, North Puget Sound, and Strait of Juan de Fuca. Rockfish were found at depths over 150 feet (46 m) on rocky bottoms, and primarily occurred in north Puget Sound, the Strait, and the outer coast. Finally, bocaccio were frequently caught in the Tacoma Narrows.

Two documents (Delacy et al. , 1972; Miller and Borton, 1980) compiled all available data on Puget Sound fish species distributions and relative number of occurrences since 1971 and 1973, respectively, from the literature (including some records noted above), fish collections, unpublished log records, and other sources. Twenty-seven representatives of the family Scorpaenidae are listed in these documents, including all five species considered in this status review (total records indicated in parentheses): greenstriped rockfish (54): most records occur in Hood Canal, although they were also collected near Seattle, primarily associated with otter trawls; bocaccio (110): most records occur from the 1970's in Tacoma Narrows and Appletree Cove (near Kingston) associated with sport catch; canary rockfish (114): most records occur from the 1960s to 1970s in Tacoma Narrows, Hood Canal, San Juan Islands, Bellingham, and Appletree Cove associated with sport catch; redstripe rockfish (26): most records are from Hood Canal sport catch, although a few were also taken in Central Sound/Seattle; yelloweye rockfish (113): most records occur from the early 1970's in the San Juan Islands (Sucia Island) a

kfish (114): most records occur from the 1960s to 1970s in Tacoma Narrows, Hood Canal, San Juan Islands, Bellingham, and Appletree Cove associated with sport catch; redstripe rockfish (26): most records are from Hood Canal sport catch, although a few were also taken in Central Sound/Seattle; yelloweye rockfish (113): most records occur from the early 1970's in the San Juan Islands (Sucia Island) and Bellingham Bay associated with the sport catch.

Summary of Previous Risk Analyses

The WDFW conducted an extensive review of the current status of all Puget Sound rockfishes (Palsson et al. , 2008). The authors examined historic patterns of abundance, results of WDFW surveys, and ecosystem stressors to produce a qualitative risk assessment. Palsson et al. (2008) note a precipitous decline in several species of rockfish, including bocaccio, yelloweye rockfish, and canary rockfish. They concluded that fishery removals (including bycatch from other fisheries) are highly likely to limit recovery of depleted rockfish populations in Puget Sound. In addition, they concluded that habitat disruption, derelict fishing gear, low dissolved oxygen, chemical toxicants, and predation are moderate threats to Puget Sound rockfish populations.

WDFW evaluated the status of rockfishes in Puget Sound using information on fishery landings trends, surveys, and species composition trends (Musick et al. , 2000). Their evaluation was based on the American Fisheries Society's Criteria for Marine Fish Stocks (Musick et al. , 2000). This method uses biological information and life history parameters such as population growth rates, age at maturity, fecundity, maximum age, etc. These parameters in concert with information regarding population trends are used to classify populations as depleted, vulnerable, precautionary or healthy. WDFW interpreted “depleted” to mean that there is a high risk of extinction in the immediate future, while “vulnerable” was considered to be likely to be endangered or threatened in the near future

age at maturity, fecundity, maximum age, etc. These parameters in concert with information regarding population trends are used to classify populations as depleted, vulnerable, precautionary or healthy. WDFW interpreted “depleted” to mean that there is a high risk of extinction in the immediate future, while “vulnerable” was considered to be likely to be endangered or threatened in the near future. “Precautionary” was interpreted to mean that populations were reduced in abundance, but that population size was stable or increasing. After applying the criteria, WDFW concluded that yelloweye rockfish were depleted in both North and South Puget Sound. Canary rockfish were also considered depleted in North and South Puget Sound. Greenstriped rockfish and redstripe rockfish were both considered to be healthy. Bocaccio were considered to have a precautionary status. The precautionary status of bocaccio was the result of a lack of information for bocaccio, as well as their increased rarity in South Puget Sound.

An evaluation on the status of yelloweye rockfish was prepared for the Canadian Committee on the Status of Endangered Wildlife in Canada (COSEWIC). COSEWIC concluded that there are two designatable units of yelloweye rockfish in Canada: an “inside” designatable unit that encompasses the Strait of Georgia, Johnstone Strait and Queen Charlotte Strait, and an “outside” designatable unit that extends from southeast Alaska to northern Oregon. The two designatable units are distinguished on the basis of genetic information indicating restricted gene flow, and age at maturity. For the inside designatable unit, submersible surveys in 1984 and 2003 showed statistically nonsignificant declines in mean, median and maximum sightings per transect. Commercial handline and longline CPUEs declined 59 percent and 49 percent respectively from 1986 to 2004. Age and length information indicates that the proportion of old individuals declined from the 1980s into the early 1990s

rity. For the inside designatable unit, submersible surveys in 1984 and 2003 showed statistically nonsignificant declines in mean, median and maximum sightings per transect. Commercial handline and longline CPUEs declined 59 percent and 49 percent respectively from 1986 to 2004. Age and length information indicates that the proportion of old individuals declined from the 1980s into the early 1990s. Overall, the COSEWIC report concluded that yelloweye rockfish abundance has declined more than 30 percent in a third of a yelloweye generation. COSEWIC also conducted status reviews for canary rockfish and

Coastal populations of yelloweye rockfish, canary rockfish and bocaccio are considered “overfished” by the U.S. Pacific Fisheries Management Council.

Current Abundance

Because of a lack of systematic sampling targeting rare rockfishes, absolute estimates of population size of the petitioned species cannot be generated with any accuracy. However, a rough estimate of the order of magnitude of population size can be determined from information assembled by WDFW. Palsson et al. (2008) extrapolated results from a video survey to estimate the population size of the common rockfish species (copper rockfish, quillback rockfish, black rockfish and brown rockfish) in Puget Sound Proper as about 40,683 and in North Puget Sound as 838, 944. The BRT applied the percent frequency of the petitioned species in the recreational catch to these numbers to conclude that the population sizes of boccacio, yelloweye rockfish, and canary rockfish are quite small, probably less than 10,000 in Georgia Basin and less than 1,000 in Puget Sound Proper. The absolute abundance of greenstriped and redstripe rockfish are unknown, but these species appear highly abundant in certain areas (Drake et al. , 2008)

species in the recreational catch to these numbers to conclude that the population sizes of boccacio, yelloweye rockfish, and canary rockfish are quite small, probably less than 10,000 in Georgia Basin and less than 1,000 in Puget Sound Proper. The absolute abundance of greenstriped and redstripe rockfish are unknown, but these species appear highly abundant in certain areas (Drake et al. , 2008).

Abundance Trends

The BRT did not generate quantitative estimates of trend in abundance for the ve species in the current petition because the low sampling of the catches in many years, particularly the early years, provides insufficient yearly estimates. Because of the nature of the available data, the BRT used the overall trend in all rockfishes (heavily influenced by common species such as copper, brown, and quillback rockfishes) to make inferences about the magnitude of trend in the petitioned species. They did this by looking for changes in the frequency of the petitioned species relative to the common species. The BRT examined this evidence for changes in the frequency of the petitioned species in the recreational catch, WDFW trawl surveys, and REEF dive surveys. If the petitioned species are not declining as fast as the “total rock sh” time series, then their frequency should be increasing relative to other more common species. On the other hand, they should become less frequent if they are declining more quickly.

The three most common species during 1965-2007 in the North Puget Sound (black rockfish, copper rockfish and quillback rockfish) and Puget Sound Proper (brown rockfish, copper rockfish, and quillback rockfish) increased in proportion of the total from 1980 through 1990, and currently comprise approximately 90 percent of the recreational catch. Four of the ve petitioned species (boccacio, canary rockfish, greenstriped rockfish, and yelloweye rockfish) became progressively less frequent in the recreational catch during the same time period

d Proper (brown rockfish, copper rockfish, and quillback rockfish) increased in proportion of the total from 1980 through 1990, and currently comprise approximately 90 percent of the recreational catch. Four of the ve petitioned species (boccacio, canary rockfish, greenstriped rockfish, and yelloweye rockfish) became progressively less frequent in the recreational catch during the same time period.

Estimates of the declining trend in the total population of rockfish in Puget Sound were approximately 3 percent per year, although this figure varied depending on what assumptions were included in the model estimating the trend (see Drake et al. , 2008 for details). This rate of annual decline corresponds to an average decline of about 70 percent over the 1965-2007 time period the BRT examined. Since the relative frequency of the petitioned species declined, the BRT concluded that the decline of the petitioned species must have been greater than the 70 percent observed in the total rockfish population.

Extinction Risk Assessment Conclusions

Bocaccio

The BRT concluded that the bocaccio Georgia Basin DPS is at “high risk” of extinction throughout all of its range. Bocaccio appear to have declined in frequency in Puget Sound Proper, relative to other species, from the 1970s to the present. From 1975-1979, bocaccio were reported as an average of 4.63 percent of the total rockfish catch. From 1980-1989, they were 0.24 percent of the rock sh identified, and from 1996 to 2007, bocaccio have not been observed out of the 2238 rock sh identified in the dockside surveys of the recreational catches. In a sample this large, the probability of observing at least 1 bocaccio would be 99.5 percent assuming it was at the same frequency (0.24 percent) as in the 1980s. The BRT concluded that there is strong support in the data for a decline in the frequency of bocaccio relative to other species in Puget Sound Proper

t of the 2238 rock sh identified in the dockside surveys of the recreational catches. In a sample this large, the probability of observing at least 1 bocaccio would be 99.5 percent assuming it was at the same frequency (0.24 percent) as in the 1980s. The BRT concluded that there is strong support in the data for a decline in the frequency of bocaccio relative to other species in Puget Sound Proper. The BRT noted that other data sources (SCUBA surveys) indicate that although rare, bocaccio rock sh were present in Puget Sound Proper as recently as 2001. Relying on the estimate of Palsson et al. (2008) of 40,683 rockfish in Puget Sound Proper, a 0.24 percent frequency rate would mean there were about 100 individual bocaccio in Puget Sound Proper in the 1980's. In North Puget Sound, bocaccio have always been rare in the surveys of the recreational shery. In the Strait of Georgia, bocaccio have been documented in some inlets, but records are sparse, isolated, and often based on anecdotal reports (COSEWIC, 2002).

A majority of the BRT concluded that the downward population size trend was, by itself, sufficient to indicate that the Georgia Basin DPS of bocaccio had a high risk of extinction. The BRT was also concerned that bocaccio as a species have a very low intrinsic rate of population growth, even in the absence of harvest or other threats that may limit productivity, and the size distribution of bocaccio in Puget Sound appeared to be trending toward smaller, less productive sizes (see above). Bocaccio are also characterized by highly variable recruitment that may be largely driven by environmental conditions which may occur only infrequently (Tolimieri and Levin, 2005). Even in the absence of continued exploitation, the BRT therefore concluded that Georgia Basin bocaccio were at risk due to their low abundance and low intrinsic population growth rate

less productive sizes (see above). Bocaccio are also characterized by highly variable recruitment that may be largely driven by environmental conditions which may occur only infrequently (Tolimieri and Levin, 2005). Even in the absence of continued exploitation, the BRT therefore concluded that Georgia Basin bocaccio were at risk due to their low abundance and low intrinsic population growth rate.

Threats to this DPS include areas of low dissolved oxygen within their range, the potential for continued losses as bycatch in recreational and commercial harvest, and the reduction of kelp habitat necessary for juvenile recruitment. The BRT's conclusions regarding the overall risk to the Georgia Basin bocaccio DPS were weighted to “high risk” (66 percent) with substantially less support for “moderate risk” (32 percent) and almost no support for “not at risk” (2 percent).

Although there have been no confirmed observations of bocaccio in Georgia Basin for approximately 7 years, the BRT concluded that there was no compelling reason to believe that the DPS has been extirpated. In particular, although it has disappeared from the recreational catch, the recreational fishery does not provide a complete sampling of Georgia Basin. Given the lack of an intensive effort to completely enumerate bocaccio, and the long life-span of the species, the BRT concluded that it is likely that the DPS still exists at a very low abundance and would be observed with a sufficiently intensive observation program.

Yelloweye Rockfish

The BRT concluded that the yelloweye rockfish Georgia Basin DPS is at “moderate risk” of extinction throughout all of its range. The frequency of yelloweye rock sh in Puget Sound Proper does not show a consistent trend, with percent et al. (2008) of 40,683 rockfish in Puget Sound Proper, a 3 percent frequency rate would mean there are about 1,200 individual canary rockfish in Puget Sound Proper

The BRT concluded that the yelloweye rockfish Georgia Basin DPS is at “moderate risk” of extinction throughout all of its range. The frequency of yelloweye rock sh in Puget Sound Proper does not show a consistent trend, with percent et al. (2008) of 40,683 rockfish in Puget Sound Proper, a 3 percent frequency rate would mean there are about 1,200 individual canary rockfish in Puget Sound Proper. In North Puget Sound, however, the frequency of yelloweye rock sh decreased from a high of greater than 3 percent in the 1970s to a frequency of 0.65 percent in the most recent samples. Based on this decline in frequency in North Puget Sound, combined with the overall decline in rockfish abundance in Puget Sound, the BRT concluded that the current trend in abundance contributes significantly to the extinction risk of the DPS. Like bocaccio and canary rockfish, the BRT also noted that the low intrinsic productivity combined with continuing threats from bycatch in commercial and recreational harvest, loss of near shore habitat, chemical contamination, and areas of low dissolved oxygen, increase the extinction risk of this species. The BRT further noted the downward trends in the size of yelloweye rockfish in Puget Sound (see above). The BRT's conclusions regarding the overall risk to the Georgia Basin canary rockfish DPS were heavily weighted toward “moderate risk” (59 percent), with minority support for “high risk” (23 percent) and “not at risk” (18 percent).

Canary Rockfish

The BRT concluded that the canary rockfish Georgia Basin DPS is at “moderate risk” of extinction throughout all of its range. There appears to be a steep decline in the abundance of canary rockfish in the Georgia Basin, reflected in the species becoming less frequent in the recreational rockfish catch data since 1965. In Puget Sound Proper, canary rockfish occurred at frequencies above 2 percent of the total rockfish catch in the 1960s and 1970s, but by the late 1990s had declined to about 0.76 percent. Relying on the estimate of Palsson et al

teep decline in the abundance of canary rockfish in the Georgia Basin, reflected in the species becoming less frequent in the recreational rockfish catch data since 1965. In Puget Sound Proper, canary rockfish occurred at frequencies above 2 percent of the total rockfish catch in the 1960s and 1970s, but by the late 1990s had declined to about 0.76 percent. Relying on the estimate of Palsson et al. (2008) of 40,683 rockfish in Puget Sound Proper, a 0.76-percent frequency rate would mean there are about 300 individual canary rockfish in Puget Sound Proper. In North Puget Sound, the frequency of canary rockfish exceeded 6 percent in the 1960s and declined to 0.56 percent in the 1990s. Based on this decline in frequency, combined with the overall decline in rockfish abundance in Puget Sound, the BRT concluded that the current trend in abundance contributes significantly to the extinction risk of the DPS.

The BRT also noted that the species' low intrinsic productivity combined with continuing threats from bycatch in commercial and recreational harvest, loss of near shore habitat, chemical contamination, and areas of low dissolved oxygen, increase the extinction risk of this species. The BRT further noted the downward trends in the size of the canary rockfish in Puget Sound (see above). The BRT noted that this species is more mobile than many other rockfish species, which may help preserve genetic diversity by increasing connectivity among breeding populations. However, the BRT noted the lack of specific information on canary rockfish population structure within the Georgia Basin, and that there does not appear to be a stronghold for canary rockfish anywhere within the range of the DPS. The BRT's conclusions regarding the overall risk to the Georgia Basin canary rockfish DPS were heavily weighted toward “moderate risk” (56 percent), with minority support for “high risk” (24 percent) and “not at risk” (20 percent)

anary rockfish population structure within the Georgia Basin, and that there does not appear to be a stronghold for canary rockfish anywhere within the range of the DPS. The BRT's conclusions regarding the overall risk to the Georgia Basin canary rockfish DPS were heavily weighted toward “moderate risk” (56 percent), with minority support for “high risk” (24 percent) and “not at risk” (20 percent).

Greenstriped Rockfish

The BRT concluded that the greenstriped rockfish Puget Sound Proper DPS is “not at risk” of extinction throughout all of its range. Greenstriped rock sh do not occur in the recreational catch data from North Puget Sound and occur very infrequently in the Puget Sound Proper recreational catch data, presumably due to the low value attached to this species. Bag limits were imposed in 1983 and the bag limit was further reduced in 1994 and 2000. Since greenstriped rock sh are smaller than other species, the bag limit may lead to discarding and thus under-representation of greenstriped rockfish in the recreational catch. Greenstriped rock sh appear in a low frequency in the WDFW sheries independent trawl survey, but they were caught in the most recent years of the WDFW trawl survey in Puget Sound Proper (in both 2002 and 2005). Thus, although greenstriped rock sh have not been reported from the recreational catch from 1999-2007, they are still present in Puget Sound Proper. The BRT noted the lack of information on the abundance trends of greenstriped rockfish, but noted that Puget Sound Proper has large areas of the unconsolidated habitats that are used by this species, and that this species has somewhat higher intrinsic productivity than other rockfish species. The BRT noted that this species is not preferred by recreational anglers, and may therefore be less susceptible to overharvest. Because this species is also more of a habitat generalist than many other rockfish, the BRT concluded it was not at risk from habitat loss or reduced diversity

d by this species, and that this species has somewhat higher intrinsic productivity than other rockfish species. The BRT noted that this species is not preferred by recreational anglers, and may therefore be less susceptible to overharvest. Because this species is also more of a habitat generalist than many other rockfish, the BRT concluded it was not at risk from habitat loss or reduced diversity. Size distributions do not suggest any size truncation since the 1970s. The BRT did note that areas of low dissolved oxygen are a potential risk factor. The BRT conclusions regarding the overall risk the DPS were weighted toward “not at risk” (59 percent), with “moderate risk” receiving minority support (32 percent) and “high risk” receiving very little support (9 percent).

Redstripe Rockfish

The BRT concluded that the redstripe rockfish Puget Sound Proper DPS is “not at risk” of extinction throughout all of its range. Redstripe rockfish do not occur in the catch data from North Puget Sound. In Puget Sound Proper, however, redstripe rock sh appeared frequently in the recreational catch (between 1-14 percent) from 1980 to 1985. Previous to that, from 1965 to 1979, redstripe rockfish appeared much less frequently (less than 1 percent). After 1985, the frequency of redstripe rockfish declined in the recreational data, and since 1996 it does not appear in the catch data. A bag limit was imposed in 1983 and the bag limit was further reduced in 1994 and 2000. Since redstripe rockfish are smaller than other species, bag limits may lead to discarding and thus under-representation of redstripe rockfish in the recreational catch. In the 1980s and 1990s, redstripe rockfish appeared at a low frequency (less than 1.5 percent) in the WDFW trawl survey. The frequency increased dramatically in 2002 and 2005, with redstripe rockfish making up 39 and 48 percent of the individuals caught

h are smaller than other species, bag limits may lead to discarding and thus under-representation of redstripe rockfish in the recreational catch. In the 1980s and 1990s, redstripe rockfish appeared at a low frequency (less than 1.5 percent) in the WDFW trawl survey. The frequency increased dramatically in 2002 and 2005, with redstripe rockfish making up 39 and 48 percent of the individuals caught. The BRT concluded that these high estimates may be statistical outliers, however, and are not necessarily indicative of an actual increase in abundance in recent years. However, the biomass of redstripe rockfish in the Puget Sound trawls was significantly higher in 2008 than in 1995, indicating a potential increase in abundance. The BRT also noted that the presence of redstripe rockfish in the WDFW trawl survey indicates that redstripe rockfish are present in Puget Sound but are no longer being recorded in the dockside surveys of the recreational catch, for undetermined reasons. Overall, the BRT noted that the total abundance and trends in abundance for this species were not well known, but concluded that the available data indicated that the species was at least locally abundant within Puget Sound.

The BRT also noted that this species has a shorter generation time and higher intrinsic rate of productivity than many other rockfish species. The BRT noted

Summary of Factors Affecting the Five DPSs of Rockfish

As described above, section 4(a)(1) of the ESA and NMFS implementing regulations (50 CFR 424) state that we must determine whether a species is endangered or threatened because of any one or a combination of the following factors: (1) the present or threatened destruction, modification, or curtailment of its habitat or range; (2) overutilization for commercial, recreational, scientific, or educational purposes; (3) disease or predation; (4) inadequacy of existing regulatory mechanisms; or (5) other natural or man-made factors affecting its continued existence

ned because of any one or a combination of the following factors: (1) the present or threatened destruction, modification, or curtailment of its habitat or range; (2) overutilization for commercial, recreational, scientific, or educational purposes; (3) disease or predation; (4) inadequacy of existing regulatory mechanisms; or (5) other natural or man-made factors affecting its continued existence. The primary factors responsible for the decline of these five DPSs of rockfishes are overutilization for commercial and recreational purposes, water quality problems including low dissolved oxygen, and inadequacy of existing regulatory mechanisms. The factors for decline are so similar for the petitioned DPSs of rockfish that they are addressed collectively in the following section. This section briefly summarizes findings regarding threats to the five DPSs of rockfishes. More details can be found in the draft status report (Drake et al. , 2008) and Palsson et al. (2008).

The Present or Threatened Destruction, Modification, or Curtailment of its Habitat or Range

The BRT identified habitat destruction as a threat to petitioned rockfish. In particular, loss of rocky habitat, loss of eelgrass and kelp, introduction of non-native species that modify habitat, and degradation of water quality were identified as specific threats to rockfish habitat in the Georgia Basin.

Adults of bocaccio, canary rockfish, and yelloweye rockfish are typically associated with rocky habitats. Palsson et al. (2008) report that such habitat is extremely limited in Puget Sound, with only 10 km 2 (3.8 sq miles) of such habitat in Puget Sound Proper, and 207 km 2 (80 sq miles) in North Puget Sound. Rocky habitat is more common in the Strait of Georgia and Strait of Juan de Fuca. Palsson et al. (2008) note that this habitat is threatened by, or has been impacted by, construction of bridges, sewer lines and other structures, deployment of cables and pipelines, and burying from dredge spoils and natural subtidal slope failures

Puget Sound Proper, and 207 km 2 (80 sq miles) in North Puget Sound. Rocky habitat is more common in the Strait of Georgia and Strait of Juan de Fuca. Palsson et al. (2008) note that this habitat is threatened by, or has been impacted by, construction of bridges, sewer lines and other structures, deployment of cables and pipelines, and burying from dredge spoils and natural subtidal slope failures.

Eelgrass, kelp, and other submerged vegetation provide important rockfish habitat, particularly for juveniles. In 2006, there were about 20,234 hectares (78 sq miles) of eelgrass in Puget Sound, with about a third of this in Padilla and Samish bays. Monitoring of eelgrass began in 2000, and although coverage declined until 2004, since that time it has remained unchanged throughout Puget Sound. Localized declines have occurred, with local losses in Hood Canal ranging from 1 to 22 percent per year ( Puget Sound Action Team, 2007). Kelp cover is highly variable and has shown long-term declines in some regions, while kelp beds have increased in areas where artificial substrate provides additional kelp habitat (Palsson et al. , 2008).

Non-indigenous species are an emerging threat to biotic habitat in Puget Sound. Sargassum muiticum is an introduced brown alga that is now common throughout much of the Sound. The degree to which Sargassum influences native macroalgae, eelgrass, or rockfish themselves is not presently understood. Several species of non-indigenous tunicates have been identified in Puget Sound. For example, Ciona savignyi was initially seen in one location in 2004, but within 2 years spread to 86 percent of sites surveyed in Hood Canal ( Puget Sound Action Team, 2007). The exact impact of invasive tunicates on rockfish or their habitats is unknown, but results in other regions (e.g., Levin et al. , 2002) suggest the potential for introduced invertebrates to have widespread impacts on rocky-reef fish populations

nyi was initially seen in one location in 2004, but within 2 years spread to 86 percent of sites surveyed in Hood Canal ( Puget Sound Action Team, 2007). The exact impact of invasive tunicates on rockfish or their habitats is unknown, but results in other regions (e.g., Levin et al. , 2002) suggest the potential for introduced invertebrates to have widespread impacts on rocky-reef fish populations.

Over the last century, human activities have introduced a variety of toxins into Puget Sound and the Georgia Basin at levels that may affect rockfish populations or the prey that support them. Several urban embayments in the Sound have high levels of heavy metals and organic compounds (Palsson et al. , 2008). About 32 percent of the sediments in Puget Sound are considered to be moderately or highly contaminated (Puget Sound Action Team, 2007). Organisms that live in or eat these sediments are consumed, thus transferring contaminants up the food web to higher level predators like rockfishes, and to a wider geographic area.

Not surprisingly, contaminants such as polychlorinated biphenyls (PCBs), chlorinated pesticides (e.g., DDT), and polybrominated diphenyl ethers (PBDEs) appear in rockfish collected in urban areas (Palsson et al. , 2008). However, while the highest levels of contamination occur in urban areas, toxins can be found in the tissues of animals in all regions of the sound (Team, 2007). Indeed, rockfish collected in rural areas of the San Juan Islands revealed high levels of mercury and hydrocarbons (West et al. , 2002).

Although risks from contaminants can affect all life history stages of rockfish, few studies have investigated the effects of toxins on rockfish ecology or physiology. Contaminants may influence growth rates of rockfish. For example, Palsson et al. (2008) describe a case in which male rockfish have lower growth rates than females an unusual pattern for rockfish since males typically grow faster than females

isks from contaminants can affect all life history stages of rockfish, few studies have investigated the effects of toxins on rockfish ecology or physiology. Contaminants may influence growth rates of rockfish. For example, Palsson et al. (2008) describe a case in which male rockfish have lower growth rates than females an unusual pattern for rockfish since males typically grow faster than females. The explanation may be that male rockfish tend to accumulate PCBs while female's body burden does not increase with time since they reduce their toxin level when they release eggs. Thus, the observed difference in growth rate may result from the higher contaminant concentration in males versus females.

Rockfish may also experience reproductive dysfunction as a result of contaminant exposure. Although no studies have shown an effect on rockfish, other fish in Puget Sound that have been studied do show a substantial impact. For instance, in English sole, reproductive function is reduced in animals from contaminated areas, and this effectively decreases the productivity of the species (Landahl et al. , 1997).

The full effect of contaminants on rockfish in the Georgia Basin remains unknown, but there is clearly a potential for impact. Unfortunately, good physical rockfish habitat is located in areas that are now subject to high levels of contaminants. This is evidenced by the fact that rockfish were historically captured in great numbers in these areas (compare Palsson et al. , 2008 and Puget Sound Action Team, 2007). Palsson et al. (2008) suggest that these areas, often in urban embayments, have become de facto no-take zones because people avoid fishing there. Now, many of the areas where rockfish are not subjected to

In addition to chemical contamination, water quality in Puget Sound is also influenced by sewage, animal waste, and nutrient inputs. The Washington Department of Ecology has been monitoring water quality in Puget Sound for several decades

s, often in urban embayments, have become de facto no-take zones because people avoid fishing there. Now, many of the areas where rockfish are not subjected to

In addition to chemical contamination, water quality in Puget Sound is also influenced by sewage, animal waste, and nutrient inputs. The Washington Department of Ecology has been monitoring water quality in Puget Sound for several decades. Monitoring includes fecal coliform, nitrogen, ammonium, and dissolved oxygen. In 2005, of the 39 sites sampled, 8 were classified as highest concern, and 10 were classified as high concern. Low levels of dissolved oxygen have been an increasing concern. Hood Canal has seen persistent and increasing areas of low dissolved oxygen since the mid 1990s. Typically, rockfish move out of areas with dissolved oxygen less than 2 mg/l; however, when low dissolved oxygen waters were quickly upwelled to the surface in 2003, about 26 percent of the rockfish population was killed (Palsson et al. , 2008). In addition to Hood Canal, Palsson et al. (2008) report that periods of low dissolved oxygen are becoming more widespread in waters south of Tacoma Narrows.

Overutilization for Commercial, Recreational, Scientific or Educational Purposes

The BRT and WDFW (Palsson et al. 2008) identify overutilization for commercial and recreational purposes as the most severe threat to petitioned rockfish in the Georgia Basin. Because individual species of rockfish were historically not indentified in fisheries statistics, it is impossible to estimate rates of fishing mortality and thus impossible to conduct a detailed quantitative analysis of the effects of fishing on rockfish populations. Nonetheless, there is little doubt that overfishing played a major role in the declines of rockfish in Puget Sound (Drake et al. , 2008; Palsson et al. , 2008)

f rockfish were historically not indentified in fisheries statistics, it is impossible to estimate rates of fishing mortality and thus impossible to conduct a detailed quantitative analysis of the effects of fishing on rockfish populations. Nonetheless, there is little doubt that overfishing played a major role in the declines of rockfish in Puget Sound (Drake et al. , 2008; Palsson et al. , 2008). Moreover, the life histories of the petitioned species (especially bocaccio, canary rockfish, and yelloweye rockfish) make them highly susceptible to overfishing and, once populations are at a low level, recovery can require decades (Levin et al. , 2006; Love et al. , 2002; Parker et al. , 2000). In particular, rockfish grow slowly, have a long life span and low natural mortality rates, mature late in life, often have sporadic reproductive success from year to year, may display high fidelity to specific habitats and locations, and require a diverse genetic and age structure to maintain healthy populations (Love et al. , 2002).

Estimates of rockfish harvest in Puget Sound are available for the last 87 years (Palsson et al. , 2008). Commercial harvest was very low prior to World War II, rose during the War, and then averaged 125,000 pounds (56,700 kg) between 1945 and 1970. In the 1970s, harvest increased dramatically, peaking in 1980 at 880,000 pounds (399,200 kg). Catches remained high until the early 1990s and then declined dramatically (Palsson et al. , 2008). From 1921-1970 a total of 3,812,000 pounds (1,729,000 kg) of rockfish were landed in Puget Sound, while nearly this same level of harvest (3,968,000 pounds; 1,800,000 kg) was achieved in only 7 years (from 1977-1983). The average annual harvest from 1977-1990 was nearly four times pre-1970 levels.

Although an estimate of fishing mortality is not available, some available evidence suggests that the fishing mortality experienced by the petitioned species would have been very high. Palsson et al

hile nearly this same level of harvest (3,968,000 pounds; 1,800,000 kg) was achieved in only 7 years (from 1977-1983). The average annual harvest from 1977-1990 was nearly four times pre-1970 levels.

Although an estimate of fishing mortality is not available, some available evidence suggests that the fishing mortality experienced by the petitioned species would have been very high. Palsson et al. (2008) provide a rough estimate of the total rockfish biomass in Puget Sound during the 1999-2004 time period of 3,205,521 pounds (1,454,000 kg) less than the total harvest from 1977-1983. Although the BRT considered the estimate provided by Palsson et al. (2008) as only a coarse estimate of biomass, it is clear that fishing removed a substantial fraction of the rockfish biomass during the 1977-1990 time frame. For comparison, exploitation rates for canary rockfish during the 1980s and 1990s along the U. S. Pacific Coast ranged from 5-19 percent (Stewart, 2007), bocaccio ranged from 5-31 percent (MacCall, 2008), and yelloweye rockfish ranged from less than 5 percent to about 17 percent (Wallace, 2007). In each of these cases, these high exploitation rates were followed by dramatic declines in population size (Sewart, 2007; Wallace, 2007; MacCall, 2008). Given the life history of rockfish and the level of harvest in Puget Sound, the BRT concurred with WDFW (Palsson et al. , 2008) and identified overutilization for commercial and recreational purposes as the most severe threat to petitioned rockfish in the Georgia Basin.

Fishery removals can affect both the absolute abundance of rockfish as well as the relative abundance of larger fish. Palsson et al. (2008) examined studies comparing rockfish populations in marine reserves in Puget Sound to populations outside reserves, and related this information to long-term trends in rockfish catch data, to draw conclusions about the effects of fishing on Puget Sound rockfish

Fishery removals can affect both the absolute abundance of rockfish as well as the relative abundance of larger fish. Palsson et al. (2008) examined studies comparing rockfish populations in marine reserves in Puget Sound to populations outside reserves, and related this information to long-term trends in rockfish catch data, to draw conclusions about the effects of fishing on Puget Sound rockfish. They noted that rockfish in marine reserves in Puget Sound generally are at higher densities than rockfish outside reserves. They considered this information in the context of steep declines in the catch of rockfish after the early 1980s to conclude that the current low abundance of rockfish in Puget Sound is likely the result of overfishing. They further noted that rockfish in marine reserves in Puget Sound are larger than rockfish outside the reserves. Coupled with information that the size of rockfish in Puget Sound has declined in recent decades, they concluded that fishing has also likely altered the age structure of rockfish populations by removing larger older individuals.

Age truncation (the removal of older fish) can occur at even moderate levels of fishing for rockfish (Berkeley et al. , 2004b). Age truncation has been widely demonstrated for Sebastes populations all along the west coast (Mason, 1998; Harvey et al. , 2006), even for species not currently categorized as overfished by the Pacific Fishery Management Council. It can have “catastrophic” effects for long-lived species such as rockfish (Longhurst, 2002). For Puget Sound rockfish, it is likely that the age truncation effects of past overfishing are long-lasting and may constitute an ongoing threat, particularly because older, larger, older females are likely to be more fecund.

In addition, fishing can have dramatic impacts on the size or age structure of the population, with effects that can influence ongoing productivity. Notably, declines in size and age of females can significantly impact reproductive success

cts of past overfishing are long-lasting and may constitute an ongoing threat, particularly because older, larger, older females are likely to be more fecund.

In addition, fishing can have dramatic impacts on the size or age structure of the population, with effects that can influence ongoing productivity. Notably, declines in size and age of females can significantly impact reproductive success. Below, we outline the evidence for maternal effects on reproductive success and discuss the possibility that such effects occur in the petitioned species.

Because most rockfish females release larvae on only one day each year (with a few exceptions in southern populations), the timing of parturition can be crucial in terms of matching favorable oceanographic conditions for larvae. Larger or older females release larvae earlier in the season compared to smaller or younger females in black, blue, yellowtail, kelp, and darkblotched rockfish (Sogard et al. , 2008; Nichol and Pikitch, 1994). Maternal effects on larval quality have been documented for black, blue, gopher, and yellowtail rockfish (Berkeley et al. , 2004; Sogard et al. , 2008). The mechanism for maternal effects on larval quality across species is the size of the oil globule provided to larvae at parturition, which provides the developing larva with energy insurance against the risks of starvation (Berkeley et al. , 2004; Fisher et al. , 2007), and in black rockfish enhances early growth rates (Berkeley et al. , 2004). An additional maternal effect in black rockfish indicates that older females are

In a broad span of species, there is evidence that age or size truncation is associated with increased variability in recruitment (e.g., Icelandic cod (Marteinsdottir and Thorarinsson, 1998), striped bass (Secor, 2000), Baltic cod (Wieland et al. , 2000), and a broad suite of California Current species (Hsieh et al. , 2006))

onal maternal effect in black rockfish indicates that older females are

In a broad span of species, there is evidence that age or size truncation is associated with increased variability in recruitment (e.g., Icelandic cod (Marteinsdottir and Thorarinsson, 1998), striped bass (Secor, 2000), Baltic cod (Wieland et al. , 2000), and a broad suite of California Current species (Hsieh et al. , 2006)). For long-lived species, reproduction over a span of many years is considered a bet-hedging strategy that has a buffering effect at the population level, increasing the likelihood of some successful reproduction over a period of variable environmental conditions (Longhurst, 2002). When reproductive effort is limited to younger ages, this buffering capacity is lost and populations more closely follow short-term fluctuations in the environment (Hsieh, 2006).

In summary, it is likely that past overfishing has reduced the abundance of the petitioned DPSs, leading to the current low abundance levels that place their future viability at risk. In addition, it is likely that past overfishing has reduced the proportion of large females in the petitioned DPSs, harming the productivity of the populations and affecting their ability to recover from current low levels of abundance. Ongoing fisheries also create risks for the petitioned DPSs, and are discussed below under The Inadequacy of Existing Regulatory Mechanisms.

Disease or Predation

The BRT identified predation as a threat to the five DPSs of rockfishes. Rockfish are important prey items of lingcod (Beaudreau and Essington, 2007). Populations of lingcod have been low in Puget Sound, but are increasing in recent years (Palsson et al. , 2008). Ruckelshaus et al. (in press) examined the potential effect of predation by lingcod on rockfish recovery

nisms.

Disease or Predation

The BRT identified predation as a threat to the five DPSs of rockfishes. Rockfish are important prey items of lingcod (Beaudreau and Essington, 2007). Populations of lingcod have been low in Puget Sound, but are increasing in recent years (Palsson et al. , 2008). Ruckelshaus et al. (in press) examined the potential effect of predation by lingcod on rockfish recovery. Their models indicate that even very small increases in predation mortality within marine protected areas (i.e., 1.2 percent) are sufficient to negate the benefit of zero fishing pressure that occurs within the protected areas.

Predation by pinnipeds may be locally significant. Four pinniped species are found in the waters of the State of Washington: harbor seals, California sea lions, Steller sea lions, and northern elephant seals. Harbor seal populations have increased from in the 100s during the 1970s to more than 10,000 at present (Jeffries et al. , 2003). The harbor seal is the only pinniped species that breeds in Washington waters, and is the only pinniped with known haul-out sites in the San Juan Islands (Jeffries et al. , 2000). Harbor seals are considered a threat to local fisheries in many areas (Bjorge et al. , 2002; Olesiuk et al. , 1990), and in Washington, Oregon, and California, consumption of rockfishes by California sea lions and harbor seals is estimated to be almost half of what is harvested in commercial fisheries (NMFS 1997). In Puget Sound, harbor seals are considered opportunistic feeders that consume seasonally and locally abundant prey (London et al. , 2001; Olesiuk et al. , 1990).

About 2,000 Steller sea lions occur seasonally in Washington waters, with dozens found in Puget Sound, particularly in the San Juan Islands (Palsson et al. , 2008). About 8 percent of the Steller sea lion diet is rockfish (Lance and Jeffries, 2007). Though not abundant, their large size and aggregated distribution suggest that their local impact on rockfish could be significant

k et al. , 1990).

About 2,000 Steller sea lions occur seasonally in Washington waters, with dozens found in Puget Sound, particularly in the San Juan Islands (Palsson et al. , 2008). About 8 percent of the Steller sea lion diet is rockfish (Lance and Jeffries, 2007). Though not abundant, their large size and aggregated distribution suggest that their local impact on rockfish could be significant.

Fifteen species of marine birds breed along the Washington coast; seven of these have historically been found breeding in the San Juan Islands/Puget Sound area (Speich and Wahl, 1989). The predominant breeding marine birds in the San Juan Islands are pigeon guillemots, double-crested cormorants, pelagic cormorants, and members of the western gull/glaucous-winged gull complex (Spe

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