Endangered Species Act (ESA) Section 7(a)(2) Biological Opinion and Magnuson-Stevens Fishery Conservation and Management Act Essential Fish Habitat (EFH) Consultation
Four Summer/Fall Chinook Salmon and Two Fall Chinook Salmon Hatchery Programs in the Upper Columbia River Basin
NMFS Consultation Number: WCR-2015-3607
Action Agencies: National Marine Fisheries Service (NMFS) U.S. Army Corps of Engineers (USACE)
Affected Species and Determinations: ESA-Listed Species Status Is the Action Is the Action Is the Action Likely to Adversely Likely To Likely To Affect Species or Jeopardize the Destroy or Critical Habitat? Species? Adversely Modify Critical Habitat? Chinook salmon (Oncorhynchus tshawytscha) Upper Columbia River Spring Endangered Yes No No Snake River Spring/Summer Threatened Yes No No Snake River Fall Threatened Yes No No Lower Columbia River Threatened Yes No No Upper Willamette River Spring Threatened Yes No No Steelhead (O. mykiss) Upper Columbia River Threatened Yes No No Snake River Threatened Yes No No Middle Columbia River Threatened Yes No No Lower Columbia River Threatened Yes No No Upper Willamette River Threatened Yes No No Sockeye salmon (O. nerka) Snake River Endangered Yes No No Chum salmon (O. keta) Columbia River Threatened Yes No No Coho salmon (O. kisutch) Lower Columbia River Threatened Yes No No Killer whales (Orcinus orca) Southern Resident Endangered No No No Green sturgeon (Acipenser medirostris) Southern Distinct Population No No No Threatened Segment Southern Distinct Population No No No Threatened Se ment
Pacific Coast Salmon No
Consultation Conducted By: National Marine Fisheries Service, West Coast Region, Sustainable Fisheries Division
Issued By: Barry A. T Regional
Date:
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TABLE OF CONTENTS
INTRODUCTION ...... 1 Background ...... 2 Consultation History ...... 2 Proposed Federal Action ...... 5 1.1.1. Chelan, Douglas, and Grant PUD Activities ...... 6 1.1.2. USACE Activities ...... 7 1.1.3. Hatchery Operator Activities ...... 7 1.1.3.1. Broodstock Collection and Mating ...... 9 1.1.3.2. Juvenile Rearing and Release ...... 10 1.1.3.3. Adult Management ...... 12 1.1.3.4. Facility Operations ...... 13 1.1.3.5. Research, Monitoring, and Evaluation (RM&E) ...... 15 1.1.4. Changes in Proposed Programs Since Last Biological Opinion ...... 15 Interrelated and Interdependent Actions ...... 16 ENDANGERED SPECIES ACT: BIOLOGICAL OPINION AND INCIDENTAL TAKE STATEMENT ..... 16 Analytical Approach ...... 16 Range-wide Status of the Species and Critical Habitat ...... 18 Status of Listed Species ...... 20 Upper Columbia River Spring Chinook Salmon ESU ...... 21 Snake River Spring/summer Chinook Salmon ESU ...... 23 Snake River Fall Chinook Salmon ESU ...... 25 Lower Columbia River Chinook Salmon ESU ...... 27 Upper Willamette River Spring Chinook Salmon ESU ...... 32 Upper Columbia River Steelhead DPS ...... 37 Snake River Steelhead DPS ...... 39 Mid-Columbia River Steelhead DPS ...... 40 Lower Columbia River Steelhead DPS ...... 44 Upper Willamette River Steelhead DPS ...... 47 Snake River Sockeye Salmon ESU ...... 54 Columbia River Chum Salmon ESU ...... 54 Lower Columbia River Coho Salmon ESU ...... 60 Range-wide Status of Critical Habitat ...... 65
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Climate Change ...... 68 Action Area ...... 68 Environmental Baseline ...... 68 Habitat and Hydropower (NMFS 2012a) ...... 68 Climate Change ...... 70 Hatcheries ...... 72 Harvest ...... 73 Effects on ESA Protected Species and on Designated Critical Habitat ...... 80 Factors That Are Considered When Analyzing Hatchery Effects ...... 80 Effects of the Proposed Action ...... 82 Factor 1. The hatchery program does or does not remove fish from the natural population and use them for broodstock ...... 82 Factor 2. Hatchery fish and the progeny of naturally spawning hatchery fish on spawning grounds and encounters with natural-origin and hatchery fish at adult collection facilities ...... 82 Factor 3. Hatchery fish and the progeny of naturally spawning hatchery fish in juvenile rearing areas, the migratory corridor, estuary, and ocean ...... 89 Factor 4. Research, monitoring, and evaluation that exists because of the hatchery program ...... 105 Factor 5. Construction, operation, and maintenance of facilities that exist because of the hatchery program ...... 106 Factor 6. Fisheries that exist because of the hatchery programs ...... 109 Cumulative Effects ...... 109 Integration and Synthesis ...... 111 UCR Spring Chinook Salmon ESU ...... 111 UCR Steelhead DPS ...... 113 Snake River ESUs/DPS, Mid-Columbia River Steelhead DPS, Columbia River Chum Salmon ESU, Lower Columbia River ESUs/DPS, and Upper Willamette River ESU/DPS...... 114 Critical Habitat ...... 116 Conclusion ...... 116 Incidental Take Statement ...... 117 Amount or Extent of Take ...... 118 Effect of the Take ...... 120 Reasonable and Prudent Measures ...... 120 Terms and Conditions ...... 120
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Conservation Recommendations ...... 122 Re-initiation of Consultation ...... 122 “Not Likely to Adversely Affect” Determinations ...... 122 Life History and Status of the Green Sturgeon Southern DPS ...... 123 Southern Resident Killer Whale DPS ...... 124 Eulachon ...... 126 MAGNUSON-STEVENS FISHERY CONSERVATION AND MANAGEMENT ACT ESSENTIAL FISH HABITAT CONSULTATION ...... 128 Essential Fish Habitat Affected by the Project ...... 128 Adverse Effects on Essential Fish Habitat ...... 128 Essential Fish Habitat Conservation Recommendations ...... 129 Statutory Response Requirement ...... 129 Supplemental Consultation ...... 130 DATA QUALITY ACT DOCUMENTATION AND PRE-DISSEMINATION REVIEW ...... 131 Utility ...... 131 Integrity ...... 131 Objectivity ...... 131 APPENDIX A-FACTORS CONSIDERED WHEN ANALYZING HATCHERY EFFECTS ...... 133 Factor 1. The hatchery program does or does not remove fish from the natural population and use them for hatchery broodstock ...... 135 Factor 2. Hatchery fish and the progeny of naturally spawning hatchery fish on spawning grounds and encounters with natural-origin and hatchery fish at adult collection facilities ...... 135 Genetic effects ...... 136 Ecological effects ...... 143 Adult Collection Facilities ...... 144 Factor 3. Hatchery fish and the progeny of naturally spawning hatchery fish in juvenile rearing areas ...... 144 Competition ...... 144 Predation ...... 146 Disease ...... 148 Acclimation ...... 149 Factor 4. Research, monitoring, and evaluation that exists because of the hatchery program ...... 150 Observing/Harassing ...... 151 Capturing/handling ...... 151
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Fin clipping and tagging ...... 151 Factor 5. Construction, operation, and maintenance, of facilities that exist because of the hatchery program ...... 153 Factor 6. Fisheries that exist because of the hatchery program ...... 153
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Table of Tables
Table 1. Programs* included in the Proposed Action...... 1 Table 2. Details of broodstock collection and mating for the six proposed programs...... 9 Table 3. Details of juvenile rearing and acclimation for the proposed programs...... 11 Table 4. Details of juvenile release for the proposed programs. CWT = coded-wire tag; PIT = passive integrated transponder...... 12 Table 5. Details of facility operations for the six proposed programs...... 14 Table 6. Summary of changes in programs since the last NMFS biological opinion ...... 15 Table 7. Federal Register notices for the final rules that list species, designate critical habitat, or apply protective regulations to ESA-listed species considered in this consultation...... 19 Table 8. Risk levels and viability ratings for natural-origin UCR spring Chinook salmon populations from the North Cascades MPG (NWFSC 2015)...... 23 Table 9. Risk levels and viability ratings for Snake River spring/summer Chinook salmon populations (NWFSC 2015); ICTRT = Interior Columbia Technical Recovery Team. Data are from 2005-2014...... 25 Table 10. LCR Chinook Salmon ESU description and MPGs (Jones Jr. 2015; NMFS 2013c; NWFSC 2015)...... 27 Table 11. Current status for LCR Chinook salmon populations and recommended status under the recovery scenario (NMFS 2013c)...... 28 Table 12. Life history and population characteristics of LCR Chinook salmon...... 31 Table 13. UWR Chinook salmon ESU description and major population group (MPG) (Jones Jr. 2015; NMFS 2016b)...... 32 Table 14. A summary of the general life history characteristics and timing of UWR Chinook salmon1...... 34 Table 15. Scores for the key elements (A/P, diversity, and spatial structure) used to determine current overall viability risk for UWR Chinook salmon (NMFS and ODFW 2011; NWFSC 2015)1...... 36 Table 16. Summary of VSP scores and recovery goals for UWR Chinook salmon populations (NWFSC 2015)...... 36 Table 17. Risk levels and viability ratings for natural-origin UCR steelhead populations (NWFSC 2015)...... 39 Table 18. Risk levels and viability ratings for Snake River steelhead populations (NWFSC 2015). Parentheses indicate range. Data are from 2004-2015. ID = insufficient data; ICTRT = Interior Columbia Technical Recovery Team...... 40 Table 19. MCR Steelhead DPS description and MPGs (Jones Jr. 2015; NWFSC 2015)...... 41 Table 20. Ecological subregions, natural populations, and scores for the key elements (A/P, diversity, and SS/D) used to determine current overall viability risk for MCR Steelhead DPS1. 43 Table 21. LCR Steelhead DPS description and MPGs (Jones Jr. 2015; NWFSC 2015)...... 44 Table 22. Current status for LCR steelhead populations and recovery scenario targets (NMFS 2013c)...... 46 Table 23. UWR Steelhead DPS description and MPGs.1 ...... 48 Table 24. A summary of the general life history characteristics and timing of UWR steelhead. Data are from (From ODFW 2010b)...... 50 Table 25. UWR Steelhead DPS natural-origin spawner abundance estimates for the four populations in the MPG from 1997-2008 (no data available after 2008) (ODFW Salmon & Steelhead Recovery Tracker1)*...... 52
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Table 26. Scores for the key elements (A/P, diversity, and spatial structure) used to determine current overall viability risk for UWR steelhead populations (NMFS 2011a).1...... 53 Table 27. Summary of VSP scores and recovery goals for UWR Steelhead populations (NWFSC 2015)...... 53 Table 28. CR Chum Salmon ESU description and MPGs. The designations “(C)” and “(G)” identify Core and Genetic Legacy populations, respectively (McElhany et al. 2003; Myers et al. 2006; NMFS 2013c)...... 55 Table 29. Current status for CR chum salmon populations and recommended status under the recovery scenario (NMFS 2013c)...... 55 Table 30. Peak spawning ground counts for fall chum salmon in index reaches in the LCR, and Bonneville Dam counts 2001-2014 (from WDFW SCORE1)*...... 58 Table 31. Columbia River Chum Salmon ESU populations and scores for the key elements (A/P, diversity, and spatial structure) used to determine current overall net persistence probability of the populations (NMFS 2013a).1 ...... 59 Table 32. Summary of VSP scores and recovery goals for CR chum salmon populations (NWFSC 2015)...... 60 Table 33. LCR Coho Salmon ESU description and MPGs (Jones Jr. 2011; NMFS 2013c)...... 61 Table 34. Current status for LCR coho salmon Gorge MPG populations and recommended status under the recovery scenario (NMFS 2013c)...... 61 Table 35. Life history and population characteristics of LCR coho salmon...... 63 Table 36. Natural-origin spawning escapement numbers and the proportion of natural spawners composed of hatchery-origin fish (pHOS) on the spawning grounds for LCR coho salmon populations in Oregon from 2002 through 2015 (http://www.odfwrecoverytracker.org/)*...... 64 Table 37. Natural-origin spawning escapement numbers and the proportion of all natural spawners composed of hatchery-origin fish (pHOS1) on the spawning grounds for LCR coho salmon populations in Washington from 2002 through 2015 (https://fortress.wa.gov/dfw/score/score/species/coho.jsp?species=Coho)*...... 64 Table 38. Upper Columbia River hatchery programs with releases in the action area...... 73 Table 39. Expected incidental take (as proportion of total run-size) of listed anadromous salmonids for non-Indian and treaty Indian fisheries included in the 2008 U.S. v. Oregon Agreement...... 73 Table 40. Annual post season performance of fisheries managed under the 2008 U.S. v. Oregon Agreement...... 76 Table 41. Summary of natural-origin UCR steelhead encounters associated with mark-selective steelhead fisheries above Priest Rapids Dam (2010-2016)...... 78 Table 42. Summary of natural-origin UCR steelhead and UCR spring Chinook salmon encounters associated with fisheries targeting non-listed fish above Priest Rapids Dam (2012- 2016)...... 79 Table 43. Timing of adult return and spawning for UCR salmonids...... 83 Table 44. Average number of hatchery-origin summer/fall and fall Chinook salmon straying into other basins...... 84 Table 45. Total phosphorous imported by adult returns from the proposed hatchery programs based on the equation, mean adult mass and phosphorous concentration in Scheuerell et al. (2005). Escapement and pHOS estimates from Hillman et al. (2017b), Richards and Pearsons (2015), and Snow et al. (2016)...... 85
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Table 46. Broodstock collection for summer/fall and fall Chinook salmon and associated biological opinions where effects on listed species have been already analyzed...... 87 Table 47. Parameters from the PCD Risk model that are the same across all programs...... 92 Table 48. Age and size of listed natural-origin salmon and steelhead encountered by juvenile hatchery fish after release...... 93 Table 49. Hatchery fish parameter values for the PCD Risk model run from release of fish to McNary Dam...... 93 Table 50. Hatchery fish parameter values for aggregate runs for the PCD Risk model, starting at McNary Dam and through the estuary...... 94 Table 51. Maximum numbers of juvenile natural-origin salmon and steelhead lost to predation (P) and competition (C) from hatchery-origin summer/fall and fall Chinook salmon from the Proposed Action for model runs from release to McNary Dam...... 96 Table 52. Maximum numbers of juvenile natural-origin salmon and steelhead lost to predation (P) and competition (C) with hatchery-origin summer/fall and fall Chinook salmon from the Proposed Action for aggregate model runs from McNary Dam through the estuary...... 98 Table 53. Comparison of results based on different travel times...... 99 Table 54. Maximum total ESA-listed natural-origin adult equivalents lost through competition and predation with juvenile hatchery fish by ESU/DPS compared to returning adults of respective ESU/DPS...... 101 Table 55. Pathogens detections in summer/fall or fall Chinook salmon reared for the proposed programs...... 104 Table 56. RM&E associated with the hatchery programs in the Proposed Action...... 105 Table 57. Program facility and water use ...... 106 Table 58. Facility water use compared to instream flow ...... 108 Table 59. Lost natural-origin adult equivalents compared to returning adults from each ESU/DPS at the mouth of the Columbia River...... 115 Table 60. Summary of NMFS determination of effects...... 117 Table 61. An overview of the range of effects on natural population viability parameters from the two categories of hatchery programs...... 134
Table of Figures
Figure 1. Map of facilities used in the Upper Columbia River Basin in the Proposed Action (Courtesy of Mike Tonseth, WDFW) ...... 8 Figure 2. Upper Columbia River Spring Chinook Salmon ESU (ICTRT 2008)...... 22 Figure 3. Map of the LCR Chinook Salmon ESU’s spawning and rearing areas, illustrating populations and MPGs. Several watersheds contain or historically contained both fall and spring runs; only the fall-run populations are illustrated here (NWFSC 2015)...... 30 Figure 4. Map of the UWR Chinook Salmon ESU’s spawning and rearing areas, illustrating populations and major population groups (From NWFSC 2015)...... 34 Figure 5. Upper Columbia River Steelhead DPS (ICTRT 2008)...... 38 Figure 6. Map of the MCR Steelhead DPS’s spawning and rearing areas, illustrating populations and MPGs (NWFSC 2015)...... 42 Figure 7. Map of populations in the LCR Steelhead DPS (NWFSC 2015)...... 45 Figure 8. UWR Steelhead DPS spawning and rearing areas, illustrating populations and MPGs (From NWFSC 2015)...... 49
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Figure 9. Map of the CR Chum Salmon ESU’s spawning and rearing areas, illustrating populations and major population groups (From NWFSC 2015)...... 56 Figure 10. Map of the LCR Coho Salmon ESU’s spawning and rearing areas, illustrating populations and MPGs (NWFSC 2015)...... 62 Figure 11. ICTRT (2007b) risk criteria associated with spawner composition for viability assessment of exogenous spawners on maintaining natural patterns of gene flow. Exogenous fish are considered to be all fish of hatchery origin, and non-normative strays of natural origin. .... 140 Figure 12. Relative proportions of types of matings as a function of proportion of hatchery-origin fish on the spawning grounds (pHOS)...... 143
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1 INTRODUCTION
2 The underlying activities that drive the Proposed Actions by the federal agencies are the funding 3 or issuance of permits for the operation of six hatchery programs rearing and releasing 4 summer/fall and fall (upriver bright) Chinook salmon (see Section 1.3 for details). Four of these 5 programs rear and release summer/fall Chinook salmon in the Upper Columbia River (UCR) 6 Basin, while the other two programs rear and release fall Chinook salmon in the Hanford Reach 7 area, all of which are in Washington State. Because the actions of the federal agencies are 8 subsumed within the effects of the hatchery program operation, the details of each hatchery 9 program are summarized in Section 1.3 of this biological opinion based on a Hatchery and 10 Genetic Management Plan (HGMP), which was submitted to NMFS for review. This 11 introduction section provides information relevant to the other sections of this document and is 12 incorporated by reference into Sections 2 and 3 below. 13 14 NMFS defines integrated hatchery programs as those that are reproductively connected or 15 “integrated” with a natural population, promote natural selection over selection in the hatchery, 16 contain genetic resources that represent the ecological and genetic diversity of a species, and are 17 included in a salmon ESU or steelhead DPS. When a hatchery program actively maintains 18 distinctions or promotes differentiation between hatchery fish and fish from a native population, 19 then NMFS refers to the program as “isolated” or “segregated.” Isolated programs promote 20 domestication or selection in the hatchery over selection in the wild and culture a stock of fish 21 with different phenotypes (e.g., different ocean migrations and/or spatial and temporal spawning 22 distribution) compared to the natural population. 23 24 Table 1. Programs* included in the Proposed Action.
Program Date1 Program Program Purpose Funding ESA Type Entity Pathway Chelan Falls March 23, 2010; Segregated Create terminal Chelan PUD Section 10 Summer/Fall May 5, 2014 Harvest fishery in Chelan Chinook Salmon River Wenatchee September 30, 2009; Integrated Create terminal Chelan PUD Section 10 Summer/Fall May 3, 2014 Supplementation fishery in Grant PUD Chinook Salmon Wenatchee and Columbia Rivers Methow September 30, 2009; Integrated Create terminal Grant PUD Section 10 Summer/Fall March 17, 2014 Supplementation fishery in Methow Chinook Salmon Columbia Rivers Wells Hatchery May 28, 2013; Segregated Create terminal Douglas PUD Section 10 Summer/Fall April 4, 2014 Harvest fishery in Chinook Salmon Columbia River Priest Rapids Fall August 26, 2005; Integrated Create terminal Grant PUD Section 10/ Chinook Salmon May 21, 2014 Harvest fishery in USACE Section 7 Columbia River Ringold Springs June 19, 2017 Integrated Create terminal USACE Section 7 Hatchery Fall Harvest fishery in Chinook Salmon Columbia River.
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1 * Currently, all of the hatchery programs are operated by the Washington Department of Fish and Wildlife (WDFW), 2 with the exception of operation of Wells Hatchery and early juvenile rearing for the Ringold Springs Hatchery Fall 3 Chinook Salmon program. 4 1 The first date is for the most recent HGMP. The second date is for the updated proposed action. 5 2 PUD = Public Utility District; USACE = U.S. Army Corps of Engineers. 6 7 Background
8 NMFS prepared the Biological Opinion (opinion) and incidental take statement (ITS) portions of 9 this document in accordance with section 7(b) of the ESA of 1973, as amended (16 U.S.C. 1531, 10 et seq.), and implementing regulations at 50 CFR 402. The opinion documents consultation on 11 the actions proposed by NMFS, the USFWS, and BOR. 12 13 NMFS also completed an Essential Fish Habitat (EFH) consultation on the proposed actions, in 14 accordance with section 305(b)(2) of the Magnuson-Stevens Fishery Conservation and 15 Management Act (MSA) (16 U.S.C. 1801, et seq.) and implementing regulations at 50 CFR 600. 16 17 We completed pre-dissemination review of this document using standards for utility, integrity, 18 and objectivity in compliance with applicable guidelines issued under the Data Quality Act 19 (section 515 of the Treasury and General Government Appropriations Act for Fiscal Year 2001, 20 Public Law 106-554). The document will be available through NMFS’ Public Consultation 21 Tracking System. A complete record of this consultation is on file at the Sustainable Fisheries 22 Division (SFD) of NMFS in Portland, Oregon. 23 24 Consultation History
25 The first hatchery consultations in the Columbia Basin followed the first listings of Columbia 26 Basin salmon under the ESA. Snake River sockeye salmon were listed as an endangered species 27 on November 20, 1991 (56 FR 58619), Snake River spring/summer Chinook salmon and Snake 28 River fall Chinook salmon were listed as a threatened species on April 22, 1992 (57 FR 14653), 29 and the first hatchery consultation and opinion was completed on April 7, 1994 (NMFS 1994). 30 The 1994 opinion was superseded by “Endangered Species Act Section 7 Biological Opinion on 31 1995-1998 Hatchery Operations in the Columbia River Basin, Consultation Number 383” 32 completed on April 5, 1995 (NMFS 1995b). This opinion determined that hatchery actions 33 jeopardize listed Snake River salmon and required implementation of reasonable and prudent 34 alternatives (RPAs) to avoid jeopardy. 35 36 A new opinion was completed on March 29, 1999, after UCR steelhead were listed under the 37 ESA (62 FR 43937, August 18, 1997) and following the expiration of the previous opinion on 38 December 31, 1998 (NMFS 1999). That opinion concluded that Federal and non-Federal 39 hatchery programs jeopardize Lower Columbia River (LCR) steelhead and Snake River 40 steelhead protected under the ESA and described RPAs necessary to avoid jeopardy. Those 41 measures and conditions included restricting the use of non-endemic steelhead for hatchery 42 broodstock and limiting stray rates of non-endemic salmon and steelhead to less than 5% of the 43 annual natural population in the receiving stream. Soon after, NMFS reinitiated consultation 44 when LCR Chinook salmon, UCR spring Chinook salmon, Upper Willamette Chinook salmon, 45 Upper Willamette steelhead, Columbia River chum salmon, and Middle Columbia steelhead 46 were added to the list of endangered and threatened species (Smith 1999).
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1 2 Between 1991 and the summer of 1999, the number of distinct groups of Columbia Basin salmon 3 and steelhead listed under the ESA increased from 3 to 12, and this prompted NMFS to reassess 4 its approach to hatchery consultations. In July 1999, NMFS announced that it intended to 5 conduct five consultations and issue five opinions “instead of writing one biological opinion on 6 all hatchery programs in the Columbia River Basin” (Smith 1999). Opinions would be issued for 7 hatchery programs in the (1) Upper Willamette, (2) Middle Columbia River (MCR), (3) LCR, (4) 8 Snake River, and (5) UCR, with the UCR NMFS’ first priority (Smith 1999). Between August 9 2002 and October 2003, NMFS completed consultations under the ESA for approximately 10 twenty hatchery programs in the UCR. For the MCR, NMFS completed a draft opinion, and 11 distributed it to hatchery operators and to funding agencies for review on January 4, 2001, but 12 completion of consultation was put on hold pending several important basin-wide review and 13 planning processes. 14 15 The increase in ESA listings during the mid to late 1990s triggered a period of investigation, 16 planning, and reporting across multiple jurisdictions and this served to complicate, at least from a 17 resources and scheduling standpoint, hatchery consultations. A review of Federal funded 18 hatchery programs ordered by Congress was underway at about the same time that the 2000 19 Federal Columbia River Power System (FCRPS) opinion was issued by NMFS (NMFS 2000a). 20 The Northwest Power and Conservation Council (Council) was asked to develop a set of 21 coordinated policies to guide the future use of artificial propagation, and RPA 169 of the FCRPS 22 opinion called for the completion of NMFS-approved hatchery operating plans (i.e., HGMPs) by 23 the end of 2003. The RPA required the Action Agencies to facilitate this process, first by 24 assisting in the development of HGMPs, and then by helping to implement identified hatchery 25 reforms. Also at this time, a new U.S. v. Oregon Columbia River Fisheries Management Plan 26 (CRFMP), which included goals for hatchery management, was under negotiation and new 27 information and science on the status and recovery goals for salmon and steelhead was emerging 28 from Technical Recovery Teams (TRTs). Work on HGMPs under the FCRPS opinion was 29 undertaken in cooperation with the Council’s Artificial Production Review and Evaluation 30 process, with CRFMP negotiations, and with ESA recovery planning (Foster 2004; Jones Jr. 31 2002). HGMPs were submitted to NMFS under RPA 169; however, many were incomplete and, 32 therefore, were not ready for ESA consultation. 33 34 ESA consultations and an opinion were completed in 2007 for nine hatchery programs that 35 produce a substantial proportion of the total number of salmon and steelhead released into the 36 Columbia River annually. These programs are located in the LCR and MCR and are operated by 37 the FWS and by the Washington Department of Fish and Wildlife (WDFW). NMFS’ opinion 38 (NMFS 2007) determined that operation of the programs would not jeopardize salmon and 39 steelhead protected under the ESA. 40 41 On May 5, 2008, NMFS published a Supplemental Comprehensive Analysis (SCA) (NMFS 42 2008h) and an opinion and RPAs for the FCRPS to avoid jeopardizing ESA-listed salmon and 43 steelhead in the Columbia Basin (NMFS 2008e). The SCA environmental baseline included “the 44 past effects of hatchery operations in the Columbia River Basin. Where hatchery consultations 45 have expired or where hatchery operations have yet to undergo ESA section 7consultation, the 46 effects of future operations cannot be included in the baseline. In some instances, effects are
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1 ongoing (e.g., returning adults from past hatchery practices) and included in this analysis despite 2 the fact that future operations cannot be included in the baseline. The Proposed Action does not 3 encompass hatchery operations per se, and therefore no incidental take coverage is offered 4 through this biological opinion to hatcheries operating in the region. Instead, we expect the 5 operators of each hatchery to address its obligations under the ESA in separate consultations, as 6 required” (see NMFS 2008h, p. 5-40). 7 8 Because it was aware of the scope and complexity of ESA consultations facing the co-managers 9 and hatchery operators, NMFS offered substantial advice and guidance to help with the 10 consultations. In September 2008, NMFS announced its intent to conduct a series of ESA 11 consultations and that “from a scientific perspective, it is advisable to review all hatchery 12 programs (i.e., Federal and non-Federal) in the UCR affecting ESA-listed salmon and steelhead 13 concurrently” (Walton 2008). In November 2008, NMFS expressed again, the need for re- 14 evaluation of UCR hatchery programs and provided a “framework for ensuring that these 15 hatchery programs are in compliance with the Federal Endangered Species Act” (Jones Jr. 2008). 16 NMFS also “promised to share key considerations in analyzing HGMPs” and provided those 17 materials to interested parties in February 2009 (Jones Jr. 2009). 18 19 On April 28, 2010 (Walton 2010), NMFS issued a letter to “co-managers, hatchery operators, 20 and hatchery funding agencies” that described how NMFS “has been working with co-managers 21 throughout the Northwest on the development and submittal of fishery and hatchery plans in 22 compliance with the Federal Endangered Species Act (ESA).” NMFS stated, “In order to 23 facilitate the evaluation of hatchery and fishery plans, we want to clarify the process, including 24 consistency with U.S. v. Oregon, habitat conservation plans and other agreements….” With 25 respect to “Development of Hatchery and Harvest Plans for Submittal under the ESA,” NMFS 26 clarified: “The development of fishery and hatchery plans for review under the ESA should 27 consider existing agreements and be based on best available science; any applicable multiparty 28 agreements should be considered, and the submittal package should explicitly reference how 29 such agreements were considered. In the Columbia River, for example, the U.S. v. Oregon 30 agreement is the starting place for developing hatchery and harvest plans for ESA review…." 31 32 In October 1999, NMFS received a request to operate artificial propagation programs, in the 33 form of three HGMPs from the WDFW (WDFW 1999a, 1999b, 1999c). These HGMPs 34 addressed programs in the UCR basin that artificially propagate and release unlisted summer 35 Chinook salmon, fall Chinook salmon, and sockeye salmon. The summer Chinook salmon 36 programs are funded by the Chelan and Douglas PUDs. The fall Chinook salmon program is 37 funded by the Grant PUD and the WDFW. The WDFW operates all the hatchery facilities and is 38 the lead co-manager of the anadromous fish resources in the state of Washington. 39 40 In April 2002, negotiations on three Habitat Conservation Plans (HCPs) were concluded. These 41 HCPs are long term agreements between NMFS, the PUDs, the WDFW, the USFWS, the 42 Colville Tribes, the Yakama Nation, and other stakeholders. They provide the PUDs with some 43 degree of certainty for the long-term operation of these projects and require the PUDs to provide 44 mitigation for unavoidable loss of natural fish production due to habitat inundation and passage 45 mortality at the projects via a tributary fund for habitat improvement projects, and artificial 46 propagation programs. The HCPs were developed to protect five species of anadromous
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1 salmonids, including the listed Upper Columbia River spring Chinook salmon and steelhead. The 2 HCP agreements restrict the PUDs and NMFS from changing the artificial propagation 3 production level during the permit period. 4 5 The three HCPs resulted in the formation of the HCP Hatchery Sub-Committees (HSCs) 6 consisting of one representative of each HCP signatory entity. The PR Salmon and Steelhead 7 Settlement Agreement resulted in the formation of the Priest Rapids Coordinating Committee 8 Hatchery Sub-Committee (PRCC HSC). NMFS is represented in the HCP and PRCC HSC 9 forums to ensure activities proposed by the HSCs are consistent with ESA recovery goals and do 10 not operate to the detriment of protected species.1 The HCP HSCs will develop monitoring and 11 evaluation plans for the hatchery programs, updating them every five years. The PUDs have 12 funded the implementation of the monitoring and evaluation plans. The monitoring plans include 13 data collection and analysis of all salmon life stages within the hatchery environment as well as 14 data collection activities outside the hatchery facilities such as spawning ground surveys, 15 juvenile fish traps, adult traps, and monitoring sites. The HCP HSCs would determine program- 16 specific monitoring activities necessary to evaluate the programs. 17 18 The proposed operation of six hatchery programs is described in a series of documents submitted 19 to NMFS by Douglas PUD, Chelan PUD, Grant PUD, WDFW, and USACE (hereafter referred 20 to as applicants). Starting in 2009, the applicants submitted final HGMPs and supplemental 21 information for formal consultation (Table 1) (Chelan PUD 2014; Chelan PUD and Grant PUD 22 2014; CPUD 2010; DPUD and WDFW 2013; GPUD 2009a; GPUD 2009b; Grant PUD 2014a; 23 Grant PUD 2014b; USACE and WDFW 2017; WDFW and GPUD 2005). 24 25 On September 20, 2013, NMFS responded to WDFW’s and the PUDs’ request for an extension 26 to their section 10 permit (1347). This permit was originally issued in 2003 and expired on 27 October 22, 2013. NMFS extended the permit until a new permit could be issued, provided the 28 applicants continue to operate the programs consistent with the expired permit and the terms and 29 conditions of the 2003 Biological Opinion (NMFS 2003). 30 31 After updated information were submitted to NMFS in 2017, NMFS reviewed the HGMPs for 32 sufficiency, and issued letters indicating that the HGMPs were sufficient for consultation 33 (Purcell 2017a; Purcell 2017b; Purcell 2017c). 34 35 Proposed Federal Action
36 “Action,” as applied under the ESA, means all activities, of any kind, authorized, funded, or 37 carried out, in whole or in part, by Federal agencies. For EFH consultation, “Federal action” 38 means any action authorized, funded, or undertaken, or proposed to be authorized, funded, or 39 undertaken by a Federal Agency (50 CFR 600.910). 40 41 There are two federal action agencies: 42 • The Proposed Action for the National Marine Fisheries Service (NMFS) is the issuance 43 of five Endangered Species Act (ESA) section 10(a)(1)(B) permits for the Columbia
1 Grant PUD is also represented in the PRCC HSC forum.
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1 River summer/fall Chinook salmon and fall Chinook salmon hatchery programs that are 2 funded by the PUDs (Table 1). 3 • The Proposed Action for the U.S. Army Corps of Engineers (USACE) is the funding of 4 the Ringold Springs Hatchery fall Chinook salmon program and a portion of the Priest 5 Rapids fall Chinook salmon program (Table 1). 6 7 The objective of this opinion is to determine the likely effects on ESA-listed salmon and 8 steelhead and their designated critical habitat resulting from these Federal actions. The effects of 9 these actions, as well as the PUDs’ funding of some of these programs, are subsumed within the 10 operation of these hatchery programs. Therefore, this Opinion will determine if the actions 11 proposed by the operators comply with the provisions of sections 7 and 10(a)(1)(B) of the ESA. 12 The duration of the Proposed Action of issuance of five Section 10 permits is 10 years from the 13 date of issuance. More information on the management of each program follows in the 14 description below. 15 16 NMFS describes a hatchery program as a group of fish that have a distinct purpose and that may 17 have independent spawning, rearing, marking and release strategies (NMFS 2008e). The 18 operation and management of every hatchery program is unique in time, and specific to an 19 identifiable stock and its native habitat (Flagg et al. 2004). The proposed hatchery programs 20 allow for mitigation for lost salmon and steelhead habitat and production associated with dam 21 constructions on the Columbia River. 22 23 The permits are jointly held by the WDFW and the Chelan, Douglas, and Grant PUDs. The 24 permit would authorize take of listed species incidental to the implementation of summer/fall and 25 fall Chinook salmon artificial propagation programs in the UCR region. Below is a description of 26 the proposed activities. 27 28 1.1.1. Chelan, Douglas, and Grant PUD Activities
29 The Chelan, Douglas, and Grant PUDs propose to provide artificial propagation compensation 30 for summer/fall Chinook salmon for the Chelan Falls, Chelan PUD’s portion of the Wenatchee, 31 and Wells programs per the Habitat Conservation Plans (HCP) (Chelan County Public Utility 32 District 2002a; Chelan County Public Utility District 2002b; Douglas County Public Utility 33 District 2002; NMFS 2008b) and the Methow, Grant PUD’s portion of the Wenatchee, and Priest 34 Rapids program per the Priest Rapids Salmon and Steelhead Settlement Agreement (SSSA) 35 (GPUD 2005). The HCP programs include Chelan Falls summer/fall Chinook Salmon, Chelan 36 PUD’s portion of the Wenatchee summer/fall Chinook Salmon, and Wells Hatchery summer/fall 37 Chinook Salmon (Table 1). The Grant PUD’s portion of the Wenatchee summer/fall Chinook 38 Salmon, Methow summer/fall Chinook Salmon, and Priest Rapids fall Chinook Salmon program 39 are to provide compensation for the SSSA (Table 1). The PUDs and the hatchery operators 40 (currently the WDFW for most programs), propose to operate the hatchery programs according 41 to the terms of section 8 “Hatchery Compensation Plan” of the HCPs, sections 9 and 10 of the 42 SSSA, the ESA section 7 authorization and section 10 permit, and in consultation with the 43 respective HCP Hatchery Committees and Priest Rapids Coordinating Committee Hatchery Sub- 44 Committee (PRCC HSC). 45
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1 The PUDs agree that over the duration of the HCPs and SSSA, new information and 2 technologies would be considered in the monitoring and evaluation of the hatchery programs. 3 The PUDs would implement monitoring and evaluation of the hatchery programs consistent with 4 the HCPs and SSSA and the Federal Energy Regulatory Commission (FERC) settlement 5 agreements, the general objectives and guidelines listed for each plan species in NMFS et al. 6 (1998), and as determined by the respective HCP Hatchery Committees and PRCC HSC 7 consistent with ESA recovery goals. 8 9 1.1.2. USACE Activities
10 The USACE proposes to fund the Ringold Springs Hatchery fall Chinook Salmon program and 11 partially for the Priest Rapids fall Chinook salmon program (1,700,000 smolts), which are part of 12 USACE’s John Day - The Dalles Mitigation Program that mitigates for salmon habitat lost by 13 the construction and operation of John Day and The Dalles dams (USACE and WDFW 2017; 14 WDFW 2010). The program is mostly operated by WDFW (see below). Oregon Department of 15 Fish and Wildlife (ODFW) performs the late incubation and early rearing (i.e., from eyed egg 16 stage to ponding) at Bonneville Hatchery; see NMFS (2017d) for the analysis of operation at 17 Bonneville Hatchery. The consultation with USFWS for the operation at the Bonneville 18 Hatchery was completed in White (2016). 19 20 1.1.3. Hatchery Operator Activities
21 The WDFW is currently the operator for all of the hatchery programs2 discussed in this opinion, 22 with the exception of Wells Hatchery, the Carlton Acclimation Facility, and late incubation and 23 early rearing for the Ringold Springs Hatchery Fall Chinook Salmon program. The WDFW is 24 also a manager with state statutory authority and state mandates regarding the fishery resources 25 of the state of Washington. The Wells Hatchery and the Carlton Acclimation Facility are 26 operated by Douglas PUD. 27 28 29 The details of the hatchery operations for each program are described below. 30
2 NMFS is aware of letters exchanged between DPUD and WDFW that terminated the contract between DPUD and WDFW for hatchery operations at the Wells Hatchery and the Carlton Acclimation Facility as described in the HGMPs. The resolution of this matter is relevant to NMFS' decision to issue a take permit under Section 10(a)(1)(B) of the ESA, and will be addressed in NMFS' record of its decision. However, for the purposes of this Opinion, NMFS will assume that the permits will only be issued, pursuant to NMFS regulations, to an entity which has demonstrated its qualifications to carry out the actions outlined in the HGMPs. Therefore, the discussion of which party will operate the programs is not a factor in this Opinion.
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1 2 Figure 1. Map of facilities used in the Upper Columbia River Basin in the Proposed Action 3 (Courtesy of Mike Tonseth, WDFW)
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1 1.1.3.1. Broodstock Collection and Mating
2 Table 2. Details of broodstock collection and mating for the six proposed programs.
Program Broodstock Collection Collection Collection Collection Numbers1 Method Location Duration Frequency Hours/Day; Days/Week Chelan Falls 358 hatchery-origin Canal trap; Chelan Falls July 15-Sept 24 hr/day, Summer/Fall Hatchery trap Canal Trap; 30 at trap; 3 days/week at trap; Chinook Entiat Hatchery; July 1-Sept 15 24 hr/day, 7 Chief Joseph at hatcheries days/week at Hatchery hatcheries Wenatchee Up to 262 natural- Dam trap Dryden Dam; July 1-Sept 15 24 hr/day, Summer/Fall origin Tumwater Dam up to 7 days/week Chinook Salmon Methow 118 natural-origin Dam trap Wells Dam July 1-Sept 15 27 hr/day, up to 7 Summer/Fall days/week2 Chinook Salmon Wells Hatchery 494, with no more Hatchery trap Wells Hatchery; July 1-Aug 28 24 hr/day, up to 7 Summer/Fall than 10% natural- Dam trap Wells Dam days/week at Chinook Salmon origin hatchery; 16 hr/day, 3 days/week at dam
Priest Rapids 4,410 adults, Hatchery trap Priest Rapids Early Sept- 24 hr/day, up to 7 Fall Chinook including up to Dam trap Hatchery; early Dec day/week at Salmon 1,323 natural- Hook and Priest Rapids hatchery; origin line Dam; 8 hr/day, 4 Hanford Reach3 days/week at dam; 3 days at Reach Ringold Springs 2,113 adults, Hatchery trap Priest Rapids Early Sept- 24 hr/day, up to 7 Hatchery Fall including up to 634 Dam trap Hatchery; early Dec day/week at Chinook Salmon natural-origin Hook and Priest Rapids hatchery; line Dam; 8 hr/day, 4 Ringold Springs days/week at dam; Rearing Facility; 3 days at Reach Hanford Reach3 3 1 Values listed are an approximation. Broodstock numbers are calculated annually, using a rolling 5-year average of 4 in-hatchery performance metrics, and reflect a ~ 99% chance of meeting the program production targets. Such 5 program adjustments are not considered a change in proposed action, provided that any adjustment will not result in 6 a level of effect greater than that analyzed in this Opinion. 7 2 Specific hours of operation for this trap are decided annually by the Wells HCP Coordinating Committee. 8 3 Natural-origin broodstock is collected in Hanford Reach using hook and line, and natural-origin adults are 9 collected from the dam trap (called Off-Ladder Adult Fish Trap, or OLAFT). 10 11 For all the proposed programs, broodstock would be collected throughout the run to ensure that 12 the range of traits associated with return timing are represented, an effort to reduce the potential 13 for inadvertent genetic selection. Traps would be checked daily when in operation and 14 incidentally captured, endangered UCR Chinook salmon and threatened steelhead would be
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1 removed. Operators would monitor the incidence of, and minimize capture, holding, and 2 handling effects on, listed salmon, steelhead, and bull trout. All incidentally captured listed fish 3 would be handled via water-to-water transfer, if possible, and immediately released upstream of 4 the trap. If water temperature at adult traps during trapping or during implementation of live 5 capture methods exceeded 21°C, trap operation and live capture would cease pending further 6 consultation with NMFS to determine if continued trap operation and live capture would pose 7 substantial risk to ESA-listed species or until temperatures fell below 21°C, with the exception of 8 the Chelan Falls Trap operation. 9 10 The operation of Chelan Falls Trap will be up to 24 hours per day, 7 days per week from July 15 11 through September 30 of each year, subject to the restriction that, from July 15 to July 31, the 12 trap will only be opened for operation by 4:00 p.m. or later. The trap will be checked at a 13 minimum of every 24 hours, and all trapped fish will be removed. When not trapping, the trap 14 will be closed to prevent fish from entering the trap. When trapping in water temperatures greater 15 than 21°C, trapping will cease if an ESA-listed species are encountered, pending further 16 consultation with NMFS or the USFWS to determine if continued trap operation poses 17 substantial risk to listed species. Any incidentally caught spring Chinook salmon, steelhead, or 18 bull trout will be handled carefully and released immediately at the Beebe Bridge Park boat 19 ramp. 20 21 To evaluate for whether spring Chinook salmon are trapped in the Chelan Falls Trap, fish that 22 phenotypically appear to be spring Chinook salmon that are collected in the Chelan Falls Trap 23 will be sampled consistent with run composition sampling at other adult trapping facilities (i.e., 24 length, sex, age (scales), origin (hatchery vs. natural), reading of external and internal tags); 25 additionally, genetic samples will be collected and analyzed to verify the frequency of spring 26 Chinook salmon encounters at the Chelan Falls Trap and to determine population/program origin 27 to further differentiate between listed and unlisted components, both of which have the potential 28 to be encountered.. 29 30 All of the proposed programs exclude age-2 and age-3 (using length at age) fall Chinook salmon 31 and age-3 summer/fall Chinook salmon retained for broodstock to reduce genetic risks/concerns 32 associated with younger age-at-maturity males. Current literature suggests younger age-at- 33 maturity fish produce younger age-at-maturity progeny—decreasing the average age-at-maturity 34 for broodstock and fish spawning in the natural environment. Natural-origin fish would be 35 prioritized for broodstock from the Priest Rapids Hatchery, unless a shortage was expected, and 36 remaining natural-origin adults would be used for Ringold production to incorporate natural- 37 origin broodstock into the Ringold production broodstock. The Priest Rapids Off Ladder Adult 38 Fish Trap (OLAFT) may be operated to collect up to 1,000 natural-origin fish. 39 40 1.1.3.2. Juvenile Rearing and Release
41 Juvenile summer/fall and fall Chinook salmon are reared and acclimated in the respective 42 facilities, some of which have different rearing and acclimation sites (Table 3). These programs 43 are operated with a 10 percent buffer in the production level to account for annual variation in 44 smolt production and survival. 45
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1 Table 3. Details of juvenile rearing and acclimation for the proposed programs.
Program Rearing Location(s) Acclimation Location Acclimation Timing Chelan Falls Eastbank Hatchery; Chelan Falls November - April* Summer/Fall Chelan Falls Acclimation Facility Chinook Salmon Acclimation Facility Wenatchee Eastbank Hatchery Dryden Acclimation March - April Summer/Fall Pond Chinook Salmon Methow Summer/Fall Eastbank Hatchery Carlton Acclimation October - May* Chinook Salmon Facility Wells Hatchery October - May* Summer/Fall Chinook Salmon (subyearling) Wells Hatchery Wells Hatchery Wells Hatchery October – October - Summer/Fall April1 Chinook Salmon (yearling) Priest Rapids Fall Priest Rapids Hatchery Priest Rapids Hatchery January - June* Chinook Salmon Ringold Springs Bonneville Hatchery Ringold Springs mid-May - mid-June Hatchery Fall Rearing Facility Chinook Salmon 2 * The acclimation timing for these programs also include timeframes for juvenile rearing because juvenile rearing 3 and acclimation take place in the same facility. 4 1 Because this yearling program acclimates the juveniles at the same location as their rearing, the juveniles are at the 5 acclimation location for about 19 months, though the fish are not on surface water for the whole duration. 6 7 Fish health staff monitor the fish throughout their rearing cycle for signs of disease. Mortalities 8 are checked daily and live grab samples are taken monthly. Fish are also tested prior to transfer 9 to acclimation sites and before release. Sampling, testing, and treatment/control procedures are 10 outlined in and consistent with IHOT (1995); NWIFC and WDFW (2006); Pacific Northwest 11 Fish Health Protection Committee (PNFHPC) (1989).
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1 Table 4. Details of juvenile release for the proposed programs. CWT = coded-wire tag; PIT = 2 passive integrated transponder.
Program Release life Number Release Mark Volitional Release Site stage and Timing Release?1 size Chelan Falls Yearlings 576,000 April- 100% Ad+CWT; No Chelan River Summer/Fall 13 fpp May PIT (RM 0.25) Chinook Salmon Wenatchee Yearlings 500,000 April- 100% Ad+CWT; Yes, forced Wenatchee Summer/Fall 18 fpp May PIT mid-May River Chinook Salmon (RM 16.0) Methow Summer/Fall Yearlings 200,000 April- 100% Ad+CWT; No Methow River Chinook Salmon 13-17 fpp May PIT (RM 37.5) Wells Hatchery Subyearlings 484,000 mid-May Yes, forced Columbia Summer/Fall 50 fpp end of May River Chinook Salmon (RM 515) 100% Ad+CWT Yearlings 320,000 mid-April Yes, forced Columbia 10 fpp mid-May River (RM 515) Priest Rapids Fall Subyearlings 5,599,504 May-June 100% otolith; No Columbia Chinook Salmon 50 fpp 605,429 Ad+CWT; River (GPUD)2 1,035,146 ad-clip; (RM 413) 605,056 CWT; PIT Priest Rapids Fall Subyearlings 1,700,000 May-June 100% ad-clipped; No Columbia Chinook Salmon 50 fpp PIT River (USACE)2 (RM 413) Ringold Springs Subyearling 3,500,000 May-July 100% ad-clipped; Yes, forced Columbia Hatchery Fall 50 fpp 400,000 CWT; after 5 days River Chinook Salmon PIT (RM 352) 3 1 Not all programs have the option for volitional release due to limited space, or force release is preferred for some 4 programs. 5 2 While these productions are funded by different entities (GPUD and USACE), these production groups have the 6 same broodstock collection methods, rearing timing and location, and release locations. 7 8 1.1.3.3. Adult Management
9 Removal of hatchery fish is expected to occur through ocean, tribal, commercial (zones 1-5), and 10 recreational/sport fisheries, broodstock collection, and surplus/harvest activities at non-target 11 facilities. Each of these removals is expected to reduce the number of hatchery fish spawning in 12 natural spawning areas, thereby reducing the pHOS of the recipient populations. The programs 13 will be managed to attempt to achieve a low pHOS level to the extent possible. 14 15 16 Surplus fish removed at UCR hatcheries may be used to support nutrient enhancement programs 17 in the UCR, given to the tribes or food banks, sold to rendering companies, or used for other 18 hatchery programs as determined by the respective committees. Nutrient enhancement programs 19 are not within the current Proposed Action and will be consulted on in the future, when such
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1 plans are created3. Surplus fish from the Priest Rapids program may also be used as broodstock 2 for other hatchery programs, including the Ringold Springs program. Surplus fish from the 3 Ringold Springs program will be donated to food banks if in good condition, sold to rendering 4 companies, used for other hatchery programs as determined by the U.S. v. Oregon parties, or 5 disposed of in a landfill. There is the potential for these adults to be used as broodstock for the 6 Ringold Springs program if infrastructure is improved in future years. 7 8 1.1.3.4. Facility Operations
9 All programs return water to the diverted creek or river (minus any leakage and evaporation) 10 along with any groundwater discharge. Water at all facilities is withdrawn in accordance with 11 state-issued water rights. All facilities that rear over 20,000 pounds of fish operate under 12 National Pollutant Discharge Elimination System (NPDES) permits. 13 14 The facilities used as part of the proposed hatchery operations are listed in Table 5. Some of 15 these facilities overlap with other hatchery programs, which have already been analyzed. The 16 operation of Eastbank Hatchery was analyzed in NMFS (2016a), the operation of Wells Hatchery 17 was analyzed in NMFS (2017e), and the operation of Bonneville Hatchery was analyzed in 18 NMFS (2017d). 19
3 Of note, these programs are likely to be in a form of direct carcass or a carcass analogue. If a nutrient enhancement program proposes to use direct carcass, the distribution will only occur within the space and temporal distribution of its natural counterpart spawning. If the program uses a carcass analogue, there would be no disease concerns because such carcass analogue will be processed to eliminate any pathogens.
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Table 5. Details of facility operations for the six proposed programs.
Program Facility Surface Ground Water Water Discharge Instream NPDES Compliant with Water Water Source Diversion Location Structures permit? NMFS Screening (cfs) (cfs) Distance Criteria?1 Chelan Falls Eastbank 0 55 Eastbank NA Columbia 1: Outfall Yes Yes Summer/Fall Hatchery2 Aquifer River Chinook Program Chelan Falls 24 0 Chelan River 290 ft. Chelan 2: Intake, outfall Yes Yes Acclimation River Facility Wenatchee Dryden Pond 32.2 0 Wenatchee 135 ft. Wenatchee 1: Outfall Yes Yes Summer/Fall River River Chinook Salmon3 Methow Carlton 7.5 For Methow 200 ft. Methow 2: Intake, outfall Yes Yes Summer/Fall Acclimation back-up River River Chinook Salmon3 Pond Wells Hatchery Wells 150 38 Columbia ~650 ft. Columbia 3: Intake, outfall, Yes Yes Summer/Fall Hatchery4 River River ladder Chinook Salmon Priest Rapids Fall Priest Rapids 102 14 Columbia 2.2 RM Columbia 3: Intake, outfall, Yes No Chinook Program Hatchery River River ladder Ringold Springs Ringold Springs 70 0 Ringold NA (out of Columbia 3: Intake, outfall, Yes Yes Hatchery Fall Rearing Facility Springs anadromy) River ladder Chinook Salmon5 1 Older criteria are NMFS (1995a); NMFS (1996). Screens are checked throughout the year. If a screen fails or is determined to be inefficient, it must be replaced with one that meets NMFS’ 2011 fish screen criteria. 2 The operation of Eastbank Hatchery was analyzed in NMFS (2016a). 3 These programs also use Eastbank Hatchery for early rearing, which was analyzed in NMFS (2016a). 4 The operation of Wells Hatchery was analyzed in NMFS (2017e). 5 This program also uses Bonneville Hatchery for early rearing. The operation of Bonneville Hatchery was analyzed in NMFS (2017d).
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1 2 1.1.3.5. Research, Monitoring, and Evaluation (RM&E)
3 All programs analyzed in this opinion will implement RM&E consistent with the PUD M&E 4 plan (Hillman et al. 2017a). Differences in program locations and objectives result in differences 5 in RM&E. Many of the RM&E activities that are implemented by the programs are described below: 6 below: 7 8 • Broodstock (and mortalities at trap locations) would be sampled to determine sex, 9 fecundity, age, genetic identity and diversity, and stray rates. 10 • Spawning ground surveys (for carcass recovery and redd survey) would be conducted to 11 determine location, number, stray rates, and timing of naturally-spawning summer/fall 12 and fall Chinook salmon in the Wenatchee, Yakima, Chelan, and Methow River basins 13 and the Hanford Reach. 14 o Carcass surveys and run composition assessment would be conducted in a manner 15 to target about 10 to 20 percent of the escapement in a given area. 16 o Analysis to determine potential coded wire tag and carcass recovery bias. 17 o Determine hatchery fish effects on population productivity, genetic diversity, 18 spawning distribution, and age and size at maturity. 19 • Operation and evaluation of PIT-tag detection systems for the purposes of stray analysis, 20 secondary smolt-to-adult return estimate, migration timing, juvenile survival, etc. 21 • Research to improve or assess program performance (such as different mating strategies 22 to improve PNI). 23 • Monitoring of each life-stage survival rates in the hatchery. 24 25 1.1.4. Changes in Proposed Programs Since Last Biological Opinion
26 Table 6. Summary of changes in programs since the last NMFS biological opinion
Program Changes1
Chelan Falls Summer/Fall • Moved from Turtle Rock Hatchery to Chelan Falls Acclimation Chinook Program Facility • Converted 1.62M sub-yearlings to 400,000 yearlings • Decreased 200K yearling NNI program by 24,000 • Reduced broodstock by 882 (71%) Wenatchee Summer/Fall • Reduced yearling release by 364,000 Chinook Salmon • Reduced broodstock by 191 (42%) Methow Summer/Fall • Reduced yearling releases by 200,000 Chinook Salmon • Reduced broodstock by 118 (50%) • Construction of a new overwinter acclimation facility. Wells Hatchery • Rebuilt Wells Hatchery (completed on August 31, 2017). Summer/Fall Chinook Summer/fall Chinook adults will now be trapped, held and spawned Salmon in a new facility that reduces handling, incubated in a new facility with biosecure incubation rooms, early rearing in the new facility, and then subsequent rearing would be conducted using components
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of the older facility, including the Bureau Ponds (concrete raceways) and Dirt Ponds. Priest Rapids Fall Chinook • Reduced 1 million subyearling NNI program to 325,543 subyearling 2 Program • Converted 1 million fry program to 273,961 subyearlings3 • Reduced broodstock by 300 (6.7%) • Rebuilding of the hatchery facility. Ringold Springs Hatchery • Changed broodstock sources from Bonneville Hatchery to broodstock Fall Chinook Salmon collected at the Priest Rapids Hatchery and the Hanford Reach, starting with brood year 2008. • Facility improvements, including replacing water supply pipe, and installing predator deterrent measures, and changing the configuration of a pond to accommodate two smaller ponds. 1 1 Changes in broodstock levels between pre- and post- NNI recalculation production targets, based on the biological 2 assumptions in the 2017 broodstock protocols.. 3 2 Includes the 1.7 million USACE fall Chinook salmon mitigation at Priest Rapids Hatchery. 4 3 Implementation of the converted fry program began with the 2013 brood consistent with the timeline identified in 5 the SSSA. 6 7 Interrelated and Interdependent Actions
8 Interrelated actions are those that are part of a larger action and depend on the larger action for 9 their justification. Interdependent actions are those that have no independent utility apart from 10 the action under consideration. NMFS has not identified any interdependent or interrelated 11 activities associated with the proposed action. The impacts of fisheries in the action area, 12 including those that may target fish produced by the proposed programs, on ESA-listed 13 salmonids are included in the environmental baseline. 14 15 ENDANGERED SPECIES ACT: BIOLOGICAL OPINION AND INCIDENTAL TAKE STATEMENT
16 The ESA establishes a national program for conserving threatened and endangered species of 17 fish, wildlife, plants, and the habitat upon which they depend. Section 7(a)(2) of the ESA 18 requires Federal agencies to consult with the FWS, NMFS, or both, to ensure that their actions 19 are not likely to jeopardize the continued existence of endangered or threatened species or 20 adversely modify or destroy their designated critical habitat. Section 7(b)(3) requires that at the 21 conclusion of consultation, the Service provide an opinion stating how the agencies’ actions will 22 affect listed species and their critical habitat. If incidental take is expected, section 7(b)(4) 23 requires the consulting agency to provide an ITS that specifies the impact of any incidental 24 taking and includes reasonable and prudent measures to minimize such impacts.
25 Analytical Approach
26 Section 7(a)(2) of the ESA requires Federal agencies, in consultation with NMFS, to ensure that 27 their actions are not likely to jeopardize the continued existence of endangered or threatened 28 species, or adversely modify or destroy their designated critical habitat. The jeopardy analysis 29 considers both survival and recovery of the species. “To jeopardize the continued existence of a 30 listed species” means to engage in an action that would be expected, directly or indirectly, to 31 reduce appreciably the likelihood of both the survival and recovery of the species in the wild by
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1 reducing the reproduction, numbers, or distribution of that species or reduce the value of 2 designated or proposed critical habitat (50 CFR 402.02). 3 4 This biological opinion relies on the definition of “destruction or adverse modification,” which 5 “means a direct or indirect alteration that appreciably diminishes the value of critical habitat for 6 the conservation of a listed species. Such alterations may include, but are not limited to, those 7 that alter the physical or biological features essential to the conservation of a species or that 8 preclude or significantly delay development of such features” (81 FR 7214, February 11, 2016). 9 10 The designations of critical habitat for the species considered in this opinion use the terms 11 primary constituent element (PCE) or essential features. The new critical habitat regulations (81 12 FR 7414, February 11, 2016) replace this term with physical or biological features (PBFs). The 13 shift in terminology does not change the approach used in conducting a “destruction or adverse 14 modification” analysis, which is the same regardless of whether the original designation 15 identified PCEs, PBFs, or essential features. In this biological opinion, we use the term PBF to 16 mean PCE or essential feature, as appropriate for the specific critical habitat. 17 18 We use the following approach to determine whether a proposed action is likely to jeopardize 19 listed species or destroy or adversely modify critical habitat. 20 21 Range-wide status of the species and critical habitat 22 This section describes the status of species and critical habitat that are the subject of this opinion. 23 The status review starts with a description of the general life history characteristics and the 24 population structure of the ESU/DPS, including the strata or major population groups (MPG) 25 where they occur. NMFS has developed specific guidance for analyzing the status of salmon and 26 steelhead populations in a “viable salmonid populations” (VSP) paper (McElhany et al. 2000). 27 The VSP approach considers four attributes, the abundance, productivity, spatial structure, and 28 diversity of each population (natural-origin fish only), as part of the overall review of a species’ 29 status. For salmon and steelhead protected under the ESA, the VSP criteria therefore encompass 30 the species’ “reproduction, numbers, or distribution” (50 CFR 402.02). In describing the range- 31 wide status of listed species, NMFS reviews available information on the VSP parameters 32 including abundance, productivity trends (information on trends, supplements the assessment of 33 abundance and productivity parameters), spatial structure and diversity. We also summarize 34 available estimates of extinction risk that are used to characterize the viability of the populations 35 and ESU/DPS, and the limiting factors and threats. To source this information, NMFS relies on 36 viability assessments and criteria in technical recovery team documents, ESA Status Review 37 updates, and recovery plans. We determine the status of critical habitat by examining its PBFs . 38 Status of the species and critical habitat are discussed in Section 2.2. 39 40 Describing the environmental baseline 41 The environmental baseline includes the past and present impacts of Federal, state, or private 42 actions and other human activities in the action area on ESA-listed species. It includes the 43 anticipated impacts of proposed Federal projects that have already undergone formal or early 44 section 7 consultation and the impacts of state or private actions that are contemporaneous with 45 the consultation in process. The environmental baseline is discussed in Section 2.3 of this 46 opinion.
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1 2 Cumulative effects
3 Cumulative effects, as defined in NMFS’ implementing regulations (50 CFR 402.02), are the 4 effects of future state or private activities, not involving Federal activities, that are reasonably 5 certain to occur within the action area. Future Federal actions that are unrelated to the proposed 6 action are not considered because they require separate section 7 consultation. Cumulative 7 effects are considered in Section 2.5 of this opinion. 8 9 Integration and synthesis 10 Integration and synthesis occurs in Section 2.6 of this opinion. In this step, NMFS adds the 11 effects of the Proposed Action (Section 2.4) to the status of ESA protected populations in the 12 Action Area under the environmental baseline (Section 2.3) and to cumulative effects (Section 13 2.5). Impacts on individuals within the affected populations are analyzed to determine their 14 effects on the VSP parameters for the affected populations. These impacts are combined with the 15 overall status of the MGP to determine the effects on the ESA-listed species (ESU/DPS), which 16 will be used to formulate the agency’s opinion as to whether the hatchery action is likely to: (1) 17 result in appreciable reductions in the likelihood of both survival and recovery of the species in 18 the wild by reducing its numbers, reproduction, or distribution; or (2) reduce the value of 19 designated or proposed critical habitat. 20 21 Jeopardy and adverse modification 22 Based on the Integration and Synthesis analysis in section 2.6, the opinion determines whether 23 the proposed action is likely to jeopardize ESA protected species or destroy or adversely modify 24 designated critical habitat in Section 2.7. 25 26 Reasonable and prudent alternative(s) to the proposed action 27 If NMFS determines that the action under consultation is likely to jeopardize the continued 28 existence of listed species or destroy or adversely modify designated critical habitat, NMFS must 29 identify a RPA or RPAs to the proposed action. 30 31 Range-wide Status of the Species and Critical Habitat
32 This opinion examines the status of each species and designated critical habitat that would be 33 affected by the Proposed Action described in Table 74. Status of the species is the level of risk 34 that the listed species face based on parameters considered in documents such as recovery plans, 35 status reviews, and ESA listing determinations. The species status section helps to inform the 36 description of the species’ current “reproduction, numbers, or distribution” as described in 50 37 CFR 402.02. The opinion also examines the status and conservation value of critical habitat in 38 the action area and discusses the current function of the essential physical and biological features 39 that help to form that conservation value. 40
4 ESA-listed bull trout (Salvelinus confluentus) are administered by the FWS and the proposed hatchery program is currently covered under a separate FWS section 7 consultation (FWS ref # 01E0FW00-2015-F-0154). Take associated with hatchery monitoring and evaluation activities is covered under USFWS TE-702631, sub-permit MCFRO-13.
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1 Table 7. Federal Register notices for the final rules that list species, designate critical habitat, or 2 apply protective regulations to ESA-listed species considered in this consultation.
Protective Species Listing Status Critical Habitat Regulations Chinook salmon (Oncorhynchus tshawytscha) Endangered 70 FR 52630; Upper Columbia River Spring 70 FR 37160; 1 ESA Section 9 Sept 2, 2005 June 28, 2005 Threatened, 79 FR 20802, 64 FR 57399, 70 FR 37160, Snake River Spring/summer April 14, 2014 October 25, 1999 June 28, 2005 Threatened, 79 FR 20802, 58 FR 68543, 70 FR 37160, Snake River Fall April 14, 2014 December 28, 1993 June 28, 2005 Threatened, 79 FR 20802, 70 FR 52706, 70 FR 37160, Lower Columbia River April 14, 2014 September 2, 2005 June 28, 2005 Threatened, 79 FR 20802, 70 FR 52720, 70 FR 37160, Upper Willamette River Spring April 14, 2014 September 2, 2005 June 28, 2005 Sockeye salmon (O. nerka) Endangered, 79 FR 20802, 70 FR 52630, Snake River ESA Section 9 April 14, 2014 September 2, 2005 Steelhead (O. mykiss) Threatened 70 FR 52630; Sept 2, 70 FR 37160; Upper Columbia River 74 FR 42605; August 24, 2005 June 28, 2005 2009 Threatened, 79 FR 20802, 70 FR 52769, 70 FR 37160, Snake River April 14, 2014 September 2, 2005 June 28, 2005 Threatened, 79 FR 20802, 70 FR 52808, 70 FR 47160, Middle Columbia River April 14, 2014 September 2, 2005 June 28, 2005 Threatened, 79 FR 20802, 70 FR 52808, 70 FR 37160, Lower Columbia River April 14, 2014 September 2, 2005 June 28, 2005 Threatened, 79 FR 20802, 70 FR 52848, 70 FR 37160, Upper Willamette River April 14, 2014 September 2, 2005 June 28, 2005 Chum salmon (O. keta) Threatened, 79 FR 20802, 70 FR 52746, 70 FR 37160, Columbia River April 14, 2014 September 2, 2005 June 28, 2005 Coho salmon (O. kisutch) Threatened, 79 FR 20802, 81 FR 9252, 70 FR 37160, Lower Columbia River April 14, 2014 February 24, 2016 June 28, 2005 3 1 Citations to “FR” are citations to the Federal Register. 4 5 “Species” Definition: The ESA of 1973, as amended, 16 U.S.C. 1531 et seq. defines “species” to 6 include any “distinct population segment (DPS) of any species of vertebrate fish or wildlife 7 which interbreeds when mature.” To identify DPSs of salmon species, NMFS follows the 8 “Policy on Applying the Definition of Species under the ESA to Pacific Salmon” (56 FR 58612, 9 November 20, 1991). Under this policy, a group of Pacific salmon is considered a DPS and 10 hence a “species” under the ESA if it represents an evolutionarily significant unit (ESU) of the 11 biological species. The group must satisfy two criteria to be considered an ESU: (1) It must be 12 substantially reproductively isolated from other con-specific population units; and (2) It must
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1 represent an important component in the evolutionary legacy of the species. To identify DPSs of 2 steelhead, NMFS applies the joint FWS-NMFS DPS policy (61 FR 4722, February 7, 1996). 3 Under this policy, a DPS of steelhead must be discrete from other populations, and it must be 4 significant to its taxon. 5 6 Status of Listed Species
7 For Pacific salmon and steelhead, NMFS commonly uses four parameters to assess the viability 8 of the populations that, together, constitute the species: abundance, productivity, spatial 9 structure, and diversity (McElhany et al. 2000). These “viable salmonid population” (VSP) 10 criteria therefore encompass the species’ “reproduction, numbers, or distribution” as described in 11 50 CFR 402.02. When these parameters are collectively at appropriate levels, they maintain a 12 population’s capacity to adapt to various environmental conditions and allow it to sustain itself in 13 the natural environment. These parameters or attributes are substantially influenced by habitat 14 and other environmental conditions. 15 16 “Abundance” generally refers to the number of naturally-produced adults (i.e., the progeny of 17 naturally-spawning parents) in the natural environment. 18 19 “Productivity,” as applied to viability factors, refers to the entire life cycle; i.e., the number of 20 naturally-spawning adults (i.e., progeny) produced per naturally spawning parental pair. When 21 progeny replace or exceed the number of parents, a population is stable or increasing. When 22 progeny fail to replace the number of parents, the population is declining. McElhany et al. (2000) 23 use the terms “population growth rate” and “productivity” interchangeably when referring to 24 production over the entire life cycle. They also refer to “trend in abundance,” which is the 25 manifestation of long-term population growth rate. 26 27 “Spatial structure” refers both to the spatial distributions of individuals in the population and the 28 processes that generate that distribution. A population’s spatial structure depends fundamentally 29 on accessibility to the habitat, on habitat quality and spatial configuration, and on the dynamics 30 and dispersal characteristics of individuals in the population. 31 32 “Diversity” refers to the distribution of traits within and among populations. These range in scale 33 from DNA sequence variation at single genes to complex life history traits (McElhany et al. 34 2000). 35 36 In describing the range-wide status of listed species, we rely on viability assessments and criteria 37 in TRT documents and recovery plans, when available, that describe VSP parameters at the 38 population, major population group (MPG), and species scales (i.e., salmon ESUs and steelhead 39 DPSs). For species with multiple populations, once the biological status of a species’ populations 40 and MPGs have been determined, NMFS assesses the status of the entire species. Considerations 41 for species viability include having multiple populations that are viable, ensuring that 42 populations with unique life histories and phenotypes are viable, and that some viable 43 populations are both widespread to avoid concurrent extinctions from mass catastrophes and 44 spatially close to allow functioning as meta-populations (McElhany et al. 2000). 45
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1 Upper Columbia River Spring Chinook Salmon ESU
2 Chinook salmon (Oncorhynchus tshawytscha) have a wide variety of life history patterns that 3 include: variation in age at seaward migration; length of freshwater, estuarine, and oceanic 4 residence; ocean distribution; ocean migratory patterns; and age and season of spawning 5 migration. Two distinct races of Chinook salmon are generally recognized: “stream-type” and 6 “ocean-type” (Healey 1991; Myers et al. 1998). ESA-listed UCR spring Chinook salmon are 7 stream-type. Stream-type Chinook salmon spend 2 to 3 years in coastal ocean waters, and enter 8 freshwater in February through April. Spring Chinook salmon also spawn and rear high in the 9 watershed and reside in freshwater for a year.
10 The historical UCR Spring Chinook Salmon ESU comprises three major population groups 11 (MPGs) and eight populations; however, the ESU is currently limited to one MPG (North 12 Cascade MPG) and three extant populations (Wenatchee, Methow and Entiat). The Okanogan 13 population has been extirpated. For the MPG to be considered viable, all three extant populations 14 are required to meet viability (i.e., a 5 percent extinction risk over a 100-year period) criteria 15 (UCSRB 2007).
16 Approximately half of the area that originally produced spring Chinook salmon in this ESU is 17 blocked by dams. What remains of the ESU includes all naturally spawned fish upstream of 18 Rock Island Dam and downstream of Chief Joseph Dam in Washington State, excluding the 19 Okanogan River (64 FR 14208, March 24, 1999) (Figure 2). The ESU originally included six 20 artificial propagation programs: the Twisp, Chewuch, Methow Composite, Winthrop NFH, 21 Chiwawa, and White River hatchery programs (79 FR 20802, April 14, 2014). Currently, the 22 three Methow Subbasin programs (Twisp, Chewuch, Methow Composite) are considered a 23 single program, with two components: Twisp and Methow (the previous Chewuch and Methow 24 programs combined). Furthermore, a Nason Creek program began in the Wenatchee Subbasin 25 (Grant County PUD et al. 2009b), while the White River releases were discontinued after 2015 26 (Grant County PUD et al. 2009a).
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1 Figure 2. Upper Columbia River Spring Chinook Salmon ESU (ICTRT 2008).
2 For the most recent period (2005-2014), abundance has increased for all three populations, but 3 productivity for all three populations remains below replacement (Table 8). Although increases 4 in natural-origin abundance relative to the extremely low levels observed during the mid-1990s 5 are encouraging, overall productivity has decreased to extremely low levels for the two largest 6 populations (Wenatchee and Methow). The predominance of hatchery fish on the spawning 7 grounds, particularly for the Wenatchee and Methow populations, is an increasing diversity risk, 8 and populations that rely on hatchery spawners are not viable (McElhany et al. 2000). Natural- 9 origin fish now make up fewer than fifty percent of the spawners for two of the three populations 10 (Table 8). Based on the combined ratings for abundance/productivity and spatial 11 structure/diversity, all three extant populations and the ESU remain at high risk of extinction 12 (Table 8).
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1 Table 8. Risk levels and viability ratings for natural-origin UCR spring Chinook salmon 2 populations from the North Cascades MPG (NWFSC 2015).
Minimum Spawning % Natural- Productivity Overall Population Abundance Abundance origin spawners (2005-2014) Risk Threshold (2005-2014) (2010-2014) Wenatchee River 2000 545 (311-1030) 0.60 35 High Entiat River 500 166 (78-354) 0.94 74 High Methow River 2000 379 (189-929) 0.46 27 High Okanogan 750 Extirpated 3 4 Many factors affect the abundance, productivity, spatial structure, and diversity of the UCR 5 Spring Chinook Salmon ESU. Factors limiting the ESU’s survival and recovery include: 6 7 • past management practices such as the Grand Coulee Fish Maintenance Project 8 • survival through the FCRPS 9 • degradation and loss of estuarine areas that help the fish survive the transition between 10 fresh and marine waters 11 • spawning and rearing areas that have lost deep pools, cover, side-channel refuge areas, 12 and high quality spawning gravels 13 • interbreeding and competition with hatchery fish that far outnumber fish from natural 14 populations. 15 16 Snake River Spring/summer Chinook Salmon ESU
17 Spring/summer-run Chinook salmon from the Snake River basin exhibit stream-type life history 18 characteristics. Chinook salmon return to the Columbia River from the ocean in early spring 19 through August. Returning fish hold in deep mainstem and tributary pools until late summer, 20 when they emigrate up into tributary areas and spawn from mid- through late August. The eggs 21 incubate over the following winter, and hatch in late winter and early spring of the following 22 year. Juveniles rear through the summer, overwinter, and typically migrate to sea in the spring of 23 their second year of life, although some juveniles may spend an additional year in fresh water. 24 Snake River spring/summer-run Chinook salmon spend two or three years in the ocean before 25 returning to tributary spawning grounds primarily as 4- and 5-year-old fish. A small fraction of 26 the fish return as 3-year-old “jacks,” heavily predominated by males. 27 28 Many factors negatively affect the abundance, productivity, spatial structure, and diversity of the 29 Snake River Spring/summer Chinook Salmon ESU. Factors that limit the ESU’s survival and 30 recovery include migration through the Federal Columbia River Power System (FCRPS) dams, 31 the degradation and loss of estuarine areas that help fish transition between fresh and marine 32 waters, spawning and rearing areas that have lost deep pools, loss of cover, reductions in side- 33 channel refuge areas, reductions in high-quality spawning gravels, and interbreeding and 34 competition with hatchery fish that may outnumber natural-origin fish (Ford 2011). The most 35 serious risk factor is low natural productivity (spawner-to-spawner return rates) and the 36 associated decline in abundance to low levels relative to historical returns. The biological review 37 team (Ford 2011) was concerned about the number of hatchery programs across the ESU, noting
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1 that these programs represent ongoing risks to natural populations and can make it difficult to 2 assess trends in natural productivity. A more detailed description of the populations that are the 3 focus of this consultation follows. 4 5 There are two independent populations within the Lower Snake River MPG: Tucannon River 6 and Asotin Creek. The ESA Recovery Plan for SEWA (SRSRB 2011) requires that the 7 Tucannon River population be at low risk (no more than a 1 percent risk of extinction in 100 8 years). The Tucannon River population is required to meet highly viable status for delisting of 9 the ESU because the Asotin Creek population is extirpated. The most recent status review by 10 NMFS (NWFSC 2015) maintains that the Tucannon population remains at high risk (Table 9). 11 12 There are six extant independent populations of spring/summer Chinook salmon within the 13 Grande Ronde/Imnaha MPG: Wenaha River, Lostine River, Minam River, Catherine Creek, 14 Upper Grande Ronde River, and the Imnaha River. The remaining two populations, 15 Lookingglass and Big Sheep Creeks, are functionally extirpated. The ICTRT criteria call for a 16 minimum of four populations at viable or highly viable status. The potential scenario identified 17 by the ICTRT (2007) would include viable populations in the Imnaha River (run timing), the 18 Lostine/Wallowa River (large size) and at least one from each of the following pairs: Catherine 19 Creek or Upper Grande Ronde (large size); and Minam or Wenaha Rivers. The most recent 20 status review by NMFS (NMFS 2015c) maintains that all extant populations remain at high risk 21 of extinction (Table 9). 22
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1 Table 9. Risk levels and viability ratings for Snake River spring/summer Chinook salmon 2 populations (NWFSC 2015); ICTRT = Interior Columbia Technical Recovery Team. Data are 3 from 2005-2014.
Population ICTRT Geometric mean Proportion Geometric mean Abundance Spatial Overall minimum natural spawning natural- productivity and structure viability threshold abundance origin (standard error) productivity and risk (standard error) spawners risk diversity rating risk Tucannon 750 267 (0.19) 0.67 0.69 (0.23) High Moderate High
Asotin Creek Extirpated
Wenaha 750 399 (0.12) 0.76 0.93 (0.21) High Moderate High Lostine/Wall 1000 332 (0.24) 0.45 0.98 (0.12) High Moderate High owa Minam 750 475 (0.12) 0.89 0.94 (0.18) High Moderate High Catherine 1000 110 (0.31) 0.45 0.95 (0.15) High Moderate High Creek Up. Grande 1000 43 (0.26) 0.18 0.59 (0.28) High High High Ronde Imnaha River 750 328 (0.21) 0.35 1.2 (0.09) High Moderate High Lookingglass 500 Extirpated Creek Big Sheep Extirpated Creek 4 5 6 Snake River Fall Chinook Salmon ESU
7 Before alteration of the Snake River Basin by dams, Snake River fall-run Chinook salmon 8 exhibited a largely ocean-type life history, where they migrated downstream during their first- 9 year. Today, fall-run Chinook salmon in the Snake River Basin exhibit one of two life histories; 10 ocean-type and reservoir-type. Juveniles exhibiting the reservoir-type life history overwinter in 11 the pools created by the dams before migrating out of the Snake River. The reservoir-type life 12 history is likely a response to early development in cooler temperatures (mainly from fish that 13 spawned in the Clearwater River), which prevents juveniles from reaching a suitable size to 14 migrate out of the Snake River and on to the ocean. 15 16 The Snake River Fall-run Chinook Salmon ESU includes naturally spawned fish in the lower 17 mainstem of the Snake River and the lower reaches of several of the associated major tributaries 18 including the Tucannon, the Grande Ronde, Clearwater, Salmon, and Imnaha Rivers, along with 19 4 artificial propagation programs (Jones Jr. 2015; NWFSC 2015). All of the hatchery programs 20 are included in the ESU along with a single natural-origin population that is currently viable, 21 with a low risk for abundance/productivity and a moderate risk for spatial structure and diversity. 22
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1 The recently released Draft NMFS Snake River Fall Chinook Recovery Plan (NMFS 2015d) 2 says that a single population viability scenario could be possible given the unique spatial 3 complexity of the Lower Mainstem Snake River fall-run Chinook salmon population. The 4 recovery plan notes that such scenario could be possible if major spawning areas supporting the 5 bulk of natural returns are operating consistent with long-term diversity objectives in the 6 proposed plan. Under this single population scenario, the requirements for a sufficient 7 combination of natural abundance and productivity could be based on a combination of total 8 population natural abundance and relatively high production from one or more major spawning 9 areas with relatively low hatchery contributions to spawning, i.e., low hatchery influence for at 10 least one major natural spawning production area. 11 12 In terms of spatial structure and diversity, the Lower Mainstem Snake River fall-run Chinook 13 salmon population was rated at low risk for Goal A (allowing natural rates and levels of spatially 14 mediated processes) and moderate risk for Goal B (maintaining natural levels of variation) in the 15 status review update (NWFSC 2015), resulting in an overall spatial structure and diversity rating 16 of moderate risk. The moderate risk rating was driven by changes in major life history patterns, 17 shifts in phenotypic traits, and high levels of genetic homogeneity in samples from natural-origin 18 returns. In addition, risk associated with indirect factors (e.g., the high levels of hatchery 19 spawners in natural spawning areas, the potential for selective pressure imposed by current 20 hydropower operations, and cumulative harvest impacts) contribute to the current rating level. 21 22 Considering the most recent information available, an increase in estimated productivity (or a 23 decrease in the year-to-year variability associated with the estimate) would be required to 24 achieve delisting status, assuming that natural-origin abundance of the single extant Snake River 25 fall-run Chinook salmon population remains relatively high. An increase in productivity could 26 occur with a further reduction in mortalities across life stages. Such an increase could be 27 generated by actions such as a reduction in harvest impacts (particularly when natural-origin 28 spawner return levels are below the minimum abundance threshold) and/or further improvements 29 in juvenile survivals during downstream migration. It is also possible that survival improvements 30 resulting from various actions (e.g., improved flow-related conditions affecting spawning and 31 rearing, expanded spill programs that increased passage survivals) in recent years have increased 32 productivity, but that increase is effectively masked as a result of the relatively high spawning 33 levels in recent years. A third possibility is that productivity levels may decrease over time as a 34 result of negative impacts of chronically high hatchery proportions across natural spawning 35 areas. Such a decrease would also be largely masked by the high annual spawning levels 36 (NWFSC 2015). 37 38 The Snake River Fall-run Chinook Salmon ESU remains at threatened status (NMFS 2015c). 39 Factors that limit the ESU’s survival and recovery include: hydropower projects, predation, 40 harvest, degraded estuary habitat, and degraded mainstem and tributary habitat (Ford 2011). 41 Ocean conditions have also affected the status of this ESU. Ocean conditions affecting the 42 survival of Snake River fall-run Chinook salmon were generally poor during the early part of the 43 last 20 years (NMFS 2012d). 44
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1 Lower Columbia River Chinook Salmon ESU
2 On March 24, 1999, NMFS listed the LCR Chinook Salmon ESU as a threatened species (64 FR 3 14308). The threatened status was reaffirmed on April 14, 2014 (Table 7). Critical Habitat for 4 LCR Chinook salmon was designated on September 2, 2005 (70 FR 52706) (Table 7). 5 6 Within the geographic range of this ESU, 27 hatchery Chinook salmon programs are currently 7 operational. Fourteen of these hatchery programs are included in the ESU (Table 10), while the 8 remaining 13 programs are excluded (Jones Jr. 2015). Willamette River Chinook salmon are 9 listed within the Willamette River Chinook Salmon ESU, but they are not listed within the LCR 10 Chinook Salmon ESU. Genetic resources that represent the ecological and genetic diversity of a 11 species can reside in a hatchery program. “Hatchery programs with a level of genetic divergence 12 relative to the local natural population(s) that is no more than what occurs within the ESU are 13 considered part of the ESU and will be included in any listing of the ESU” (NMFS 2005c). For a 14 detailed description of how NMFS evaluates and determines whether to include hatchery fish in 15 an ESU or DPS, see Section 2.4.1 (NMFS 2005b).
16 Table 10. LCR Chinook Salmon ESU description and MPGs (Jones Jr. 2015; NMFS 2013c; 17 NWFSC 2015).
ESU Description1 Threatened Listed under ESA in 1999; updated in 2014 (Table 7) 6 major population 32 historical populations groups Major Population Group Populations Upper Cowlitz (C,G), Cispus (C), Tilton, Toutle, Kalama, NF Lewis (C), Cascade Spring Sandy (C,G) Gorge Spring (Big) White Salmon (C), Hood Grays/Chinook, Elochoman (C), Mill Creek, Youngs Bay, Big Creek (C), Coast Fall Clatskanie, Scappoose Lower Cowlitz (C), Upper Cowlitz, Toutle (C), Coweeman (G), Kalama, Cascade Fall EF Lewis (G), Salmon Creek, Washougal, Clackamas (C), Sandy River early Gorge Fall Lower Gorge, Upper Gorge (C), (Big) White Salmon (C), Hood Cascade Late Fall North Fork Lewis (C,G), Sandy (C,G) Artificial production Hatchery programs Big Creek Tule Fall Chinook, Astoria High School (STEP), Tule Fall included in ESU (14) Chinook, Warrenton High School (STEP), Tule Fall Chinook, Cowlitz Tule Fall Chinook Salmon Program, North Fork Toutle Tule Fall Chinook, Kalama Tule Fall Chinook, Washougal River Tule Fall Chinook, Spring Creek National Fish Hatchery (NFH) Tule Chinook, Cowlitz spring Chinook salmon (2 programs), Friends of Cowlitz spring Chinook, Kalama River Spring Chinook, Lewis River Spring Chinook, Fish First Spring Chinook, Sandy River Hatchery Spring Chinook salmon (ODFW stock #11)
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Hatchery programs not Deep River Net-Pens Spring Chinook, Clatsop County Fisheries (CCF) included in ESU (13) Select Area Brights Program Fall Chinook, CCF Spring Chinook salmon Program, Carson NFH Spring Chinook salmon Program, Little White Salmon NFH Tule Fall Chinook salmon Program, Bonneville Hatchery Tule Fall Chinook salmon Program, Hood River Spring Chinook salmon Program, Deep River Net Pens Tule Fall Chinook, Klaskanine Hatchery Tule Fall Chinook, Bonneville Hatchery Fall Chinook, Little White Salmon NFH Tule Fall Chinook, Cathlamet Channel Net Pens Spring Chinook, Little White Salmon NFH Spring Chinook 1 1 The designations "(C)" and "(G)" identify Core and Genetic Legacy populations, respectively.5 2 3 Thirty-two historical populations within six MPGs compose the LCR Chinook Salmon ESU. 4 These are distributed through three ecological zones6, which, through a combination of life 5 history types based on run timing and ecological zones, result in the six MPGs, some of which 6 are considered extirpated or nearly so (Table 11). The run-timing distributions across the 32 7 historical populations are: nine spring populations, 21 early-fall populations, and two late-fall 8 populations (Figure 3).
9 Table 11. Current status for LCR Chinook salmon populations and recommended status under 10 the recovery scenario (NMFS 2013c).
Status Assessment Recovery Scenario Major Baseline Target Population Population (State) Abundance Persistence Contribution2 Persistence Group Target3 Probability1 Probability Upper Cowlitz (WA) VL Primary H+ 1,800 Cispus (WA) VL Primary H+ 1,800 Tilton (WA) VL Stabilizing VL 100 Cascade Toutle (WA) VL Contributing M 1,100 Spring Kalama (WA) VL Contributing L 300 North Fork Lewis VL Primary H 1,500 (WA) Sandy (OR) M Primary H 1,230 Gorge White Salmon (WA) VL Contributing L+ 500 Spring Hood (OR) VL Primary4 VH4 1,493 Youngs Bay (OR) L Stabilizing L 505 Coast Fall Grays/Chinook (WA) VL Contributing M+ 1,000
5 Core populations are defined as those that, historically, represented a substantial portion of the species abundance. Genetic legacy populations are defined as those that have had minimal influence from nonendemic fish due to artificial propagation activities, or may exhibit important life history characteristics that are no longer found throughout the ESU Myers, J., C. Busack, D. Rawding, and A. Marshall. 2003. Historical Population Structure of Willamette and Lower Columbia River Basin Pacific Salmonids. October 2003. NOAA Fisheries Service, Northwest Fisheries Science Center, Seattle, Washington. 195p.. 6 There are a number of methods of classifying freshwater, terrestrial, and climatic regions. The WLC TRT used the term ecological zone as a reference, in combination with an understanding of the ecological features relevant to salmon, to designate four ecological areas in the domain: (1) Coast Range zone, (2) Cascade zone, (3) Columbia Gorge zone, and (4) Willamette zone. This concept provides geographic structure to ESUs in the domain. Maintaining each life-history type across the ecological zones reduces the probability of shared catastrophic risks. Additionally, ecological differences among zones reduce the impact of climate events across entire ESUs ibid., ibid..
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Status Assessment Recovery Scenario Major Baseline Target Population Population (State) Abundance Persistence Contribution2 Persistence Group Target3 Probability1 Probability Big Creek (OR) VL Contributing L 577 Elochoman/Skamokawa VL Primary H 1,500 (WA) Clatskanie (OR) VL Primary H 1,277 Mill/Aber/Germ (WA) VL Primary H 900 Scappoose (OR) L Primary H 1,222 Lower Cowlitz (WA) VL Contributing M+ 3,000 Upper Cowlitz (WA) VL Stabilizing VL -- Toutle (WA) VL Primary H+ 4,000 Coweeman (WA) VL Primary H+ 900 Cascade Kalama (WA) VL Contributing M 500 Fall Lewis (WA) VL Primary H+ 1,500 Salmon (WA) VL Stabilizing VL -- Clackamas (OR) VL Contributing M 1,551 Sandy (OR) VL Contributing M 1,031 Washougal (WA) VL Primary H+ 1,200 Lower Gorge (WA/OR) VL Contributing M 1,200 Upper Gorge (WA/OR) VL Contributing M 1,200 Gorge Fall White Salmon (WA) VL Contributing M 500 Hood (OR) VL Primary4 H4 1,245 North Fork Lewis VH Cascade Primary VH 7,300 (WA) Late Fall Sandy (OR) H Primary VH 3,561 1 2
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1 2 Figure 3. Map of the LCR Chinook Salmon ESU’s spawning and rearing areas, illustrating 3 populations and MPGs. Several watersheds contain or historically contained both fall 4 and spring runs; only the fall-run populations are illustrated here (NWFSC 2015).
5 LCR Chinook salmon are classified into three life history types including spring runs, early-fall 6 runs (“tules”, pronounced (too-lees)), and late-fall runs (“brights”) based on when adults return 7 to freshwater (Table 12). LCR spring Chinook salmon are stream-type, while LCR early-fall and 8 late-fall Chinook salmon are ocean-type. Other life history differences among run types include 9 the timing of spawning, incubation, emergence in freshwater, migration to the ocean, maturation, 10 and return to freshwater. This life history diversity allows different runs of Chinook salmon to 11 use streams as small as 10 feet wide and rivers as large as the main stem Columbia (NMFS 12 2013c). Stream characteristics determine the distribution of run types among LCR streams. 13 Depending on run type, Chinook salmon may rear for a few months to a year or more in 14 freshwater streams, rivers, or the estuary before migrating to the ocean in spring, summer, or fall. 15 All runs migrate far into the north Pacific on a multi-year journey along the continental shelf to 16 Alaska before circling back to their river of origin. The spawning run typically includes three or 17 more age classes. Adult Chinook salmon are the largest of the salmon species, and LCR fish 18 occasionally reach sizes up to 25 kilograms (55 lbs). Chinook salmon require clean gravels for 19 spawning and pool and side-channel habitats for rearing. All Chinook salmon die after spawning 20 once (NMFS 2013c).
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1 Table 12. Life history and population characteristics of LCR Chinook salmon. Life-History Features Characteristic Spring Early-fall (tule) Late-fall (bright) Number of extant population 9 21 2 Life history type Stream Ocean Ocean River entry timing March-June August-September August-October September- Spawn timing August-September November-January November Headwater large Main stem large Main stem large Spawning habitat type tributaries tributaries tributaries Emergence timing December-January January-April March-May Usually 12-14 1-4 months, a few up 1-4 months, a few up Duration in freshwater months to 12 months to 12 months Main stem, Main stem, Tributaries and main Rearing habitat tributaries, sloughs, tributaries, sloughs, stem estuary estuary Several weeks up to Several weeks up to Estuarine use A few days to weeks several months several months As far north as As far north as As far north as Ocean migration Alaska Alaska Alaska Age at return 4-5 years 3-5 years 3-5 years Recent natural spawners 800 6,500 9,000 Recent hatchery adults 12,600 (1999-2000) 37,000 (1991-1995) NA
2 All LCR Chinook salmon runs have been designated as part of a LCR Chinook Salmon ESU that 3 includes natural populations in Oregon and Washington from the ocean upstream to and 4 including the White Salmon River in Washington and Hood River in Oregon. Fall Chinook 5 salmon (tules and brights) historically were found throughout the entire range, while spring 6 Chinook salmon historically were only found in the upper portions of basins with snowmelt 7 driven flow regimes (western Cascade Crest and Columbia Gorge tributaries) (LCFRB 2010). 8 Bright Chinook salmon were identified in only two basins in the western Cascade Crest 9 tributaries. In general, bright Chinook salmon mature at an older average age than either LCR 10 spring or tule Chinook salmon, and have a more northerly oceanic distribution. Currently, the 11 abundance of all fall Chinook salmon greatly exceeds that of the spring component (NWFSC 12 2015). 13 14 Status of the species is determined based on the abundance, productivity, spatial structure, and 15 diversity of its constituent natural populations. Best available information indicates that the 16 species, in this case the LCR Chinook Salmon ESU, is at high risk and remains at threatened 17 status. Each LCR Chinook salmon natural population baseline and target persistence probability 18 level is summarized in Table 11, along with target abundance for each population that would be 19 consistent with delisting. Persistence probability is measured over a 100 year time period and 20 ranges from very low (probability < 40%) to very high (probability >99%). 21 22 If the recovery scenario in Table 11 were achieved, it would exceed the WLC TRT’s MPG-level 23 viability criteria for the Coast and Cascade fall MPGs, the Cascade spring MPG, and the Cascade
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1 late-fall MPG. However, the recovery scenario for Gorge spring and Gorge fall Chinook salmon 2 does not meet WLC TRT criteria because, within each MPG, the scenario targets only one 3 population (the Hood) for high persistence probability. Exceeding the WLC TRT criteria, 4 particularly in the Cascade fall and Cascade spring Chinook salmon MPG, was intentional on the 5 part of local recovery planners to compensate for uncertainties about meeting the WLC TRT’s 6 criteria in the Gorge fall and spring MPGs. In addition, multiple spring Chinook salmon natural 7 populations are prioritized for aggressive recovery efforts to balance risks associated with the 8 uncertainty of success in reintroducing spring Chinook salmon populations above tributary dams 9 in the Cowlitz and Lewis systems. 10 11 NMFS (2013c) commented on the uncertainties and practical limits to achieving high viability 12 for the spring and tule populations in the Gorge MPGs. Recovery opportunities in the Gorge 13 were limited by the small numbers of natural populations and the high uncertainty related to 14 restoration because of Bonneville Dam passage and inundation of historically productive 15 habitats. NMFS also recognized the uncertainty regarding the TRT’s MPG delineations between 16 the Gorge and Cascade MPG populations and that several Chinook salmon populations 17 downstream from Bonneville Dam may be quite similar to those upstream of Bonneville Dam. 18 As a result, the recovery plan recommends that additional natural populations in the Coast and 19 Cascade MPGs achieve recovery status to provide a safety factor to offset the anticipated 20 shortcomings for the Gorge MPGs. This was considered a more precautionary approach to 21 recovery than merely assuming that efforts related to the Gorge MPG would be successful. 22 23 Based on the information provided by the WLC TRT and the management unit recovery 24 planners, NMFS concluded in the recovery plan that the recovery scenario in Table 11 represents 25 one of multiple possible scenarios that would meet biological criteria for delisting. The 26 similarities between the Gorge and Cascade MPG, coupled with compensation in the other strata 27 for not meeting TRT criteria in the Gorge stratum would provide an ESU no longer likely to 28 become endangered. 29 30 Upper Willamette River Spring Chinook Salmon ESU
31 On March 24, 1999, NMFS listed the UWR Chinook Salmon ESU as a threatened species (64 32 FR 14308). The threatened status was reaffirmed on June 28, 2005 (70 FR 37160) and on April 33 14, 2014 (79 FR 20802) (Table 7). Critical habitat was designated on June 28, 2005 (70 FR 34 37160) (Table 7). 35 36 The ESU includes all naturally spawned populations of spring-run Chinook salmon in the 37 Clackamas River and in the Willamette River, and its tributaries, above Willamette Falls, 38 Oregon, as well as several artificial propagation programs (Figure 4). The ESU contains seven 39 historical populations, within a single MPG (western Cascade Range, Table 13). 40 41 Table 13. UWR Chinook salmon ESU description and major population group (MPG) (Jones Jr. 42 2015; NMFS 2016b). ESU Description
Threatened Listed under ESA in 1999; updated in 2014 (see Table 7)
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1 major population group 7 historical populations
Major Population Populations Group
Western Cascade Range Clackamas River, Molalla River, North Santiam River, South Santiam River, Calapooia River, McKenzie River, Middle Fork Willamette River
Artificial production
Hatchery programs McKenzie River spring, North Santiam spring, Mollala spring, South included in ESU (6) Santiam spring, MF Willamette spring, Clackamas spring
Hatchery programs not n/a included in ESU (0)
1 2 UWR Chinook salmon’s genetics have been shown to be strongly differentiated from nearby 3 populations, and are considered one of the most genetically distinct groups of Chinook salmon in 4 the Columbia River Basin (Beacham et al. 2006; Waples et al. 2004). For adult Chinook salmon, 5 Willamette Falls historically acted as an intermittent physical barrier to upstream migration into 6 the UWR basin, where adult fish could only ascend the falls at high spring flows. It has been 7 proposed that the falls serve as an zoogeographic isolating mechanism for a considerable period 8 of time (Waples et al. 2004), and has led to, among other attributes, the unique early run timing 9 of these populations relative to other LCR spring-run populations. Historically, the peak 10 migration of adult salmon over the falls occurred in late May. Low flows during the summer and 11 autumn months prevented fall-run salmon and coho from reaching the UWR basin (NMFS and 12 ODFW 2011). 13 14 The generalized life history traits of UWR Chinook are summarized in Table 14. Today, adult 15 UWR Chinook salmon begin appearing in the lower Willamette River in January, with fish 16 entering the Clackamas Rivers as early as March. The majority of the run ascends Willamette 17 Falls from late April through May, with the run extending into mid-August (Myers et al. 2006). 18
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1 2 Figure 4. Map of the UWR Chinook Salmon ESU’s spawning and rearing areas, illustrating 3 populations and major population groups (From NWFSC 2015). 4 Chinook migration past the falls generally coincides with a rise in river temperatures above 50°F 5 (Howell et al. 1985; Mattson 1948; Nicholas 1995). Historically, passage over the falls may 6 have been marginal in June because of diminishing flows, and only larger fish would have been 7 able to ascend. Mattson (1963) discusses a late spring Chinook run that once ascended the falls 8 in June. The disappearance of the June run in the 1920s and 1930s was associated with the 9 dramatic decline in water quality in the lower Willamette River (Mattson 1963). This was also 10 the period of heaviest dredging activity in the lower Willamette River. Dredge material was not 11 only used to increase the size of Swan Island, but to fill floodplain areas like Guilds Lakes. 12 These activities were thought to heavily influence the water quality at the time. Chinook salmon 13 now ascend the falls via a fish ladder at Willamette Falls. 14 15 Table 14. A summary of the general life history characteristics and timing of UWR Chinook 16 salmon1. Life-History Trait Characteristic January-April; ascending Willamette Falls April- Willamette River entry timing August Spawn timing August-October, peaking in September Spawning habitat type Larger headwater streams Emergence timing December-March
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Rearing habitat Rears in larger tributaries and mainstem Willamette Duration in freshwater 12-14 months; rarely 2-5 months Estuarine use Days to several weeks Life history type Stream Ocean migration Predominately north, as far as southeast Alaska Age at return 3-6 years, primarily 4-5 years 1 Data are from numerous sources (From NMFS and ODFW 2011). 1 2 Status of the species is determined based on the abundance, productivity, spatial structure, and 3 diversity of its constituent natural populations. Best available information indicates that the 4 UWR Chinook Salmon ESU, is at moderate to high risk and remains at threatened status. The 5 Willamette Valley was not glaciated during the last epoch (McPhail and Lindsey 1970), and 6 Willamette Falls likely served as a physical barrier for reproductive isolation of Chinook salmon 7 populations. This isolation had the potential to produce local adaptation relative to other 8 Columbia River populations (Myers et al. 2006). Fish ladders were constructed at the falls in 9 1872 and again in 1971, but it is not clear what role they may have played up to the present day 10 in reducing localized adaptations in UWR fish populations. Little information exists on the life 11 history characteristics of the historical UWR Chinook populations, especially since early fishery 12 exploitation (starting in the mid-1880s), habitat degradation in the lower Willamette Valley 13 (starting in the early 1800s), and pollution in the lower Willamette River (by early 1900s) likely 14 altered life history diversity before data collections began in the mid-1900s. Nevertheless, it is 15 thought that UWR Chinook salmon still contain a unique set of genetic resources compared to 16 other Chinook salmon stocks in the WLC Domain (NMFS and ODFW 2011). 17 18 According to the most recent status review (NWFSC 2015), abundance levels for five of the 19 seven individual populations in this ESU remain well below their recovery goals. Of these, the 20 Calapooia River population may be functionally extinct, and the Molalla River population 21 remains critically low (although perhaps only marginally better than the 0 VSP score estimated 22 in the Recovery Plan). Abundances in the North and South Santiam Rivers have risen since the 23 last review (Ford 2011), but still range only in the high hundreds of fish. Improvements in the 24 status of the Middle Fork Willamette River population relates solely to the return of natural 25 adults to Fall Creek; however, the capacity of the Fall Creek basin alone is insufficient to achieve 26 the recovery goals for the Middle Fork Willamette River individual population. The status 27 review incorporates valuable information from the Fall Creek program that is relevant to the use 28 of reservoir draw downs as a method of juvenile downstream passage. The proportion of natural- 29 origin spawners improved in the North and South Santiam Basins, but was still below identified 30 recovery goals. The presence of juvenile (subyearling) Chinook salmon in the Molalla River 31 suggests that there is some limited natural production in the Molalla River. Additionally, the 32 Clackamas and McKenzie Rivers have previously been viewed as natural population 33 strongholds, but both individual populations experienced declines in abundance7 (NWFSC 34 2015).
7 Spring-run Chinook salmon counts on the Clackamas River are taken at North Fork Dam, where only unmarked fish are passed above the Dam presently. A small percentage of these unmarked fish are of hatchery-origin. While there is some spawning below the Dam, it is not clear whether any progeny from the downstream redds contribute to escapement.
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1 2 All seven historical populations of UWR Chinook salmon identified by the WLC-TRT occur 3 within the action area and are contained within a single ecological subregion, the Western 4 Cascade Range (Table 15). 5 6 Table 15. Scores for the key elements (A/P, diversity, and spatial structure) used to determine 7 current overall viability risk for UWR Chinook salmon (NMFS and ODFW 2011; 8 NWFSC 2015)1. Spatial Overall Extinction Population (Watershed) A/P Diversity Structure Risk Clackamas River M M L M Molalla River VH H H VH North Santiam River VH H H VH South Santiam River VH M M VH Calapooia River VH H VH VH McKenzie River VL M M L Middle Fork Willamette River VH H H VH 1 All populations are in the Western Cascade Range ecological subregion. Risk ratings range from very low (VL), low (L), moderate (M), high (H), to very high (VH). All populations originate in the action area (From NMFS 2016b). 9 10 The Clackamas and McKenzie River populations had the best overall risk ratings for A/P, spatial 11 structure, and diversity, as of 2016. Data collected since the BRT status update in 2005 12 highlighted the substantial risks associated with pre-spawning mortality. A recovery plan was 13 finalized for this species on August 5, 2011 (NMFS and ODFW 2011). Although recovery plans 14 are targeting key limiting factors for future actions, there have been no significant on-the- 15 ground-actions since the 2011 status review to resolve the lack of access to historical habitat 16 above dams nor substantial actions removing hatchery fish from the spawning grounds (NMFS 17 2016b). Furthermore, no data is available for natural-origin spawner abundance for UWR 18 Chinook salmon populations. 19 20 Population status is characterized relative to persistence (which combines the abundance and 21 productivity criteria), spatial structure, diversity, and also habitat characteristics. The overview 22 above for UWR Chinook salmon populations suggests that there has been relatively little net 23 change in the VSP score for the ESU since the last review, so the ESU remains at moderate risk 24 (Table 16) (NWFSC 2015). 25 26 Table 16. Summary of VSP scores and recovery goals for UWR Chinook salmon populations 27 (NWFSC 2015). Total Recovery MPG State Population VSP Goal Score OR Clackamas River 2 4 OR Molalla River 0 1 Western Cascade Range OR North Santiam River 0 3 OR South Santiam River 0 2 OR Calapooia River 0 1
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OR McKenzie River 3 4 OR Middle Fork Willamette River 0 3 1 2 3 Upper Columbia River Steelhead DPS
4 Steelhead (O. mykiss) occur as two basic anadromous run types based on the level of sexual 5 maturity at the time of river entry and the duration of the spawning migration (Burgner et al. 6 1992). The stream-maturing type (inland), or summer steelhead, enters freshwater in a sexually 7 immature condition and requires several months in freshwater to mature and spawn. The ocean- 8 maturing type (coastal), or winter steelhead, enters freshwater with well-developed gonads and 9 spawns shortly after river entry (Barnhart 1986).
10 UCR steelhead are summer steelhead, returning to freshwater between May and October, and 11 require up to 1 year in freshwater to mature before spawning (Chapman et al. 1994). Spawning 12 occurs between January and June. In general, summer steelhead prefer smaller, higher-gradient 13 streams relative to other Pacific salmon, and they spawn farther upstream than winter steelhead 14 (Behnke and American Fisheries Society 1992; Withler 1966). Progeny typically reside in 15 freshwater for two years before migrating to the ocean, but freshwater residence can vary from 1- 16 7 years (Peven et al. 1994). For UCR steelhead, marine residence is typically one year, although 17 the proportion of two-year ocean fish can be substantial in some years. They migrate directly 18 offshore during their first summer rather than migrating nearer to the coast as do salmon. During 19 fall and winter, juveniles move southward and eastward (Hartt and Dell 1986).
20 The UCR Steelhead DPS includes all naturally spawned steelhead populations below natural and 21 man-made impassable barriers in streams in the Columbia River Basin upstream of the Yakima 22 River, Washington to the U.S.–Canada border. The UCR Steelhead DPS also includes six 23 artificial propagation programs: the Wenatchee River, Wells Hatchery (in the Methow and 24 Okanogan rivers), WNFH, Omak Creek, and the Ringold steelhead hatchery programs.
25 The UCR Steelhead DPS consisted of three MPGs before the construction of Grand Coulee 26 Dam, but it is currently limited to one MPG with four extant populations: Wenatchee, Methow, 27 Okanogan, and Entiat. A fifth population in the Crab Creek drainage is believed to be 28 functionally extinct. What remains of the DPS includes all naturally spawned populations in all 29 tributaries accessible to steelhead upstream from the Yakima River in Washington State, to the 30 U.S. – Canada border (Figure 5). 31
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1 2 Figure 5. Upper Columbia River Steelhead DPS (ICTRT 2008). 3 4 Status of the species is determined based on the abundance, productivity, spatial structure, and 5 diversity of its constituent natural populations. Best available information indicates that the UCR 6 Steelhead DPS is at high risk and remains at threatened status. The ESA Recovery Plan (UCSRB 7 2007) requires each of the four extant steelhead populations to be viable. For the 2005-2014 8 period, abundance has increased for natural-origin spawners in each of the four extant 9 populations (Table 17). However, natural-origin returns remain well below target levels for three 10 of the four populations. Productivity remained the same for three of the four populations and 11 decreased for the Entiat population relative to the last review (Ford 2011). For spatial structure 12 and diversity, hatchery origin returns continue to constitute a high fraction (Table 17) of total 13 spawners in natural spawning areas for the DPS as a whole (NWFSC 2015). The predominance 14 of hatchery fish on the spawning grounds is an increasing risk, and populations that rely solely 15 on hatchery spawners are not viable over the long-term (McElhany et al. 2000). Based on the 16 combined ratings for abundance/productivity and spatial structure/diversity, three of the four 17 extant populations and the DPS remain at high risk of extinction. 18
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1 Table 17. Risk levels and viability ratings for natural-origin UCR steelhead populations (NWFSC 2 2015). Minimum Spawning % Natural- Productivity Overall Population Abundance Abundance origin spawners (2005-2014) Risk Threshold (2005-2014) (2010-2014) Wenatchee River 1000 1025 (386-2235) 1.207 58 Maintained Entiat River 500 146 (59-310) 0.434 31 High Methow River 1000 651 (365-1105) 0.371 24 High Okanogan River 750 189 (107-310) 0.154 13 High 3 4 Many factors affect the abundance, productivity, spatial structure, and diversity of the UCR 5 Steelhead DPS. Factors limiting the DPS’s survival and recovery include: 6 • past management practices such as the Grand Coulee Fish Maintenance Project 7 • survival through the FCRPS 8 • degradation and loss of estuarine areas that help the fish survive the transition between 9 fresh and marine waters 10 • spawning and rearing areas that have lost deep pools, cover, side-channel refuge areas, 11 and high quality spawning gravels 12 • predation by native and non-native species 13 • harvest 14 • interbreeding and competition with hatchery fish that far outnumber fish from natural 15 populations 16 17 Snake River Steelhead DPS
18 O. mykiss exhibit perhaps the most complex suite of life-history traits of any species of Pacific 19 salmonid. They can be anadromous or freshwater resident, and under some circumstances, yield 20 offspring of the opposite form. Steelhead are the anadromous form. A non-anadromous form of 21 O. mykiss (redband trout) co-occurs with the anadromous form in this DPS, and juvenile life 22 stages of the two forms can be very difficult to differentiate. Steelhead can spend up to 7 years in 23 fresh water prior to smoltification, and then spend up to 3 years in salt water prior to first 24 spawning. This species can also spawn more than once (iteroparous), whereas all other species of 25 Oncorhynchus, except O. clarkii, spawn once and then die (semelparous). Snake River steelhead 26 are classified as summer-run because they enter the Columbia River from late June to October. 27 After holding over the winter, summer steelhead spawn the following spring (March to May). 28 Factors that limit the DPS’s survival and recovery include: juvenile and adult migration through 29 the FCRPS; the degradation and loss of estuarine areas that help fish transition between fresh and 30 marine waters; spawning and rearing areas that have lost deep pools, cover, side-channel refuge 31 areas, high quality spawning gravels, and; interbreeding and competition with hatchery fish that 32 outnumber natural-origin fish. A more detailed description of the populations that are the focus 33 of this consultation follows. 34 35 There are two independent populations within the Lower Snake River MPG: Tucannon River 36 and Asotin Creek. The ESA Recovery Plan for southeast Washington (SRSRB 2011) requires 37 that the Tucannon River population be at moderate risk and for the Asotin Creek population to be
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1 at low risk of extinction. The most recent status review (NWFSC 2015) found that the Tucannon 2 River population remains at high risk, and the Asotin Creek population is maintained (Table 18). 3 However, both populations have insufficient data on abundance and productivity to assess 4 accurately these metrics. 5 6 There are four independent populations of steelhead within the Grand Ronde MPG: Joseph 7 Creek, Lower Grand Ronde River, Upper Grand Ronde River, and Wallowa River. The Draft 8 ESA Recovery Plan for northeast Oregon (NMFS 2012a) requires that the Upper Grand Ronde 9 and Wallowa River populations have a minimum of moderate risk, the Joseph Creek population 10 maintain its current low risk status, and the Lower Grand Ronde population achieve low or 11 moderate risk. Although these populations are close to achieving recovery requirements, there is 12 a large amount of uncertainty in the data. 13 14 There is one independent population of steelhead within the Imnaha MPG, the Imnaha River 15 population. The Draft ESA Recovery Plan for northeast Oregon (NMFS 2012a) requires that the 16 Imnaha River population achieve low risk. NMFS’ status review (NWFSC 2015) found that 17 information for this population is insufficient to be able to assess risk reliably, but estimates the 18 population is most likely at moderate risk of extinction (Table 18). 19 20 Table 18. Risk levels and viability ratings for Snake River steelhead populations (NWFSC 21 2015). Parentheses indicate range. Data are from 2004-2015. ID = insufficient data; 22 ICTRT = Interior Columbia Technical Recovery Team. Population ICTRT Natural Productivity Abundance Spatial Overall risk minimum spawning and structure and viability rating threshold abundance productivity diversity risk risk Tucannon River 1000 ID ID High1 Moderate High1
Asotin Creek 500 ID2 ID Moderate1 Moderate Moderate1
Lo. Grande Ronde 1000 ID ID 1 Moderate Moderate1
Joseph Creek 500 1839 1.86 Very low Low Low
Up. Grande Ronde 1500 1649 (0.21) 3.15 (0.4) Moderate Moderate Moderate
Wallowa River 1000 ID ID High1 Moderate High1
Imnaha River 1000 ID ID Moderate1 Moderate Moderate1 23 1Uncertain due to lack of data, only a few years of data, or large gaps in data series. 24 2Monitoring beginning in 2005 suggests that the average annual natural-origin population seems is ~900-1100 (J. 25 Bumgarner, WDFW, personal communication, April 6, 2017). 26 27 Mid-Columbia River Steelhead DPS
28 On March 25, 1999, NMFS listed the Mid-Columbia River Steelhead DPS as a threatened 29 species (64 FR 14517). The threatened status was reaffirmed in 2006 and most recently on April 30 14, 2014 (79 FR 20802). Critical habitat for the Mid-Columbia River steelhead was designated 31 on September 2, 2005 (70 FR 52808) (Table 7).
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1 2 The Mid-Columbia River Steelhead DPS includes naturally spawned anadromous O. mykiss 3 originating from below natural and manmade impassable barriers from the Columbia River and 4 its tributaries upstream of the Wind River (Washington) and Hood River (Oregon) to and 5 including the Yakima River, excluding the Upper Columbia River tributaries (upstream of Priest 6 Rapids Dam) and the Snake River (Figure 6). Four MPGs, composed of 19 historical 7 populations (2 extirpated), compose the Mid Columbia River Steelhead DPS (Figure 6). Inside 8 the geographic range of the DPS, 11 hatchery steelhead programs are currently operational. 9 Seven of these artificial programs are included in the DPS (Table 19). 10 11 Table 19. MCR Steelhead DPS description and MPGs (Jones Jr. 2015; NWFSC 2015).
DPS Description Listed under ESA as threatened in 1999; updated in 2014 (see Threatened Table 7) 4 major population groups 19 historical populations (2 extirpated) Major Population Group Populations Deschutes River Eastside, Deschutes River Westside, Fifteenmile Cascades Eastern Slope Tributaries Creek*, Klickitat River*, Rock Creek* John Day River Lower Mainstem Tributaries, John Day River John Day River Upper Mainsteam Tributaries, MF John Day River, NF John Day River, SF John Day River Naches River, Satus Creek, Toppenish Creek, Yakima River Yakima River Upstream Mainstem
Umatilla/Walla Walla rivers Touchet River, Umatilla River, Walla Walla River
Artificial production Touchet River Endemic summer, Yakima River Kelt Hatchery programs included in DPS Reconditioning summer (in Satus Creek, Toppenish Creek, Naches (7) River, and Upper Yakima River), Umatilla River summer, Deschutes River summer
Hatchery programs not included in Lyons Ferry NFH summer, Walla Walla River Release summer, DPS (4) Skamania Stock Release summer, Skamania Stock Release winter
12 * These populations are winter steelhead populations. All other populations are summer steelhead populations. 13 14 15
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1 2 Figure 6. Map of the MCR Steelhead DPS’s spawning and rearing areas, illustrating 3 populations and MPGs (NWFSC 2015). 4 5 Most fish in this DPS smolt at two years and spend one to two years in salt water before re- 6 entering fresh water, where they may remain up to a year before spawning (Howell et al. 1985; 7 BPA 1992). Summer steelhead typically enter freshwater from June through October with peak 8 entry occurring in July (Busby et al. 1996). Juvenile life stages (i.e., eggs, alevins, fry, and parr) 9 inhabit freshwater/riverine areas throughout the range of the DPS. A non-anadromous form of O. 10 mykiss (redband trout) co-occurs with the anadromous form in this DPS, and juvenile life stages 11 of the two forms can be very difficult to differentiate. 12 13 Best available information indicates that the MCR Steelhead DPS is at moderate risk and 14 remains at threatened status. The most recent status update (NWFSC 2015) used updated 15 abundance and hatchery contribution estimates provided by regional fishery managers to inform 16 the analysis on this DPS. However, this DPS has been noted as difficult to evaluate in several of 17 the reviews for reasons such as: the wide variation in abundance for individual natural 18 populations across the DPS, chronically high levels of hatchery strays into the Deschutes River, 19 and a lack of consistent information on annual spawning escapements in some tributaries 20 (NWFSC 2015). 21
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1 Abundance and productivity are linked, as populations with low productivity can still persist if 2 they are sufficiently large, and small populations can persist if they are sufficiently productive. 3 A viable natural population needs sufficient abundance to maintain genetic health and to respond 4 to normal environmental variation, and sufficient productivity to enable the population to quickly 5 rebound from periods of poor ocean conditions or freshwater perturbations (Table 20) (NMFS ). 6 2009). 7 8 Table 20. Ecological subregions, natural populations, and scores for the key elements (A/P, 9 diversity, and SS/D) used to determine current overall viability risk for MCR 10 Steelhead DPS1.
Overall Ecological Integrated Population (Watershed) A/P Diversity Viability Subregions SS/D Risk Fifteenmile Creek L L L Viable Klickitat River M M M MT Eastside Deschutes River L M M Viable Cascade Eastern Slope Tributaries Westside Deschutes River H M M H* Rock Creek H M M H White Salmon2 E* Crooked River3 E* Upper Mainstem M M M MT Highly North Fork VL L L Viable John Day River Middle Fork M M M MT South Fork M M M MT Lower Mainstem M M M MT Umatilla River M M M MT Walla Walla and Touchet River M M M H Umatilla rivers Walla Walla River M M M MT Viable Satus Creek M M M (MT) Viable Yakima River Toppenish Creek M M M (MT) Naches River H M M H Upper Yakima H H H H 1 Risk ratings range from very low (VL), low (L), moderate (M), high (H), to very high (VH), and extirpated €. Maintained (MT) population status indicates that the population does not meet the criteria for a viable population but does support ecological functions and preserve options for recovery of the DPS. Extirpated populations were not evaluated as indicated by the blank cells. * Re-introduction efforts underway (NMFS 2009). 2 This population is re-establishing itself following removal of Condit Dam. 3 This population was designated an experimental population on January 15, 2013 (78 FR 2893)
11 Limited population abundance data are available for the populations in the MCR Steelhead DPS. 12 Of the 17 populations in this DPS, data on natural-origin spawner abundances for 14 populations 13 are provided below; such information for the remaining three populations is not available. In the 14 2010 status review, Ford (2011) summarized that natural-origin and total spawning escapements 15 have increased in the most recent brood cycle, relative to the period associated with the 2005
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1 BRT review, for all four populations in the Yakima River MPG. It is apparent that this trend is 2 continuing through the recent years as well (Table 20). The 15-year trend in natural-origin 3 spawners was positive for the West Side Deschutes population, and negative for the East Side 4 Deschutes run (Table 20). There is significant tribal and sport harvest associated with the 5 Klickitat steelhead run, with the sport harvest being targeted on hatchery fish (NWFSC 2015). 6 Overall, natural-origin spawning estimates are highly variable relative to minimum abundance 7 thresholds across the populations in the DPS. Natural-origin returns to the Umatilla, Walla 8 Walla, John Day, and Klickitat rivers have increased over the last several years 9 (http://odfwrecoverytracker.org/explorer/). 10 11 The most recent status review update (NWFSC 2015) revealed that updated information on 12 spawner and juvenile rearing distributions does not support a change in the spatial structure 13 status for the MCR Steelhead DPS natural populations. Status indicators for within population 14 diversity have changed for some populations, although in most cases the changes have not been 15 sufficient to shift composite risk ratings for any particular populations (NWFSC 2015). 16 17 18 Lower Columbia River Steelhead DPS
19 On March 19, 1998, NMFS listed the LCR Steelhead DPS as a threatened species (63 FR 20 13347). The threatened status was reaffirmed on January 5, 2006 (71 FR 834) and most recently 21 on April 14, 2014 (79 FR 20802) (Table 7). Critical habitat for LCR steelhead was designated on 22 September 2, 2005 (70 FR 52833) (Table 7). 23 24 The DPS includes all naturally spawned anadromous steelhead populations below natural and 25 manmade impassable barriers in streams and tributaries to the Columbia River between the 26 Cowlitz and Wind Rivers, Washington (inclusive), and the Willamette and Hood Rivers, Oregon 27 (inclusive), as well as multiple artificial propagation programs (NWFSC 2015). 28 29 Inside the geographic range of the DPS, 29 hatchery programs are currently operational, of 30 which only 7 are considered part of the ESA-listed DPS description (Table 21). Excluded are 31 steelhead in the upper Willamette River Basin above Willamette Falls, Oregon, and from the 32 Little White Salmon and White Salmon Rivers, Washington. The LCR Steelhead DPS is 33 composed of 23 historical populations, distributed through two ecological zones, split by summer 34 or winter life history resulting in four MPGs (Table 22). There are six summer populations and 35 seventeen winter populations (Figure 7). 36 37 Table 21. LCR Steelhead DPS description and MPGs (Jones Jr. 2015; NWFSC 2015).
DPS Description Threatened Listed under ESA in 1998; updated in 2014 (see Table 7) 4 major population 23 historical populations groups Major Population Group Populations Cascade summer Kalama (C), North Fork Lewis, East Fork Lewis (G), Washougal (C) Gorge summer Wind (C), Hood
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Cascade winter Lower Cowlitz, Upper Cowlitz (C, G), Cispus (C, G), Tilton, South Fork Toutle, North Fork Toutle (C), Coweeman, Kalama, North Fork Lewis (C), East Fork Lewis, Salmon Creek, Washougal, Clackamas (C), Sandy (C) Gorge winter Lower Gorge, Upper Gorge, Hood (C, G) Artificial production Hatchery programs Kalama River Wild Winter, Kalama River Wild Summer, Hood River included in DPS (7) Winter (ODFW stock # 50), Cowlitz Trout Hatchery Late Winter, Clackamas Hatchery Late Winter (ODFW stock # 122), Sandy Hatchery Late Winter (ODFW stock # 11), Lewis River Wild Late Winter. Hatchery programs not Upper Cowlitz River Wild Late Winter, Tilton River Wild Late Winter, included in ESU (22) Cowlitz Summer, Friends of the Cowlitz Summer, Cowlitz Game and Anglers Summer, North Toutle Summer, Kalama River Summer, Merwin Summer, Fish First Summer, Speelyai Bay Net-Pen Summer, EF Lewis Summer, Skamania Summer, Kalama River Winter, Cowlitz Early Winter, Merwin Winter, Coweeman Ponds Winter, EF Lewis Winter, Skamania Winter, Klineline Ponds Winter, Eagle Creek NFH Winter, Clackamas Summer, Sandy River Summer. 1 The designations "(C)" and "(G)" identify Core and Genetic Legacy populations, respectively (NMFS 2013c).
1
2 3 Figure 7. Map of populations in the LCR Steelhead DPS (NWFSC 2015).
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1 LCR basin populations include summer and winter steelhead (Table 22). The two life history 2 types differ in degree of sexual maturity at freshwater entry, spawning time, and frequency of 3 repeat spawning (NMFS 2013c). Generally, summer steelhead enter fresh water from May to 4 October in a sexually immature condition, and require several months in fresh water to reach 5 sexual maturity and spawn between late February and early April. Winter steelhead enter fresh 6 water from November to April in a sexually mature condition and spawn in late April and early 7 May. Iteroparity (repeat spawning) rates for Columbia Basin steelhead have been reported as 8 high as 2% to 6% for summer steelhead and 8% to 17% for winter steelhead (Busby et al. 1996; 9 Hulett et al. 1996; Leider et al. 1986). 10 11 Status of the species is determined based on the abundance, productivity, spatial structure, and 12 diversity of its constituent natural populations. Best available information indicates that the 13 species, in this case the LCR Steelhead DPS, is at moderate risk and remains at threatened status. 14 Each natural population’s baseline and target persistence probabilities are summarized in Table 15 22, along with target abundance for each population that would be consistent with delisting. 16 Persistence probability is measured over a 100 year time period and ranges from very low 17 (probability < 40%) to very high (probability >99%). 18 19 Table 22. Current status for LCR steelhead populations and recovery scenario targets (NMFS 20 2013c). Status Assessment Recovery Scenario Baseline Target MPG Population (State) Abundance Persistence Contribution2 Persistence Target3 Probability1 Probability Kalama (WA) M Primary H 500 Cascade North Fork Lewis (WA) VL Stabilizing VL -- summer EF Lewis (WA) VL Primary H 500 Washougal (WA) M Primary H 500 Gorge Wind (WA) H Primary VH 1,000 summer Hood (OR) VL Primary H* 2,008 Lower Cowlitz (WA) L Contributing M 400 Upper Cowlitz (WA) VL Primary H 500 Cispus (WA) VL Primary H 500 Tilton (WA) VL Contributing L 200 South Fork Toutle (WA) M Primary H+ 600 North Fork Toutle (WA) VL Primary H 600 Cascade Coweeman (WA) L Primary H 500 winter Kalama (WA) L Primary H+ 600 North Fork Lewis (WA) VL Contributing M 400 East Fork Lewis (WA) M Primary H 500 Salmon Creek (WA) VL Stabilizing VL -- Washougal (WA) L Contributing M 350 Clackamas (OR) M Primary H* 10,671 Sandy (OR) L Primary VH 1,519 Lower Gorge (WA/OR) L Primary H 300 Gorge Upper Gorge (WA/OR) L Stabilizing L -- winter Hood (OR) M Primary H 2,079
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1 1 LCFRB (2010) used the late 1990s as a baseline period for evaluating status; ODFW (2010a) assume average 2 environmental conditions of the period 1974-2004. VL = very low, L = low, M = moderate, H = high, VH = very 3 high. These are adopted in the recovery plan NMFS (2013c). 4 2 Primary, contributing, and stabilizing designations reflect the relative contribution of a population to recovery 5 goals and delisting criteria. Primary populations are targeted for restoration to a high or very high persistence 6 probability. Contributing populations are targeted for medium or medium-plus viability. Stabilizing populations are 7 those that will be maintained at current levels (generally low to very low viability), which is likely to require 8 substantive recovery actions to avoid further degradation. 9 3 Abundance objectives account for related goals for productivity (NMFS 2013c). 10 * Oregon’s analysis indicates a low probability of meeting the delisting objective of high persistence probability for 11 this population. 12 13 If the recovery scenario in Table 22 is achieved, it would exceed the WLC TRT’s viability 14 criteria in the Cascade winter and summer MPGs. This is intentional given the scenario for 15 uncertainties about the feasibility of meeting the viability criteria for populations within the 16 Gorge MPGs. Questions remain concerning the historical role of the populations, specifically 17 with the winter populations in the Gorge MPGs, and the current habitat potential (NMFS 2013c). 18 19 NMFS (2013c) commented on the uncertainties and practical limits to achieving high viability 20 for the populations in the Gorge MPG. Recovery opportunities in the Gorge were limited by the 21 small number of populations and the high uncertainty related to restoration because of 22 Bonneville Dam passage and inundation of historically productive habitats. NMFS recognized 23 the uncertainty regarding the TRT’s MPG delineations between the Gorge and Cascade MPG 24 populations, including questions of whether the Gorge populations were highly persistent 25 historically, whether they functioned as independent populations within their stratum in the same 26 way that the Cascade populations did, and whether the Gorge stratum itself should be considered 27 a separate stratum from the Cascade stratum. As a result, the recovery plan recommends 28 improvements in more than the minimum number of populations required in the Cascade 29 summer and winter MPGs, to provide a safety factor to offset the anticipated shortcomings for 30 the Gorge MPGs. This was considered a more precautionary approach to recovery than merely 31 assuming that efforts related to the Gorge MPG would be successful. 32 33 Upper Willamette River Steelhead DPS
34 On March 25, 1999, NMFS listed the Upper Willamette River (UWR) Steelhead DPS as a 35 threatened species (64 FR 14517). The threatened status was reaffirmed in 2006 and most 36 recently on April 14, 2014 (79 FR 20802) (Table 7). Critical habitat for the DPS was designated 37 on September 2, 2005 (70 FR 52848) (Table 7). 38 The UWR steelhead DPS includes all naturally spawned anadromous winter-run steelhead 39 originating below natural and manmade impassable barriers in the Willamette River, Oregon, 40 and its tributaries upstream from Willamette Falls to the Calapooia River (NWFSC 2015). One 41 MPG, composed of 4 historical populations, comprises the UWR Steelhead DPs. Inside the 42 geographic range of the DPS, 1 hatchery program is currently operational., though it is not 43 included in the DPS (Table 23, Figure 8) (Jones Jr. 2015). Hatchery summer-run steelhead also 44 occur in the Willamette River Basin but are an out-of-basin stock that is not included as part of 45 this DPS (NMFS 2011a). 46
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1 The DPS/ESU Boundaries Review Group considered new genetic information relating to the 2 relationship between the Clackamas River winter steelhead and steelhead native to the LCR and 3 UWR DPSs. The Review Group concluded that there was sufficient information available for 4 considering reassigning the Clackamas River winter steelhead population to the UWR River 5 Steelhead DPS. The most recent status review concluded that further review is necessary before 6 there can be any consideration of redefining the DPS; therefore, the most recent status review 7 evaluation was conducted based on existing DPS boundaries (Figure 8) (NWFSC 2015). 8 Table 23. UWR Steelhead DPS description and MPGs.1 DPS Description Listed under ESA as threatened in 1999; updated in 2014 (see Threatened Table 7) 1 major population group 4 historical populations Major Population Group Populations South Santiam River (C,G), North Santiam River (C,G), Willamette Molalla River, Calapooia River Artificial production Hatchery programs included in n/a DPS (0) Hatchery programs not included Upper Willamette summer (in South Santiam River, North in DPS (1) Santiam, McKenzie, MF Willamette) 9 1 The designations “(C)” and “(G)” identify core and genetic legacy populations, respectively 10 (Jones Jr. 2015; McElhany et al. 2003; NWFSC 2015). 11
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1 2 Figure 8. UWR Steelhead DPS spawning and rearing areas, illustrating populations and MPGs 3 (From NWFSC 2015). 4 5 Before the construction of a fish ladder at Willamette Falls in the early 1900s, flow conditions 6 allowed steelhead to ascend Willamette Falls only during the late winter and spring. Presently, 7 the majority of the UWR winter steelhead run return to freshwater from January through April, 8 pass Willamette Falls from mid-February to mid-May, and spawn from March through June 9 (with peak spawning in late April and early May). Table 24 summarizes the general life history 10 traits for UWR steelhead. This species may spawn more than once; however, the frequency of 11 repeat spawning is relatively low. The repeat spawners are typically females that spend more 12 than one year post spawning in the ocean and spawn again the following spring (ODFW 2010b). 13 14 UWR steelhead currently exhibit a stream-type life history with individuals exhibiting yearling 15 life history strategy. Juvenile steelhead rear in headwater tributaries and upper portions of the 16 subbasins from one to four years (average of two years), then as smoltification occurs in April 17 through May, migration downstream through the mainstem Willamette and Columbia River 18 estuaries and into the ocean occurs. The downstream migration speed depends on factors 19 including river flow, temperature, turbidity, and others, but with the quickest migration occurring 20 with high river flows. UWR steelhead can forage in the ocean for one to two years (average of 21 two years) and during this time period, are thought to migrate north to Canada and Alaska and 22 into the North Pacific including the Alaska Gyre (Table 24) (Myers et al. 2006; ODFW 2010b).
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1 Table 24. A summary of the general life history characteristics and timing of UWR steelhead. 2 Data are from (From ODFW 2010b). Life-History Trait Characteristic
Willamette River entry timing February-March
Spawn timing March-June
Spawning habitat type Headwater streams
Emergence timing 8-9 weeks after spawning, June-August
Rearing habitat Headwater streams
Duration in freshwater 1-4 years (mostly 2), smolt in April-May
Estuarine use Briefly in the spring, peak use in May
North to Canada and Alaska, and into the Ocean migration North Pacific
Age at return 3-6 years, primarily 4 years
3 4 There is no directed fishery for winter steelhead in the UWR, and they are the only life-history 5 displayed by natural steelhead in this area. Due to differences in return timing between native 6 winter steelhead, introduced hatchery-origin summer steelhead, and hatchery-origin spring 7 Chinook salmon, the encounter rates for winter steelhead in the recreational fishery are thought 8 to be low. Sport fishery mortality rates were estimated at 0 to 3 % (Ford 2011). There is 9 additional incidental mortality in the commercial net fisheries for Chinook salmon and steelhead 10 in the LCR. Tribal fisheries occur above Bonneville Dam and do not impact UWR steelhead 11 (NWFSC 2015). 12 13 Status of the species is determined based on the abundance, productivity, spatial structure, and 14 diversity of its constituent natural populations. Best available information indicates that the 15 species, in this case the UWR Steelhead DPS, is at moderate risk and remains at threatened 16 status. The most recent status update (NWFSC 2015) determined that there has been no change 17 in the biological risk category since the last reviews of these populations. Although new data was 18 available and analyzed for each of the populations in the most recent review, there is still 19 uncertainty in the underlying causes of the long-term declines in spawner abundances that these 20 populations have experienced. Although the recent magnitude of these declines is relatively 21 moderate, continued declines would be a cause for concern (NWFSC 2015). 22 Estimation of steelhead abundance for this DPS were based on redd counts in the North and 23 South Santiam Basins. Adult counts were also available from observations at Willamette Falls, 24 Bennett Dam, the Minto Fish Facility (North Santiam River), and Foster Dam (South Santiam 25 River). In addition, results from tracking studies of radio-tagged winter steelhead were expanded 26 to estimate spawner abundance in specific individual populations. Steelhead arriving at 27 Willamette Falls were also sampled for genetic analysis to determine the relative proportions of
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1 native (late winter steelhead) and out-of-DPS (early winter, or summer/winter hybrid steelhead) 2 genotypes represented in the run (NWFSC 2015). 3 4 Winter steelhead hatchery programs were terminated in the late 1990s. Currently, the only 5 steelhead programs in the UWR release Skamania Hatchery-origin summer steelhead, though 6 this program is not part of the DPS. Annual total releases have been relatively stable at around 7 600,000 from 2009 to 2014, although the distribution has changed, with fewer fish being 8 released in the North Santiam River and corresponding increases in the South Santiam and 9 Middle Fork Willamette Rivers to maintain the release level of about 600,000 fish. However, 10 there has been some concern regarding the effect of introduced summer steelhead on native late- 11 winter steelhead. There is some overlap in the spawn timing for summer- and late-winter 12 steelhead, and genetic analysis has identified approximately 10 % of the juvenile steelhead 13 hybrids of summer and winter steelhead at Willamette Falls and in the Santiam Basin (Johnson et 14 al. 2013; NWFSC 2015). 15 16 The presence of hatchery-reared and feral hatchery-origin fish in the UWR Basin may also affect 17 the growth and survival of juvenile late-winter steelhead. In the North and South Santiam 18 Rivers, juveniles are largely confined below much of their historical spawning and rearing 19 habitat. Releases of large numbers of hatchery-origin summer steelhead may temporarily exceed 20 rearing capacities and displace winter juvenile steelhead. 21 22 In the Molalla River, population abundance estimates based on spawner (redd) surveys are only 23 available for the Molalla River and associated tributaries (Pudding River, Abiqua Creek) through 24 2006. Recent estimates, based on the proportional migration of winter steelhead tagged at 25 Willamette Falls (Jepson et al. 2014; Jepson et al. 2013) indicate that a significantly smaller 26 portion of the steelhead arriving at Willamette Falls are destined for the Molalla River. Estimated 27 declines in the Molalla River are based on correlations with observed trends in the North and 28 South Santiam Rivers. Given that the Molalla River has no major migrational barriers, limiting 29 factors in the Molalla River are likely related to habitat degradation; abundance is likely 30 relatively stable but at a depressed level (NWFSC 2015). 31 32 Currently, the best measure of steelhead abundance is the count of returning winter-run adults to 33 the Upper and Lower Bennett Dams for the North Santiam River population. Recent passage 34 improvements at the dams and an upgraded video counting system have contributed to a higher 35 level of certainty in adult estimates. The Bennett Dam counts may also approximate spawner 36 counts, given that post-dam prespawning mortality is thought to be low for winter steelhead. 37 Unfortunately, steelhead were not counted at Bennett Dam from 2006 to 2010, due to budget 38 constraints. The most recent average count for unmarked (presumed native) winter steelhead 39 (2010-1014) is only 1195 ± 194. Longer term trends 1999-2014 are negative, -5 ±3 % (NWFSC 40 2015). 41 42 Survey data (index redd counts) is available for a number of tributaries to the South Santiam 43 River; in addition, live counts are available for winter steelhead transported above Foster Dam. 44 Temporal differences in the index reaches surveyed and the conditions under which surveys were 45 undertaken make the standardization of data among tributaries very difficult. For the Foster 46 Dam time series, the most recent 5-year average (2010-2014) has been 304 fish, with a negative
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1 trend in the abundance over those years (recognizing that the 2010 return reflected good ocean 2 conditions). In addition to steelhead spawning in the mainstem South Santiam River, annual 3 spawning surveys of tributaries below Foster Dam (Thomas, Crabtree, and Wiley Creeks) 4 indicate the consistent presence of low numbers of spawning steelhead (NWFSC 2015). 5 6 The Calapooia River DPS has a nearly consistent and complete time series for index reach redd 7 counts dating back to 1985. While there is not an expansion available from index reach to 8 population spawner abundance, the trend in redds per mile is generally negative, although this is 9 due in part to the time series beginning with the time of good ocean conditions. Abundance is 10 thought to be rather low, with population estimates based on radio tagged winter steelhead for 11 2012, 2013, and 2014 are 127, 204, and 126 respectively (Jepson et al. 2014; Jepson et al. 2015; 12 Jepson et al. 2013). These numbers would suggest that abundances have been fairly stable, albeit 13 at a depressed level (NWFSC 2015). 14 15 The available online data on natural-origin spawner abundances for the four populations in the 16 MPG are summarized below in Table 25. 17 18 Table 25. UWR Steelhead DPS natural-origin spawner abundance estimates for the four 19 populations in the MPG from 1997-2008 (no data available after 2008) (ODFW Salmon 20 & Steelhead Recovery Tracker1)*. Molalla North Santiam South Santiam Calapooia Year River River River River
1997 525 1,919 979 253
1998 1,256 1,970 1,043 358
1999 1,079 2,211 1,748 264
2000 1,898 2,437 1,608 225
2001 1,654 3,375 3,268 446
2002 2,476 3,227 2,282 351
2003 1,707 4,013 2,033 458
2004 1,987 3,863 3,546 684
2005 1,388 1,650 1,519 140
2006 1,433 2,965 1,805 257
2007 1,341 2,863 1,535 245
2008 1,273 2,789 1,534 236
21 1 Data available at: http://odfwrecoverytracker.org/explorer/ 22 *Date Accessed: April 29, 2016 23
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1 Since the 2005 status review, UWR steelhead initially increased in abundance but subsequently 2 declined and current abundance is at the levels observed in the mid-1990s when the DPS was 3 first listed. The DPS appears to be at lower risk than the UWR Chinook Salmon ESU, but 4 continues to demonstrate the overall low abundance pattern that was of concern during the 2005 5 status review (Table 26). The elimination of winter hatchery release in the basin reduces 6 hatchery threats, but non-native summer steelhead hatchery releases are still a concern for 7 species diversity. In 2011 and 2015, a 5-year review for the UWR steelhead concluded that the 8 species should maintain its threatened listing classification (Ford 2011; NWFSC 2015). 9 10 Table 26. Scores for the key elements (A/P, diversity, and spatial structure) used to determine 11 current overall viability risk for UWR steelhead populations (NMFS 2011a).1 Spatial Overall Extinction Population (Watershed) A/P Diversity Structure Risk Molalla River VL M M L North Santiam River VL M H L South Santiam River VL M M L Calapooia River M M VH M 1 All populations are in the Western Cascade Range MPG. Risk ratings range from very low (VL), low (L), moderate (M), high (H), to very high (VH) (NWFSC 2015). 12 13 Recovery strategies outlined in the Upper Willamette River Conservation and Recovery Plan for 14 Chinook Salmon and Steelhead (recovery plan) (ODFW 2010b) are targeted on achieving viable 15 criteria identified by the WLC-TRT (McElhany et al. 2003), which are used as the foundation for 16 biological delisting criteria. Though the viability criteria relate to the biological delisting 17 criteria, they are not identical (ODFW 2010b). The most recent status review (NWFSC 2015) 18 determined that none of the populations are meeting their recovery goal (Table 27). 19 Table 27. Summary of VSP scores and recovery goals for UWR Steelhead populations (NWFSC 20 2015). Total VSP MPG Population Recovery Goal Score
Molalla River 3 4
North Santiam River 3 4 Willamette South Santiam River 3 4
Calapooia River 2 2
21 Note: Summaries taken directly from Figure 98 in NWFSC (2015). All are on a 4 point scale, with 4 being the 22 lowest risk and 0 being the highest risk. VSP scores represent a combined assessment of population abundance and 23 productivity, spatial structure, and diversity (McElhany et al. 2006). A VSP score of 3.0 represents a population with 24 a 5 % risk of extinction within a 100 year period. 25
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1 Snake River Sockeye Salmon ESU
2 While there are very few sockeye salmon currently following an anadromous life cycle in the 3 Snake River, the small remnant run of the historical population migrates 900 miles downstream 4 from the Sawtooth Valley through the Salmon, Snake, and Columbia Rivers to the ocean. After 5 one to three years in the ocean, they return to the Sawtooth Valley as adults, passing once again 6 through these mainstem rivers and through eight major federal dams, four on the Columbia River 7 and four on the lower Snake River. Anadromous sockeye salmon returning to Redfish Lake in 8 Idaho’s Sawtooth Valley travel a greater distance, and to a higher elevation (6,500 ft.) than any 9 other sockeye salmon population. They are currently the southernmost population of sockeye 10 salmon in the world (NMFS 2015b). 11 12 The ESU includes naturally spawned anadromous and residual sockeye salmon originating from 13 the Snake River Basin in Idaho, as well as artificially propagated sockeye salmon from the 14 Redfish Lake captive propagation program (Jones Jr. 2015). At this stage of the recovery efforts, 15 there is only one extant population, and the ESU remains endangered with a high risk for spatial 16 structure, diversity, abundance, and productivity (NWFSC 2015). At present, anadromous 17 returns are dominated by production from the captive spawning component. The ongoing 18 reintroduction program is still in the phase of building sufficient returns to allow for large scale 19 reintroduction into Redfish Lake, the initial target for restoring natural program (NMFS 2015b). 20 21 Factors that limit the ESU have been, and continue to be impaired mainstem and tributary 22 passage, historical commercial fisheries, chemical treatment of Sawtooth Valley lakes in the 23 1950s and 1960s, poor ocean conditions, Snake and Columbia River hydropower system, and 24 reduced tributary stream flows and high temperatures. The decline in abundance itself has 25 become a major limiting factor, making the remaining population vulnerable to catastrophic loss 26 and posing significant risks to genetic diversity (NMFS 2015b; NWFSC 2015). However, some 27 limiting factors have improved since the listing. Fisheries are now better regulated through ESA 28 constraints and management agreements, significantly reducing harvest-related mortality. 29 Potential habitat-related threats to the fish, especially in the Sawtooth Valley, pose limited 30 concern since most passage barriers have been removed and much of the natal lake area and 31 headwaters remain protected. Hatchery-related concerns have also been reduced through 32 improved management actions (NMFS 2015b). 33 34 Columbia River Chum Salmon ESU
35 On March 25, 1999, NMFS listed the Columbia River (CR) Chum Salmon ESU as a threatened 36 species (64 FR 14508). The threatened status was reaffirmed on April 14, 2014 (Table 7). 37 Critical habitat was designated on September 2, 2005 (70 FR 52746). 38 39 Inside the geographic range of the ESU, four hatchery chum salmon programs are currently 40 operational. Table 28 lists these hatchery programs, with three included in the ESU and one 41 excluded from the ESU. 42
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1 Table 28. CR Chum Salmon ESU description and MPGs. The designations “(C)” and “(G)” 2 identify Core and Genetic Legacy populations, respectively (McElhany et al. 2003; 3 Myers et al. 2006; NMFS 2013c). ESU Description Threatened Listed under ESA in 1999; updated in 2014 (see Table 7) 3 major population 17 historical populations groups Major Population Populations Group Coast Youngs Bay (C), Grays/Chinook (C,G), Big Creek (C), Elochoman/Skamakowa (C), Clatskanie, Mill/Abernathy/Germany Creeks, Scappoose Cascade Cowlitz-fall (C), Cowlitz-summer (C), Kalama, Lewis (C), Salmon Creek, Clackamas (C), Sandy, Washougal Gorge Lower Gorge (C,G), Upper Gorge1 Artificial production Hatchery programs Chinook River/Sea Resources Hatchery, Grays River, Washougal included in ESU (3) Hatchery/Duncan Creek Hatchery programs not Big Creek Hatchery included in ESU (1) 4 1Includes White Salmon population. 5 6 The ESU includes all naturally spawning populations of chum salmon in the Columbia River and 7 its tributaries in Washington and Oregon, along with the hatchery chum salmon described in 8 Table 28. This ESU is comprised of three MPGs that has 17 populations (Table 29). Chum 9 salmon are primarily limited to the tributaries downstream of Bonneville Dam and the majority 10 of the fish spawn in Washington tributaries of the Columbia River (Figure 9). 11 12 Table 29. Current status for CR chum salmon populations and recommended status under the 13 recovery scenario (NMFS 2013c). Status Assessment Recovery Scenario Major Baseline Target Populatio Population (State) Persistence Contributio Persistence Abundanc n Group Probability n Probability e Target3 1 2 Youngs Bay (OR) VL Stabilizing VL <500 Grays/Chinook (WA) M Primary VH 1,600 Big Creek (OR) VL Stabilizing VL <500 Elochoman/Skamakow VL Primary H 1,300 Coast a (WA) Clatskanie (OR) VL Primary H 1.000 Mill/Abernathy/Germa VL Primary H 1,300 ny (WA) Scappoose (OR) VL Primary H 1,000 Cascade Cowlitz – fall (WA) VL Contributing M 900
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Cowlitz – summer VL Contributing M 900 (WA) Kalama (WA) VL Contributing M 900 Lewis (WA) VL Primary H 1,300 Salmon Creek (WA) VL Stabilizing VL -- Clackamas (OR) VL Contributing M 500 Sandy (OR) VL Primary H 1,000 Washougal (WA) VL Primary H+ 1,300 Lower Gorge H Primary VH 2,000 Gorge (WA/OR) Upper Gorge (WA/OR) VL Contributing M 900 1 1 VL=very low, L=low, M=moderate, H=high, VH = very high. These are adopted in the recovery plan. 2 2 Primary, contributing, and stabilizing designations reflect the relative contribution of a population to recovery 3 goals and delisting criteria. Primary populations are targeted for restoration to a high or very high persistence 4 probability. Contributing populations are targeted for medium or medium-plus viability. Stabilizing populations are 5 those that will be maintained at current levels (generally low to very low viability), which is likely to require 6 substantive recovery actions to avoid further degradation. 7 3 Abundance objectives account for related goals for productivity. 8
9 10 Figure 9. Map of the CR Chum Salmon ESU’s spawning and rearing areas, illustrating 11 populations and major population groups (From NWFSC 2015). 12
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1 Columbia River chum salmon are classified as fall-run fish, entering fresh water from mid- 2 October through November and spawning from early November to late December in the lower 3 main stems of the tributaries and side channels. There is evidence that a summer-run chum 4 salmon population returned historically to the Cowlitz River, and fish displaying this life history 5 are occasionally observed there. The recovery scenario currently includes this as an identified 6 population in the Cascade MPG (Table 29). Historically, chum salmon had the widest 7 distribution of all Pacific salmon species, comprising up to 50 % of annual biomass of the seven 8 species, and may have spawned as far up the Columbia River drainage as the Walla Walla River 9 (Nehlsen et al. 1991). Chum salmon fry emerge from March through May (LCFRB 2010), 10 typically at night (ODFW 2010a), and are believed to migrate promptly downstream to the 11 estuary for rearing. Chum salmon fry are capable of adapting to seawater soon after emergence 12 from gravel (LCFRB 2010). Their small size at emigration is thought to make chum salmon 13 susceptible to predation mortality during this life stage (LCFRB 2010). 14 15 Given the minimal time juvenile chum salmon spend in their natural streams, the period of 16 estuarine residency appears to be a critical phase in their life history and may play a major role in 17 determining the size of returning adults (NMFS 2013d). Chum and ocean-type Chinook salmon 18 usually spend more time in estuaries than do other anadromous salmonids—weeks or months, 19 rather than days or weeks (NMFS 2013d). Shallow, protected habitats, such as salt marshes, 20 tidal creeks, and intertidal flats serve as significant rearing areas for juvenile chum salmon 21 during estuarine residency (LCFRB 2010). 22 23 Juvenile chum salmon rear in the Columbia River estuary from February through June before 24 beginning long-distance ocean migrations (LCFRB 2010). Chum salmon remain in the North 25 Pacific and Bering Sea for 2 to 6 years, with most adults returning to the Columbia River as 4- 26 year-olds (ODFW 2010). All chum salmon die after spawning once. 27 28 Status of the species is determined based on the abundance, productivity, spatial structure, and 29 diversity of its constituent natural populations. Best available information indicates that the 30 species, in this case the Columbia River Chum Salmon ESU, is at high risk and remains at 31 threatened status. Each Columbia River chum salmon population baseline and target persistence 32 probability is summarized in Table 29 along with target abundance for each population that 33 would be consistent with delisting criteria. Persistence probability is measured over a 100 year 34 time period and ranges from very low (probability of less than 40 %) to very high (probability of 35 greather than 99 %). 36 37 Over the last century, Columbia River chum salmon returns have collapsed from hundreds of 38 thousands to just a few thousand per year (NMFS 2013c). Of the 17 populations that historically 39 made up this ESU, 15 of them (six in Oregon and nine in Washington) are so depleted that either 40 their baseline probability of persistence is very low, extirpated, or nearly so (Ford 2011; NMFS 41 2013c; NWFSC 2015). The Grays River and Lower Gorge populations showed a sharp increase 42 in 2002 for several years, but have since declined back to relatively low abundance levels in the 43 range of variation observed over the last several decades. The abundance targets in Table 29 for 44 Oregon populations are minimum abundance thresholds (MATs) because Oregon lacked 45 sufficient data to quantify abundance targets. MATs are a relationship between abundance,
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1 productivity, and extinction risk based on specific assumptions about productivity; more 2 information about MATs can be found in McElhany et al. (2006). 3 4 Currently almost all natural production occurs in just two populations: the Grays/Chinook and 5 the Lower Gorge. The most recent total abundance information for Columbia River chum 6 salmon in Washington is provided in Table 30, including chum salmon counted passing 7 Bonneville Dam. For the other Washington populations not listed in Table 30 and all Oregon 8 populations there are only occasional reports of only a few chum salmon (NWFSC 2015). 9 10 Table 30. Peak spawning ground counts for fall chum salmon in index reaches in the LCR, and 11 Bonneville Dam counts 2001-2014 (from WDFW SCORE1)*. Grays River Main stem Hamilton Return Crazy West Grays Hardy Columbia Bonneville Main Creek Year Johnson Fork River Creek (area Count stem Total Creek Grays Total near I- 205) 2001 1,234 811 2,201 4,246 617 835 na 29 2002 2,792 2,952 4,749 10,493 1,794 343 3,145 98 2003 4,876 5,026 5,657 15,559 821 413 2,932 411 2004 1,051 5,344 6,757 13,152 717 52 2,324 42 2005 1,337 1,292 1,166 3,795 257 71 902 139 2006 3,672 1,444 1,129 6,245 478 109 869 165 2007 837 1,176 1,803 3,816 180 12 576 142 2008 992 684 725 2,401 221 3 644 75 2009 968 724 1,084 2,776 216 46 1,118 109 2010 843 3,536 1,704 6,083 594 175 2,148 124 2011 2,133 2,317 5,603 10,053 867 157 4,801 50 2012 3,363 1,706 2,713 7,782 489 75 2,498 65 2013 1,786 1,292 1,754 4,832 647 56 1,364 167 2014 1,380 1,801 1,078 4,259 922 108 1,387 122 12 1 online at https://fortress.wa.gov/dfw/score/score/species/chum.jsp?species=Chum 13 *Date Accessed: April 12, 2016. 14 15 The methods and results for categorizing spatial distribution from the LCFRB Plan (2010) for 16 Columbia River chum salmon populations are reported in the recovery plan, and updated scores 17 are summarized here in Table 32. Under baseline conditions, constrained spatial structure at the 18 ESU level (related to conversion, degradation, and inundation of habitat) contributes to very low 19 abundance and low genetic diversity in most populations, increasing risk to the ESU from local 20 disturbances. Diversity has been greatly reduced at the ESU level because of presumed 21 extirpations and low abundance in the remaining populations (LCRFRB 2010). Population 22 status is characterized relative to persistence (which combines the abundance and productivity 23 criteria), spatial structure, diversity, and also habitat characteristics. This overview for chum 24 salmon populations suggests that risks related to diversity are higher than those for spatial 25 structure (Table 32). The scores generally average between 2 and 3 for spatial structure, and 26 between 1 and 2 for diversity. McElhany et al. (2006) reported the methods used to score the
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1 spatial structure and diversity attributes for chum salmon populations in Oregon required more 2 data. 3 4 Table 31. Columbia River Chum Salmon ESU populations and scores for the key elements (A/P, 5 diversity, and spatial structure) used to determine current overall net persistence 6 probability of the populations (NMFS 2013a).1 MPG Overall Spawning Population Spatial Ecological Run A/P Diversity Persistence (Watershed) Structure Subregion Timing Probability Youngs Bay (OR) * * * VL Grays/Chinook rivers VH M H M (WA) Big Creek (OR) * * * VL Coast Elochoman/Skamokawa Fall VL H L VL Range rivers (WA) Clatskanie River (OR) * * * VL Mill, Abernathy and VL H L VL Germany creeks (WA) Scappoose Creek (OR) * * * VL Summer Cowlitz River (WA) VL L L VL Cowlitz River (WA) VL H L VL Kalama River (WA) VL H L VL Cascade Lewis River (WA) VL H L VL Range Fall Salmon Creek (WA) VL L L VL Clackamas River (OR) * * * VL Sandy River (OR) * * * VL Washougal River (WA) VL H L VL Lower Gorge (WA & VH H VH H Columbia OR) Fall Gorge Upper Gorge (WA & VL L L VL OR) 1 Ratings range from low (VL), low (L), moderate (M), high (H), to very high (VH) (NMFS 2013c; NWFSC 2015). * No data are available to make a quantitative assessment.
7 The most recent status review (NWFSC 2015) concluded that a total of 3 of 17 populations are at 8 or near their recovery viability goals, although under the recovery plan scenario these 9 populations have very low recovery goals of 0 (Table 32). The remaining populations generally 10 require a higher level of viability and most require substantial improvements to reach their 11 viability goals. Even with the improvements observed during the last five years, the majority of 12 individual populations in this ESU remain at a high or very high risk category and considereable 13 progress remains to be made to achieve the recovery goals (NWFSC 2015). 14
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1 Table 32. Summary of VSP scores and recovery goals for CR chum salmon populations 2 (NWFSC 2015). Total VSP Recovery MPG State Population Score Goal OR Youngs Bay 0 0 WA Grays/Chinook 2 4 OR Big Creek 0 0 OR Clatskamie 0 3 Coast Elochoman/Skamok WA 0.5 3 awa WA Mill/Abern/Ger 0.5 3 OR Scappoose 0 3 WA Cowlitz (fall) 0.5 2 WA Cowlitz (summer) 0.5 2 WA Kalama 0.5 2 WA Lewis 0.5 3 Cascade WA Salmon Creek 0.5 0 OR Clackamas 0 2 OR Sandy 0 3 WA Washougal 0.5 3.5 WA Lower Gorge 3 4 Gorge WA Upper Gorge 0 2 3 Notes: Summaries taken directly from Figure 82 in NWFSC (2015). All are on a 4 point scale, with 4 being the 4 lowest risk and 0 being the highest risk. Viable Salmon Population scores represent a combined assessment of 5 population abundance and productivity, spatial structure and diversity (McElhany et al. 2006). A VSP score of 3.0 6 represents a population with a 5% risk of extinction within a 100 year period. 7 8 Lower Columbia River Coho Salmon ESU
9 On June 28, 2005, NMFS listed the listed the LCR Coho Salmon ESU as a threatened species 10 (70 FR 37160). The threatened status was reaffirmed on April 14, 2014. Critical habitat was 11 originally proposed for designation on January 14, 2013, and was finalized on January 24, 2016 12 (81 FR 9252) (Table 7). 13 14 The ESU includes all naturally spawned populations of coho salmon in the Columbia River and 15 its tributaries from the mouth of the Columbia River up to and including the White Salmon and 16 Hood rivers (Figure 10). Coho salmon in the Willamette River spawning above Willamette Falls 17 are not considered part of the LCR Coho Salmon ESU (70 FR 37160). LCR coho salmon are 18 divided into 3 major population groups, with the majority of the populations and associated 19 hatchery programs located below Bonneville Dam ( 20 Table 33). NMFS has determined that any effects from the Proposed Action would be limited to 21 Gorge MPG, primarily the Upper Gorge/White Salmon, and the Upper Gorge/Hood River 22 populations due to the proximity to the LWS NFH. Generally, these populations have low 23 baseline persistence probabilities (Table 34).
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1 2 Table 33. LCR Coho Salmon ESU description and MPGs (Jones Jr. 2011; NMFS 2013c).8 ESU Description Threatened Listed under ESA in 2005; updated in 2014 (see Table 7) 3 major population groups 24 historical populations Major Population Group Population Coast Youngs Bay, Grays/Chinook, Big Creek, Elochoman/Skamokawa, Clatskanie, Mill/Abernathy/Germany Creeks, Scappoose Cascade Lower Cowlitz, Upper Cowlitz, Cispus, Tilton, South Fork Toutle, North Fork Toutle, Coweeman, Kalama, North Fork Lewis, East Fork Lewis, Salmon Creek, Clackamas, Sandy, Washougal Gorge Lower Gorge, Upper Gorge/White Salmon, Upper Gorge/Hood Artificial production Hatchery programs Grays River (Type-S), Sea Resources (Type-S), Peterson Coho Salmon included in ESU (23) Project (Type-S), Big Creek Hatchery (ODFW stock #13), Astoria High School (STEP) Coho Salmon Program, Warrenton High School (STEP) Coho Salmon Program, Cathlamet High School FFA Type-N Coho Salmon Program, Cowlitz Type-N Coho Salmon Program, Cowlitz Game and Anglers Coho Salmon Program, Friends of the Cowlitz Coho Salmon Program, North Fork Toutle River Hatchery (type-S), Kalama River Type -N Coho Salmon Program, Kalama River Type-S Coho Salmon Program, Lewis River Type-N Coho Salmon Program, Lewis River Type-S Coho Salmon Program, Fish First Wild Coho Salmon Program, Fish First Type-N Coho Salmon Program, Syverson Project Type-N Coho Salmon Program, Washougal River Type-N Coho Salmon Program, Eagle Creek NFH, Sandy Hatchery (ODFW stock #11), Bonneville/Cascade/Oxbow Complex (ODFW stock #14) Hatchery programs not CCF Coho Salmon Program (Klaskanine River origin) included in ESU (1) *The Elochoman Type-S and Type-N coho salmon hatchery programs have been discontinued and NMFS has recommended removed them from the ESU (Jones Jr. 2015) 3 4 Table 34. Current status for LCR coho salmon Gorge MPG populations and recommended status 5 under the recovery scenario (NMFS 2013c). Status Assessment Recovery Scenario Major Baseline Target Populatio Population (State) Contribution Abundance Persistence Persistence n Group 2 Target3 Probability1 Probability Lower Gorge (WA/OR) - VL Primary H 1,900 Late Upper Gorge/White Salmon Gorge VL Primary H 1,900 (WA) - Late Upper Gorge/Hood (OR) - VL Primary H* 5,162 Early
8 Because NMFS had not yet listed this ESU in 2003 when the WLC TRT designated core and genetic legacy populations for other ESUs, there are no such designations for LCR coho salmon.
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11 VL = very low, L = low, M = moderate, H = high, VH = very high. These are adopted in the recovery plan 22 Primary, contributing, and stabilizing designations reflect the relative contribution of a population to recovery goals and 3 delisting criteria. Primary populations are targeted for restoration to a high or very high persistence probability. 4 Contributing populations are targeted for medium or medium-plus viability. Stabilizing populations are those that will 5 be maintained at current levels (generally low to very low viability), which is likely to require substantive recovery 6 actions to avoid further degradation. 73 Abundance objectives account for related goals for productivity. 8* Oregon’s analysis indicates a low probability of meeting the delisting objective of high persistence probability for this 9 population. 10 11
12 13 Figure 10. Map of the LCR Coho Salmon ESU’s spawning and rearing areas, illustrating 14 populations and MPGs (NWFSC 2015). 15 16 Although run-time variation is considered inherent to overall coho salmon life history, LCR coho 17 salmon typically display one of two major life history types, either early- or late-returning 18 freshwater entry. Freshwater entry timing for this ESU is also associated with ocean migration 19 patterns (Table 35) based on the recovery of CWT hatchery fish north or south of the Columbia 20 River (Myers et al. 2006). Early returning (Type-S) coho salmon generally migrate south of the 21 Columbia River once they reach the ocean, returning to fresh water in mid-August and to the 22 spawning tributaries in early September. Spawning peaks from mid-October to early November. 23 Late returning (Type-N) coho salmon have a northern distribution in the ocean, returning to the 24 LCR from late September through December and enter the tributaries from October through
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1 January. Most of the spawning for Type-N occurs from November through January, but some 2 spawning occurs in February and as late as March (NMFS 2013c). 3 4 Table 35. Life history and population characteristics of LCR coho salmon. Life History Features Characteristic Early-returning (Type-S) Late-returning (Type-N) Number of extant 10 23 population Life history type Stream Stream River entry timing August-September September-December Spawn timing October-November November-January Spawning habitat type Higher tributaries Lower tributaries Emergence timing January-April January-April Duration in freshwater Usually 12-15 months Usually 12-15 months Smaller tributaries, river edges, Smaller tributaries, river edges, Rearing habitat sloughs, off-channel ponds sloughs, off-channel ponds Estuarine use A few days to weeks A few days to weeks South of the Columbia River, as North of the Columbia River, as Ocean migration far south as northern California far north as British Columbia Age at return 2-3 years 2-3 years Recent natural spawners 6,000 Recent hatchery adults 5,000 – 90,000 12,000 – 180,000 5 6 Regardless of adult freshwater entry timing, coho salmon fry move to shallow, low-velocity 7 rearing areas after emergence, primarily along the stream edges and in side channels. All coho 8 salmon juveniles remain in freshwater rearing areas for a full year after emerging from the 9 gravel. Most juvenile coho salmon migrate seaward as one-year smolts from April to June. 10 Salmon with stream-type life histories, like coho salmon, typically do not linger for extended 11 periods in the Columbia River estuary, but the estuary is critical habitat used for foraging during 12 the physiological adjustment to the marine environment (NMFS 2013c). 13 14 Status of the species is determined based on the abundance, productivity, spatial structure, and 15 diversity of its constituent natural populations. Best available information indicates that the LCR 16 Coho Salmon ESU is at high risk and remains at threatened status. Each population’s baseline 17 and target persistence probabilities is summarized in Table 34, along with target abundance for 18 each population that would be consistent with delisting the species. Persistence probability is 19 measured over a 100-year time period and ranges from very low (probability of persistence over 20 100 years less than 40%) to very high (probability greater than 99%). 21 22 Table 36 presents escapement of LCR coho salmon in Oregon Gorge tributaries (2002- 2015). 23 Table 37 presents escapement of LCR coho salmon in Washington Gorge tributaries (2002 - 24 2015). It is unclear how comprehensive the surveys are or if the estimates are intended to be 25 expanded estimates for the population as a whole. On the Washington side, the estimates are 26 characterized as cumulative fish per mile index counts. 27
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Table 36. Natural-origin spawning escapement numbers and the proportion of natural spawners composed of hatchery-origin fish (pHOS) on the spawning grounds for LCR coho salmon populations in Oregon from 2002 through 2015 (http://www.odfwrecoverytracker.org/)*. Major Oregon Population Origin 2002 2003 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 Populations Group Natural 338 - - 263 226 126 223 468 920 216 96 151 362 30 Lower Gorge pHOS 17% - - 85% 70% 67% 46% 29% 7% 54% 56% 6% 51% 38% Gorge Upper Gorge/ Natural 147 41 126 1,262 373 170 69 65 223 232 169 561 42 4 Hood pHOS 60% - - 45% 48% 45% 29% 0% 85% 69% 78% 65% 76% 64% *Date accessed: April 13, 2016.
Table 37. Natural-origin spawning escapement numbers and the proportion of all natural spawners composed of hatchery-origin fish (pHOS1) on the spawning grounds for LCR coho salmon populations in Washington from 2002 through 2015 (https://fortress.wa.gov/dfw/score/score/species/coho.jsp?species=Coho)*. Major Washington Population Origin 2002 2003 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 Populations Group Natural - - - - 28 - - - 385 504 524 - 704 650 Lower Gorge ------35% 11% Gorge pHOS 0% 29% 13% 20% Upper Gorge/ Natural - - - - - 152 86 71 35 111 96 106 24 80 Hood pHOS ------23% 24% * Date accessed: April 13, 2016
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1 This information, although limited, indicates there are several hundred spawners in these 2 tributaries that collectively make up the population and that hatchery fractions are actually 3 relatively low. 4 5 In the 2015 status review (NWFSC 2015), NMFS concluded that the LCR Coho Salmon ESU is 6 still at very high risk. A total of 6 of the 23 populations in the ESU are at or near their recovery 7 viability goals (Figure 69 in NWFSC 2015), although under the recovery plan scenario these 8 populations had recovery goals only greater than 2.0 (moderate risk). The remaining populations 9 require a higher level of viability (NWFSC 2015) and therefore still require substantial 10 improvements. Best available information indicates that the LCR Coho Salmon ESU is at a very 11 high risk and remains at threatened status. 12 13 Range-wide Status of Critical Habitat
14 NMFS determines the range-wide status of critical habitat by examining the condition of its 15 PBFs that were identified when critical habitat was designated. These features are essential to the 16 conservation of the listed species because they support one or more of the species’ life stages. An 17 example of some PBFs are listed below. These are often similar among listed salmon and 18 steelhead; specific differences can be found in the critical habitat designation for each species 19 (Table 7). 20 21 (1) Freshwater spawning sites with water quantity and quality conditions and substrate 22 supporting spawning, incubation and larval development; 23 (2) Freshwater rearing sites with: (i) Water quantity and floodplain connectivity to form and 24 maintain physical habitat conditions and support juvenile growth and mobility; (ii) Water 25 quality and forage supporting juvenile development; and (iii) Natural cover such as shade, 26 submerged and overhanging large wood, log jams and beaver dams, aquatic vegetation, 27 large rocks and boulders, side channels, and undercut banks; 28 (3) Freshwater migration corridors free of obstruction and excessive predation with water 29 quantity and quality conditions and natural cover such as submerged and overhanging 30 large wood, aquatic vegetation, large rocks and boulders, side channels, and undercut 31 banks supporting juvenile and adult mobility and survival; 32 (4) Estuarine areas free of obstruction and excessive predation with: (i) Water quality, water 33 quantity, salinity conditions supporting juvenile and adult physiological transitions 34 between fresh- and saltwater; (ii) Natural cover such as submerged and overhanging large 35 wood, aquatic vegetation, large rocks and boulders, side channels; and (iii) Juvenile and 36 adult forage, including aquatic invertebrates and fishes, supporting growth and maturation; 37 (5) Near-shore marine areas free of obstruction and excessive predation with: (i) Water quality 38 and quantity conditions and forage, including aquatic invertebrates and fishes, supporting 39 growth and maturation; and (ii) Natural cover such as submerged and overhanging large 40 wood, aquatic vegetation, large rocks and boulders, and side channels; 41 (6) Offshore marine areas with water-quality conditions and forage, including aquatic 42 invertebrates and fishes, supporting growth and maturation. 43 44 The status of critical habitat is based primarily on a watershed-level analysis of conservation 45 value that focused on the presence of ESA-listed species and physical features that are essential 46 to the species’ conservation. NMFS organized information at the 5th field hydrologic unit code
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1 (HUC) watershed scale because it corresponds to the spatial distribution and site fidelity scales 2 of salmon and steelhead populations (McElhany et al. 2000). The analysis for the 2005 3 designations of salmon and steelhead species was completed by Critical Habitat Analytical 4 Review Teams (CHARTs) that focused on large geographical areas corresponding approximately 5 to recovery domains (NMFS 2005b). Each watershed was ranked using a conservation value 6 attributed to the quantity of stream habitat with physical and biological features (PBFs; also 7 known as primary and constituent elements ((PCEs)), the present condition of those PBFs, the 8 likelihood of achieving PBF potential (either naturally or through active restoration), support for 9 rare or important genetic or life history characteristics, support for abundant populations, and 10 support for spawning and rearing populations. In some cases, our understanding of these interim 11 conservation values has been further refined by the work of technical recovery teams and other 12 recovery planning efforts that have better explained the habitat attributes, ecological interactions, 13 and population characteristics important to each species. 14 15 The HUCs that have been identified as critical habitat for these species are largely ranked as 16 having high conservation value. Conservation value reflects several factors: (1) how important 17 the area is for various life history stages, (2) how necessary the area is to access other vital areas 18 of habitat, and (3) the relative importance of the populations the area supports relative to the 19 overall viability of the ESU or DPS. 20 21 No CHART reviews have been conducted for the two Snake River Chinook Salmon ESUs and 22 Snake River Sockeye Salmon ESU. The description of critical habitat for the other species are 23 described below. 24 25 Critical Habitat for Upper Columbia River Spring Chinook Salmon 26 The UCR Spring Chinook Salmon ESU’s range consists of 31 watersheds. The CHART assigned 27 5 watersheds a medium rating, and 26 received a high rating of conservation value to the ESU 28 (NMFS 2005b). The following are the major factors limiting the conservation value of UCR 29 spring Chinook salmon critical habitat: 30 • Forestry practices 31 • Fire activity and disturbance 32 • Livestock grazing 33 • Agriculture 34 • Channel modifications/diking 35 • Road building/maintenance 36 • Urbanization 37 • Sand and gravel mining 38 • Mineral mining 39 • Dams 40 • Irrigation 41 42 Critical Habitat for Upper Columbia River Steelhead 43 The UCR Steelhead DPS’s range includes 42 watersheds. The CHART assigned low, medium, 44 and high conservation value ratings to 3, 8, and 31 watersheds, respectively (NMFS 2005b). The 45 following are the major factors limiting the conservation value of critical habitat for UCR 46 steelhead:
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1 • Forestry practices 2 • Grazing 3 • Agriculture 4 • Channel modifications/diking 5 • Road building/maintenance 6 • Urbanization 7 • Sand and gravel mining 8 • Mineral mining 9 • Dams 10 • Irrigation impoundments and withdrawals 11 • River, estuary, and ocean traffic 12 • Wetland loss/removal 13 • Beaver removal 14 • Exotic/invasive species introductions 15 • Forage fish/species harvest
16 Critical Habitat for Snake River Steelhead DPS 17 The Snake River Steelhead DPS’s range includes 291 watersheds. The CHART assigned low, 18 medium, and high conservation value ratings to 14, 43, and 230 watersheds, respectively (NMFS 19 2005b). They also identified 4 watersheds that had no conservation value. The following are the 20 major factors limiting the conservation value of critical habitat for Snake River steelhead: 21 22 ● Agriculture 23 ● Channel modifications/diking 24 ● Dams, 25 ● Forestry 26 ● Fire activity and disturbance 27 ● Grazing 28 ● Irrigation impoundments and withdrawals, 29 ● Mineral mining 30 ● Recreational facilities and activities management 31 ● Exotic/ invasive species introductions 32 33 Critical Habitat for Mid-Columbia River Steelhead 34 The Mid-Columbia River Steelhead DPS’s range includes 111 watersheds. The CHART 35 assigned low, medium, and high conservation value ratings to 9, 24, and 78 watersheds, 36 respectively (NMFS 2005a). They also identified 1 watershed with an unknown conservation 37 value. The following are the major factors limiting the conservation value of critical habitat for 38 Mid-Columbia River steelhead: 39 40 ● Agriculture 41 ● Channel modifications/diking 42 ● Dams, 43 ● Forestry 44 ● Fire activity and disturbance 45 ● Grazing
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1 ● Irrigation impoundments and withdrawals, 2 ● Urbanization 3 ● Road building/maintenance 4 5 Climate Change
6 Climate change has negative implications for salmonid species and designated critical habitats in 7 the Pacific Northwest (Climate Impacts Group 2004; ISAB 2007; Scheuerell and Williams 2005; 8 Zabel et al. 2006). For a detailed discussion of climate change and how it affects salmonid 9 species in the Pacific Northwest, see below in Section 2.4.2. 10 11 Action Area
12 The “action area” means all areas to be affected directly or indirectly by the Proposed Action, in 13 which the effects of the action can be meaningfully detected measured, and evaluated (50 CFR 14 402.02). The action area resulting from this analysis includes the mainstem Columbia River from 15 the confluence with the Methow River through the estuary (i.e., mouth of the Columbia River), 16 which is a migration corridor for outmigrating juveniles. The action area also includes the 17 Methow, Chelan, Entiat, and Wenatchee Subbasins and their tributaries, which are areas where 18 fish are captured, reared, and released, as well as areas where they may be monitored, or to 19 which they might stray. 20 21 Environmental Baseline
22 Under the Environmental Baseline, NMFS describes what is affecting listed species and 23 designated critical habitat before including any effects resulting from the Proposed Action. The 24 ‘Environmental Baseline’ includes the past and present impacts of all Federal, state, or private 25 actions and other human activities in the action area and the anticipated impacts of all proposed 26 Federal projects in the action area that have already undergone formal or early section 7 27 consultation (50 CFR 402.02). 28 29 Habitat and Hydropower (NMFS 2012a)
30 A discussion of the baseline condition of habitat and hydropower throughout the Columbia River 31 Basin occurs in our Biological Opinion on the Mitchell Act Hatchery programs (NMFS 2017d). 32 Here we summarize some of the key impacts on salmon and steelhead habitat in the Action Area. 33 34 Anywhere hydropower exists, some general effects exist on salmon habitat, though those effects 35 vary depending on the hydropower system. In the Action Area, some of these general effects 36 from hydropower systems on biotic and abiotic factors include, but are not limited to: 37 • Juvenile and adult passage survival (safe passage in the migration corridor); 38 • Water quantity (i.e., flow) and seasonal timing (water quantity and velocity and safe 39 passage in the migration corridor; cover/shelter, food/prey, riparian vegetation, and space 40 associated with the connectivity of the estuarine floodplain); 41 • Temperature in the reaches below the large mainstem storage projects (water quality and 42 safe passage in the migration corridor)
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1 • Sediment transport and turbidity (water quality and safe passage in the migration 2 corridor) 3 • Total dissolved gas (water quality and safe passage in the migration corridor) 4 • Food webs, including both predators and prey (food/prey and safe passage in the 5 migration corridor) 6 7 While harmful land-use practices continue in some areas, many land management activities, 8 including forestry practices, now have fewer impacts on salmonid habitat due to raised 9 awareness and less invasive techniques. For example, timber harvest on public land has declined 10 drastically since the 1980s and current harvest techniques (e.g., the use of mechanical harvesters 11 and forwarders) and silvicultural prescriptions (i.e., thinning and cleaning) require little, if any, 12 road construction and produce much less sediment. In addition, the Federal Conservation 13 Reserve and Enhancement Program (CREP) began in the 1990’s nearly 80 percent of all 14 salmonid bearing streams in the area have been re-vegetated with native species and protected 15 from impacts. Under the CREP, highly erodible and other environmentally sensitive lands that 16 have produced crops are converted to a long-term resource-conserving vegetative cover. 17 Participants in the CREP are required to seed native or introduced perennial grasses or a 18 combination of shrubs and trees with native forbs and grasses. 19 20 Upper Columbia River 21 Many factors have contributed to habitat degradation in the Wenatchee, Entiat, Methow, and 22 Okanogan subbasins. The historical land use patterns are similar in each; beaver trapping, which 23 began in the early 1800s, had some effect on riparian conditions. Mining, which began in the 24 1860s, was probably the first major activity affecting riparian and stream conditions. This was 25 followed by a period of intense livestock grazing with pressure highest from the late 1800s to the 26 1930s. Grazing pressure then fell as allotment systems replaced the open range. Water diversion 27 began in the mid-1880s, affecting stream flow, which impacted adult salmonid migration and 28 juvenile rearing capacity. Timber harvest began in the 1920s and up until 1955 selective harvest 29 was the primary method. Since then partial cutting and clear-cutting have predominated, with the 30 most intense harvest occurring in the 1980s. Some of these factors have been partially addressed 31 through changes in land‐use practices and/or implementation of BMPs (e.g., fish screens at water 32 diversions; UCSRB 2014). In addition, some of the headwater areas are in relatively pristine 33 condition and serve as strongholds for the listed species. However, many of the factor effects 34 remain as a result of remnant infrastructure and previous land conversion/modifications (UCSRB 35 2007).
36 Limits to the viability of salmon and steelhead in the Wenatchee Basin include lack of habitat 37 diversity and quantity, excessive sediment load, obstructions, a lack of channel stability, low 38 flows, and high summer temperatures. Habitat diversity is affected by channel confinement, loss 39 of floodplain connectivity and off-channel habitat, reduced quantities of large wood, and a lack 40 of riparian vegetation. The mainstem and many of its tributaries also lack high-quality pools and 41 spawning areas.
42 Limits to the viability of salmon and steelhead in the Entiat Basin include reduced stream 43 channel configuration and complexity due to logging and flood control measures. These 44 historical and ongoing activities have led to a condition with low instream habitat diversity 45 including few pools, lack of large wood accumulations, and disconnected side channels,
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1 wetlands, and floodplains. The result is a reduction in resting and rearing areas for both adult and 2 juvenile salmon throughout the Entiat River. 3 4 Limits to the viability of salmon and steelhead in the Methow basin include housing and 5 agricultural development that have diminished the overall function of the stream channel and 6 floodplain. This has impaired stream complexity, wood and gravel recruitment, floodwater 7 retention, and water quality. Additionally, late summer and winter instream flow conditions often 8 reduce migration, spawning, and rearing habitat for native salmonids. This problem is partly 9 natural (a result of watershed-specific weather and geomorphic conditions) but is exacerbated by 10 irrigation withdrawals. 11 12 Limits to the viability of salmon and steelhead in the Okanogan Basin include barriers, poor 13 water quality, and low late-summer instream flows (mainstem and tributary). Summer water 14 temperatures often exceed lethal tolerance levels for salmonids along the Okanogan River 15 mainstem. These high temperatures are partially due to natural phenomena (low gradient, aspect, 16 high ambient air temperatures, and upstream lake effects), but are exacerbated by activities like 17 dam operations, irrigation, and land management. High water temperatures and low flows in 18 summer and fall may limit adult run timing as well as juvenile salmonid rearing in the mainstem 19 and in several tributaries. 20 21 Mainstem Columbia River 22 A discussion of the baseline condition of habitat and hydropower throughout the Columbia River 23 Basin occurs in our Biological Opinion on the Mitchell Act Hatchery programs (NMFS 2017d). 24 The baseline includes all federally-authorized hydropower projects, including projects with 25 licenses issued by the Federal Energy Regulatory Commission, the Federal Columbia River 26 Power System, and other developments which have undergone ESA §7 consultation. 27 Furthermore, the mainstem dams and the associated reservoirs present fish-passage hazards, 28 causing passage delays and varying rates of injury and mortality. The altered habitats in project 29 reservoirs reduce smolt migration rates and create more favorable habitat conditions for fish 30 predators (NMFS 2017d). Mainstem dams and reservoirs can also affect water quality by 31 influencing temperature due to storage, diversions, and irrigation return flows, reducing 32 turbidity, increasing total dissolved gas, and contributing toxic contaminants. All of these 33 impacts affect the migration of adults and juveniles in the mainstem Columbia River.
34 Climate Change
35 Climate change has negative implications for designated critical habitats in the Pacific Northwest 36 (ISAB 2007; Scheuerell and Williams 2005; Zabel et al. 2006). During the last century, average 37 regional air temperatures increased by 1.5°F, and increased up to 4°F in some areas. As the 38 climate changes, air temperatures in the Pacific Northwest are expected to increase <1°C in the 39 Columbia Basin by the 2020s and 2°C to 8°C by the 2080s (Mantua et al. 2010). Overall, about 40 one-third of the current cold-water fish habitat in the Pacific Northwest is likely to exceed key 41 water temperature thresholds by the end of this century (USGCRP 2009). While total 42 precipitation changes are uncertain, increasing air temperature will result in more precipitation 43 falling as rain rather than snow in watersheds across the basin (NMFS 2015d). 44
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1 These changes will not be spatially homogenous across the entire Pacific Northwest. There is 2 likely no trend in precipitation (neither strongly increase nor decrease), although summers may 3 become drier and winters wetter due to changes in the same amount of precipitation being 4 subjected to altered seasonal temperatures (Mote and Eric P. Salathé Jr. 2010; PCIC 2016). 5 Warmer winters will result in reduced snowpack throughout the Pacific Northwest, leading to 6 substantial reductions in stream volume and changes in the magnitude and timing of low and 7 high flow patterns (Beechie et al. 2013; Dalton et al. 2013). Many basins that currently have a 8 snowmelt-dominated hydrological regime (maximum flows during spring snow melt) will 9 become either transitional (high flows during both spring snowmelt and fall-winter) or rain- 10 dominated (high flows during fall-winter floods; (Beechie et al. 2013; Schnorbus et al. 2014). 11 Summer low flows are expected to be reduced between 10-70% in areas west of the Cascade 12 Mountains over the next century, while increased precipitation and snowpack is expected for the 13 Canadian Rockies. More precipitation falling as rain and larger future flood events are expected 14 to increase maximum flows by 10-50% across the region (Beechie et al. 2013). Climate change 15 is also predicted to increase the intensity of storms, reduce winter snow pack at low and middle 16 elevations, and increase snowpack at high elevations in northern areas. Middle and lower 17 elevation streams will have larger fall/winter flood events and lower late summer flows, while 18 higher elevations may have higher minimum flows. 19 20 21 The effects of climate change are likely to be already occurring, though the effects are difficult to 22 distinguish from effects of climate variability in the near term. Climate change is currently 23 causing, and is predicted to cause in the future, a variety of impacts on Pacific salmon as well as 24 their ecosystems (Crozier et al. 2008a; Martins et al. 2012; Mote et al. 2003; Wainwright and 25 Weitkamp 2013). While all habitats used by Pacific salmon will be affected, the impacts and 26 certainty of the change vary by habitat type. Some impacts (e.g., increasing temperature) affect 27 salmon at all life stages in all habitats, while others are habitat-specific (e.g., stream flow 28 variation in freshwater). Effects are likely to include:
29 • Warmer air temperatures will result in diminished snowpacks and a shift to more 30 winter/spring rain and runoff, rather than snow that is stored until the spring/summer melt 31 season. 32 • With a smaller snowpack, seasonal hydrology in Pacific Northwest watersheds will shift 33 to more frequent and severe early large storms, changing stream flow timing, which may 34 limit salmon survival (Mantua et al. 2009). 35 • Water temperatures are expected to rise, especially during the summer months when 36 lower streamflows co-occur with warmer air temperatures. 37 38 The complex life cycles of anadromous fishes including salmon rely on productive freshwater, 39 estuarine, and marine habitats for growth and survival, making them particularly vulnerable to 40 environmental variation (Morrison et al. 2016). Ultimately, the effect of climate change on 41 salmon and steelhead across the Pacific Northwest will be determined by the specific nature, 42 level, and rate of change and the synergy between interconnected terrestrial/freshwater, 43 estuarine, nearshore, and ocean environments. The primary effects of climate change on Pacific 44 Northwest salmon and steelhead are:
45 • Direct effects of increased water temperatures on fish physiology
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1 • Temperature-induced changes to stream flow patterns 2 • Alterations to freshwater, estuarine, and marine food webs
3 How climate change will affect each stock or population of salmon also varies widely depending 4 on the level or extent of change and the rate of change and the unique life history characteristics 5 of different natural populations (Crozier et al. 2008b). Dittmer (2013) suggests that juveniles 6 may outmigrate earlier if they are faced with less tributary water. Lower and warmer summer 7 flows may be challenging for returning adults. In addition, the warmer water temperatures in the 8 summer months may persist for longer periods and more frequently reach and exceed thermal 9 tolerance thresholds for salmon and steelhead (Mantua et al. 2009). Larger winter streamflows 10 may increase redd scouring for those adults that do reach spawning areas and successfully 11 spawn. Climate change may also have long-term effects that include accelerated embryo 12 development, premature emergence of fry, and increased competition among species (ISAB 13 2007). The uncertainty associated with these potential outcomes of climate change do provide 14 some justification for hatchery programs as reservoirs for some salmon stocks. For more detail 15 on climate change effects, see NMFS (2017d). 16 17 Hatcheries
18 A broader discussion of hatchery programs in the Action Area can be found in our opinions on: 19 • Mitchell Act-funded programs (NMFS 2017d). 20 • Methow/Winthrop spring Chinook salmon programs (NMFS 2016 ). 21 • WNFH/Wells Complex steelhead programs (NMFS 2017e). 22 • Entiat National Fish Hatchery summer Chinook salmon program (NMFS 2013b). 23 • Wenatchee spring Chinook salmon programs (NMFS 2013a). 24 • Wenatchee steelhead program (NMFS 2016a). 25 • Leavenworth spring Chinook salmon program (NMFS 2017b). 26 • Okanogan Tribal Resource Management Plan (NMFS 2017c). 27 28 Included in the Environmental Baseline are the ongoing effects of hatchery programs or facilities 29 which have undergone Federal review under the ESA, as well as the past effects of programs 30 which have not yet undergone such review, including those found in the proposed action. A more 31 comprehensive discussion of hatchery programs in the Columbia Basin can be found in our 32 opinion on Mitchell Act funded programs (NMFS 2017d). In summary, because most programs 33 are ongoing, the effects of each are reflected in the most recent status of the species (NWFSC 34 2015) and was summarized in Section 2.2.1 of this Opinion. In the past, hatcheries have been 35 used to compensate for factors that limit anadromous salmonid viability (e.g., harvest, human 36 development) by maintaining fishable returns of adult salmon and steelhead. A new role for 37 hatcheries emerged during the 1980s and 1990s as a tool to conserve the genetic resources of 38 depressed natural populations and to reduce short-term extinction risk (e.g., Snake River sockeye 39 salmon). Hatchery programs also can be used to help improve viability by supplementing natural 40 population abundance and expanding spatial distribution. However, the long-term benefits and 41 risks of hatchery supplementation remain untested (Christie et al. 2014). Therefore, fixing the 42 factors limiting viability is essential for long-term viability. 43
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1 Below, we summarize releases within the Action Area in the UCR Basin (Table 39) because the 2 releases from the proposed action is in the UCR Basin, and the returning adults from the 3 proposed action would return to the UCR Basin. 4 5 Table 38. Upper Columbia River hatchery programs with releases in the action area.
Biological Opinion Program Name Maximum Release Level Methow/Winthrop spring Methow Hatchery 224,000 Chinook salmon programs Winthrop National Fish Hatchery 400,000 (NMFS 2016 ) Wells Complex steelhead Wells Complex1 308,000 programs (NMFS 2017e) Winthrop National Fish Hatchery 200,000 Entiat National Fish Hatchery Entiat National Fish Hatchery 400,000 summer Chinook salmon program (NMFS 2013b) Wenatchee spring Chinook Chiwawa 205,000 salmon programs (NMFS 2013a) Nason Creek 223,7600 Wenatchee steelhead program Wenatchee 247,300 (NMFS 2016a) Leavenworth spring Chinook Leavenworth National Fish 1,200,000 salmon program (NMFS 2017b) Hatchery 6 1 The Wells Complex steelhead program produces an additional 100,000 smolts, which is transferred for release in 7 the Okanogan Basin (NMFS 2017c), which is outside of the action area. 8 9 Harvest
10 There are many fisheries action area that harvest or encounter ESA-listed fish. These fisheries 11 are roughly categorized into U.S. v. Oregon fisheries and fisheries above Priest Rapids Dam, and 12 take place from Buoy 10 up through the tributaries of the Columbia River. 13 14 U.S. v. Oregon Fisheries 15 The fisheries that take place as a result of the U.S. v. Oregon agreement occur between Buoy 10 16 and Priest Rapids Dam. A detailed discussion of the history of U.S. v. Oregon agreement can be 17 found in NMFS (2017a). Within this area, fisheries are divided into six zones below McNary 18 Dam, and fisheries also take place between McNary Dam and Priest Rapids Dam (i.e., Hanford 19 Reach). Commercial and recreational fisheries take place from Zones 1 through 5 (between Buoy 20 10 and Bonneville Dam), while tribal and recreational fisheries take place in Zone 6 (between 21 Bonneville Dam and McNary Dam) and in the Hanford Reach. The effects of these fisheries on 22 ESA-listed species are analyzed in NMFS (2008d). The expected incidental take and the actual 23 harvest that occurred from these fisheries are summarized in Table 39 and in Table 40, 24 respectively. 25 26 Table 39. Expected incidental take (as proportion of total run-size) of listed anadromous 27 salmonids for non-Indian and treaty Indian fisheries included in the 2008 U.S. v. Oregon 28 Agreement.
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Treaty Indian Non-Indian ESU or DPS Take Limits (%) (%) (%) Snake River fall-run Chinook Salmon 21.5 – 45.0 1 20.0 – 30.0 1.5 – 15.0 Snake River spring/summer-run Chinook 5.5 – 17.0 2 5.0 – 14.3 2 0.5 – 2.7 Salmon LCR Chinook Salmon Managed by components listed below Managed For Hatchery spring-run component 0 3 Escapement Goals 41% 41% Exploitation tule component (early-fall run) 0 exploitation Rate4 rate4 5,700 Managed For bright component (late-fall run) 0 escapement Escapement Goal goal UWR Chinook Salmon 15.0 0 15.0 Snake River Basin Steelhead Managed by components listed below A-Run Component 4.0 5 6 4.0 B-Run Component 15 – 22 7 13 – 20 7 2.0 7 LCR Steelhead Managed by components listed below winter component 2.0 6 2.0 summer component 4.0 5 6 4.0 UWR Steelhead 2.0 5 0 2.0 MCR Steelhead Managed by components listed below winter component 2.0 6 2.0 summer component 4.0 5 6 4.0 UCR spring-run Chinook Salmon 5.5 – 17.0 2 5.0 – 14.3 2 0.5 – 2.7 CR Chum Salmon 5.0 0 5.0 UCR Steelhead Managed by components listed below Natural-Origin Component 4.0 5 6 4.0 Hatchery- Origin Component 8 8 8 Snake River Sockeye Salmon 6.0 – 8.0 1 5.0 – 7.0 1.0 LCR Coho Salmon 10 – 30 9 0 10 – 30 9 Monitoring, Evaluation, and Research 0.1 - 0.5 10 1 1 Allowable take depends on run size. 2 2 Impacts in treaty fisheries on listed wild fish can be up to 0.8% higher than the river mouth runsize harvest rates 3 (indicated in table above) due to the potential for changes in the proportion wild between the river mouth and 4 Bonneville Dam. 5 3 NMFS (2012c) determined fisheries have ranged from exploitation rates of 2% to 28% over the last ten years, and 6 are expected to remain within this range through managing for hatchery escapement until other actions 7 concerning terminal fish passage in the LCR are addressed. 8 4 Total exploitation rate limits include ocean and mainstem Columbia River fisheries. NMFS (2012c) evaluated the 9 PFMC’s harvest matrix for total exploitation, including ocean and mainstem Columbia River fisheries, tiered on 10 abundance. 11 5 Applies to non-Indian fisheries only; 2% in winter/spring/summer seasons and 2% in fall season. 12 6 There is no specific harvest rate limit proposed for treaty fisheries on winter steelhead above Bonneville Dam or 13 on A-run summer steelhead. 14 7 For fall fisheries only. 15 8 There is no take prohibition on ad-clipped hatchery fish even if they are part of a threatened ESA-listed group.
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1 9 Total exploitation rate limits include ocean and mainstem Columbia River fisheries. NMFS (2017d) evaluated the 2 PFMC’s harvest matrix for total exploitation, including ocean and mainstem Columbia River fisheries, tiered on 3 abundance. 4 10 Total exploitation rate limits include ocean and inriver fisheries 5
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1 Table 40. Annual post season performance of fisheries managed under the 2008 U.S. v. Oregon Agreement.
ESU or DPS Total impact annually achieved based on postseason reporting Combined Rates1 2008 2009 2010 2011 2012 2013 2014 2015 Snake River spring/ summer-run Chinook 9.1% 10.0% 9.1% 8.8% 10.6% 9.2% 12.5% 13.4% UCR spring-run Chinook 9.1% 9.1% 10.8% 8.7% 10.5% 9.1% 12.4% 13.4% UWR spring-run Chinook In spring fisheries 5.9% 7.6% 16.4% 12.9% 10.0% 9.3% 8.9% 9.0% LCR Chinook Spring component3 yes yes yes yes yes yes yes yes Fall tule component2 33.0% 37.0% 35.0% 40.8% 44.5% 32.9% 40.8% 34.90% Fall bright component4 5,485 6,283 9,294 8,205 8,143 15,197 20,809 2,149 Snake River fall-run Chinook 27.4% 37.9% 25.9% 33.0% 34.6% 31.3% 34.8% 31.3% LCR Coho2 7.3% 18.7% 10.7% 13.5% 14.0% 13.7% 17.4% 24.4% CR Chum 1.6% 1.6% 4.7% 0.1% 0.1% 0.8% 1.4% Snake River Sockeye 4.6% 6.0% 6.8% 7.8% 9.7% 4.7% 5.0% 6.2% Separate Rates Tribal only Steelhead B-Run (in fall fisheries) 15.2% 16.8% 15.7% 21.1% 13.5% 14.0% 12.5% 12.1% Non-tribal only Snake River Steelhead Group A Index (in winter/spring/summer fisheries) 0.8% 0.7% 0.9% 0.9% 2.2% 0.8% 0.7% 0.5% Snake River Steelhead Group B Index (in winter/spring/summer fisheries) 0.1% 0.0% 0.1% 0.2% 0.2% 0.0% 0.0% 0.0% Snake River Steelhead Group A Index (in fall fisheries) 0.6% 1.0% 0.8% 1.6% 1.2% 1.6% 1.3% 1.1% Snake River Steelhead Group B Index (in fall fisheries) 1.1% 1.3% 1.8% 1.9% 1.8% 2.0% 1.6% 2.0% UCR Steelhead In winter/spring/summer fisheries 0.8% 0.7% 0.9% 1.5% 1.9% 0.9% 0.8% 0.5% UCR Steelhead In fall fisheries 1.0% 0.8% 0.8% 1.5% 1.2% 1.6% 1.3% 1.1% Summer component (in winter/spring/summer MCR Steelhead 0.8% 0.7% 0.9% 0.9% 2.2% 0.8% 0.7% 0.5% fisheries) MCR Steelhead Summer Component (in fall fisheries) 0.6% 1.0% 0.8% 1.6% 1.2% 1.6% 1.3% 1.1% MCR Steelhead Winter Component (winter fisheries) 0.3% 0.4% 0.7% 0.7% 0.8% 0.4% 0.7% 0.6% Summer component (in winter/spring/summer LCR Steelhead 0.3% 0.4% 0.7% 0.7% 0.8% 0.4% 0.7% 0.6% fisheries) LCR Steelhead Summer Component (in fall fisheries) 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% LCR Steelhead Winter Component (in winter fisheries) 0.3% 0.3% 0.7% 0.7% 0.8% 0.6% 0.6% 0.6% UWR Steelhead Winter Component (in winter fisheries) ------0.3% 0.5% 0.6% 0.6% 0.6% 1 Rate allocations are specified in 2008 U.S. v. Oregon Agreement, but can be added together for reporting purposes
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2 Rate set annually in coordination with PFMC for combined exploitation rate for ocean and Columbia River mainstem fisheries up to Bonneville Dam. 3 Managed for hatchery escapement goals to the Cowlitz, Lewis and Sandy Rivers. If annual box is yes, then H.E. goal was met 100%. 4 Managed for an escapement goal of 5,700 fish in the North Lewis River.
1
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1 Fisheries above Priest Rapids Dam 2 Fisheries above Priest Rapids Dam occur both on the Columbia River and on its tributaries. 3 Within this area, there are a mark-selective spring Chinook salmon and steelhead fisheries and 4 various fisheries targeting non-ESA-listed fish. 5 6 ESA-listed UCR spring Chinook salmon are not harvested in the action area above Priest Rapids 7 Dam. 8 9 Mark-selective steelhead fisheries operate in the action area under permit 1395 (NMFS 2003). 10 Allowable incidental take is based on natural-origin returns, with the idea being that as the 11 number of natural-origin returns increases, a higher percentage of natural-origin fish is allowed 12 to be encountered in the fishery. There are no encounters with spring Chinook salmon because 13 these fisheries occur from September through March (before and after spring Chinook salmon 14 return to this area), although seasons are often shorter because of in-season management of 15 steelhead returns. Table 41 summarizes the incidental take associated with the mark-selective 16 steelhead fisheries from 2010 through 2016. 17 18 Table 41. Summary of natural-origin UCR steelhead encounters associated with mark-selective 19 steelhead fisheries above Priest Rapids Dam (2010-2016). Season Area Natural-origin Allowable Realized escapement incidental take incidental take1 2010-2011 Methow River 1773 71 70 Columbia River1 4050 81 34 2011-2012 Methow River 1187 24 24 Columbia River2 1185 24 10 2012-2013 Methow River 905 18 14 Columbia River2 545 11 12 2013-2014 Methow River 1481 30 23 Columbia River3 359 7 5 2014-2015 Methow River 2168 43 17 Columbia River3 283 6 8 2015-2016 Methow River 1248 25 25 Columbia River3 98 2 4 20 Sources:WDFW (2011); WDFW (2012); WDFW (2014a); WDFW (2015a); WDFW (2016a) 21 1 Based on 5 percent assumed catch and release mortality. 22 2 This includes the reach from Priest to Wells Dam and the Entiat River.
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1 3 This includes the reach from Rock Island to Wells Dam. 2 3 The Wenatchee River also has a conservation fishery that may impact ESA-listed steelhead, 4 which was analyzed in NMFS (2013a), and which found that up to 10 natural-origin adult UCR 5 steelhead may be caught and released, with no more than 1 percent incidental mortality. 6 7 In this area, there are four other fisheries that incidentally impact ESA-listed spring Chinook 8 salmon and steelhead. The Methow River resident trout fishery, which occurs from June through 9 September, has incidentally killed up to 650 juveniles and encountered up to 12 adult steelhead 10 annually over the last five years, and remains within their allowed take through NMFS permit 11 1554 (Table 42). The summer Chinook and sockeye salmon fishery has incidentally killed up to 12 10 adult steelhead annually (Table 42), which is within their allotted take under permit 1554 13 (NMFS 2008g). This fishery is unlikely to encounter spring Chinook salmon because it operates 14 from July to October after spring Chinook salmon have already entered or spawned in the 15 tributary habitats, and does not take place in the Methow River. Another fishery operating under 16 permit 1554 is a recreational fishery targeting non-ESA listed spring Chinook salmon (Carson 17 stock) in Icicle Creek, which has encountered spring Chinook salmon and steelhead in the past 18 (The non-game fishery above Priest Rapids has not resulted in take of listed spring Chinook 19 salmon and steelhead despite operating year-round (WDFW 2013; WDFW 2014b; WDFW 20 2015b; WDFW 2016b; WDFW 2017a). 21 22 Table 42. Summary of natural-origin UCR steelhead and UCR spring Chinook salmon 23 encounters associated with fisheries targeting non-listed fish above Priest Rapids 24 Dam (2012-2016).
Year Fishery Allowable Realized Allowable Realized steelhead steelhead spring spring Chinook Chinook salmon salmon 2012 Methow River 1250 juveniles 429 juveniles 8 juveniles 0 juveniles resident trout 20 adults 12 adults Summer Chinook 10 adults 9 adults 0 0 and sockeye salmon Icicle Creek spring 10 adults 0 3 adults 1 adult Chinook salmon 2013 Methow River 1250 juveniles 650 juveniles 8 juveniles 8 juveniles resident trout 20 adults 12 adults Summer Chinook 10 adults 4 adults 0 0 and sockeye salmon Icicle Creek spring 10 adults 14 adults 3 adults No Chinook salmon information 2014 Methow River 1250 juveniles 302 juveniles 8 juveniles 8 juveniles resident trout 20 adults 4 adults Summer Chinook 10 adults 10 adults 0 0 and sockeye salmon Icicle Creek spring 10 adults 0 3 adults No Chinook salmon information
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2015 Methow River 1250 juveniles 396 juveniles 8 juveniles 2 juveniles resident trout 20 adults 0 adults Summer Chinook 10 adults 9 adults 0 0 and sockeye salmon Icicle Creek spring 10 adults 0 3 adults No Chinook salmon information 2016 Methow River 1250 juveniles 495 juveniles 8 juveniles 4 juveniles resident trout 20 adults 0 adults Summer Chinook 10 adults 3 adults 0 0 and sockeye salmon Icicle Creek spring 10 adults 2 adults 3 adults No Chinook salmon information 1 Sources: WDFW (2013); WDFW (2014b); WDFW (2015b); WDFW (2016b); WDFW (2017a) 2 3 Effects on ESA Protected Species and on Designated Critical Habitat
4 This section describes the effects of the Proposed Action, independent of the Environmental 5 Baseline and Cumulative Effects. The methodology and best scientific information NMFS 6 follows for analyzing hatchery effects is summarized in Appendix A and application of the 7 methodology and analysis of the Proposed Action is in Section 2.4.2. The “effects of the action” 8 means the direct and indirect effects of the action on the species and on designated critical 9 habitat, together with the effects of other activities that are interrelated or interdependent, that 10 will be added to the environmental baseline (50 CFR 402.02). Indirect effects are those that are 11 caused by the Proposed Action and are later in time, but still are reasonably certain to occur. 12 Effects of the Proposed Action that are expected to occur later in time (i.e., after the 10-year 13 timeframe of the Proposed Action) are included in the analysis in this opinion to the extent they 14 can be meaningfully evaluated. The Proposed Action, the status of ESA-protected species and 15 designated critical habitat, the Environmental Baseline, and the Cumulative Effects are 16 considered together to determine whether the Proposed Action is likely to appreciably reduce the 17 likelihood of survival and recovery of ESA protected species or result in the destruction or 18 adverse modification of their designated critical habitat.
19 Factors That Are Considered When Analyzing Hatchery Effects
20 NMFS has substantial experience with hatchery programs and has developed and published a 21 series of guidance documents for designing and evaluating hatchery programs following best 22 available science (Hard et al. 1992; Jones 2006; McElhany et al. 2000; NMFS 2004b; NMFS 23 2005c; NMFS 2008a; NMFS 2011b). For Pacific salmon, NMFS evaluates extinction processes 24 and effects of the Proposed Action beginning at the population scale (McElhany et al. 2000). 25 NMFS defines population performance measures in terms of natural-origin fish and four key 26 parameters or attributes; abundance, productivity, spatial structure, and diversity and then relates 27 effects of the Proposed Action at the population scale to the MPG level and ultimately to the 28 survival and recovery of an entire ESU or DPS.
29 “Because of the potential for circumventing the high rates of early mortality typically 30 experienced in the wild, artificial propagation may be useful in the recovery of listed salmon 31 species. However, artificial propagation entails risks as well as opportunities for salmon 32 conservation” (Hard et al. 1992). A Proposed Action is analyzed for effects, positive and
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1 negative, on the attributes that define population viability: abundance, productivity, spatial 2 structure, and diversity. The effects of a hatchery program on the status of an ESU or steelhead 3 DPS and designated critical habitat “will depend on which of the four key attributes are currently 4 limiting the ESU, and how the hatchery fish within the ESU affect each of the attributes” (70 FR 5 37215, June 28, 2005). The presence of hatchery fish within the ESU can positively affect the 6 overall status of the ESU by increasing the number of natural spawners, by serving as a source 7 population for repopulating unoccupied habitat and increasing spatial distribution, and by 8 conserving genetic resources. “Conversely, a hatchery program managed without adequate 9 consideration can affect a listing determination by reducing adaptive genetic diversity of the 10 ESU, and by reducing the reproductive fitness and productivity of the ESU”.
11 NMFS’ analysis of the Proposed Action is in terms of effects it would be expected to have on 12 ESA-listed species and on designated critical habitat, based on the best scientific information 13 available. This allows for quantification (wherever possible) of the effects of the seven factors of 14 hatchery operation on each listed species at the population level (in Section 2.5.2), which in turn 15 allows the combination of all such effects with other effects accruing to the species to determine 16 the likelihood of posing jeopardy to the species as a whole (Section 2.8).
17 Information that NMFS needs to analyze the effects of a hatchery program on ESA-listed species 18 must be included in an HGMP. Draft HGMPs are reviewed by NMFS for their sufficiency before 19 formal review and analysis of the Proposed Action can begin. Analysis of an HGMP or Proposed 20 Action for its effects on ESA-listed species and on designated critical habitat depends on six 21 factors. These factors are:
22 (1) the hatchery program does or does not remove fish from the natural population and 23 use them for hatchery broodstock 24 (2) hatchery fish and the progeny of naturally spawning hatchery fish on spawning 25 grounds and encounters with natural-origin and hatchery fish at adult collection 26 facilities 27 (3) hatchery fish and the progeny of naturally spawning hatchery fish in juvenile rearing 28 areas, migratory corridor, estuary, and ocean 29 (4) RM&E that exists because of the hatchery program 30 (5) the operation, maintenance, and construction of hatchery facilities that exist because 31 of the hatchery program 32 (6) fisheries that exist because of the hatchery program, including terminal fisheries 33 intended to reduce the escapement of hatchery-origin fish to spawning grounds
34 NMFS analysis assigns an effect category for each factor (negative, negligible, or 35 positive/beneficial) on population viability. The effect category assigned is based on: (1) an 36 analysis of each factor weighed against the affected population(s) current risk level for 37 abundance, productivity, spatial structure, and diversity; (2) the role or importance of the 38 affected natural population(s) in salmon ESU or steelhead DPS recovery; (3) the target viability 39 for the affected natural population(s) and; (4) the Environmental Baseline, including the factors 40 currently limiting population viability. For more information on how NMFS evaluates each 41 factor, please see Appendix A.
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1 Effects of the Proposed Action 2 3 This section discusses the effects of the proposed action on the ESA-listed species in the action 4 area. Most of the effects here focus on Upper Columbia River spring Chinook salmon and Upper 5 Columbia River steelhead because the facilities operate and releases occur in the Upper 6 Columbia River basin. The effects analysis of juvenile outmigration (Section 2.5.2.3, Factor 3) 7 looks at the effects on other ESA-listed salmonids, such as the Snake River, Mid-Columbia, 8 Lower Columbia, and Willamette species. 9 10 Factor 1. The hatchery program does or does not remove fish from the natural 11 population and use them for broodstock
12 Because the programs included in the proposed action all propagate non-ESA-listed summer/fall 13 or fall Chinook salmon, which is a different species/run of salmonid than the listed Upper 14 Columbia River spring Chinook salmon and steelhead, no fish from natural populations of listed 15 species will be removed for hatchery broodstock. The other ESA-listed species considered in this 16 opinion do not occur in areas where broodstock collection takes place, so they would not be 17 exposed to broodstock collection activities. Therefore, there is no overall effect of this factor on 18 these species. Inadvertent collection of listed species will be considered under Factor 2. 19 20 Factor 2. Hatchery fish and the progeny of naturally spawning hatchery fish on 21 spawning grounds and encounters with natural-origin and hatchery fish at adult 22 collection facilities
23 The proposed hatchery programs pose ecological risks and risks from handling related to adult 24 collection to UCR spring Chinook salmon and UCR steelhead, while posing no genetic risks 25 because the species propagated does not interbreed with any ESA-listed individuals. The overall 26 effect of this factor on these Upper Columbia River species is negligible. There is no effect of 27 this factor on other ESA-listed species because those species are not present on the spawning 28 grounds or in adult collection facilities of these hatchery fish. 29 30 Genetic Effects 31 Because the fish from the proposed action return to the UCR Basin as an adult to potentially 32 spawn, only listed species which are present in UCR (i.e., UCR spring Chinook salmon and UCR 33 steelhead) have the potential to be affected genetically by the proposed action.9 Within the UCR 34 Basin, there is a possibility that late returning spring Chinook salmon could interbreed with 35 summer/fall Chinook salmon from the early part of the run (Table 43) in some areas where 36 spawning distribution overlaps. However, based on spring Chinook salmon spawning timing in 37 subbasins where hatchery summer/fall Chinook salmon are released (e.g., Snow et al. (2016), 38 Hillman et al. (2016)), there is little to no temporal overlap with summer/fall Chinook salmon 39 spawning, so interbreeding between hatchery-origin summer/fall Chinook salmon and UCR 40 spring Chinook salmon is unlikely.
9 Thus, Snake River spring summer Chinook salmon, Snake River fall Chinook salmon, Lower Columbia River Chinook salmon, Upper Willamette River spring Chinook salmon, Snake River steelhead, Middle Columbia River steelhead, Lower Columbia River steelhead, Upper Willamette River steelhead, Snake River sockeye salmon, Columbia River chum salmon, and Lower Columbia coho salmon will not experience population-level genetic effects due to the proposed action.
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1 2 Spring Chinook salmon are not likely to interbreed with hatchery-origin fall Chinook salmon 3 because spring Chinook salmon would finish spawning before fall Chinook salmon would start 4 spawning (Table 43) and their spawning spatial distributions do not overlap. 5 6 Also, steelhead do not interbreed with Chinook salmon, so there are no genetic effects on UCR 7 steelhead from hatchery-origin summer/fall or fall Chinook salmon. 8 9 Table 43. Timing of adult return and spawning for UCR salmonids.
Fish Run and Species Freshwater Entry Spawning Duration Spawning Peak Summer/fall Chinook June to August Late September to Early to mid- Salmon end of November October Fall Chinook Salmon Mid-August to Late October to early November October December Spring Chinook May to June Early August to mid- Mid to late August Salmon September Summer Steelhead July to mid-June March to mid-July April to May
10 Sources: (WDFW 2002) 11 12 Ecological Effects 13 Ecological effects from returning adult hatchery-origin fish include redd superimposition, 14 competition for spawning grounds, and contribution of marine derived nutrients. Because these 15 effects could occur once the hatchery-origin fish return to the tributaries, the analysis here is 16 limited to effects on UCR spring Chinook salmon and UCR steelhead, which are the only ESA- 17 listed species present in the tributaries to which these hatchery-origin adults return.10 Predation 18 by the returning adult hatchery-origin is not likely to be an ecological effect because these adult 19 fish cease to eat upon freshwater entry. 20 21 In Table 44 below, the average number of fish for each program that have strayed to other basins 22 is summarized. These numbers are the number of hatchery-origin fish that could interact with 23 ESA-listed fish in the recipient basins, as discussed below. 24 25
10 Thus, Snake River spring summer Chinook salmon, Snake River fall Chinook salmon, Lower Columbia River Chinook salmon, Upper Willamette River spring Chinook salmon, Snake River steelhead, Middle Columbia River steelhead, Lower Columbia River steelhead, Upper Willamette River steelhead, Snake River sockeye salmon, Columbia River chum salmon, and Lower Columbia coho salmon will not experience population-level ecological effecs as a result of the proposed action.
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1 Table 44. Average number of hatchery-origin summer/fall and fall Chinook salmon straying into 2 other basins.
Program Chelan1 Entiat1 Hanford Methow3 Okanogan3 Wenatchee3 Reach2 Chelan Falls4 71 34 3 122 72 21
Wenatchee 24 30 3 102 24 N/A5
Methow 3 0 1 N/A5 19 0
Wells 63 8 (not 108 69 4 reported)
Priest Rapids 06 (not N/A5 06 06 06 /Ringold Springs reported)
3 1 Source: (Hillman et al. 2017b) 4 2 Source: (Richards and Pearsons 2015) 5 3 Source: (Snow et al. 2016) 6 4 Chelan Falls numbers include data from when the program released fish from Turtle Rock facility (located on the 7 Columbia River). Strays into the Chelan River were from releases from the Turtle Rock facility and not the Chelan 8 Falls Acclimation Facility. 9 5 These are target areas for the programs, and hatchery-origin fish from the respective programs are intended to 10 spawn naturally. Thus, any hatchery-origin fish from the respective programs would not be considered a stray in 11 these target areas. 12 6 While no Priest Rapids or Ringold Springs fall Chinook salmon have been detected in these basins, the actual 13 number of Priest Rapids or Ringold Springs hatchery fish straying into these basins may be higher than noted 14 because the number of these strays into these tributaries is undeterminable unless one of the few PIT-tagged or 15 CTW-tagged adults enters and is encountered or detected in the tributaries. 16 17 Spawning site competition and redd superimposition are possible ecological effects between 18 spring Chinook salmon and hatchery-origin summer/fall Chinook salmon. The potential effects 19 of spawning site competition could occur in September when spawning timing of UCR spring 20 and summer/fall Chinook salmon runs could briefly overlap (Table 43). However, the likelihood 21 of spatial overlap is minimal because spring Chinook salmon tend to spawn farther upstream 22 than summer/fall Chinook salmon (e.g., Snow et al. (2016), Hillman et al. (2016)). 23 24 Even though summer/fall and spring Chinook salmon may overlap spatially in some tributary 25 mainstems, the likelihood of redd superimposition appears to be low even in target areas, based
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1 on patterns observed in the Wenatchee River, which is a target area for the Wenatchee 2 summer/fall Chinook salmon program. In the Wenatchee River, redd superimposition of spring 3 Chinook salmon redds by summer/fall Chinook salmon were observed to be very limited, 4 typically 2 or 3 per year (Willard 2017), compared to the average of 48 spring Chinook salmon 5 redds observed in the mainstem Wenatchee River (Hillman et al. 2016). Because this tributary is 6 a spawning ground for both natural-origin and hatchery-origin summer/fall Chinook salmon, 7 only a subset of the observed redd superimposition is a result of redd superimposition by the 8 hatchery-origin fish from the Wenatchee summer/fall Chinook salmon program. We expect to 9 see similar level of redd superimposition in the Methow River. We, therefore, conclude that the 10 likelihood of redd superimposition on UCR spring Chinook salmon by hatchery-origin 11 summer/fall Chinook salmon is low, and the adverse effects, therefore, minimal. 12 13 Spawning site competition and redd superimposition by the hatchery-origin fish could occur 14 when there is a spatial overlap between two species. Spawning site competition and redd 15 superimposition are not likely to occur between spring Chinook salmon and fall Chinook salmon 16 because the distributions do not overlap. Fall Chinook salmon spawn primarily in the mainstem 17 Columbia River and the extreme downstream reaches of the tributary mainstems, while spring 18 Chinook salmon spawn primarily in the upper tributaries and upper reaches of the mainstem of 19 the Wenatchee, Entiat, and Methow Rivers, so there is virtually no overlap between fall and 20 spring Chinook salmon in space. Thus, spawning site competition and redd superimposition are 21 not likely to occur between spring Chinook salmon and fall Chinook salmon. 22 23 Spawning site competition and redd superimposition by summer/fall and fall Chinook salmon as 24 a result of the proposed action are not likely to affect steelhead because steelhead spawning and 25 emergence occur before summer/fall and fall Chinook salmon spawn. 26 27 Because the average numbers of strays into other basins are small and because the likelihood of 28 competition or redd superimposition is minimal to none, the strays from these hatchery programs 29 are unlikely to have any detectable ecological effects on any of the naturally spawning ESA- 30 listed species. 31 32 Hatchery fish contributes marine-derived nutrients to the ecosystem in the Upper Columbia 33 River. Two of the six programs do not intend for returning adults to spawn naturally. The four 34 programs that do intend for hatchery-origin adults to spawn naturally contribute about 428 kg of 35 phosphorous to the UCR Basin annually (Table 45), which is approximately 22% of the 36 phosphorus input in the Action Area (Table 10). 37 38 Table 45. Total phosphorous imported by adult returns from the proposed hatchery programs 39 based on the equation, mean adult mass and phosphorous concentration in Scheuerell et al.
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1 (2005). Escapement and pHOS estimates from Hillman et al. (2017b), Richards and Pearsons 2 (2015), and Snow et al. (2016).
Phosphorous imported (kg/year) Number Average Concentration of Subbasin Total adult of From Program pHOS Hatchery Location Escapement mass phosphorous hatchery -origin 5 (kg)2 (kg/adult)3 -origin Total Adults1 adults (only)4
Wenatchee Wenatchee 9,100 0.14 1,274 6.75 0.0038 32.68 233.42
Methow Methow 1,913 0.33 631 6.75 0.0038 16.19 49.07
Chelan Chelan 821 0.59 484 6.75 0.0038 12.42 21.06 Falls
No No Wells Multiple 4,3886 6.75 0.0038 112.55 information information Hanford Priest Reach Rapids/ (Columbia 65,518 0.151 9,893 6.75 0.0038 253.76 1,680.54 Ringold River Springs7 mainstem) Total 427.60 1,984.08 3 1 The number of hatchery-origin adults are determined by multiplying total escapement numbers by pHOS. 4 2 Source: Cederholm et al. (2000). 5 3 Source: Scheuerell et al. (2005). 6 4 These numbers are determined by multiplying together the number of hatchery-origin adults, average adult mass, 7 and concentration of phosphorus. 8 5 These numbers are determined by multiplying together the number of total escapement, average adult mass, and 9 concentration of phosphorus. 10 6 The number of hatchery fish is based on average number of returns per release life history (sub-yearling or 11 yearling) added together from (Snow et al. 2016). 12 7 Analysis for Priest Rapids and Ringold Springs hatchery programs are combined for this table because the 13 escapement numbers are from the Hanford Reach, which includes both programs. 14 15 Adult Collection Facilities 16 Negligible: While broodstock collection for these programs target summer/fall or fall Chinook 17 salmon, ESA-listed spring Chinook salmon or steelhead could be encountered incidentally to the 18 broodstock collection; these encountered spring Chinook salmon or steelhead are handled, but do 19 not lead to mortality. Most of the encounters of UCR spring Chinook salmon during broodstock 20 collection for summer/fall Chinook salmon occur concurrently with RM&E associated with the 21 spring Chinook salmon. Collection of fall Chinook salmon, occurring later than the summer/fall 22 collection, does not result in the incidental encounter of UCR spring Chinook salmon because of
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1 the difference in the run-timing. Similarly, broodstock collection for these programs occur 2 concurrently with many steelhead hatchery broodstock collection or sampling programs. Thus, 3 only a small number of spring Chinook salmon and steelhead are expected to be encountered in 4 addition to encounters analyzed in other opinions. Table 46 summarizes where the effects have 5 already been considered in other opinions. 6 7 Table 46. Broodstock collection for summer/fall and fall Chinook salmon and associated 8 biological opinions where effects on listed species have been already analyzed.
Program Collection Location Collection Spring Chinook Summer Duration Salmon Analysis Steelhead Analysis Chelan Falls Entiat Hatchery July 1-September NMFS (2013b); NMFS Chief Joseph Hatchery 15 NMFS (2017c) (2013b); NMFS (2017c) Wenatchee Dryden Dam July 1-September NMFS (2013a) NMFS (2016a) Tumwater Dam 15 Methow Wells dam July 1-September NMFS (2016 ) NMFS (2017e) 15 Wells Wells Hatchery/Dam July 1-August 28 NMFS (2016 ) NMFS (2017e) Hatchery Priest Rapids; Priest Rapids Mid-September- NA NMFS Ringold Hatchery/Dam; early December (2016a);NMFS Springs Hanford Reach (2008c)
9 10 Chelan Falls Canal Trap will be used to primarily trap summer/fall Chinook salmon for the 11 Chelan Falls program, with the Entiat Hatchery and Chief Joseph Hatchery being the back-up 12 facilities to provide additional broodstock if needed. The trap will be operated above 21°C, 13 which is a temperature threshold that could start migration blockage (Richter and Kolmes 2005), 14 but the operation of the Chelan Falls Trap above 21°C is likely to be a minimal risk to ESA- 15 listed species because, while UCR spring Chinook salmon and UCR steelhead are potentially 16 present in the area, these species are not likely to be encountered during broodstock trapping 17 operations based on observations from past trap operations. In addition, trapping will cease if an 18 ESA-listed species are encountered in waters above 21°C, pending further consultation with 19 NMFS or the USFWS to determine if continued trap operation poses substantial risk to listed 20 species. Since the start of the Chelan Falls Trap operation in 2016, no steelhead have been 21 encountered at the trap. Some unidentified Chinook salmon have been encountered at the trap 22 (none in 2016 and 10 in 2017) (Willard 2017), but most, if not all, of these fish are likely to be 23 summer/fall Chinook salmon for several reasons. First, the trap has been and will be operated 24 after the spring Chinook salmon run is complete (August 4 in 2016, July 21 in 2017, and after 25 July 15 in future years), so the likelihood of encountering spring Chinook salmon is very low. 26 Second, WDFW errs on the conservative side, and assumes a Chinook salmon to be spring 27 Chinook salmon if it cannot visually be identified as a summer Chinook salmon11; however,
11 WDFW typically relies on morphology and/or coloration to distinguish between spring Chinook salmon and summer/fall Chinook salmon. For example, spring Chinook salmon tend to have stream-lined body, be heavily spotted with greenish yellow hue, while summer/fall Chinook salmon tend to be more robust bodied.
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1 these unidentifiable Chinook salmon are likely to be summer/fall Chinook salmon based on an 2 evaluation at the Eastbank Hatchery Outfall (for 2015 and 2016), which found that 60 to 86 3 percent (with 75% probability of positive assignment) of unidentified Chinook salmon at the 4 Eastbank Hatchery Outfall (collected as part of broodstock collection for their summer/fall 5 Chinook salmon program) were summer/fall Chinook salmon (Small and Bell 2015; Small and 6 Bowman 2017). To verify that these Chinook salmon are, in fact, not spring Chinook salmon, 7 genetic samples will be collected and analyzed for these unidentified Chinook salmon. 8 9 To the extent that the unidentified Chinook salmon are spring Chinook salmon, a wide range of 10 effects could occur. Because these fish will only be handled for sampling and released, direct 11 mortality is not likely to occur. Being trapped in a trap, depending on the timing, could delay fish 12 from getting to the spawning grounds; spring Chinook salmon spawning occurs from early 13 August to mid-September. Spawning location has been shown to be an important factor in 14 reproductive success for some spring Chinook salmon populations (Hughes and Murdoch 2017), 15 but because it appears that most, if not all, spring Chinook salmon have migrated past the Chelan 16 River at this time (Faulkner et al. 2015), it is not anticipated that trapping could cause spring 17 Chinook salmon to spawn in sub-optimal habitat. However, fish that die from indirect effects of 18 trapping will be very low based on the number of encounters (e.g., 10 in 2017). Mortality could 19 occur if the water temperature is too high, but it is not likely because the summer/fall Chinook 20 salmon (which have physiological characteristics similar to spring Chinook salmon) that are also 21 in the trap have not had any health issues (CPUD and WDFW 2017). 22 23 For the Priest Rapids and Ringold Springs programs, the broodstock collection can occur at the 24 volunteer trap at the Priest Rapids Hatchery, at the OLAFT, or through hook-and-line angling in 25 Hanford Reach. Spring Chinook salmon are not likely to be encountered during these activities. 26 The steelhead encounters at the OLAFT were analyzed in NMFS (2016a), which found that up to 27 15% of adult steelhead would be handled with no more than 2% incidental mortality through 28 RM&E performed by WDFW, of which the operation of OLAFT for broodstock collection for 29 Priest Rapids Hatchery is a subset. The steelhead encounters during hook-and-line angling were 30 analyzed in NMFS (2008c), which found that up to 162 adult UCR steelhead may be 31 encountered with 16 mortalities during the Hanford Reach summer Chinook salmon fishery, of 32 which the broodstock collection for Priest Rapids Hatchery occurs as a subset. 33 34 At the Priest Rapids volunteer trap, three categories of steelhead are encountered: no external 35 marking, ad-clip only, and ad-clip and right ventricle clip. Of these, fish with no external 36 marking and fish with ad-clip only could be ESA-listed UCR steelhead. Thus, we focus our 37 analysis here on them. The volunteer trap encountered 5, 10, and 3 potentially listed steelhead 38 (based on marking) in 2014, 2015, and 2016, respectively, with no mortality in any year 39 (Richards 2017). Thus, we expect that the operation of Priest Rapids volunteer trap can 40 encounter up to 15 adult UCR steelhead with up to 3 mortality, accounting for a year with a good 41 return and representing a worst-case-scenario level of mortality. 42 43 At the Ringold Springs Rearing Facility, steelhead are occasionally handled during broodstock 44 collection. When they are collected, they are immediately released upstream of the hatchery 45 discharge channel in the Columbia River, through a new pipe that was recently installed to 46 replace hauling in a truck, which used to occur (USACE and WDFW 2017). Encounter rates at
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1 the Ringold Facility have been very low; five natural-origin steelhead (visually identified as ad- 2 present) were encountered in 2010 and three in 2011(USACE and WDFW 2017), none of which 3 encounters resulted in mortality during handling. 4 5 Factor 3. Hatchery fish and the progeny of naturally spawning hatchery fish in 6 juvenile rearing areas, the migratory corridor, estuary, and ocean
7 NMFS also analyzes the potential for competition and predation when the progeny of naturally 8 spawning hatchery fish and hatchery releases share juvenile rearing areas and migratory 9 corridors. Because the fish released from the proposed action are likely to affect natural-origin 10 fish as they emigrate, the effects analysis here includes the distance through the estuary (i.e., 11 mouth of the Columbia River). This factor can have effects on the productivity VSP parameter 12 (Section 2.5) of the natural population. The effect of this factor on all listed salmonid species is 13 negative. It is important to keep in mind that some results of the model below are an 14 overestimation of interaction and predation values for those fish that also includes non-listed 15 species (e.g., summer/fall Chinook salmon in Upper Columbia River) because of uncertainty in 16 the data used for the model run. While we cannot characterize or quantify the amount of 17 overestimation, this approach is a precautionary approach because it assumes the maximum 18 possible effect on listed species. 19 20 Hatchery release competition and predation effects 21 In reviewing competition and predation effects in the mainstem Columbia River, NMFS used the 22 PCD Risk model of Pearsons and Busack (2012) PCD Risk, to quantify the potential number of 23 natural-origin salmon and steelhead juveniles lost to competition and predation from the release 24 of hatchery-origin juveniles. The original version of the model suffered from operating system 25 conflicts that prevented completion of model runs and was suspected of also having coding 26 errors. As a result, the program was modified by Busack in 2017 into a considerably simpler 27 version to increase supportability and reliability. At present, the program does not include 28 disease effects and probabilistic output. Our model also does not account for the beneficial 29 effects of juvenile hatchery-origin fish releases, mainly in the form of prey for natural-origin 30 salmon and steelhead, or growth that likely occurs post-release. Also, the model was designed to 31 address interference competition associated with territorial interactions; as such, it likely 32 overestimates the effects of competitive interactions when territories are not formed. Parameter 33 values used in the model runs are shown in Table 47 - Table 50. 34 35 For our model runs, we assumed a 100 percent population overlap between hatchery fish and all 36 natural-origin species present. Hatchery summer/fall Chinook salmon are released from April- 37 May whereas hatchery fall Chinook salmon are released anywhere between May-July, with a 38 large proportion being released in June (all 7,299,504 fall Chinook salmon from Priest Rapids). 39 These releases may overlap with natural-origin chum, coho, sockeye, spring, and fall Chinook 40 salmon, and steelhead in the Action Area. However, our analysis is limited to assessing effects 41 on listed species, and this limits overlap of those species to certain areas. To address this, we 42 modified residence times for hatchery summer/fall and fall Chinook salmon if they did not 43 overlap completely with certain natural-origin species, by adjusting the total distance traveled. 44 For example, Snake River fall Chinook salmon do not inhabit the upper Columbia River (UCR) 45 above McNary Dam and thus effects on Snake River fall Chinook salmon from hatchery 46 summer/fall and fall Chinook salmon releases as part of the Proposed Action would not occur
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1 until they comingled in the mainstem Snake River (or below McNary Dam; more detailed 2 calculations can be found in Kondo (2017d)). We believed it was better to address overlap by 3 adjusting residence time than by adjusting population overlap, because the population overlap 4 parameter represents microhabitat overlap not basinwide-scale overlap. We acknowledge that a 5 100-percent population overlap in microhabitats is likely an overestimation. 6 7 The model was run in two segments: from release to McNary Dam, and as an aggregate run from 8 McNary Dam through the estuary. The model run from release to McNary Dam was further 9 broken into three individual runs: (1) release to confluence of UCR (only necessary for two 10 release sites: Wenatchee River at RM 16 and Methow River at RM 37.5, discussed below), (2) 11 mouth of tributaries to McNary Dam, and (3) confluence of Columbia River and Snake River to 12 McNary Dam. The model runs from release to McNary Dam were split into three individual 13 segments based on the different age/species of natural-origin salmon and steelhead likely to be 14 encountered during different stretches of the river. The following explains the caveats regarding 15 each step of this 3-part model run from release to McNary Dam: 16 1. Release to confluence of tributary and UCR: Three release sites are on tributaries of the 17 mainstem UCR; however, Chelan Falls release site is located at RM 0.25 on the Chelan 18 River. Because the travel time of the Chelan Falls summer/fall Chinook salmon to the mouth 19 of Chelan River would be less than a day, we do not expect the released fish to have 20 meaningful interactions with natural-origin fish during this short stretch. Therefore, this 21 release site was treated as if the fish were direct release on the mainstem UCR. The two 22 release sites that were considered for this part of the model run are for the Wenatchee and 23 Methow summer/fall Chinook salmon yearling programs at RM 16 and 37.5 on the 24 Wenatchee and Methow Rivers, respectively. The following assumptions were made for 25 these model runs: 26 • Travel (residence) time was proportional to what the fish’s travel time was from 27 release to McNary Dam (e.g., if the fish took 100 days to travel from release to 28 McNary at a rate of 5 miles/day, that same rate was applied to the distance these 29 fish had to swim from release to the mouth of UCR; see Kondo (2017d) for more 30 details). 31 • Survival rate of hatchery fish was assumed to be 100% during these short 32 stretches in the tributary. 33 • Temperatures at the release sites were used in model runs. 34 • Model runs account for hatchery fish predation and competition effects on 35 natural-origin Chinook salmon ages 0 and 1, and steelhead ages 1 and 2. 36 2. Mouth of tributaries to McNary Dam: Releases from all programs were analyzed for this 37 stretch because all fish migrate through this area. Chelan Falls (located at RM 0.25 on the 38 Chelan River) included that 0.25 RM in the travel (residence) time calculation. The following 39 assumptions were made for these model runs: 40 • Travel (residence) time was proportional to what the fish’s travel time was from 41 release to McNary Dam. 42 • Survival rate of hatchery fish was assumed to be the same as the survival from 43 release to McNary Dam, as we are assuming the losses of hatchery fish will take 44 place in the main UCR stretch.
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1 • Temperatures at the release sites were used in model runs. 2 • Model runs account for hatchery fish predation and competition effects on 3 natural-origin age 1 Chinook salmon and age 2 steelhead because rearing fish (age 4 0 Chinook salmon and age 1 steelhead) would not be present in the mainstem 5 Columbia River. 6 3. Confluence of Columbia River and Snake River to McNary Dam: Releases from all 7 programs were analyzed for this stretch because all fish migrate through this area. The 8 segment between the Snake River and McNary Dam is being replicated during this model run 9 (as it was also analyzed in the model run above, see step 2) because different natural-origin 10 species are now present beginning where the Snake River meets the UCR, and from there 11 downstream. This is the most accurate way of accounting for hatchery-origin effects on 12 natural-origin fish that are only present in that specific stretch of the river, rather than 13 assuming certain natural-origin fish are throughout the entire river. The following 14 assumptions were made for these model runs: 15 • Travel (residence) time was proportional to what the fish’s travel time was from 16 release to McNary Dam. 17 • Hatchery-origin fish numbers for each release site is reduced from the original 18 release number at the release site because we assume that only a percentage of 19 these fish have survived to the mouth of the Snake River (e.g., if a release of 20 100,000 fish has a 55% survival rate from release to McNary Dam, this model 21 segment would be run with 55% of 100,000 or 55,000 hatchery-origin fish; see 22 Kondo (2017d) for more details). 23 • Survival rate of hatchery fish was assumed to be 100% from the confluence of 24 Columbia River and Snake River to McNary Dam, as they were assumed to be 25 reduced in the mainstem of the UCR, before they reach the confluence of the 26 Snake River. 27 • Temperatures at McNary Dam forebay were used in model runs. 28 • Model runs account for hatchery fish predation and competition effects on 29 natural-origin Chinook salmon age 0 and sockeye salmon age 1 and 2 because 30 these fish commingle with the hatchery-origin fish at the confluence of Columbia 31 River and Snake River; age 2 Snake River steelhead would also join the hatchery- 32 origin fish from confluence of the two rivers, but the effect of these age 2 33 steelhead were analyzed in the run from the mouth of the tributary to McNary 34 Dam (#2, above). 35 36 The aggregate model run from McNary Dam through the estuary further grouped the individual 37 release sites into three groups: summer/fall Chinook salmon yearlings, summer/fall Chinook 38 salmon subyearlings, and fall Chinook salmon subyearlings. Within each group, some hatchery 39 fish parameters were averaged to obtain one value to use for that group. The following 40 assumptions were made for these model runs: 41 • Travel (residence) time was proportional to what the fish’s travel time was from 42 release to McNary Dam and averaged by grouping to obtain one travel time per 43 group.
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1 • Survival rate of hatchery fish from McNary Dam to Bonneville Dam was used as 2 proxy by assuming that the survival rate of hatchery fish below Bonneville Dam 3 to the mouth of the Columbia River is 100 percent. 4 • Hatchery-origin fish numbers for each aggregate group are reduced from the 5 original release number by using the survival rate to McNary Dam. 6 • Temperatures at McNary Dam forebay were used in model runs. 7 • Model runs account for hatchery fish predation and competition effects on 8 natural-origin Chinook salmon age 0 and 1, steelhead age 2, chum salmon age 0, 9 sockeye salmon age 1 and 2, and coho salmon age 2. 10 11 Table 47. Parameters from the PCD Risk model that are the same across all programs.
Parameter Value1
Habitat complexity 0.1
Population overlap 1.0 0.3 for Chinook salmon; Habitat segregation 0.6 for all other species Dominance mode 3 0.002 for Chinook, Coho, and Chum salmon (when interacting Piscivory with yearling summer/fall Chinook salmon); 0 for all other species Maximum encounters per day 3
Predator:prey length ratio for 0.252 predation
12 1 All values from HETT (2014) unless otherwise noted. 13 2 Daly et al. (2014) 14
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1 Table 48. Age and size of listed natural-origin salmon and steelhead encountered by juvenile 2 hatchery fish after release.
Species Age Class Size in mm (SD) Source
0 38 (4) HETT (2014) Chinook salmon 1 98 (4) HETT (2014)
1 126 (24) HETT (2014) Steelhead 2 170 (24) HETT (2014)
1 86 (7) HETT (2014) Sockeye salmon 2 128 (8) HETT (2014)
Coho salmon 2 90 (20) Simpson (2017)
Chum salmon 0 40 (3) Hillson et al. (2017)
3 4 Table 49. Hatchery fish parameter values for the PCD Risk model run from release of fish to 5 McNary Dam.
Travel (residence) Time (median days) Temp. Size in Survival Mouth at Release mm Rates to Release Program Release Site of trib. release Number (SD) at McNary to UCR to Snake Release 2 release (mean) mouth mouth confluence to (°C) (if of to McNary McNary applica- Snake ble) River Chelan Falls Chelan summer/fall 161 River 576,000 0.615 n/a* 18.8 3.2 22 9.7 Chinook salmon (20) (RM 0.25) (yearlings) Wenatchee Wenatchee summer/fall 145 River 550,000 0.77 1.3 12.1 2.6 16 8 Chinook salmon (20) (RM 16) (yearlings) Methow Methow summer/fall 154 River 220,000 0.55 3.5 18.7 2.9 25 12.7 Chinook salmon (20) (RM 37.5) (yearlings) Wells summer/fall Columbia 103 Chinook salmon River 484,000 0.35 n/a 35.3 5.7 41 9.7 (20) (subyearlings) (RM 515)
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Wells summer/fall 176 Chinook salmon 320,000 0.74 n/a 23.1 3.7 26.8 (20) (yearlings) Priest Rapids fall Columbia Chinook salmon River 7,299,504 0.68 n/a 10 3 13 14.9 (subyearlings) (RM 413) 103 Ringold Springs fall Columbia (20) Chinook salmon River 3,500,000 0.68 n/a 6 7 13 13.33 (subyearlings) (RM 352) 1 * Because this release on the Chelan River is a short distance to the Columbia River and we do not expect the 2 released fish to have meaningful interactions with natural-origin fish during this short stretch, we did not analyze the 3 effect from release to the mouth of the Chelan River. 4 2 Data from HETT (2014) unless otherwise noted. 5 3 Data from http://www.cbr.washington.edu/dart/query/river_graph_text; access date August 16, 2017. 10 year 6 average (2007-2016) of temperature (WQM). 7 8 Table 50. Hatchery fish parameter values for aggregate runs for the PCD Risk model, starting at 9 McNary Dam and through the estuary.
Number of Survival Travel Hatchery Mean Temperature Rates (residence) Aggregate Fish sizes in (°C) at Program (mean for Time Run Group Survived to mm McNary McNary to (median McNary (SD) (mean)2 Bonneville1) days) Dam
Chelan Falls summer/fall Chinook 354,240 0.91 30.3 salmon (yearlings) Wenatchee summer/fall Chinook 423,500 0.92 24.3 salmon Summer/fall (yearlings) N/A N/A Chinook Methow yearling summer/fall salmon Chinook 121,000 0.87 27.1 salmon (yearlings) Wells summer/fall Chinook 236,800 0.66 35.1 salmon (yearlings) Aggregate 163.14 1,135,540 0.84 29 13.2 Parameters (20)
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Wells Summer/fall summer/fall Chinook 102.98 Chinook 169,400 0.34 53.7 13.2 subyearling (20) salmon salmon (subyearlings) Priest Rapids fall Chinook 4,951,496 0.18 33.0 salmon (subyearlings) Fall Ringold N/A N/A Chinook Springs fall subyearling Chinook 2,410,625 0.17 64.7 salmon salmon (subyearlings) Aggregate 102.98 7,362,121 0.17 49 16.1 Parameters (20) 1 1 Survival rate of hatchery fish from McNary Dam to Bonneville Dam was used as surrogate by assuming that 2 survival rate of hatchery fish is the same through the estuary as it is to the Bonneville Dam because we have no 3 other survival data. 4 2 Fish Passage Center, last accessed: September 19, 2017 (average McNary forebay temperature from May 20-31, 5 2007-2016 used for summer Chinook yearlings and subyearlings model runs, and June 15-30, 2007-2016 average 6 McNary forebay temperatures used for fall Chinook subyearling model runs). 7 8 We conducted model runs with natural-origin fish numbers at the point where all possible 9 hatchery-origin fish interactions are exhausted at the end of each day. It is possible that in doing 10 this, we ran the models with natural-origin juvenile abundances that exceed actual numbers 11 available. Using natural-origin juvenile numbers at the point where all possible hatchery-origin 12 fish interactions are exhausted at the end of each day allows us to estimate worst-case impacts on 13 listed natural-origin fish. The exception to this is for sockeye salmon because we have data for 14 natural-origin abundance for the one population that composes the entire ESU that demonstrates 15 that, from 2006-2016, the maximum number of natural-origin sockeye salmon produced was 16 ~61,000. Thus, we used this value in the model along with the actual proportions of each age- 17 class (87 percent age-1, and 13 percent age-2) available (Kozfkay 2017). To ensure the effects 18 due to competition and predation are within our model estimates, we will continue to monitor 19 median travel times from release to McNary Dam on an annual basis (using a 5-year rolling 20 median) compared to the values used in our analyses (see Table 49). 21 22 The resulting juveniles lost from release to McNary Dam for all natural-origin species are 23 summarized in Table 51. The resulting juveniles lost from McNary Dam through the estuary are 24 summarized in Table 52. Using the smolt-to-adult survival rate (SAR) representative of each 25 species, these lost juveniles equate to 2,488 Chinook salmon, 517 steelhead, 15 sockeye salmon, 26 96 chum salmon, and 468 coho salmon adult equivalents (Table 51, Table 52) from release to the 27 mouth of the Columbia River. 28 29
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Table 51. Maximum numbers of juvenile natural-origin salmon and steelhead lost to predation (P) and competition (C) from hatchery- origin summer/fall and fall Chinook salmon from the Proposed Action for model runs from release to McNary Dam.
Chinook Salmon1 Steelhead2 Sockeye Salmon3 Program Release Site P4 C5 C5 C5 Chelan Falls summer/fall Chelan River 3,216 15,487 2,711 107 Chinook salmon (yearlings) (RM 0.25) Wenatchee summer/fall Chinook Wenatchee River 1,322 6,428 1,363 78 salmon (yearlings) (RM 16) Methow summer/fall Chinook Methow River 1,684 9,388 1,444 74 salmon (yearlings) (RM 37.5) Wells summer/fall Chinook 0 7,486 378 69 salmon (subyearlings) Columbia River Wells summer/fall Chinook (RM 515) 2,834 8,105 1,261 107 salmon (yearlings) Priest Rapids fall Chinook Columbia River 0 169,721 4,279 128 salmon (subyearlings) (RM 413) Ringold Springs fall Chinook Columbia River 0 79,627 1,866 128 salmon (subyearlings) (RM 352) Total 305,298 13,302 691 SAR6 0.0037 0.011 0.005 Adult Equivalents 1,130 146 4 1 The Chinook salmon lost here includes age 0 and age 1 fish from release to the mouth of the respective tributaries, age 1 fish from mouth of the respective tributaries to McNary Dam, and age 0 Snake River Chinook salmon from the confluence of the Columbia River and Snake River to McNary Dam. 2 The steelhead lost here includes age 1 and 2 fish from release to the mouth of the respective tributaries and age 2 fish from mouth of the respective tributaries to McNary Dam. 3 The sockeye salmon lost here includes age 1 and 2 fish from the confluence of the Columbia River and Snake River to McNary Dam because there are no listed species of sockeye salmon in UCR. 4 Predation values only shown for Chinook salmon interactions because no predation occurs on steelhead or sockeye salmon from Chinook salmon (HETT 2014). 5 Competition, as used here, is the number of natural-origin fish lost to competitive interactions assuming that all competitive interactions that result in body weight loss are applied to each fish until death occurs (i.e., when a fish loses 50% of its body weight). This is not reality, but does provide a maximum mortality estimate using these parameter values. 6 SAR for Chinook salmon (average of: Grant County PUD et al. 2009b; NMFS 2016 ), steelhead (NMFS 2017e), and sockeye (IDFG 2012).
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1 Recent travel time information from the applicants (GPUD 2017) suggests that our assumption 2 of 100% population overlap between hatchery-origin fish and natural-origin Chinook yearlings 3 above McNary Dam may be a substantial overestimate; it is possible that overlap may be as low 4 as 5% for fish released from the Priest Rapids fall Chinook program above McNary Dam 5 (GPUD, DPUD, CPUD, personal communication, December 20, 2017). Using 5% as the 6 population overlap parameter in the model would yield in having 33,328 juvenile ESA-listed and 7 non-listed Chinook salmon lost to competition above McNary Dam, compared to the 169,721 8 juveniles lost under the 100% population overlap scenario. While the information provided by 9 the operators is still under review, it is likely that it is much closer to reality than our earlier 10 assumption. NMFS plans to continue refining model parameters to better assess ecological 11 effects in the future.
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Table 52. Maximum numbers of juvenile natural-origin salmon and steelhead lost to predation (P) and competition (C) with hatchery- origin summer/fall and fall Chinook salmon from the Proposed Action for aggregate model runs from McNary Dam through the estuary.
1 2 Sockeye 4 5 Program(s) in Chinook salmon Steelhead 3 Chum salmon Coho salmon Aggregate Group salmon Group 6 P6 C7 C7 C7 P C7 P6 C7 Chelan Falls, Summer/fall Chinook Wenatchee, 31,591 34,535 11,965 767 10,247 17,431 234 24,510 yearling salmon Methow, Wells Summer/fall Chinook Wells 0 6,531 240 627 N/A8 N/A8 N/A8 N/A8 subyearling salmon Fall Chinook Priest Rapids, 0 258,472 9,590 781 N/A8 N/A8 N/A8 N/A8 subyearling salmon Ringold Springs Total 331,129 21,795 2,175 27,678 24,744 SAR9 0.0041 0.017 0.005 0.0039 0.0189 Adult Equivalents 1,358 371 11 96 468 1 The Chinook salmon lost here includes age 0 and age 1 fish. 2 The steelhead lost here are only age 2 fish. 3 Chum salmon lost here are only age 0 fish. 4 The sockeye salmon lost here includes age 1 and age 2 fish. 5 The coho salmon lost here are age 2 fish. 6 Predation values only shown for Chinook salmon and chum salmon interactions with Chinook salmon because no predation occurs on steelhead and sockeye salmon from Chinook salmon (HETT 2014). 7 Competition, as used here, is the number of natural-origin fish lost to competitive interactions assuming that all competitive interactions that result in body weight loss are applied to each fish until death occurs (i.e., when a fish loses 50% of its body weight). This is not reality, but does provide a maximum mortality estimate using these parameter values. 8 Summer/fall and fall Chinook subyearlings are not likely to interact with chum and coho salmon because the chum and coho salmon would already be emigrated out of the freshwater system before the subyearlings reach White Salmon River (where chum and coho salmon would spatially overlap with the hatchery releases). 9 Smolt-to-adult survival rate for Chinook salmon (average of: Grant County PUD et al. 2009b; NMFS 2016 ; NMFS 2017f; NMFS 2017g), steelhead (average of: NMFS 2017e; NMFS 2017f; NMFS 2017g), sockeye (IDFG 2012), chum (Hillson 2015), and coho salmon (ODFW 2011).
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1 Table 52 summarizes the likely number of adults that would be lost from each ESU between 2 McNary Dam through the estuary. While these numbers represent the maximum potential effect 3 from the proposed action, these ecological interactions also occur between natural-origin species; 4 thus, the effects attributable to the proposed action is only that portion that exceeds the natural 5 level of ecological interactions. Because the Chinook salmon lost to ecological effects between 6 release and the estuary includes both listed and non-listed fish, only a portion of the lost adult 7 Chinook salmon equivalents are likely to be listed. However, our analysis assumes that all 8 Chinook salmon lost are listed in order to represent an absolute maximum total (and in the 9 absence of more precise data). In addition, the SAR for subyearlings tend to be lower than for 10 yearlings, so adult equivalents for subyearlings may also be lower than what is noted in Table 52. 11 We also assume that the effects on each population within each ESU is proportional to their ESU 12 composition. For example if a single population represents 5 percent of the natural-origin adults, 13 then the loss our model predicts would be some percentage of the 5 percent contribution of that 14 population to the ESU. 15 16 While we assume in our analysis that the fish would continue to travel at the same rate below 17 McNary Dam as the rate from release to McNary Dam, this assumption likely overestimates the 18 effect these fish would have on natural-origin fish below McNary Dam because these hatchery- 19 origin fish are likely to be traveling quicker as they get closer to the mouth of the Columbia 20 River. For illustrative purposes, we also ran the model for effects on natural-origin Chinook 21 salmon between McNary Dam through the estuary using the travel rate of yearling (7 days) and 22 subyearling Chinook salmon (8 days) from McMichael et al. (2010) and from G.A. et al. (2011). 23 For this model run, we assume that the summer/fall and fall Chinook subyearlings have the same 24 travel rate below McNary Dam. The results are compared below in Table 53, which summarizes 25 the effect on listed and non-listed Chinook salmon juveniles. 26 27 Table 53. Comparison of results based on different travel times.
Chinook salmon Chinook salmon from Program(s) in Aggregate Group from Table 53 quicker travel time Group P C P C Chelan Falls, Summer/fall Chinook Wenatchee, 31,591 34,535 7,078 8,697 yearling salmon Methow, Wells Summer/fall Chinook Wells 0 6,531 0 1,026 subyearling salmon Fall Chinook Priest Rapids, 0 258,472 0 46,510 subyearling salmon Ringold Springs Total 331,129 63,311 SAR1 0.0041 0.0041 Adult Equivalents 1,358 260 28 1 Smolt-to-adult survival rate for Chinook salmon (average of: Grant County PUD et al. 2009b; NMFS 2016 ; NMFS 29 2017f; NMFS 2017g). 30 31 To understand the potential effect on each Chinook ESU, we calculated the likely number of 32 adults that would be lost from each ESU between release to McNary Dam (Table 54) using the
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1 percent of listed wild yearlings (96) and subyearlings (4), and proportion of each attributable to 2 each listed ESU at McNary Dam (taking the average of values from 2012 through 2016; Table 7a 3 of: Zabel 2013; Zabel 2014a; Zabel 2014b; Zabel 2015; Zabel 2017). We then applied a similar 4 methodology at Tongue Point (i.e., mouth of the Columbia River) for the reach from McNary 5 Dam to the Columbia River mouth, where 27 percent of listed Chinook salmon are likely to be 6 yearlings, while 73 percent of listed Chinook salmon are likely to be subyearlings, to be able to 7 estimate ESU level loss (taking the average of values from 2012 through 2016; Table 7a of: 8 Zabel 2013; Zabel 2014a; Zabel 2014b; Zabel 2015; Zabel 2017). In addition, we applied the 9 ratio of UCR spring Chinook salmon returns compared to the UCR summer/fall Chinook salmon 10 returns (0.24) in order to calculate the UCR spring Chinook salmon adult equivalent for each 11 segment of the run (781 and 18, respectively) to better estimate the effect on UCR Spring 12 Chinook Salmon ESU. Effects on all ESUs are less than 4 percent, a relatively small amount of 13 loss. The ESU with the largest proportional effect was the UCR Spring Chinook Salmon ESU 14 (3.8 percent loss). However, it is important to remember that this also includes some unlisted 15 subyearling Chinook salmon from the UCR, and our ESU proportion estimates do not account 16 for some unlisted fish. Thus, we believe effects on Chinook salmon abundance and productivity 17 due to ecological interactions with outmigrating hatchery juveniles are negative, and would be 18 divided proportionally among the extant populations within each ESU. 19 20 All 517 adult steelhead lost to ecological effects from release through the estuary are listed fish. 21 Our analysis shows that loss of steelhead adult equivalents due to ecological effects with 22 outmigrating juvenile hatchery fish is less than 1.5 percent for each listed DPS. Thus, we believe 23 this to be a small negative effect on DPS abundance and productivity, which would be divided 24 proportionally among the extant populations within each DPS. 25 26 The 15 adult sockeye salmon lost to these ecological effects are from the Snake River sockeye 27 ESU. This loss equates to a one percent loss from the ESU; a small negative effect on ESU 28 abundance and productivity. 29 30 For both chum and coho salmon, there is only a single ESU in the Columbia River Basin (i.e., 31 Columbia River Chum Salmon ESU and Lower Columbia River Coho Salmon ESU). The 32 percentages of chum and coho salmon adult equivalents lost to ecological interactions ae less 33 than one percent, and we assume would be divided proportionally among the 17 chum and 24 34 coho salmon populations within the ESUs.
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Table 54. Maximum total ESA-listed natural-origin adult equivalents lost through competition and predation with juvenile hatchery fish by ESU/DPS compared to returning adults of respective ESU/DPS.
Percent Yearling Percent Subyearling Yearling Percent Subyearling Percentage Total Yearlings at AEs from subyearlings AEs from Percent AEs from Subyearlings AEs from of Lost Total Adults at McNary Release to at McNary Release to Yearlings McNary at Tongue McNary Adults to Listed Species (ESU/DPS) Lost Mouth of Dam McNary Dam McNary at Tongue Dam to Point Dam to Total AEs Columbia Dam Dam Point Tongue Tongue Adults at River Point Point Mouth Total 100 1085 100 45 100 367 100 991 2488 141,728 1.8 Snake River Spring/Summer 28 651 0 0 26 95 0 0 746 32,8233 2.3 Chinook Salmon ESU Snake River Fall Chinook 0 0 100 45 0 0 4 40 85 23,1984 0.4 Salmon ESU UCR Spring Chinook Chinook 72 1871 0 0 5 42 0 0 191 5,0645 3.8 Salmon Salmon ESU Lower Columbia 0 0 0 0 33 121 96 951 1,072 38,4646 2.8 River Chinook Salmon ESU Upper Willamette River Spring 0 0 0 0 36 132 0 0 132 9,3567 1.4 Chinook Salmon ESU Total 100 146 0 0 100 371 0 0 517 115,833 1.0 Snake River 11 15 0 0 47 174 0 0 189 54,4148 0.3 Steelhead DPS UCR Steelhead 45 66 0 0 6 22 0 0 88 6,9298 1.3 DPS Steelhead Middle Columbia 42 62 0 0 19 70 0 0 132 22,3008 0.6 Steelhead DPS Lower Columbia 0 0 0 0 19 70 0 0 70 22,0318 0.3 River Steelhead DPS
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Upper Willamette 0 0 0 0 9 33 0 0 33 10,1598 0.3 River Steelhead DPS Snake River Sockeye 100 4 0 0 100 11 0 0 15 1,6239 0.9 Salmon ESU Columbia River Chum 0 0 0 0 0 0 100 96 96 18,49810 0.5 Salmon ESU
Lower Columbia River 11 Coho Salmon ESU 0 0 0 0 100 468 0 0 468 267,060 0.2 1 We accounted for effects on the listed UCR Spring Chinook Salmon ESU from our model by applying the total Chinook adult equivalents to McNary from the UCR by the ratio of UCR spring Chinook salmon to UCR River summer Chinook salmon. This was calculated by summing the average total return (hatchery and natural) of UCR spring Chinook salmon (Table 8 of ODFW and WDFW 2016) and the total return of summer Chinook salmon (Table 10 of ODFW and WDFW 2016) from 2011-2015, and then dividing the total UCR spring Chinook return into this sum. We then applied this average proportion (0.24) of UCR spring Chinook to the total number of UCR Chinook salmon adult equivalents estimated to be lost from our model analysis (781). 2 We accounted for effects on the listed UCR Spring Chinook Salmon ESU from our model by applying the total Chinook adult equivalents from McNary to the mouth of Columbia River by applying the ratio of UCR spring Chinook salmon to UCR River summer Chinook salmon described above (0.24) to the total number of UCR Chinook salmon adult equivalents estimated to be lost from our model analysis (18). 3 This number was obtained by taking the average number of wild adult returns to the Columbia River from 2011 to 2015 from Table 9 of ODFW and WDFW (2016). 4 This number was obtained by taking the average number of adult returns to the Columbia River from 2011 to 2015 from Table 5 of WDFW and ODFW (2017). 5 This number was obtained by taking the average number of wild adult returns to the Columbia River from 2011 to 2015 from Table 8 of ODFW and WDFW (2016). 6 This number was obtained by taking the average of the sum of the estimated number of Lower Columbia River fall bright Chinook salmon, fall tule Chinook salmon, and spring/summer Chinook salmon for 2011 to 2015. The fall bright Chinook salmon numbers were obtained by summing the total natural spawner abundance estimates of each population from Tables 2.1.12 through 2.1.14 of TAC (2017) from 2011 to 2015. Then, we accounted for harvest impacts using LRH impact numbers of sport and commercial fisheries from the respective (Table 9 of TAC 2012; Table 12 of TAC 2013; Table 16 of TAC 2014; Table 17 of TAC 2015; Table 18 of TAC 2016). The fall tule Chinook salmon numbers were obtained from Table 4 of WDFW and ODFW (2017) by using the 2011 to 2015 actual return numbers for the Lower River Wild stock. The spring/summer Chinook salmon numbers were obtained by summing the total natural spawner abundance estimates of each population from Tables 2.1.10 and 2.1.11 of TAC (2017) from 2011 to 2015. Then, we accounted for harvest impacts using the total impact of the Upper Willamette River spring-run Chinook salmon fishery from the respective years (Table 88 of NMFS 2017d) as a surrogate. 7 This number was obtained by taking the average number of estimated natural-origin returns to the Columbia River mouth from 2011 to 2015. For each year, the natural-origin returns number was estimated by multiplying the projected spring Chinook run size by the percent of unmarked fish (100 minus total mark rate) obtained from http://www.dfw.state.or.us/fish/fish_counts/willamette/archives.asp, last accessed on October 30, 2017. 8 To obtain these numbers, we summed the total wild summer steelhead returns (Table 6 of WDFW and ODFW 2017) and total wild winter steelhead returns (Table 11 of ODFW and WDFW 2016) for 2011 to 2015, then applied the proportions of DPS obtained from Zabel (2013); Zabel (2014a); Zabel (2014b); Zabel (2015); Zabel (2017), described above. 9 This number was obtained by taking the average number of Snake River sockeye returns to the Columbia River from 2011 to 2015 from Table 18 of ODFW and WDFW (2016). 10 This number was obtained by taking the average number of total Colubmia River Chum abundance from Table 12 of WDFW and ODFW (2017). 11 This number was obtained by taking the average number of total coho salmon returns minus hatchery coho returns; Table 8 in WDFW and ODFW (2017).
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1 Another effect on natural-origin fish can result from released fish that residualize in a tributary. 2 Residual hatchery fish are those fish that do not emigrate following release from the hatchery. 3 These fish have the potential to compete with and prey on natural-origin juvenile fish for a 4 longer period of time relative to migrants. Residuals are not explicitly accounted for in our model 5 at this time. The ecological impacts of hatchery fish residualizing are likely to occur in the 6 tributaries, where natural-origin fish are rearing because residual fish would compete with or 7 prey on rearing fish. Conversely, residuals from programs that release into mainstem Columbia 8 River (i.e., Wells Hatchery summer/fall Chinook salmon, Priest Rapids fall Chinook salmon, and 9 Ringold Springs fall Chinook salmon programs) would not be expected to have any effect if they 10 stay in mainstem Columbia River; however, if they migrate to a tributary, they could also have 11 ecological effects on natural-origin fish. Because natural-origin summer/fall Chinook salmon 12 migrate as subyearlings migrate out as subyearlings, the risk that subyearlings released through 13 these hatchery programs remain to residualize and affect ESA-listed species is negligible. 14 15 For the proposed yearling programs, residual hatchery fish are likely to occur in proportions 16 larger than found in natural populations when the hatchery fish mature early (i.e., precocial 17 maturation). Harstad et al. (2017) examined the precocial maturation rate of the Chelan Falls, 18 Wenatchee (Dryden) and Methow (Carlton) yearling summer/fall Chinook salmon programs. 19 This study showed that the Chelan Falls program had an average of 19.1% minijack rates (early 20 male maturation rate) between 2007 and 2008, the Wenatchee program had an average of 17.3% 21 minijack rates between 2006 and 2009, and the Methow program had an average of 33.5% 22 minijack rates between 2006 and 2009. Another assessment was made in 2016 for these 23 programs that showed that the Chelan Falls summer/fall Chinook salmon, Wenatchee 24 summer/fall Chinook salmon, and Methow summer/fall Chinook salmon programs had 6.2 25 percent, 3.1 percent, and 10.1 percent male maturation rates, respectively (USFWS 2016). 26 Because hatchery practices have changed to minimize early maturation, it is likely that the 27 precocial maturation rate of current practices are within the range of 6.2-19.1% for the Chelan 28 Falls program, 3.1-17.3% for the Wenatchee program, and 10.1-33.5% for the Methow program. 29 There is no information available for the Wells program. 30 31 Because residuals are likely to occur as a subset of early mature fish, only a subset, if any, of 32 these hatchery fish would have residualized, though the extent is unknown. In addition, residuals 33 that linger around the release site may not encounter listed juvenile fish if the natural-origin 34 juvenile rearing occurs higher in the tributary than the release site. While females were not 35 sampled during this assessment, IDFG (2003) found that only a few females, if any, were found 36 to be precocially mature. NMFS recommends expanding this metric to include female samples in 37 the calculation; thus, the maximum average observed male maturation rate of 33% , combined 38 with only a few to no females maturation rates would equate to about a 15 percent potential 39 residualism rate. 40 41 Applicants have proposed actions, which are expected to minimize their ecological impacts, and 42 continue to improve their hatchery rearing practice to minimize early maturation. For example, 43 cold water is used, when available, to minimize rapid fish growth that tends to contribute to early 44 maturation. Some facilities also use circular tanks that allows more control over fish growth than 45 straight raceways because the vessels have higher flows than traditional raceways that allows the 46 fish to “exercise”, resulting in lower fat content of fish which results in lower rates of precocious 47 maturation.
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1 2 Naturally-produced progeny competition 3 Naturally spawning hatchery-origin summer/fall and fall Chinook salmon are likely to be less 4 efficient at reproduction than their natural-origin counterparts (Christie et al. 2014), but the 5 progeny of such hatchery-origin spawners are likely to make up a sizable portion of the juvenile 6 fish population. This is actually a desired result of the integrated recovery programs. Therefore, 7 added production could result in a density-dependent response of decreasing growth/mortality, 8 earlier migration due to high densities, and potential exceedance of habitat capacity. However, 9 ecological impacts on listed species may increase in the future if the summer/fall or fall Chinook 10 salmon populations grow. 11 12 Because summer/fall and fall Chinook salmon historically coexisted in substantial numbers with 13 listed salmon and steelhead in the Upper Columbia Basin, it follows that there must have been 14 adequate passage and habitat to allow both species to be productive and abundant. It does not 15 follow automatically, however, that the historical situation can be restored under present-day 16 conditions. In the short-term, we do not believe current densities are limiting natural-origin 17 salmon and steelhead production. Should the situation arise where steelhead natural production is 18 limiting spring Chinook salmon natural production, recovery planners would have to prioritize 19 one species over another. NMFS expects that the monitoring efforts would detect negative 20 impacts before they reach problematic levels, and we include language in the ITS (Section 2.9) 21 to ensure that appropriate monitoring takes place. 22 23 Disease 24 The risk of pathogen transmission to natural-origin salmon and steelhead is negligible for these 25 hatchery programs. This is because no detections of exotic pathogens have occurred in the last 26 three years and epidemics have all been caused by endemic pathogens with available treatments 27 (Table 55). Diseases that could be caused by pathogens outlined in Table 55 were treated 28 accordingly (e.g., medicated feed, formalin) (WDFW 2017b). 29 30 Table 55. Pathogens detections in summer/fall or fall Chinook salmon reared for the proposed 31 programs.
Program Pathogen Detected 2014 2015 2016 Priest Not Available Flavobacterium None Rapids Fall columnare Chinook Ringold Fall Not Available None None Chinook Wenatchee Fungus; None None Summer Flavobacterium Chinook psychrophilum Wells Ichthyophthirius Flavobacterium None Summer multifiliis psychrophilum Chinook
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Methow Fungus; Icthyobodo Icthyobodo spp; Fungus; Icthyobodo spp; Summer spp; bacterial gill bacterial gill disease bacterial gill disease Chinook disease Chelan Falls Fungus; None Fungus; bacterial gill Summer Flavobacterium disease; external parasites Chinook psychrophilum 1 2 3 Furthermore, to prevent outbreaks and reduce the amplification of IHNV in natural 4 environments, hatchery staff drain the coelomic fluid from females during spawning and treat 5 eggs with an iodophor solution, controlling, to some extent, the transmission of IHNV (IHOT 6 1995; NWIFC and WDFW 2006; ODFW 2003; Pacific Northwest Fish Health Protection 7 Committee (PNFHPC) 1989). Because of these preventative measures, no epidemics of IHNV 8 associated with these programs have occurred in recent years. Thus, NMFS believes the risk of 9 pathogen transmission to wild fish from hatchery fish and amplification of pathogens in the 10 natural environment is low. 11 12 Factor 4. Research, monitoring, and evaluation that exists because of the hatchery 13 program
14 NMFS has already evaluated the effects of a large portion of the research, monitoring and 15 evaluation (RM&E) for the summer/fall and fall Chinook salmon programs during consultations 16 for upper Columbia River spring Chinook salmon and steelhead programs (NMFS 2015a; NMFS 17 2016a; NMFS 2016 ). This is because RM&E for the summer/fall and fall Chinook salmon 18 programs is conducted opportunistically with hatchery programs that rear listed species. Thus, 19 our analysis here focuses only on those programs that specifically conduct RM&E on 20 summer/fall Chinook salmon as outlined in Table 56 and concludes that ESA-listed species are 21 not likely to be affected, as discussed below. 22 23 Table 56. RM&E associated with the hatchery programs in the Proposed Action. Activity Species Program Collection Site Timing Previously Evaluated? Smolt Summer/ Wenatchee; Methow trap Feb-Dec (Methow) Yes Traps fall Methow Twisp trap Mar-Nov (Twisp) Chinook Low Wen trap Feb-Oct (Low Wen) salmon Chiwawa trap Mar-Nov (Chiwawa)
Wells; No sampling N/A N/A Chelan Falls Fall Priest Rapids No sampling N/A N/A Chinook salmon Ringold No sampling N/A N/A Springs
Spawning/ Summer/ Wenatchee; Wenatchee; Sep-Nov No Carcass fall Methow; Methow and Surveys Chinook Chelan Falls Chelan Rivers salmon Wells No sampling N/A N/A
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Fall Priest Rapids; Hanford Reach Oct-Dec No Chinook Ringold Yakima River salmon Springs Wanapaum pool Priest Rapids pool 1 2 Many RM&E activities do not affect any ESA-listed species. Any tagging or clipping for these 3 programs occur on summer/fall and fall Chinook salmon, which are not listed species in the UCR 4 Basin. Also, no adult listed spring Chinook salmon are likely to be present when the spawning 5 and carcass surveys occur for these programs. Even if some listed species are present during 6 these activities (e.g., steelhead, rearing juveniles), the typical response of fish to spawning and 7 carcass survey is within the range of normal behaviors (i.e., startling response to a predator) and 8 would not adversely affect listed species. 9 10 Factor 5. Construction, operation, and maintenance of facilities that exist because 11 of the hatchery program
12 Best available information indicates that the most hatchery facility operations have no effect on 13 ESA-listed species, while the intake pipe at the Priest Rapids Hatchery may have negligible 14 effects on Upper Columbia River spring Chinook salmon and steelhead. As described below, we 15 assume that a maximum of 0.5 percent of outmigrating juvenile Upper Columbia River spring 16 Chinook salmon and steelhead are entrained into the Priest Rapids Hatchery. The analysis here 17 focuses on the effects on Upper Columbia River spring Chinook salmon and steelhead because 18 other ESA-listed species are not present in areas where hatchery facility operations could cause 19 an effect. 20 21 Table 57. Program facility and water use Program Facility Surface Ground Water Water Discharge Water Water Source Diversion Location (cfs) (cfs) Distance Chelan Falls Eastbank 0 55 Eastbank NA Columbia Summer/Fall Hatchery1 Aquifer River Chinook Program Chelan Falls 24 0 Chelan River 290 ft. Chelan Acclimation River Facility Wenatchee Dryden Pond 32.2 0 Wenatchee 135 ft. Wenatchee Summer/Fall River River Chinook Salmon2 Methow Carlton 7.5 total Methow 200 ft. Methow Summer/Fall Acclimation River River Chinook Salmon2 Pond Wells Hatchery Wells 150 38 Columbia ~650 ft. Columbia Summer/Fall Hatchery3 River River Chinook Salmon Priest Rapids Fall Priest Rapids 102 14 Columbia 2.2 RM Columbia Chinook Program Hatchery River River Ringold Springs Ringold Springs 70 0 Ringold NA (out of Columbia Hatchery Fall Rearing Facility Springs anadromy) River Chinook Salmon4 22 1 The operation of Eastbank Hatchery was analyzed in NMFS (2016a). 23 2 These programs also use Eastbank Hatchery for early rearing, which was analyzed in NMFS (2016a). 24 3 The operation of Wells Hatchery was analyzed in NMFS (2017e).
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1 4 This program also uses Bonneville Hatchery for early rearing. The operation of Bonneville Hatchery was analyzed 2 in NMFS (2017d). 3 4 As described in Table 57, the operation of some facilities have been analyzed in previous 5 consultations (NMFS 2016a; NMFS 2017d; NMFS 2017e). In addition, because Ringold Springs 6 fall Chinook salmon program does not withdraw water from anadromous water (i.e., ditches 7 designed to collect rain water, which do not allow natural-origin salmonid passage, are the 8 source of the hatchery water), there is no effect on ESA-listed salmonids as a result of 9 withdrawing water into the Ringold Springs Rearing Facility. Thus, we focus our analysis here 10 on the operation of Chelan Falls Acclimation Facility, Dryden Pond, Carlton Acclimation Pond, 11 and the Priest Rapids Hatchery, as well as the discharge from the Ringold Springs Rearing 12 Facility. 13 14 All of these facilities are appropriately screened and in compliance with NMFS criteria for their 15 intake pipes (Table 5) and are not likely to adversely affect ESA-listed salmonids through 16 impingement or entrainment, with the exception of the Priest Rapids Hatchery. The Priest Rapids 17 Hatchery has an intake screen that is not compliant with the NMFS screening criteria, though 18 Grant PUD (as the owner of the facility) has a plan to replace it to meet the NMFS screening 19 criteria (PUD 2009). 20 21 Currently, there are no good estimates of how many ESA-listed fish get entrained (if at all) into 22 the intake pipe at the Priest Rapids Hatchery. Thus, we will use the proportion of water intake 23 compared to the stream flow to estimate the proportion of fish that may get entrained as the fish 24 migrate downstream past the intake. While this estimate relies on many assumptions that are not 25 likely to reflect the reality12, it is the best available information we have. Because Upper 26 Columbia River spring Chinook salmon and steelhead outmigrate from March through June, we 27 focus our analysis on flows between March and June. The lowest flow and the average flow 28 between March 1 and June 30 of 2013-2017 was 20.6 kilo-cubic-feet-per-second (kcfs) on April 29 2, 2013, and 2014 and 202 kcfs, respectively (Kondo 2017a; Kondo 2017b), while the hatchery 30 would, at most, withdraw 102 cfs during this time. Using the average instream flow, the 31 proportion of the hatchery intake compared to the instream flow is 0.05 percent (102 divided by 32 202,000). The proportion of the hatchery intake compared to the minimum instream flow is 0.5 33 percent (102 divided by 20,600). Therefore, we expect that 0.5 percent of outmigrating juvenile 34 spring Chinook salmon and steelhead are entrained into the Priest Rapids Hatchery as the 35 maximum proportion. 36 37 These hatchery facilities also withdraw water from the river, which could affect Upper Columbia 38 River spring Chinook salmon or steelhead by reducing the flow. However, the proportion of 39 withdrawal compared to the amount of available instream flow are not at levels that 40 adverselyaffect any ESA-listed species for the programs described here (Table 58). Chelan Falls 41 Acclimation Facility draws its water from the Chelan Dam tailrace, located on the Chelan River,
12 For example, fish are typically not evenly distributed in the river. The intake pipe is located far from the main flow of the river where migrating juveniles are more likely to be encountered. In addition, Grant PUD has conducted numerous studies examining survival of steelhead, yearling Chinook salmon, and sockeye smolts in this area, including route specific assessments. None of the studies have indicated that smolts pass through, or even near-to, the siphon intake. Further, as there is no documented spawning of listed species in the Priest Rapids Pool, it is unlikely that fry would be present to be pulled into the siphon intake.
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1 so it does not reduce instream flow of Chelan River. In addition, the Chelan Dam tailrace has 2 water exchange or inflow from the Columbia River (the amount fluctuates), water from the 3 powerhouse (amount fluctuates), and from the Chelan River (80 cfs minimum), allowing the 4 tailrace pool to be maintained at approximately 3,857,300 cubic feet; the Chelan Falls 5 Acclimation Facility withdraws water at 24 cfs, which equates to about 2 percent of the tailrace 6 water being withdrawn per hour (24*60*60/3,857,300). Dryden Pond13 is likely to reduce at 7 most 3.9 percent of instream flow during March and April for 135 feet (i.e., the facility’s water 8 diversion distance). Similarly, Carlton Acclimation Pond is likely to reduce at most 3 percent of 9 instream flow from October through May for 200 feet. Priest Rapids Hatchery diverts water for a 10 longer distance (2.2 RM), but its water diversion would only withdraw at most 2.9 percent of the 11 flow, with over 3300 cfs of flow remaining in the river (Table 58). 12 13 Table 58. Facility water use compared to instream flow Facility Surface Period of Use Water Source Diversion Minimum Proportion of Water Distance Instream Flow Withdrawal Use (cfs) during Water compared to Use (cfs) Instream Flow Chelan Falls 24 Nov - April Chelan River 290 ft. NA1 NA Acclimation Facility Dryden Pond 32.2 March - April Wenatchee 135 ft. 8212 3.9% River Carlton 7.5 Oct - May Methow River 200 ft. 2533 3.0% Acclimation Pond Priest Rapids 102 Sept - June Columbia River 2.2 RM 35004 2.9% Hatchery 14 1 The Chelan Dam tailrace is a pool of water that does not have an instream flow. 15 2 This number was obtained from (USGS 2012), USGS Gage #12459000, by querying the flow between March 1 16 and April 30 of 2012-2015. This number (821 cfs) is from March 3, 2014. 17 3 This number was obtained from (USGS 2012), USGS Gage #12449500, by querying the flow between March 1 18 and April 30 of 2012-2015. This number (253 cfs) is from March 2, 2012. 19 4 Kondo (2017c). 20 21 All of the hatchery facilities listed above and the Ringold Springs Rearing Facility are either 22 operated under NPDES permits, or do not need a NPDES permit because rearing levels in the 23 acclimation pond are below permit minimums (Table 5). Facility effluent is monitored to ensure 24 compliance with permit requirements. Though compliance with NPDES permit conditions is not 25 an assurance that effects on ESA-listed salmonids will not occur, the facilities use the water 26 specifically for the purposes of rearing ESA-listed Chinook salmon and steelhead, which have a 27 low mortality during hatchery residence compared to survival in the natural-environment ( ~70 28 percent compared to 7 percent (Bradford 1995)). This suggests that the effects of effluent, which 29 is further diluted once discharged, will have a minimal impact on ESA-listed salmonids in the 30 area, as discussed below.
13 Dryden Pond withdraws its water from a canal that diverts water in from the Wenatchee River, upstream of the Pond. However, this canal is shared with other water users (e.g., irrigators), so the amount of water that enters the canal is not reflective of how much water is used by the operation of Dryden Pond. Therefore, we use the maximum water right that Chelan PUD has for Dryden Pond (i.e., 32.2 cfs) as the amount of water that is taken out of the Wenatchee River as a result of the proposed action.
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1 2 The total facility discharges proportionally small volumes of water with waste (predominantly 3 biological waste) into a larger water body, which results in temporary, very low or undetectable 4 levels of contaminants. General effects of various biological waste in hatchery effluent are 5 summarized in NMFS (2004a), though the biological waste is not likely to have a detectable 6 effect on listed species because of an abatement pond at Chelan Falls Acclimation Facility and 7 Priest Rapids Hatchery and other features at Dryden Pond, Carlton Acclimation Pond, and 8 Ringold Springs Rearing Facility that reduces the biological waste, as well as the small volume 9 of effluent compared to the stream flow. 10 11 Therapeutic chemicals used to control or eliminate pathogens (i.e., formaldehyde, sodium 12 chloride, iodine, potassium permanganate, hydrogen peroxide, antibiotics), can also be present in 13 hatchery effluent. However, these chemicals are not likely to be problematic for ESA-listed 14 species because they are quickly diluted beyond manufacturer’s instructions when added to the 15 total effluent and again after discharge into the recipient water body. Therapeutants are also used 16 periodically, and not constantly during hatchery rearing. In addition, many of them break down 17 quickly in the water and/or are not likely to bioaccumulate in the environment. For example, 18 formaldehyde readily biodegrades within 30 to 40 hours in stagnant waters. Similarly, potassium 19 permanganate would be reduced to compounds of low toxicity within several minutes. Aquatic 20 organisms are also capable of transforming formaldehyde through various metabolic pathways 21 into non-toxic substances, preventing bioaccumulation in organisms (EPA 2015). 22 23 Factor 6. Fisheries that exist because of the hatchery programs
24 There are no fisheries that exist because of the Proposed Action. The effects of fisheries that may 25 impact fish produced by these programs are described in Section 2.4.4. 26 27 Cumulative Effects
28 “Cumulative effects” are those effects of future state or private activities, not involving Federal 29 activities, that are reasonably certain to occur within the action area of the Federal action subject 30 to consultation (50 CFR 402.02). For the purpose of this analysis, the action area is that part of 31 the Columbia River Basin described in Section 1.4. To the extent ongoing activities have 32 occurred in the past and are currently occurring, their effects are included in the baseline 33 (whether they are Federal, state, tribal or private). This includes the impacts of other hatchery 34 programs in the action area that were included in the environmental baseline (Section 2.4). To 35 the extent those same activities are reasonably certain to occur in the future (and are tribal, state 36 or private), their future effects are included in the cumulative effects analysis. This is the case 37 even if the ongoing tribal, state or private activities may become the subject of section 38 10(a)(1)(B) incidental take permits in the future until an opinion for the take permit has been 39 issued. 40 41 State, tribal, and local governments have developed plans and initiatives to benefit listed species 42 and these plans must be implemented and sustained in a comprehensive manner for NMFS to 43 consider them “reasonably foreseeable” in its analysis of cumulative effects. Recovery Plans for 44 various species in the Columbia River Basin (NMFS 2009; NMFS 2013c; NMFS 2015b; NMFS 45 2015d; NMFS 2016c; NMFS and ODFW 2011; UCSRB 2007) are such plans and it describes, in
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1 detail, the on-going and proposed Federal, state, tribal, and local government actions that are targeted 2 to reduce known threats to ESA-listed salmon and steelhead in the Columbia River Basin. It is 3 acknowledged, however, that such future state, tribal, and local government actions would likely 4 be in the form of legislation, administrative rules, or policy initiatives, and land-use and other 5 types of permits, and that government actions are subject to political, legislative, and fiscal 6 uncertainties. 7 8 A full discussion of cumulative effects can also be found in the FCRPS Biological Opinion (NMFS 9 2008e) and the Mitchell Act Biological Opinion (NMFS 2017a), many of which are relevant to this 10 Action Area. It should be noted that the actions in the FCRPS Biological Opinion – the operation 11 of the Columbia River Federal Hydropower system – and the Mitchell Act biological opinion – 12 the operation of Columbia River hatchery programs – are included in the baseline for this 13 opinion. 14 15 The cumulative impacts from these programs contribute to the total impacts from hatcheries in 16 the entire Columbia River Basin, which is noted in the Mitchell Act Biological Opinion (NMFS 17 2017a). Between those programs which have already undergone consultation and those for which 18 consultation is underway, it is likely (though uncertain for ongoing consultations) that the type 19 and extent of salmon and steelhead hatchery programs and the numbers of fish released in the 20 Columbia River Basin will change over time. Although adverse effects will continue, these 21 changes are likely to reduce effects such as competition and predation on natural-origin salmon 22 and steelhead compared to current levels, especially for those species that are listed under the 23 ESA. This is because all salmon and steelhead hatchery programs funded and operated by non- 24 federal agencies and tribes in the Columbia River Basin have to undergo review under the ESA 25 to ensure that listed species are not jeopardized and that “take” under the ESA from salmon and 26 steelhead hatchery programs is minimized or avoided. Although adverse effects on natural-origin 27 salmon and steelhead will likely not be completely eliminated, effects would be expected to 28 decrease from current levels over time to the extent that hatchery programs are reviewed and 29 approved by NMFS under the ESA. Where needed, reductions in effects on listed salmon and 30 steelhead are likely to occur through changes in: 31 • Hatchery monitoring information and best available science 32 • Times and locations of fish releases to reduce risks of competition and predation 33 • Management of overlap in hatchery- and natural-origin spawners to meet gene flow 34 objectives 35 • Incorporation of new research results and improved best management practices for 36 hatchery operations
37 • More accurate estimates of natural-origin salmon and steelhead abundance for 38 abundance-based fishery management approaches 39 40 Some continuing non-Federal activities are reasonably certain to contribute to climate effects 41 within the action area. However, it is difficult, if not impossible, to distinguish between the 42 action area’s future environmental conditions caused by global climate change that are properly 43 part of the environmental baseline versus cumulative effects. Therefore, all relevant past, present 44 and future climate-related environmental effects in the action area are described together in the 45 environmental baseline section.
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1 2 These potential changes to hatchery operations across the region combined with the proposed 3 action result in a net improvement over current conditions. While the hatchery programs around 4 the basin, and those under review here as well, lead to negative impacts to listed salmonid 5 species as described above, when the beneficial changes to hatchery practices are also combined 6 with the potential negative impacts from these hatchery programs and the rest of the operations 7 in the Columbia River basin, a net beneficial result is expected as hatchery practices continue to 8 improve and to reduce their negative impacts. 9 10 Integration and Synthesis
11 The Integration and Synthesis section is the final step in our assessment of the risk posed to 12 species and critical habitat as a result of implementing the Proposed Action. In this section, 13 NMFS adds the effects of the Proposed Action (Section 2.4.2) to the environmental baseline 14 (2.3) and to cumulative effects (2.5) to formulate the agency’s opinion as to whether the 15 Proposed Action is likely to: (1) result in appreciable reductions in the likelihood of both 16 survival and recovery of the species in the wild by reducing its numbers, reproduction, or 17 distribution; or (2) reduce the value of designated or proposed critical habitat. This assessment is 18 made in full consideration of the status of the species and critical habitat and the status and role 19 of the affected population(s) in recovery (Sections 2.2.1, 2.2.2, and 2.2.3). 20 21 In assessing the overall risk of the Proposed Action on each species, NMFS considers the risks of 22 each factor discussed in Section 2.4.2., above, in combination, considering their potential 23 additive effects with each other and with other actions in the area (environmental baseline and 24 cumulative effects). This combination serves to translate the positive and negative effects posed 25 by the Proposed Action into a determination as to whether the Proposed Action as a whole would 26 appreciably reduce the likelihood of survival and recovery of the listed species and their 27 designated critical habitat. 28 29 UCR Spring Chinook Salmon ESU
30 Best available information indicates that the UCR Spring Chinook Salmon ESU is at high risk 31 and remains Endangered (NWFSC 2015). After taking into account the current viability status of 32 these species, the Environmental Baseline, and other pertinent cumulative effects, including any 33 anticipated Federal, state, or private projects, NMFS concludes that the effects of the Proposed 34 Action will not appreciably reduce the likelihood of survival and recovery of this ESA-listed 35 ESU. 36 37 Our environmental baseline analysis considers the effects of hydropower, changes in habitat 38 (both beneficial and adverse), fisheries, and hatcheries on these ESUs. Although all may have 39 contributed to the listing of these ESUs, all factors have also seen improvements in the way they 40 are managed/operated. As we continue to deal with a changing climate, management of these 41 factors may also alleviate some of the potential adverse effects (e.g., hatcheries serving as a 42 genetic reserve for natural populations). 43 44 The effects of our proposed action on this ESU beyond those included in the baseline are limited 45 to ecological effects, broodstock collection at Chelan Falls Trap, and facilities effect of the Priest
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1 Rapids Hatchery’s intake. Adverse ecological effects on adults are small because of the 2 differences in spatial and temporal overlap between UCR spring Chinook salmon and the 3 hatchery-origin adults. However, natural-origin juveniles may potentially undergo larger effects 4 because of the overlap in outmigration timing with the hatchery-origin juveniles. Our analysis 5 showed that the impacts of these programs could equate up to a loss of 799 salmon adult 6 equivalents from the ESU, which constitutes 2.1 percent of returning adults from this ESU at the 7 mouth of the Columbia River. Because the model differentiates fish by size and not by run 8 timing, these 799 adult equivalents could also include the unlisted summer/fall Chinook salmon 9 as well. 10 11 The effect of broodstock collection from the summer/fall Chinook salmon programs are also 12 small. The Chelan Falls Trap could encounter up to 10 unidentified Chinook salmon that may 13 potentially be spring Chinook salmon, but many of these encounters are likely to be summer/fall 14 Chinook salmon rather than spring Chinook salmon; none of these encounters would result in 15 mortality. Thus, there is very little incidental effect on the UCR Spring Chinook Salmon ESU. 16 17 The negative effect of operating the Priest Rapids Hatchery is limited to the entrainment that 18 may be occurring because of an intake screen that is not compliant with the NMFS screening 19 criteria. Because there are no good estimates of how many ESA-listed fish get entrained (if at 20 all), we extrapolate from the diversion of flow that 0.5 percent of outmigrating juvenile UCR 21 spring Chinook salmon are entrained into the Priest Rapids Hatchery. 22 23 The total impacts on the UCR Spring Chinook ESU as a result of the Proposed Action would be 24 the loss of an estimated 3.8% of adult equivalents from ecological interactions during juvenile 25 outmigration, and a loss of approximately 0.5% of outmigrating juveniles at the Priest Rapids 26 hatchery water intake. The effect of these losses would be to reduce the abundance and 27 productivity of the ESU. While up to 10 spring Chinook salmon are expected to be encountered 28 at the Chelan Falls Trap, none of these encounters would result in mortality from handling. As 29 described in Section 2.2.1.6, above, all three remaining populations in this ESU are at High risk, 30 while the Okanogan population is extirpated. For each of the High-risk populations, current 31 abundances are well below minimum abundance thresholds, and productivities are well below 32 replacement (1.0) with the exception of the Entiat River population (Table 8). NMFS expects 33 that, because the impacts of the Proposed Action on this ESU would accrue during downstream 34 migration, the effects of the Proposed Action would apply proportionally to the three 35 populations. Therefore, each population would be expected to lose approximately 4.3% of the 36 outmigrating juvenile abundance as a result of the Proposed Action. This 4.3% loss would not be 37 large enough to have a marked effect on the abundance or productivity of any of the populations. 38 In addition, as described in Section 2.5.2.3, the actual predation and competition effects may be 39 smaller to an unknown extent than those modeled, though even the conservative assessment of 40 effects utilized in this Opinion does not suggest an extensive risk to the species. Taken together, 41 NMFS has determined that the level of impact on abundance and, therefore, productivity, of the 42 Proposed Action would not appreciably reduce the likelihood of survival and recovery of this . 43 ESU. 44 45 Added to the Species’ Status, Environmental Baseline, and effects of the Proposed Action are the 46 effects of future state, private, or tribal activities, not involving Federal activities, within the
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1 Action Area. The recovery plans for the ESU describe the on-going and proposed state, tribal, 2 and local government actions that are targeted to reduce known threats to ESA-listed steelhead. 3 Such actions are improving habitat conditions, and hatchery and harvest practices to protect 4 listed salmon ESU. NMFS expects this trend to continue and could lead to increases in 5 abundance, productivity, spatial structure and diversity. 6 7 After taking into account the current viability status of these species, the Environmental 8 Baseline, and other pertinent cumulative effects, including any anticipated Federal, state, or 9 private projects, NMFS concludes that the small effects of the Proposed Action on abundance, 10 productivity, spatial structure, and diversity, will not appreciably reduce the likelihood of 11 survival and recovery of these ESA-listed ESU in the wild. 12 13 UCR Steelhead DPS
14 Best available information indicates that the Snake River Steelhead DPS is at high risk and 15 remains at threatened status (Ford 2011). Ford (2011) determined that all populations remain 16 below minimum natural-origin abundance thresholds. In addition, the biological review team 17 identified the lack of direct data on spawning escapements and pHOS in the individual 18 population tributaries as a key uncertainty, rendering quantitative assessment of viability for the 19 DPS difficult (Ford 2011). Still, after taking into account the current viability status of these 20 species, the Environmental Baseline, and other pertinent cumulative effects, including any 21 anticipated Federal, state, or private projects, NMFS concludes that the effects of the Proposed 22 Action will not appreciably reduce the likelihood of survival and recovery of the ESA-listed DPS 23 in the wild. 24 25 Our environmental baseline analysis considers the effects of hydropower, changes in habitat 26 (both beneficial and adverse), fisheries, and hatcheries on this DPS. Although all may have 27 contributed to the listing, all factors have also seen improvements in the way they are 28 managed/operated. As we continue to deal with a changing climate, management of these factors 29 may also alleviate some of the potential adverse effects (e.g., through hatcheries serving as a 30 genetic reserve for natural populations). 31 32 The effects of our proposed action on this DPS beyond those included in the baseline are limited 33 to ecological effects, broodstock collection at Priest Rapids volunteer trap and at Ringold Springs 34 Rearing Facility, and facilities effect of the Priest Rapids Hatchery’s intake. No adverse 35 ecological effects on adults are expected because of the differences in spatial and temporal 36 overlap between UCR steelhead and the hatchery-origin adults. However, natural-origin 37 juveniles may potentially experience a negative effect because of the overlap in outmigration 38 timing with the hatchery-origin juveniles. Our analysis showed that the impacts of these 39 programs equates to a loss of 88 steelhead adult equivalents from the DPS, which constitutes 1.3 40 percent of returning adults from this DPS at the mouth of the Columbia River. 41 42 The effect of broodstock collection from the fall Chinook salmon programs are also small. The 43 Priest Rapids volunteer trap could encounter up to 15 steelhead (as identified by no external 44 marking or ad-clip only), none of which would likely result in mortality. The Ringold Springs 45 Rearing Facility could encounter up to five steelhead, none of which would result in mortality. 46 Thus, there is little to no effect on the UCR Steelhead DPS as a result of broodstock collection.
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1 2 The negative effect of operating the Priest Rapids Hatchery is limited to the entrainment that 3 may be occurring because of an intake screen that is not compliant with the NMFS screening 4 criteria. Because there are no good estimates of how many ESA-listed fish get entrained (if at 5 all), we assume that 0.5 percent of outmigrating juvenile UCR steelhead are entrained into the 6 Priest Rapids Hatchery. 7 8 The total impacts on the UCR Steelhead DPS as a result of the Proposed Action would be the 9 loss an estimated 1.3% of adult equivalents from ecological interactions during juvenile 10 outmigration and a loss of approximately 0.5% of outmigrating juveniles at the Priest Rapids 11 hatchery water intake. The effect of these losses would be to reduce the abundance and 12 productivity of the DPS. As described in Section 2.2.1.6, above, three of the four populations in 13 this DPS are at High risk, while the Wenatchee population is rated Maintained. For each of the 14 High-risk populations, current abundances are well below minimum abundance thresholds, and 15 productivities are well below replacement (1.0) (Table 17). NMFS expects that, because the 16 impacts of the Proposed Action on this DPS would accrue during downstream migration, the 17 effects of the Proposed Action would apply proportionally to the four populations. Therefore, 18 each population would be expected to lose approximately 1.8% of the outmigrating juvenile 19 abundance as a result of the Proposed Action. This 1.8% loss would not be large enough to have 20 a marked effect on the abundance or productivity of any of the populations. In addition, as 21 described in Section 2.5.2.3, the actual predation and competition effects may be smaller to an 22 unknown extent than those modeled, though even the conservative assessment of effects utilized 23 in this Opinion does not suggest an extensive risk to the species. Taken together, NMFS has 24 determined that the level of impact on abundance and, therefore, productivity, of the Proposed 25 Action would not appreciably reduce the likelihood of survival and recovery of this DPS. 26 27 Added to the Species’ Status, Environmental Baseline, and effects of the Proposed Action are the 28 effects of future state, private, or tribal activities, not involving Federal activities, within the 29 Action Area. The recovery plans for each DPS describe the on-going and proposed state, tribal, 30 and local government actions that are targeted to reduce known threats to ESA-listed steelhead. 31 Such actions are improving habitat conditions, and hatchery and harvest practices to protect 32 listed steelhead DPSs. NMFS expects this trend to continue and could lead to increases in 33 abundance, productivity, spatial structure and diversity. 34 35 After taking into account the current viability status of these species, the Environmental 36 Baseline, and other pertinent cumulative effects, including any anticipated Federal, state, or 37 private projects, NMFS concludes that the small effects of the Proposed Action on abundance, 38 productivity, spatial structure, and diversity, will not appreciably reduce the likelihood of 39 survival and recovery of these ESA-listed DPS in the wild. 40 41 Snake River ESUs/DPS, Mid-Columbia River Steelhead DPS, Columbia River 42 Chum Salmon ESU, Lower Columbia River ESUs/DPS, and Upper Willamette River 43 ESU/DPS
44 Best available information indicates that the Snake River Spring/Summer Chinook, Fall 45 Chinook, and Sockeye Salmon ESUs, Snake River Steelhead DPS, Mid-Columbia River 46 Steelhead DPS, Columbia River Chum Salmon ESU, Lower Columbia River Chinook and Coho
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1 Salmon ESUs, Lower Columbia River Steelhead DPS, Upper Willamette River Spring Chinook 2 Salmon ESU, and Upper Willamette River Steelhead DPS are all at high risk and remain 3 threatened. The Snake River Sockeye Salmon ESU is at high risk and remains endangered 4 (NWFSC 2015). After taking into account the current viability status of these species, the 5 Environmental Baseline, and other pertinent cumulative effects, including any anticipated 6 Federal, state, or private projects, NMFS concludes that the effects of the Proposed Action will 7 not appreciably reduce the likelihood of survival and recovery of these ESA-listed ESUs and 8 DPSs in the wild. 9 10 Our environmental baseline analysis considers the effects of hydropower, changes in habitat 11 (both beneficial and adverse), fisheries, and hatcheries on these species. Although all may have 12 contributed to the listing of these species, all factors have also seen improvements in the way 13 they are managed/operated. As we continue to deal with a changing climate, management of 14 these factors may also alleviate some of the potential adverse effects (e.g., hatcheries serving a 15 genetic reserve for natural populations). 16 17 The effects of our proposed action on these ESUs and DPSs are limited to ecological effects 18 from hatchery-origin juvenile fish because of the overlap in outmigration timing. The results of 19 our analysis are summarized in Table 59. Impacts of these programs equates to a loss ranging 20 from 15 sockeye salmon adult equivalents from the Snake River Sockeye Salmon ESU to 1,072 21 Chinook salmon adult equivalents from the Lower Columbia River Chinook Salmon ESU. These 22 impacts are also characterized as a proportion of lost adults compared to the total returning adults 23 from each ESU/DPS at the mouth of the Columbia River, ranging from 0.2 percent for the Lower 24 Columbia River Coho Salmon ESU to 2.7 percent for the Lower Columbia River Chinook 25 Salmon ESU. The small percentage loss within these ESU and DPS is unlikely to substantially 26 affect the abundance and productivity of these natural-origin fish in the Columbia River Basin. 27 28 Table 59. Lost natural-origin adult equivalents compared to returning adults from each ESU/DPS 29 at the mouth of the Columbia River.
Total Lost Proportion of Lost Adults Species (ESU/DPS) Adult to Total Returning Adults Equivalents from ESU/DPS (%) Snake River Spring/Summer 746 2.3 Chinook Salmon ESU Snake River Fall Chinook Salmon 85 0.4 Chinook ESU Salmon Lower Columbia River Chinook 1,072 2.8 Salmon ESU Upper Willamette River Spring 132 1.4 Chinook Salmon ESU Snake River Steelhead DPS 189 0.3 Middle Columbia Steelhead DPS 132 0.6 Steelhead Lower Columbia River Steelhead 70 0.3 DPS Upper Willamette River Steelhead 33 0.4 DPS
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Snake River Sockeye Salmon ESU 15 0.9 Columbia River Chum Salmon ESU 96 0.5 Lower Columbia River Coho Salmon ESU 468 0.2 1 2 Added to the Species’ Status, Environmental Baseline, and effects of the Proposed Action are the 3 effects of future state, private, or tribal activities, not involving Federal activities, within the 4 Action Area. The recovery plans for each ESU and DPS describe the on-going and proposed 5 state, tribal, and local government actions that are targeted to reduce known threats to ESA-listed 6 steelhead. Such actions are improving habitat conditions, and hatchery and harvest practices to 7 protect listed salmon ESUs and steelhead DPSs. NMFS expects this trend to continue and could 8 lead to increases in abundance, productivity, spatial structure and diversity. 9 10 After taking into account the current viability status of these species, the Environmental 11 Baseline, and other pertinent cumulative effects, including any anticipated Federal, state, or 12 private projects, NMFS concludes that the small effects of the Proposed Action on abundance, 13 productivity, spatial structure, and diversity, will not appreciably reduce the likelihood of 14 survival and recovery of these ESA-listed ESUs and DPSs in the wild. 15 16 Critical Habitat
17 Only the PBFs for UCR spring Chinook salmon and UCR steelhead are likely to be affected 18 from the proposed action. The hatchery water diversion and the discharge pose a negligible 19 effect on designated critical habitat for UCR spring Chinook salmon and UCR steelhead in the 20 action area (Section 2.5.2.5). Existing hatchery facilities have not contributed to altered channel 21 morphology and stability, reduced and degraded floodplain connectivity, excessive sediment 22 input, or the loss of habitat diversity. The operation of the traps and other hatchery facilities may 23 impact only the migration PBFs for UCR spring Chinook salmon and UCR steelhead due to 24 delay at these structures and possible rejection. However, the number of natural-origin adults 25 delayed is expected to be small and the delay would be for only a short period. Thus, the impact 26 on the spawning, rearing, and migration PBFs of UCR spring Chinook salmon and UCR 27 steelhead will be small in scale, and will not appreciably diminish the capability of the critical 28 habitat to satisfy the essential requirements of the species. 29 30 Climate change may have some effects on critical habitat as discussed in Section 2.4.2. With 31 continued losses in snowpack and increasing water temperatures, it is possible that increases in 32 the density and residence time of fish using cold-water refugia could result in increases in 33 ecological interactions between hatchery and natural-origin fish of all life stages, with unknown, 34 but likely small effects. The continued restoration of habitat may also provide additional refugia 35 for fish. After reviewing the Proposed Action and conducting the effects analysis, NMFS has 36 determined that the Proposed Action will not alter PBFs essential to the conservation of a species 37 or preclude or significantly delay development of such features. 38 39 Conclusion
40 After reviewing the current status of the listed species, the environmental baseline within the 41 action area, the effects of the Proposed Action, including effects of the Proposed Action that are 42 likely to persist following expiration of the Proposed Action, and cumulative effects, it is NMFS’
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1 biological opinion that the Proposed Action is not likely to jeopardize the continued existence or 2 recovery of any of the ESUs and DPSs listed in the Columbia River Basin (Table 7), or destroy 3 or adversely modify designated critical habitat.
4 Table 60. Summary of NMFS determination of effects.
ESA-Listed Species Is the Action Is the Action Is the Action Is the Action Likely to Adversely Likely to Likely To Likely To Affect Species? Adversely Jeopardize the Destroy or Affect Critical Species? Adversely Habitat? Modify Critical Habitat? Upper Columbia River Spring Yes Yes No No Chinook salmon Snake River Spring/Summer Yes No No No Chinook salmon Snake River Fall Chinook Yes No No No salmon Lower Columbia River Yes No No No Chinook salmon Upper Willamette River Spring Yes No No No Chinook salmon Upper Columbia River Yes Yes No No steelhead Snake River steelhead Yes No No No Middle Columbia River Yes No No No steelhead Lower Columbia River Yes No No No steelhead Upper Willamette River Yes No No No steelhead Snake River sockeye salmon Yes No No No Columbia River chum salmon Yes No No No Lower Columbia River coho Yes No No No salmon 5
6 Incidental Take Statement
7 Section 9 of the ESA and Federal regulation pursuant to section 4(d) of the ESA prohibit the take 8 of endangered and threatened species, respectively, without a special exemption. Take is defined 9 as to harass14, harm, pursue, hunt, shoot, wound, kill, trap, capture or collect, or to attempt to
14 NMFS recognizes the benefit of providing guidance on the interpretation of the term "harass". As a first step, for use on an interim basis, NMFS will interpret harass in a manner similar to the USFWS regulatory definition for non- captive wildlife: “Create the likelihood of injury to wildlife by annoying it to such an extent as to significantly disrupt normal behavioral patterns which include, but are not limited to, breeding, feeding, or sheltering.” NMFS interprets the phrase “significantly disrupt normal behavioral patterns” to mean a change in the animal’s behavior (breeding, feeding, sheltering, resting, migrating, etc.) that could reasonably be expected, alone or in concert with other factors, to create or increase the risk of injury to an [ESA-listed] animal when added to the condition of the
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1 engage in any such conduct. Harm is further defined by regulation to include significant habitat 2 modification or degradation that results in death or injury to listed species by significantly 3 impairing essential behavioral patterns, including breeding, feeding, or sheltering (50 CFR 17.3). 4 Incidental take is defined as take that is incidental to, and not the purpose of, the carrying out of 5 an otherwise lawful activity. Section 7(b)(4) and section 7(o)(2) provide that taking that is 6 incidental to an otherwise lawful agency action is not prohibited under the ESA, if that action is 7 performed in compliance with the terms and conditions of the ITS. 8 9 Amount or Extent of Take
10 NMFS expects incidental take of ESA-listed steelhead and Chinook salmon will occur as a result 11 of the proposed action for the following factors. Take as a result of Factor 1 does not apply here, 12 as none of the ESA-listed salmon and steelhead species affected here are explicitly targeted for 13 broodstock collection—incidental take of these species take during collection of target fish for 14 broodstock is addressed under Factor 2. 15 16 Factor 2: Hatchery fish and the progeny of naturally spawning hatchery fish on spawning 17 grounds and encounters with natural-origin and hatchery fish at adult collection facilities 18 At the Chelan Falls Trap, up to 10 unidentified Chinook salmon are expected to be handled each 19 year, all of which could be ESA-listed Upper Columbia River spring Chinook salmon, and none 20 of which would die as a result of handling. 21 22 At the Priest Rapids volunteer trap, up to 15 ESA-listed Upper Columbia River steelhead could 23 be taken by handling (as identified by no external marking or with ad-clip only) annually, of 24 which up to 3 could die as a result of handling. 25 26 At the Ringold Springs Rearing Facility, up to 5 ESA-listed Upper Columbia River steelhead 27 could be encountered annually, none of which would die as a result of handling. 28 29 Factor 3: Hatchery fish and the progeny of naturally spawning hatchery fish in juvenile 30 rearing areas and the migratory corridor 31 Predation and competition (collectively referred to as ecological interactions for the purposes of 32 this opinion) between natural-origin juvenile salmon and steelhead and hatchery summer/fall and 33 fall Chinook salmon smolts could result in take of natural-origin salmon and steelhead. However, 34 it is difficult to quantify this take because ecological interactions cannot be directly or reliably 35 measured and/or observed. Thus, we will monitor ecological effects using two different 36 surrogates, one specifically addressing residualism of hatchery steelhead and the second related 37 to how quickly hatchery summer/fall and fall Chinook salmon leave the system. 38 39 For residualism, the take surrogate is the percentage of summer/fall and fall Chinook salmon 40 from the yearling release group that are observed to be either parr, precociously maturing, or 41 precociously mature prior to release. This surrogate has a causal link to the amount of take 42 expected from residualism because precocious summer/fall and fall Chinook salmon and parr
exposed animal before the disruption occurred. See Weiting (2016) for more information on the interim definition of “harass.”
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1 may residualize after release from the hatchery. This take surrogate covers the take pathway 2 whereby the residual hatchery fish potentially compete with or prey on juvenile natural-origin 3 fish for an extended period of time. NMFS considers, for the purpose of this take surrogate, that 4 no more than 15 percent of program fish from each release group should be observed as having 5 the potential to residualize. The take surrogate can be monitored using a running five-year 6 average beginning with the 2018 release15 by either of the following methods: 1) lethal visual 7 assessment that would look for precocial mature fish; or 2) non-lethal visual assessment that 8 would look for precocial mature male and parr (as defined by the unlikelihood of it smolting; i.e., 9 if there is any indication that it would smolt, it would not be considered a parr). For the second 10 method, the nonlethal visual assessments are likely to detect a lower rate of potentially 11 residualizing fish, adding parr to the sampling would lead to a higher detection rate than visually 12 assessing for precocially mature males alone. The take surrogate can be reliably measured and 13 monitored through either methods of visual assessment of the hatchery population and/or migrant 14 fish prior to release, both of which NMFS considers to be an effect method of monitoring. 15 16 For ecological effects of competition and predation caused by emigrating hatchery summer/fall 17 and fall Chinook salmon, NMFS applies a take surrogate that relates to the median travel time 18 for hatchery fish to reach McNary Dam after release. Specifically, the extent of take from 19 interactions between hatchery and natural-origin juvenile salmonids through the estuary are 20 measured as follows: the travel time for emigrating juvenile hatchery steelhead is five days 21 longer than the median value (which equates to 50% of the fish) identified in Table 49 for each 22 program for 3 of the previous 5 years of 5-year running medians. For example, if the 5-year 23 running median of the median value in Table 49 is 20, and then the median for the next three 24 years for a particular release group is 23, this would exceed the take threshold. This surrogate has 25 a causal link to the extent of incidental take because, if travel time increases in more years than 26 not, it is a sign that fish are not exiting the action area as quickly as expected, and that the 27 recurring increase in time indicates that the issue is not related to a single external factor but to a 28 more fundamental change in migration timing. This threshold can be reliably monitored using 29 emigration estimates from PIT tags though NMFS expects the operators to develop additional 30 juvenile monitoring techniques during the proposed action. 31 32 Factor 5: Operation of facilities that exist because of the hatchery program 33 Use of the intake pipe at the Priest Rapids Hatchery could cause incidental take of listed juvenile 34 ESA-listed Upper Columbia River spring Chinook salmon and steelhead through entrainment. 35 However, it is not practical to quantify and track the number of these ESA-listed juvenile fish 36 entrained by the intake pipe because no methods are available to observe or record fish 37 encountering the intake. However, it is possible to estimate the number of individuals 38 encountering the intake and, therefore, being killed through entrainment by estimating the 39 proportion of river flow that is withdrawn at the intake and assuming the proportion of the run of 40 the given species is similar. Therefore, NMFS will designate, as a surrogate take indicator, the 41 proportion of the flow at any given time that is withdrawn by the hatchery. This surrogate has a 42 rational connection to the take of the listed species because the proportion of fish affected 43 correlates to the proportion of flow diverted (and, as discussed above, likely yields an
15 However, if it is apparent, from numbers observed in years prior to the fifth year, that the average is certain to exceed 5 percent after five years, operators will contact NMFS in the year the likely exceedance is discovered.
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1 overestimate of take). Take will be considered exceeded for entrainment at the intake pipe if 2 more than 0.5 percent of the river’s flow as measured downstream of the Wanapaum Dam 3 (upriver from the intake pipe) is withdrawn at the intake pipe during juvenile migration periods. 4 The instream flow can be reliably monitored by a gauge downstream of the Wanapaum Dam. 5 6 Effect of the Take
7 In Section 2.8, NMFS determined that the level of anticipated take, coupled with other effects of 8 the Proposed Action, is not likely to jeopardize the continued existence of the Upper Columbia 9 River Spring Chinook Salmon ESU, and Upper Columbia River Steelhead DPS or result in the 10 destruction or adverse modification of their designated critical habitat.
11 Reasonable and Prudent Measures
12 “Reasonable and prudent measures” are nondiscretionary measures to minimize the amount or 13 extent of incidental take (50 CFR 402.02).
14 NMFS concludes that the following reasonable and prudent measures are necessary and 15 appropriate to minimize incidental take. NMFS and the USACE shall ensure that: 16 17 1. The applicants implement the hatchery programs and operate the hatchery facilities as 18 described in the Proposed Action (Section 1.3) and in the submitted HGMPs. 19 2. The applicants provide reports to SFD annually for all hatchery programs, and associated 20 RM&E. 21 22 Terms and Conditions
23 The terms and conditions described below are non-discretionary, and NMFS must comply with 24 them in order to implement the reasonable and prudent measures (50 CFR 402.14). Action 25 Agencies have a continuing duty to monitor the impacts of incidental take and must report the 26 progress of the action and its impact on the species as specified in this incidental take statement 27 (50 CFR 402.14). If the entity to whom a term and condition is directed does not comply, NMFS 28 would consider whether it is necessary to reinitiate consultation. 29 30 The USACE shall ensure for the Ringold Springs fall Chinook salmon program and their portion 31 of the Priest Rapids fall Chinook salmon program that:
32 1.a. The applicants implement the hatchery program as described in the Proposed Action 33 (Section 1.3) and in the submitted HGMPs, including: 34 i. Providing advance notice to NMFS of any change in hatchery program 35 operation (including early releases) that potentially increases the amount or 36 extent of take, or results in an effect of take not previously considered. 37 ii. Providing notice if monitoring reveals an increase in the amount or extent 38 of take, or discovers an effect of the Proposed Action not considered in this 39 opinion.
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1 iii. Allowing NMFS to accompany any employee or representative field 2 personnel while they conduct activities covered by their biological opinion. 3 4 1.b. The applicants implement application of at least the minimum number of PIT-tags for 5 the Ringold Springs fall Chinook salmon program that would adequately track the 6 program’s hatchery-origin fish emigration time. The USACE shall secure funding for 7 this monitoring starting with the next available fiscal year budget submittal (2020), 8 and the applicants shall implement this monitoring thereafter. If USACE cannot 9 secure the funding, the USACE shall notify NMFS. 10 2. The applicants provide reports to NMFS SFD annually for all hatchery programs, and 11 associated RM&E. 12 i. All reports/notifications be submitted electronically to the NMFS SFD 13 point of contact for this opinion: Emi Kondo (503) 736-4739, 14 [email protected]. 15 ii. Applicants will notify NMFS SFD within 48 hours after knowledge of 16 exceeding any authorized take, and shall submit a written report detailing 17 why the authorized take was exceeded within two weeks of the event. 18 iii. Applicants will include the reporting information detailed in the WDFW’s 19 section 10 permits in their reports. 20 21 NMFS shall include in the section 10 permits conditions that:
22 1a. The applicants implement the Chelan Falls, the Wenatchee, the Methow, and the 23 Wells summer/fall Chinook salmon programs and the Priest Rapids fall Chinook 24 salmon program as described in the Proposed Action (Section 1.3) and the submitted 25 HGMPs, including: 26 i. Providing advance notice to NMFS of any change in hatchery program 27 operation that potentially increases the amount or extent of take, or results 28 in an effect of take not previously considered. 29 ii. Providing notice if monitoring reveals an increase in the amount or extent 30 of take, or discovers an effect of the Proposed Action not considered in 31 this opinion. 32 iii. Allowing NMFS to accompany any employee or representative field 33 personnel while they conduct activities covered by their biological 34 opinion. 35 1.b. Douglas PUD shall fund and the applicants shall implement monitoring with a 36 minimum of 5,000 PIT-tags per life-stage for the Wells Hatchery summer/fall 37 Chinook salmon program. 38 39 1.c. Grant PUD shall coordinate with NMFS environmental service branch to conduct a 40 review of The Priest Rapids Hatchery Siphon Intake Screen Upgrade Concept Study 41 to ensure compliance with the screening criteria. Grant PUD shall notify NMFS SFD 42 if the project becomes designated as lower priority than 2-2 or if it is not funded by 43 the end of calendar year 2024. 44
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1 1.d. Grant PUD shall monitor and report annually the percentage of water withdrawal 2 compared to the instream flow at the Priest Rapids Hatchery until the NMFS 3 screening criteria compliant intake screen is installed at the Priest Rapids Hatchery. 4 5 2. The applicants provide reports to NMFS SFD annually for all hatchery programs, and 6 associated RM&E. 7 a. All reports/notifications be submitted electronically to the NMFS SFD point of 8 contact for this opinion: Emi Kondo (503) 736-4739, [email protected]. 9 b. Applicants will notify NMFS SFD within 48 hours after exceeding any authorized 10 take, and shall submit a written report detailing why the authorized take was 11 exceeded within two weeks of the event. 12 c. Applicants will include the reporting information detailed in their section 10 13 Permit in their reports. 14 15 Conservation Recommendations
16 Section 7(a)(1) of the ESA directs Federal agencies to use their authorities to further the 17 purposes of the ESA by carrying out conservation programs for the benefit of threatened and 18 endangered species. Specifically, conservation recommendations are suggestions regarding 19 discretionary measures to minimize or avoid adverse effects of a Proposed Action on listed 20 species or critical habitat (50 CFR 402.02). NMFS has identified one conservation 21 recommendation appropriate to the Proposed Action: 22 23 1. Implement pHOS goals as described in submitted HGMPs. 24 25 Re-initiation of Consultation
26 This concludes formal consultation on the approval and implementation of four hatchery 27 programs rearing and releasing summer/fall Chinook salmon and two hatchery programs rearing 28 and releasing fall Chinook salmon in the UCR Basin. 29 As 50 CFR 402.16 states, re-initiation of formal consultation is required where discretionary 30 Federal agency involvement or control over the action has been retained or is authorized by law 31 and if: (1) The amount or extent of incidental taking specified in the ITS is exceeded, (2) new 32 information reveals effects of the agency action that may affect listed species or critical habitat in 33 a manner or to an extent not considered in this opinion, (3) the agency action is subsequently 34 modified in a manner that causes an effect on the listed species or critical habitat that was not 35 considered in this opinion, or (4) a new species is listed or critical habitat designated that may be 36 affected by the action. 37 38 “Not Likely to Adversely Affect” Determinations
39 The applicable standard to find that a Proposed Action is “not likely to adversely affect” ESA 40 listed species or critical habitat is that all of the effects of the action are expected to be either 41 discountable or insignificant, or the action is expected to be wholly beneficial (USFWS and 42 NMFS 1998). Beneficial effects are contemporaneous positive effects without any adverse 43 effects on the species. Insignificant effects relate to the size of the impact and should never reach
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1 the scale where take occurs. Discountable effects are extremely unlikely to occur. NMFS has 2 determined that the Proposed Action may affect, but is not likely to adversely affect, the Green 3 Sturgeon Southern DPS, the Southern Resident Killer Whale DPS, and the southern DPS of 4 eulachon. 5 6 Life History and Status of the Green Sturgeon Southern DPS
7 The Green Sturgeon Southern DPS may be affected by the proposed summer/fall and fall 8 Chinook salmon programs as a result of increased competition for resources between hatchery 9 salmonids and green sturgeon, but the DPS is not likely to be adversely affected, as described 10 here. 11 12 The anadromous North American green sturgeon occurs throughout the West Coast from El 13 Socorro Bay, Baja California, to the Bering Sea, Alaska, inhabiting coastal bays and estuaries 14 and migrating to spawning habitats in cool, deep freshwater rivers. Juveniles rear in their natal 15 rivers for two to three years before migrating to the ocean. Two Distinct Population Segments 16 are recognized based on spawning site fidelity and genetic analyses, with the Southern DPS 17 spawning only in the Sacramento River system and the Northern DPS spawning only in the 18 Klamath and Rogue rivers (NMFS and NOAA 2006). The Southern DPS was listed as 19 threatened April 7, 2006 (71 FR 17757) and the Northern DPS was determined to be a NMFS 20 Species of Concern. The population size of the Southern DPS is estimated to be smaller than the 21 Northern DPS. Although the populations overlap in their marine and estuarine distribution, high 22 spawning fidelity has resulted in genetic differentiation between the two green sturgeon DPSs 23 (Israel et al. 2009). 24 25 Major threats to the Southern DPS include alterations to aquatic habit such as barriers to 26 migration, insufficient flows, increased temperatures, and pollution (NMFS 2006), none of 27 which apply to the current Proposed Action. 28 29 Critical habitat for Southern Green Sturgeon DPS was designated on October 9, 2009 (74 FR 30 52300). Coastal waters included as critical habitat stretch from Monterey Bay, California, to 31 Cape Flattery, Washington, and include the Strait of Juan de Fuca to the U.S. border with 32 Canada. Bays in California, Oregon, and Washington are included as well as the Columbia 33 River estuary, the Sacramento-San Joaquin Delta, and the Sacramento, lower Feather, and lower 34 Yuba Rivers in California (NMFS and NOAA 2009). 35 36 The release of hatchery summer/fall and fall Chinook salmon has not been identified as a threat 37 to the survival or persistence of Southern Green Sturgeon DPS. An in-depth literature search has 38 revealed no identified interactions between green sturgeon and hatchery released fish even 39 though both Northern and Southern Green Sturgeon DPS occur in the Columbia estuary and 40 River up to Bonneville Dam. One potential effect is increased competition for resources 41 between hatchery salmonids and green sturgeon. This may be a concern for large releases of 42 hatchery salmonids in natal rivers; however, the Columbia River is not a natal river for green 43 sturgeon. The green sturgeon found in the Columbia River estuary are subadults and adults 44 (Moser and Lindley 2007) and do not occupy the same foraging habitats as URB fall Chinook 45 salmon juveniles, making the potential increase in competition unlikely and, therefore,
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1 discountable. Based on this analysis, NMFS concludes that the Proposed Action is not likely to 2 adversely affect the Southern Green Sturgeon DPS or their designated critical habitat. 3 4 Southern Resident Killer Whale DPS
5 The Southern Resident Killer Whales (SRKW; Southern Residents) DPS consist of three pods (J, 6 K, and L) and was listed as endangered on February 16, 2006 (70 FR 69903), and critical habitat 7 in inland waters of Washington was designated on November 29, 2006 (71 FR 69054). On 8 February 24, 2015, NMFS announced a 12-month finding regarding a petition requesting we 9 designate coastal critical habitat, which identified how we intend to proceed with a revision to 10 critical habitat and develop a proposed rule for publication in 2017 (80 FR 9682). The limiting 11 factors described in the final recovery plan included reduced prey availability and quality, high 12 levels of contaminants from pollution, and disturbances from vessels and sound (NMFS 2008f). 13 Although it is not clear which threat or threats are most significant to the survival and recovery 14 of Southern Residents, it is likely that multiple threats are acting together to impact the whales 15 (NMFS 2008f). 16 17 Southern Residents inhabit coastal waters off Washington, Oregon, and Vancouver Island and 18 are known to travel as far south as central California and as far north as northern British 19 Columbia (Hanson et al. 2013; NMFS 2008f). During the spring, summer, and fall, Southern 20 Residents spend a substantial amount of time in the inland waterways of the Strait of Georgia, 21 Strait of Juan de Fuca, and Puget Sound (Bigg 1982; Ford 2000; Hanson and Emmons 2010; 22 Krahn et al. 2004). In March 2005, L pod was sighted working a circuit across the Columbia 23 River plume from the North Jetty across to the South Jetty during the spring Chinook salmon run 24 in the Columbia River (Zamon et al. 2007). Recent evidence shows K and L pods are spending 25 significantly more time off of the Columbia River in March than previously recognized, 26 suggesting the importance of Columbia River spring Chinook salmon in their diet (Hanson et al. 27 2013). Detection rates of K and L pods on passive acoustic recorders indicate the whales occur 28 with greater frequency off Columbia River and Westport and are most common in March 29 (Hanson et al. 2013). Satellite-linked tag deployments on K and L pod individuals have also 30 provided more data on the whales’ movements in the winter (NWFSC unpubl. data). These data 31 indicate that K and L pods use the coastal waters along Washington, Oregon, and California 32 during non-summer months, whereas J pod occurs more frequently in inland waters, particularly 33 in the northern Georgia Strait. 34 35 The only potential effect of the Proposed Action on SRKW is as a result of changes in prey 36 availability. The Proposed Action affects SRKW prey availability in two ways: by producing fish 37 that the whales can feed on, and by reducing (through hatchery-production-related effects 38 described in greater detail elsewhere) the number of natural-origin fish that would ultimately be 39 available to the whales as prey. 40 41 Southern Residents consume a variety of fish species but salmon are identified as their primary 42 prey (i.e., a high percentage of prey consumed during spring, summer and fall, from long-term 43 studies of resident killer whale diet; Ford and Ellis 2006; Ford et al. 2016; Hanson et al. 2010). 44 Southern Residents are the subject of ongoing research, including direct observation, scale and 45 tissue sampling of prey remains, and fecal sampling. Scale and tissue sampling in inland waters 46 from May to September indicate that Southern Residents’ diet consists of a high percentage of
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1 Chinook, with an overall average of 88% Chinook across the timeframe and monthly proportions 2 as high as >90% Chinook (Ford et al. 2016; Hanson et al. 2010). Prey and fecal samples 3 collected in the winter months also indicate the whales’ primary prey is Chinook salmon, with a 4 smaller number of steelhead, chum salmon, and halibut in their diet (NWFSC unpubl. data). 5 Chinook salmon have the highest value of total energy content compared to other salmonids 6 because of their larger body size and higher energy density (kcal/kg) (O’Neill et al. 2014). 7 8 The Proposed Action may affect SRKWs indirectly by affecting the availability of their primary 9 prey, Chinook salmon. Hatchery-produced Chinook salmon may benefit SRKW by enhancing 10 prey availability, as scarcity of prey has been identified as a threat to SRKW survival and 11 recovery, and hatchery fish often contribute to the salmon stocks consumed by SRKW (Hanson 12 et al. 2010). The release of 1,596,000 summer/fall Chinook salmon yearlings, 484,000 13 summer/fall Chinook salmon subyearlings, and 10,799,504 fall Chinook salmon subyearlings 14 under the Proposed Action could potentially increase the number of Chinook salmon available to 15 the SRKW in coastal waters by 152,755 summer/fall and 31,967 fall Chinook salmon adults 16 annually. These adult survival numbers are calculated by applying the Chinook salmon SARs to 17 the release numbers16. Because SARs account for mortality occurring after adult salmon re-enter 18 freshwater, these adult numbers are an underestimation of the available prey for SRKW. NMFS 19 (2017d) estimated that the annual average Chinook salmon abundance from all west coast 20 sources, that could potentially provide prey for SRKW, was approximately 2,035,778 fish. The 21 contribution of summer/fall and fall Chinook salmon to this total from the release of hatchery 22 fish under the Proposed Action is less than 9.07% of the total Chinook salmon abundance. 23 24 As described in Section 2.5.2.3, the release of hatchery fish in the Upper Columbia River Basin 25 may affect the natural-origin Chinook salmon production in the basin and reduce the number of 26 natural-origin fish available to SRKW as prey by some small amount because of competition or 27 predation between hatchery-origin and natural-origin juveniles as they emigrate. These losses of 28 juveniles equate to a range from 0.2 to 3.7 percent of returning adults at the mouth within each 29 ESU, though, as mentioned above, these numbers are likely an overestimate (see section 2.5.2.3 30 and Table 54); however, these lost natural-origin fish would be replaced by the hatchery fish, and 31 natural-origin fish numbers may increase over time as the goal of the program is to increase the 32 number of naturally-produced fish spawning in the Upper Columbia River Basin. Based on the 33 current natural-origin abundance in the Upper Columbia River Basin, any increase or decrease in 34 overall natural-origin abundance would not have any discernible effect on the total abundance of 35 Chinook salmon off the west coast. It is unlikely that SRKW would have encountered and
16 For the summer Chinook yearling releases, we used the average SARs of all of the relevant programs for the last 5 years, obtained from (Hillman, T., and coauthors. 2017b. Monitoring and Evaluation of the Chelan and Grant County PUDs Hatchery Programs: 2016 Annual Report, September 15, 2017. Report to the HCP and PRCC Hatchery Committees, Wenatchee and Ephrata, Washington. 834p.; brood year 2006-2010) and (Snow, C., C. Frady, D. Grundy, B. Goodman, and A. Murdoch. 2016. Monitoring and Evalutation of the Wells Hatchery and Methow Hatchery Programs: 2015 Annual Report. July 1, 2016. Report to Douglas PUD, Grant PUD, Chelan PUD and the Wells and Rocky Reach HCP Hatchery Committees and the Priest Rapids Hatchery Subcommittees, East Wenatchee, Washington. 210p.; brood year 2004-2008). For the summer Chinook subyearling releases, we used the average SARs for the Wells subyearling program for brood year 2004-2008 (ibid.). For the fall Chinook salmon releases, we used the average SARs for the Priest Rapids Hatchery program for brood years 2004-2008 (Richards, S. P., and T. N. Pearsons. 2015. Final Priest Rapids Hatchery Monitoring and Evaluation Annual Report for 2014-15. September 14, 2015. 113p.).
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1 consumed all of these fish lost to competition and predation (Table 54) annually because the 2 spatial and temporal distributions of SRKW and Chinook salmon are not entirely overlapping, 3 and there is a low probability that all of these lost natural-origin Chinook would be intercepted 4 by SRKW across their vast range in the absence of the Proposed Action. Therefore, any adverse 5 effect on SRKW as a result of reductions in natural-origin Chinook salmon as prey would be 6 insignificant. 7 8 Given the Proposed Action is likely to benefit SRKW with production of hatchery summer/fall 9 and fall Chinook salmon and providing an increase in prey availability, and the effects of the 10 action on the status of listed salmon is small, the release of summer/fall and fall Chinook salmon 11 in the Upper Columbia River under the proposed action is not likely to adversely affect the 12 SRKW. 13 14 Eulachon
15 Eulachon (Thaleichthys pacificus) are endemic to the northeastern Pacific Ocean; they range 16 from northern California to southwest and south-central Alaska and into the southeastern Bering 17 Sea. There are two distinct population segments (DPS); the northern DPS and the southern DPS. 18 The southern DPS of eulachon is comprised of fish that spawn in rivers south of the Nass River 19 in British Columbia to, and including, the Mad River in California (Gustafson et al. 2010), and 20 was listed as a threatened species under the ESA on March 18, 2010 (75 FR 13012). NMFS’ 21 2016 ESA five-year review concluded that the DPS’s threatened designation remained 22 appropriate. Critical habitat was designated under the ESA for eulachon on October 20, 2011 (76 23 FR 65324). 24 25 The Columbia River and its tributaries support the largest eulachon run in the world (Hay et al. 26 2002). Eulachon use the mainstem Columbia River to migrate to spawning grounds as adults and 27 to emigrate from freshwater into marine waters as larvae. Smith and Saalfeld (1955) stated that 28 eulachon spawned in the Hood River (river-mile 169.5) and the Klickitat River (river-mile 180) 29 above Bonneville Dam before the construction of Bonneville Dam in 1938, but were not known 30 to ascend beyond Cascade Rapids until 1896, when the locks and canal were built for steamboat 31 passage. 32 33 Adult eulachon migrate into the Columbia River November through June, with peak migration 34 typically occurring in January through March. Following spawning, eulachon eggs hatch in 20 to 35 40 days with incubation time dependent on water temperature (Gustafson et al. 2010). Shortly 36 after hatching, larvae are carried downstream and are dispersed by river, estuarine, tidal, and 37 ocean currents to the ocean. However, larval eulachon may remain in low salinity, surface waters 38 of estuaries for several weeks or longer before entering the ocean (Hay and McCarter 2000)(Hay 39 and McCarter 2000). Timing of peak larval emergence-drift in the Columbia River estuary 40 occurs January through April, and non-peak larval emergence-drift occurs November through 41 July. 42 43 Effects of the Action 44
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1 The effects of the proposed action considered here include competition for space and predation 2 on eulachon. Eulachon larvae and salmon juveniles/smolts, especially hatchery fish, have 3 different habitat requirements. Larval eulachon are carried downstream and are dispersed by 4 river, estuarine, and tidal currents, and are generally distributed throughout the water column, 5 whereas, once salmon juveniles/smolts pass through/over Bonneville Dam, they generally 6 migrate rapidly through the Columbia River estuary to the ocean, with most juveniles/smolts 7 migrating in or near the navigation channel. Therefore, effects of the proposed action as a result 8 of competition for space are likely to be minor, if any occur at all, and therefore insignificant. 9 10 Releases and down-river migration (April through July) of hatchery fish considered in this 11 opinion overlap with the presence of eulachon larvae (November through July) in the Columbia 12 River estuary. Therefore, the potential for salmon and steelhead hatchery fish to prey on larval 13 eulachon exists, but it is considered to be unlikely, and therefore discountable, based on (1) the 14 timing of peak eulachon larval emergence-drift prey (January through April) occurring earlier 15 than the peak salmon outmigration period, and (2) the best available information regarding prey 16 resources for juvenile salmon and steelhead in freshwater or estuarine habitats, which indicates a 17 prey preference for juvenile salmon that is not primarily eulachon: 18 19 A review by Weitkamp et al. (2014) found that the primary prey consumed by salmon 20 and steelhead in tidal freshwater are aquatic and terrestrial insects (e.g., dipterans, 21 hemipteran), amphipods, mysids, and freshwater crustaceans. In the brackish waters, 22 primary prey are larval and juvenile fish, amphipods, insects, krill (euphasiids), and 23 copepods. In the estuary, the diets of Chinook and coho salmon and steelhead are 24 dominated by amphipods and dipteran insects. 25 26 Based on the above information, especially information regarding the diet composition of 27 juvenile salmonid fishes in freshwater and estuarine habitats, the release of summer/fall and fall 28 Chinook salmon in the Upper Columbia River under the proposed action is not likely to 29 adversely affect the southern DPS of eulachon or its designated critical habitat. 30
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1 MAGNUSON-STEVENS FISHERY CONSERVATION AND MANAGEMENT ACT ESSENTIAL FISH 2 HABITAT CONSULTATION
3 The consultation requirement of section 305(b) of the MSA directs Federal agencies to consult 4 with NMFS on all actions or Proposed Actions that may adversely affect EFH. The MSA 5 (Section 3) defines EFH as “those waters and substrate necessary to fish for spawning, breeding, 6 feeding, or growth to maturity.” Adverse effects include the direct or indirect physical, chemical, 7 or biological alterations of the waters or substrate and loss of, or injury to, benthic organisms, 8 prey species and their habitat, and other ecosystem components, if such modifications reduce the 9 quality or quantity of EFH. Adverse effects on EFH may result from actions occurring within 10 EFH or outside EFH, and may include site-specific or EFH-wide impacts, including individual, 11 cumulative, or synergistic consequences of actions (50 CFR 600.810). Section 305(b) also 12 requires NMFS to recommend measures that can be taken by the action agency to conserve EFH.
13 This analysis is based, in part, on the descriptions of EFH for Pacific Coast salmon (PFMC 2014) 14 contained in the fishery management plans developed by the PFMC and approved by the 15 Secretary of Commerce.
16 Essential Fish Habitat Affected by the Project
17 The Proposed Action is the implementation of four summer/fall Chinook salmon and two fall 18 Chinook salmon hatchery programs, as described in Section 1.3. The action area of the Proposed 19 Action includes habitat described as EFH for Chinook and coho salmon (PFMC 2003) within the 20 Upper Columbia River Basin. Because EFH has not been described for steelhead, the analysis is 21 restricted to the effects of the Proposed Action on EFH for Chinook and coho salmon.
22 As described by PFMC (2003), the freshwater EFH for Chinook and coho salmon has five 23 habitat areas of particular concern (HAPCs): (1) complex channels and floodplain habitat; (2) 24 thermal refugia; (3) spawning habitat; (4) estuaries; and (5) marine and estuarine submerged 25 aquatic vegetation. The aspects of EFH that might be affected by the Proposed Action include 26 effects of hatchery operations on ecological interactions on natural-origin Chinook and coho 27 salmon in spawning and rearing areas and adult migration corridors and adult holding habitat, 28 and genetic effects on natural-origin Chinook salmon in spawning areas (primarily addressing 29 HAPC 3).
30 Adverse Effects on Essential Fish Habitat
31 The Proposed Action has small effects on the major components of EFH. As described in Section 32 2.5.2, facilities used for hatchery operations can adversely affect salmon by reducing streamflow, 33 or impeding migration. However, water withdrawals are non-consumptive and small enough in 34 scale that changes in flow within spawning habitat would be undetectable.
35 The PFMC (2003) recognized concerns regarding the “genetic and ecological interactions of 36 hatchery and wild fish… [which have] been identified as risk factors for wild populations.” The 37 biological opinion describes in considerable detail the impacts hatchery programs might have on 38 natural salmon and steelhead populations (Section 5). Ecological effects of juvenile and adult 39 hatchery-origin fish on natural-origin Chinook salmon are discussed in Sections 2.5.2.2 and 40 2.5.2.3. Hatchery summer/fall Chinook salmon returning to the Upper Columbia River are not
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1 expected to compete for space with spring Chinook or coho salmon because of the usage of 2 different habitats based on fish body size and due to differences in run and spawn timing; spring 3 Chinook salmon spawn in the late summer, and coho salmon spawn in the mid-late fall. In 4 contrast, fish produced by the proposed hatchery programs typically spawn from late September 5 to early December (Table 43). Because of this small likelihood of overlap in spawn timing and 6 usage of habitat, the spawning habitat HAPC would not be adversely affected by the proposed 7 action.
8 EFH for Chinook and coho salmon would likely be affected by the proposed action through 9 ecological interactions. Some summer/fall and fall Chinook salmon from the programs would 10 stray into other rivers (Section 2.5.2.2), but not in numbers that would exceed the carrying 11 capacities of natural production areas, or that would result in increased incidence of disease or 12 predators. Some predation by adult hatchery Chinook salmon on juvenile natural-origin Chinook 13 or coho salmon may occur as summer/fall and fall Chinook salmon hold for a potentially long 14 period of time before spawning. Predation and competition by juvenile hatchery summer/fall and 15 fall Chinook salmon on juvenile natural-origin Chinook or coho salmon is likely small. Our 16 analysis in Section 2.5.2.3 shows that fewer than 2,488 Chinook salmon adult equivalents and 17 468 coho salmon adult equivalents are likely to be lost to predation and competition with 18 hatchery summer/fall and fall Chinook salmon at the juvenile stage within our action area for this 19 consultation. However, some areas within the action area are not included in the EFH 20 designation (e.g., HUC 17020016 for Priest Rapids does not include EFH for coho salmon), so 21 the level of effect is likely to be less than described here.
22 NMFS has determined that the Proposed Action is likely to adversely affect EFH for Pacific 23 salmon, specifically through small amounts of predation by, and competition with, hatchery fish 24 produced by the proposed action. 25 26 Essential Fish Habitat Conservation Recommendations
27 For each of the potential adverse effects by the Proposed Action on EFH for Chinook and coho 28 salmon, NMFS believes that the Proposed Action, as described in the HGMPs and the ITS 29 (Section 2.9), includes the best approaches to avoid or minimize those adverse effects. Thus, 30 NMFS has no additional conservation recommendations specifically for Chinook and coho 31 salmon EFH besides fully implementing the proposed action and ITS. However, the Reasonable 32 and Prudent Measures and Terms and Conditions included in the ITS, specifically under RPM #1 33 and its associated Terms and Conditions, sufficiently address potential EFH effects. 34 35 Statutory Response Requirement
36 As required by section 305(b)(4)(B) of the MSA, the Federal action agencies must provide a 37 detailed response in writing to NMFS within 30 days after receiving an EFH Conservation 38 Recommendation. Such a response must be provided at least 10 days prior to final approval of 39 the action if the response is inconsistent with any of NMFS’ EFH Conservation 40 Recommendations unless NMFS and the Federal agency have agreed to use alternative time 41 frames for the Federal agency response. The response must include a description of measures 42 proposed by the agency for avoiding, minimizing, mitigating, or otherwise offsetting the impact 43 of the activity on EFH. In the case of a response that is inconsistent with the Conservation
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1 Recommendations, the Federal agency must explain its reasons for not following the 2 recommendations, including the scientific justification for any disagreements with NMFS over 3 the anticipated effects of the action and the measures needed to avoid, minimize, mitigate, or 4 offset such effects (50 CFR 600.920(k)(1)).
5 In response to increased oversight of overall EFH program effectiveness by the Office of 6 Management and Budget, NMFS established a quarterly reporting requirement to determine how 7 many conservation recommendations are provided as part of each EFH consultation and how 8 many are adopted by the action agency. Therefore, we ask that, in your statutory reply to the 9 EFH portion of this consultation, you clearly identify the number of conservation 10 recommendations accepted.
11 Supplemental Consultation
12 The Federal action agencies must reinitiate EFH consultation with NMFS if the Proposed Action 13 is substantially revised in a way that may adversely affect EFH, or if new information becomes 14 available that affects the basis for NMFS’ EFH conservation recommendations (50 CFR 15 600.920(l)).
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1 DATA QUALITY ACT DOCUMENTATION AND PRE-DISSEMINATION REVIEW
2 Section 515 of the Treasury and General Government Appropriations Act of 2001 (Public Law 3 106-554) (“Data Quality Act”) specifies three components contributing to the quality of a 4 document. They are utility, integrity, and objectivity. This section of the opinion addresses these 5 DQA components, document compliance with the Data Quality Act, and certifies that this 6 opinion has undergone pre-dissemination review.
7 Utility
8 Utility principally refers to ensuring that the information contained in this consultation is helpful, 9 serviceable, and beneficial to the intended users. NMFS has determined, through this ESA 10 section 7 consultation, that operation of the four summer/fall Chinook salmon and two fall 11 Chinook salmon hatchery programs in the Upper Columbia River as proposed will not jeopardize 12 ESA-listed species and will not destroy or adversely modify designated critical habitat. 13 Therefore, NMFS can issue an ITS. The intended users of this opinion are: the NMFS 14 (permitting entity); the WDFW (operating entity); the Chelan, and Grant Public Utility Districts 15 (funding entities); the Douglas Public Utility District (funding and operating entity) and the 16 USACE (funding entity). The scientific community, resource managers, and stakeholders benefit 17 from the consultation through the anticipated increase in returns of summer/fall and fall Chinook 18 salmon to the Upper Columbia River basin for conservation and harvest, and through the 19 collection of data indicating the potential effects of the operation on the viability of natural 20 populations of ESA-listed salmonids. This information will improve scientific understanding of 21 hatchery-origin steelhead effects that can be applied broadly within the Pacific Northwest area 22 for managing benefits and risks associated with hatchery operations. This opinion will be posted 23 on NMFS’ West Coast Region web site (http://www.westcoast.fisheries.noaa.gov/). The format 24 and naming adheres to conventional standards for style.
25 Integrity
26 This consultation was completed on a computer system managed by NMFS in accordance with 27 relevant information technology security policies and standards set out in Appendix III, 28 “Security of Automated Information Resources,” Office of Management and Budget Circular A- 29 130; the Computer Security Act; and the Government Information Security Reform Act.
30 Objectivity
31 Information Product Category: Natural Resource Plan
32 Standards: This consultation and supporting documents are clear, concise, complete, and 33 unbiased, and were developed using commonly accepted scientific research methods. They 34 adhere to published standards including the NMFS ESA Consultation Handbook, ESA 35 Regulations, 50 CFR 402.01 et seq., and the MSA implementing regulations regarding EFH, 50 36 CFR 600.920(j).
37 Best Available Information: This consultation and supporting documents use the best available 38 information, as described in the references section. The analyses in this biological opinion/EFH 39 consultation contain more background on information sources and quality.
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1 Referencing: All supporting materials, information, data, and analyses are properly referenced, 2 consistent with standard scientific referencing style.
3 Review Process: This consultation was drafted by NMFS staff with training in ESA and MSA 4 implementation, and reviewed in accordance with West Coast Region ESA quality control and 5 assurance processes.
6
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1 2 APPENDIX A-FACTORS CONSIDERED WHEN ANALYZING HATCHERY EFFECTS
3 NMFS’ analysis of the Proposed Action is in terms of effects the Proposed Action would be 4 expected to have on ESA-listed species and on designated critical habitat, based on the best 5 scientific information available. The effects, positive and negative, for the two categories of 6 hatchery programs are summarized in Table 61. Generally speaking, effects range from 7 beneficial to negative when programs use local fish17 for hatchery broodstock, and from 8 negligible to negative when programs do not use local fish for broodstock18. Hatchery programs 9 can benefit population viability, but only if they use genetic resources that represent the 10 ecological and genetic diversity of the target or affected natural population(s). When hatchery 11 programs use genetic resources that do not represent the ecological and genetic diversity of the 12 target or affected natural population(s), NMFS is particularly interested in how effective the 13 program will be at isolating hatchery fish and at avoiding co-occurrence and effects that 14 potentially disadvantage fish from natural populations. NMFS applies available scientific 15 information, identifies the types of circumstances and conditions that are unique to individual 16 hatchery programs, then refines the range in effects for a specific hatchery program. Analysis of 17 a Proposed Action for its effects on ESA-listed species and on designated critical habitat depends 18 on six factors. These factors are: 19 20 (1) the hatchery program does or does not remove fish from the natural population and use 21 them for hatchery broodstock, 22 (2) hatchery fish and the progeny of naturally spawning hatchery fish on spawning grounds 23 and encounters with natural-origin and hatchery fish at adult collection facilities, 24 (3) hatchery fish and the progeny of naturally spawning hatchery fish in juvenile rearing 25 areas, the migration corridor, estuary, and ocean, 26 (4) RM&E that exists because of the hatchery program, 27 (5) operation, maintenance, and construction of hatchery facilities that exist because of the 28 hatchery program, and 29 (6) fisheries that exist because of the hatchery program, including terminal fisheries intended 30 to reduce the escapement of hatchery-origin fish to spawning grounds. 31 32 The analysis assigns an effect for each factor from the following categories: 33 34 (1) positive or beneficial effect on population viability, 35 (2) negligible effect on population viability, and 36 (3) negative effect on population viability. 37 38 The effects of hatchery fish on ESU/DPS status will depend on which of the four VSP criteria 39 are currently limiting the ESU/DPS and how the hatchery program affects each of the criteria 40 (NMFS 2005c). The category of effect assigned to a factor is based on an analysis of each factor 41 weighed against each affected population’s current risk level for abundance, productivity, spatial 42 structure, and diversity, the role or importance of the affected natural population(s) in ESU or
17 The term “local fish” is defined to mean fish with a level of genetic divergence relative to the local natural population(s) that is no more than what occurs within the ESU or steelhead DPS (70 FR 37215, June 28, 2005). 18 Exceptions include restoring extirpated populations and gene banks.
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1 steelhead DPS recovery, the target viability for the affected natural population(s), and the 2 environmental baseline including the factors currently limiting population viability. 3 4 Table 61. An overview of the range of effects on natural population viability parameters from the 5 two categories of hatchery programs. Hatchery broodstock originate from a Hatchery broodstock originate from Natural population non-local population or from fish that the local population and are included viability parameter are not included in the same ESU or in the ESU or DPS DPS Positive to negative effect Negligible to negative effect Hatcheries are unlikely to benefit Productivity is dependent on differences productivity except in cases where the between hatchery fish and the local natural natural population’s small size is, in itself, a population (i.e., the more distant the origin of Productivity predominant factor limiting population the hatchery fish, the greater the threat), the growth (i.e., productivity) (NMFS 2004c). duration and strength of selection in the hatchery, and the level of isolation achieved by the hatchery program (i.e., the greater the isolation, the closer to a negligible effect). Positive to negative effect Negligible to negative effect Hatcheries can temporarily support natural Diversity is dependent on the differences populations that might otherwise be between hatchery fish and the local natural extirpated or suffer severe bottlenecks and population (i.e., the more distant the origin of Diversity have the potential to increase the effective the hatchery fish, the greater the threat) and size of small natural populations. On the the level of isolation achieved by the other hand, broodstock collection that hatchery program (i.e., the greater the homogenizes population structure is a threat isolation, the closer to a negligible effect). to population diversity. Positive to negative effect Negligible to negative effect Hatchery-origin fish can positively affect Abundance is dependent on the level of the status of an ESU by contributing to the isolation achieved by the hatchery program Abundance abundance of the natural populations in the (i.e., the greater the isolation, the closer to a ESU (70 FR 37204, June 28, 2005, at negligible effect), handling, RM&E, and 37215). Increased abundance can also facility operation, maintenance and increase density dependent effects. construction effects. Positive to negative effect Negligible to negative effect Hatcheries can accelerate re-colonization Spatial structure is dependent on facility and increase population spatial structure, operation, maintenance, and construction but only in conjunction with remediation of effects and the level of isolation achieved by Spatial Structure the factor(s) that limited spatial structure in the hatchery program (i.e., the greater the the first place. “Any benefits to spatial isolation, the closer to a negligible effect). structure over the long term depend on the degree to which the hatchery stock(s) add to (rather than replace) natural populations” (70 FR 37204, June 28, 2005 at 37213). 6 7
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1 Factor 1. The hatchery program does or does not remove fish from the natural 2 population and use them for hatchery broodstock
3 This factor considers the risk to a natural population from the removal of natural-origin fish for 4 hatchery broodstock. The level of effect for this factor ranges from neutral or negligible to 5 negative. 6 7 A primary consideration in analyzing and assigning effects for broodstock collection is the origin 8 and number of fish collected. The analysis considers whether broodstock are of local origin and 9 the biological pros and cons of using ESA-listed fish (natural or hatchery-origin) for hatchery 10 broodstock. It considers the maximum number of fish proposed for collection and the proportion 11 of the donor population tapped to provide hatchery broodstock. “Mining” a natural population to 12 supply hatchery broodstock can reduce population abundance and spatial structure. Also 13 considered here is whether the program “backfills” with fish from outside the local or immediate 14 area. The physical process of collecting hatchery broodstock and the effect of the process on 15 ESA-listed species is considered under Factor 2. 16 17 Factor 2. Hatchery fish and the progeny of naturally spawning hatchery fish on 18 spawning grounds and encounters with natural-origin and hatchery fish at adult 19 collection facilities
20 NMFS also analyzes the effects of hatchery fish and the progeny of naturally spawning hatchery 21 fish on the spawning grounds. The level of effect for this factor ranges from positive to negative. 22 23 There are two aspects to this part of the analysis: genetic effects and ecological effects. NMFS 24 generally views genetic effects as detrimental because we believe that artificial breeding and 25 rearing is likely to result in some degree of genetic change and fitness reduction in hatchery fish 26 and in the progeny of naturally spawning hatchery fish relative to desired levels of diversity and 27 productivity for natural populations based on the weight of available scientific information at this 28 time. Hatchery fish can thus pose a risk to diversity and to natural population rebuilding and 29 recovery when they interbreed with fish from natural populations. 30 31 However, NMFS recognizes that beneficial effects exist as well, and that the risks just mentioned 32 may be outweighed under circumstances where demographic or short-term extinction risk to the 33 population is greater than risks to population diversity and productivity. Conservation hatchery 34 programs may accelerate recovery of a target population by increasing abundance faster than 35 may occur naturally (Waples 1999). Hatchery programs can also be used to create genetic 36 reserves for a population to prevent the loss of its unique traits due to catastrophes (Ford 2011). 37 38 NMFS also recognizes there is considerable debate regarding genetic risk. The extent and 39 duration of genetic change and fitness loss and the short- and long-term implications and 40 consequences for different species (i.e., for species with multiple life-history types and species 41 subjected to different hatchery practices and protocols) remain unclear and should be the subject 42 of further scientific investigation. As a result, NMFS believes that hatchery intervention is a 43 legitimate and useful tool to alleviate short-term extinction risk, but otherwise managers should 44 seek to limit interactions between hatchery and natural-origin fish and implement hatchery
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1 practices that harmonize conservation with the implementation of treaty Indian fishing rights and 2 other applicable laws and policies (NMFS 2011d). 3 4 Genetic effects
5 Hatchery fish can have a variety of genetic effects on natural population productivity and 6 diversity when they interbreed with natural-origin fish. Although there is biological 7 interdependence between them, NMFS considers three major areas of genetic effects of hatchery 8 programs: within-population diversity, outbreeding effects, and hatchery-induced selection. As 9 we have stated above, in most cases, the effects are viewed as risks, but in small populations 10 these effects can sometimes be beneficial, reducing extinction risks. 11 12 First, within-population genetic diversity is a general term for the quantity, variety, and 13 combinations of genetic material in a population (Busack and Currens 1995). Within-population 14 diversity is gained through mutations or gene flow from other populations (described below 15 under outbreeding effects) and is lost primarily due to genetic drift, a random loss of diversity 16 due to population size. The rate of loss is determined by the population’s effective population 17 size (Ne), which can be considerably smaller than its census size. For a population to maintain 18 genetic diversity reasonably well, the effective size should be in the hundreds (e.g., Lande 1987), 19 and diversity loss can be severe if Ne drops to a few dozen. 20 21 Hatchery programs, simply by virtue of creating more fish, can increase Ne. In very small 22 populations, this increase can be a benefit, making selection more effective and reducing other 23 small-population risks (e.g., (e.g., Lacy 1987; Whitlock 2000; Willi et al. 2006). Conservation 24 hatchery programs can thus serve to protect genetic diversity; several programs, such as the 25 Snake River sockeye salmon program, are important genetic reserves. However, hatchery 26 programs can also directly depress Ne by two principal methods. One is by the simple removal of 27 fish from the population so that they can be used in the hatchery broodstock. If a substantial 28 portion of the population is taken into a hatchery, the hatchery becomes responsible for that 29 portion of the effective size, and if the operation fails, the effective size of the population will be 30 reduced (Waples and Do 1994). Two is when Ne is reduced considerably below the census 31 number of broodstock by using a skewed sex ratio, spawning males multiple times (Busack 32 2007), and by pooling gametes. Pooling semen is especially problematic because when semen of 33 several males is mixed and applied to eggs, a large portion of the eggs may be fertilized by a 34 single male (Gharrett and Shirley 1985; Withler 1988). An extreme form of Ne reduction is the 35 Ryman-Laikre effect (Ryman et al. 1995; Ryman and Laikre 1991), when Ne is reduced through 36 the return to the spawning grounds of large numbers of hatchery fish from very few parents. On 37 the other hand, factorial mating schemes, in which fish are systematically mated multiple times, 38 can be used to increase Ne (Busack and Knudsen 2007; Fiumera et al. 2004). 39 40 Inbreeding depression, another Ne-related phenomenon, is caused by the mating of closely 41 related individuals (e.g., siblings, half-siblings, cousins). The smaller the population, the more 42 likely spawners will be related. Related individuals are likely to contain similar genetic material, 43 and the resulting offspring may then have reduced survival because they are less variable 44 genetically or have double doses of deleterious mutations. The lowered fitness of fish due to 45 inbreeding depression accentuates the genetic risk problem, helping to push a small population 46 toward extinction.
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1 2 Outbreeding effects, the second major area of genetic effects of hatchery programs, are caused 3 by gene flow from other populations. Gene flow occurs naturally among salmon and steelhead 4 populations, a process referred to as straying (Quinn 1993; Quinn 1997). Natural straying serves 5 a valuable function in preserving diversity that would otherwise be lost through genetic drift and 6 in re-colonizing vacant habitat, and straying is considered a risk only when it occurs at unnatural 7 levels or from unnatural sources. Hatchery programs can result in straying outside natural 8 patterns for two reasons. First, hatchery fish may exhibit reduced homing fidelity relative to 9 natural-origin fish (Goodman 2005; Grant 1997; Jonsson et al. 2003; Quinn 1997), resulting in 10 unnatural levels of gene flow into recipient populations, either in terms of sources or rates. 11 Second, even if hatchery fish home at the same level of fidelity as natural-origin fish, their higher 12 abundance can cause unnatural straying levels into recipient populations. One goal for hatchery 13 programs should be to ensure that hatchery practices do not lead to higher rates of genetic 14 exchange with fish from natural populations than would occur naturally (Ryman 1991). Rearing 15 and release practices and ancestral origin of the hatchery fish can all play a role in straying 16 (Quinn 1997). 17 18 Gene flow from other populations can have two effects. It can increase genetic diversity (e.g., 19 Ayllon et al. 2006), which can be a benefit in small populations, but it can also alter established 20 allele frequencies (and co-adapted gene complexes) and reduce the population’s level of 21 adaptation, a phenomenon called outbreeding depression (Edmands 2007; McClelland and Naish 22 2007). In general, the greater the geographic separation between the source or origin of hatchery 23 fish and the recipient natural population, the greater the genetic difference between the two 24 populations (ICTRT 2007), and the greater potential for outbreeding depression. For this reason, 25 NMFS advises hatchery action agencies to develop locally derived hatchery broodstock. 26 Additionally, unusual rates of straying into other populations within or beyond the population’s 27 MPG, salmon ESU, or a steelhead DPS can have an homogenizing effect, decreasing intra- 28 population genetic variability (e.g.(Vasemagi et al. 2005), and increasing risk to population 29 diversity, one of the four attributes measured to determine population viability. Reduction of 30 within-population and among-population diversity can reduce adaptive potential. 31 32 The proportion of hatchery fish (pHOS)19 among natural spawners is often used as a surrogate 33 measure of gene flow. Appropriate cautions and qualifications should be considered when using 34 this proportion to analyze outbreeding effects. Adult salmon may wander on their return 35 migration, entering and then leaving tributary streams before spawning (Pastor 2004). These 36 “dip-in” fish may be detected and counted as strays, but may eventually spawn in other areas, 37 resulting in an overestimate of the number of strays that potentially interbreed with the natural 38 population (Keefer et al. 2008). Caution must also be taken in assuming that strays contribute 39 genetically in proportion to their abundance. Several studies demonstrate little genetic impact 40 from straying despite a considerable presence of strays in the spawning population (Blankenship 41 et al. 2007; Saisa et al. 2003). The causative factors for poorer breeding success of strays are 42 likely similar to those identified as responsible for reduced productivity of hatchery-origin fish in 43 general, e.g., differences in run and spawn timing, spawning in less productive habitats, and
19 It is important to reiterate that as NMFS analyzes them, outbreeding effects are a risk only when the hatchery fish are from a different population than the naturally produced fish. If they are from the same population, then the risk is from hatchery-influenced selection.
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1 reduced survival of their progeny (Leider et al. 1990; Reisenbichler and McIntyre 1977; 2 Williamson et al. 2010). 3 4 Hatchery-influenced selection (often called domestication), the third major area of genetic effects 5 of hatchery programs, occurs when selection pressures imposed by hatchery spawning and 6 rearing differ greatly from those imposed by the natural environment and causes genetic change 7 that is passed on to natural populations through interbreeding with hatchery-origin fish. These 8 differing selection pressures can be a result of differences in environments or a consequence of 9 protocols and practices used by a hatchery program. Hatchery-influenced selection can range 10 from relaxation of selection that would normally occur in nature, to selection for different 11 characteristics in the hatchery and natural environments, to intentional selection for desired 12 characteristics (Waples 1999). 13 14 Genetic change and fitness reduction resulting from hatchery-influenced selection depends on: 15 (1) the difference in selection pressures; (2) the exposure or amount of time the fish spends in the 16 hatchery environment; and (3) the duration of hatchery program operation (i.e., the number of 17 generations that fish are propagated by the program). For an individual, the amount of time a fish 18 spend in the hatchery mostly equates to fish culture. For a population, exposure is determined by 19 the proportion of natural-origin fish in the hatchery broodstock, the proportion of natural 20 spawners consisting of hatchery-origin fish (Ford 2002; Lynch and O'Hely 2001), and the 21 number of years the exposure takes place. In assessing risk or determining impact, all three 22 factors must be considered. Strong selective fish culture with low hatchery-wild interbreeding 23 can pose less risk than relatively weaker selective fish culture with high levels of interbreeding. 24 25 Most of the empirical evidence of fitness depression due to hatchery-influenced selection comes 26 from studies of species that are reared in the hatchery environment for an extended period – one 27 to two years – prior to release (Berejikian and Ford 2004). Exposure time in the hatchery for fall 28 and summer Chinook salmon and Chum salmon is much shorter, just a few months. One 29 especially well-publicized steelhead study (Araki et al. 2007; Araki et al. 2008), showed 30 dramatic fitness declines in the progeny of naturally spawning Hood River hatchery steelhead. 31 Researchers and managers alike have wondered if these results could be considered a potential 32 outcome applicable to all salmonid species, life-history types, and hatchery rearing strategies, but 33 researchers have not reached a definitive conclusion. 34 35 Besides the Hood River steelhead work, a number of studies are available on the relative 36 reproductive success (RRS) of hatchery- and natural-origin fish (e.g., Berntson et al. 2011; Ford 37 et al. 2012; Hess et al. 2012; Theriault et al. 2011). All have shown that, generally, hatchery- 38 origin fish have lower reproductive success; however, the differences have not always been 39 statistically significant and, in some years in some studies, the opposite was true. Lowered 40 reproductive success of hatchery-origin fish in these studies is typically considered evidence of 41 hatchery-influenced selection. Although RRS may be a result of hatchery-influenced selection, 42 studies must be carried out for multiple generations to unambiguously detect a genetic effect. To 43 date, only the Hood River steelhead (Araki et al. 2007; Christie et al. 2011) and Wenatchee 44 spring Chinook salmon (Ford et al. 2012) RRS studies have reported multiple-generation effects. 45
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1 Critical information for analysis of hatchery-induced selection includes the number, location, and 2 timing of naturally spawning hatchery fish, the estimated level of gene flow between hatchery- 3 origin and natural-origin fish, the origin of the hatchery stock (the more distant the origin 4 compared to the affected natural population, the greater the threat), the level and intensity of 5 hatchery selection and the number of years the operation has been run in this way. Efforts to 6 control and evaluate the risk of hatchery-influenced selection are currently largely focused on 7 gene flow between natural-origin and hatchery-origin fish20. The Interior Columbia Technical 8 Recovery Team (ICTRT) developed guidelines based on the proportion of spawners in the wild 9 consisting of hatchery-origin fish (pHOS) (Figure 11). 10 11 More recently, the Hatchery Scientific Review Group (HSRG) developed gene-flow guidelines 12 based on mathematical models developed by (Ford 2002) and by (Lynch and O'Hely 2001). 13 Guidelines for isolated programs are based on pHOS, but guidelines for integrated programs are 14 based also on a metric called proportionate natural influence (PNI), which is a function of pHOS 15 and the proportion of natural-origin fish in the broodstock (pNOB)21. PNI is, in theory, a 16 reflection of the relative strength of selection in the hatchery and natural environments; a PNI 17 value greater than 0.5 indicates dominance of natural selective forces. The HSRG guidelines 18 vary according to type of program and conservation importance of the population. When the 19 underlying natural population is of high conservation importance, the guidelines are a pHOS of 20 no greater than 5 percent for isolated programs. For integrated programs, the guidelines are a 21 pHOS no greater than 30 percent and PNI of at least 67 percent for integrated programs (HSRG 22 2009). Higher levels of hatchery influence are acceptable, however, when a population is at high 23 risk or very high risk of extinction due to low abundance and the hatchery program is being used 24 to conserve the population and reduce extinction risk in the short-term. (HSRG 2004)offered 25 additional guidance regarding isolated programs, stating that risk increases dramatically as the 26 level of divergence increases, especially if the hatchery stock has been selected directly or 27 indirectly for characteristics that differ from the natural population. The HSRG recently 28 produced an update report (HSRG 2014) that stated that the guidelines for isolated programs may 29 not provide as much protection from fitness loss as the corresponding guidelines for integrated 30 programs. 31
20 Gene flow between natural-origin and hatchery-origin fish is often interpreted as meaning actual matings between natural-origin and hatchery-origin fish. In some contexts, it can mean that. However, in this document, unless otherwise specified, gene flow means contributing to the same progeny population. For example, hatchery-origin spawners in the wild will either spawn with other hatchery-origin fish or with natural-origin fish. Natural-origin spawners in the wild will either spawn with other natural-origin fish or with hatchery-origin fish. But all these matings, to the extent they are successful, will generate the next generation of natural-origin fish. In other words, all will contribute to the natural-origin gene pool. 21 PNI is computed as pNOB/(pNOB+pHOS). This statistic is really an approximation of the true proportionate natural influence, but operationally the distinction is unimportant.
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1 2 Figure 11. ICTRT (2007b) risk criteria associated with spawner composition for viability 3 assessment of exogenous spawners on maintaining natural patterns of gene flow. 4 Exogenous fish are considered to be all fish of hatchery origin, and non-normative strays 5 of natural origin. 6 Another HSRG team recently reviewed California hatchery programs and developed guidelines 7 that differed considerably from those developed by the earlier group (California HSRG 2012). 8 The California HSRG felt that truly isolated programs in which no hatchery-origin returnees 9 interact genetically with natural populations were impossible in California, and was “generally 10 unsupportive” of the concept. However, if programs were to be managed as isolated, they 11 recommend a pHOS of less than 5 percent. They rejected development of overall pHOS 12 guidelines for integrated programs because the optimal pHOS will depend upon multiple factors, 13 such as “the amount of spawning by natural-origin fish in areas integrated with the hatchery, the 14 value of pNOB, the importance of the integrated population to the larger stock, the fitness 15 differences between hatchery- and natural-origin fish, and societal values, such as angling 16 opportunity.” They recommended that program-specific plans be developed with corresponding 17 population-specific targets and thresholds for pHOS, pNOB, and PNI that reflect these factors. 18 However, they did state that PNI should exceed 50 percent in most cases, although in 19 supplementation or reintroduction programs the acceptable pHOS could be much higher than 5 20 percent, even approaching 100 percent at times. They also recommended for conservation 21 programs that pNOB approach 100 percent, but pNOB levels should not be so high they pose 22 demographic risk to the natural population. 23
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1 Discussions involving pHOS can be problematic due to variation in its definition. Most 2 commonly, the term pHOS refers to the proportion of the total natural spawning population 3 consisting of hatchery fish, and the term has been used in this way in all NMFS documents. 4 However, the HSRG has defined pHOS inconsistently in its Columbia Basin system report, 5 equating it with “the proportion of the natural spawning population that is made up of hatchery 6 fish” in the Conclusion, Principles and Recommendations section (HSRG 2009), but with “the 7 proportion of effective hatchery-origin spawners” in their gene-flow criteria. In addition, in their 8 Analytical Methods and Information Sources section (appendix C in HSRG 2009) they introduce 9 a new term, effective pHOS (pHOSeff) defined as the effective proportion of hatchery fish in the 10 naturally spawning population. This confusion was cleared up in the 2014 update document, 11 where it is clearly stated that the metric of interest is effective pHOS (HSRG 2014). 12 13 The HSRG recognized that hatchery fish spawning naturally may on average produce fewer 14 adult progeny than natural-origin spawners, as described above. To account for this difference 15 the HSRG defined effective pHOS as: 16 17 pHOSeff = RRS * pHOScensus 18 19 where pHOScensus is the proportion of the naturally spawning population that is composed of 20 hatchery-origin adults (HSRG 2014). In the 2014 report, the HSRG explicitly addressed the 21 differences between census pHOS and effective pHOS, by defining PNI as: 22 23 PNI = _____pNOB_____ 24 (pNOB + pHOSeff) 25 26 NMFS feels that adjustment of census pHOS by RRS should be done very cautiously, not nearly 27 as freely as the HSRG document would suggest because the Ford (2002) model, which is the 28 foundation of the HSRG gene-flow guidelines, implicitly includes a genetic component of RRS. 29 In that model, hatchery fish are expected to have RRS < 1 (compared to natural fish) due to 30 selection in the hatchery. A component of reduced RRS of hatchery fish is therefore already 31 incorporated in the model and by extension the calculation of PNI. Therefore reducing pHOS 32 values by multiplying by RRS will result in underestimating the relevant pHOS and therefore 33 overestimating PNI. Such adjustments would be particularly inappropriate for hatchery programs 34 with low pNOB, as these programs may well have a substantial reduction in RRS due to genetic 35 factors already incorporated in the model. 36 37 In some cases, adjusting pHOS downward may be appropriate, however, particularly if there is 38 strong evidence of a non-genetic component to RRS. Wenatchee spring Chinook salmon 39 (Williamson et al. 2010) is an example case with potentially justified adjustment by RRS, where 40 the spatial distribution of natural-origin and hatchery-origin spawners differs, and the hatchery- 41 origin fish tend to spawn in poorer habitat. However, even in a situation like the Wenatchee 42 spring Chinook salmon, it is unclear how much of an adjustment would be appropriate. By the 43 same logic, it might also be appropriate to adjust pNOB in some circumstances. For example, if 44 hatchery juveniles produced from natural-origin broodstock tend to mature early and residualize 45 (due to non-genetic effects of rearing), as has been documented in some spring Chinook salmon 46 and steelhead programs, the “effective” pNOB might be much lower than the census pNOB.
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1 2 It is also important to recognize that PNI is only an approximation of relative trait value, based 3 on a model that is itself very simplistic. To the degree that PNI fails to capture important 4 biological information, it would be better to work to include this biological information in the 5 underlying models rather than make ad hoc adjustments to a statistic that was only intended to be 6 rough guideline to managers. We look forward to seeing this issue further clarified in the near 7 future. In the meantime, except for cases in which an adjustment for RRS has strong justification, 8 NMFS feels that census pHOS, rather than effective pHOS, is the appropriate metric to use for 9 genetic risk evaluation. 10 11 Additional perspective on pHOS that is independent of HSRG modelling is provided by a simple 12 analysis of the expected proportions of mating types. Figure 12 shows the expected proportion of 13 mating types in a mixed population of natural-origin (N) and hatchery-origin (H) fish as a 14 function of the census pHOS, assuming that N and H adults mate randomly22. For example, at a 15 census pHOS level of 10 percent, 81 percent of the matings will be NxN, 18 percent will be 16 NxH, and 1 percent will be HxH. This diagram can also be interpreted as probability of 17 parentage of naturally produced progeny, assuming random mating and equal reproductive 18 success of all mating types. Under this interpretation, progeny produced by a parental group with 19 a pHOS level of 10 percent will have an 81 percent chance of having two natural-origin parents, 20 etc. 21 22 Random mating assumes that the natural-origin and hatchery-origin spawners overlap completely 23 spatially and temporally. As overlap decreases, the proportion of NxH matings decreases; with 24 no overlap, the proportion of NxN matings is 1 minus pHOS and the proportion of HxH matings 25 equals pHOS. RRS does not affect the mating type proportions directly but changes their 26 effective proportions. Overlap and RRS can be related. For example, in the Wenatchee River, 27 hatchery spring Chinook salmon tend to spawn lower in the system than natural-origin fish, and 28 this accounts for a considerable amount of their lowered reproductive success (Williamson et al. 29 2010). In that particular situation the hatchery-origin fish were spawning in inferior habitat.
22 These computations are purely theoretical, based on a simple mathematical binomial expansion ((a+b)2=a2 + 2ab + b2 ).
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1 2 Figure 12. Relative proportions of types of matings as a function of proportion of hatchery-origin 3 fish on the spawning grounds (pHOS). 4 Ecological effects
5 Ecological effects for this factor (i.e., hatchery fish and the progeny of naturally spawning 6 hatchery fish on the spawning grounds) refer to effects from competition for spawning sites and 7 redd superimposition, contributions to marine-derived nutrients, and the removal of fine 8 sediments from spawning gravels. Ecological effects on the spawning grounds may be positive 9 or negative. To the extent that hatcheries contribute added fish to the ecosystem, there can be 10 positive effects. For example, when anadromous salmonids return to spawn, hatchery-origin and 11 natural-origin alike, they transport marine-derived nutrients stored in their bodies to freshwater 12 and terrestrial ecosystems. Their carcasses provide a direct food source for juvenile salmonids 13 and other fish, aquatic invertebrates, and terrestrial animals, and their decomposition supplies 14 nutrients that may increase primary and secondary production (Gresh et al. 2000; Kline et al. 15 1990; Larkin and Slaney 1996; Murota 2003; Piorkowski 1995; Quamme and Slaney 2003; 16 Wipfli et al. 2003). As a result, the growth and survival of juvenile salmonids may increase (Bell 17 2001; Bilton et al. 1982; Bradford et al. 2000; Brakensiek 2002; Hager and Noble 1976; Hartman 18 and Scrivener 1990; Holtby 1988; Johnston et al. 1990; Larkin and Slaney 1996; Quinn and 19 Peterson 1996; Ward and Slaney 1988). 20 21 Additionally, studies have demonstrated that perturbation of spawning gravels by spawning 22 salmonids loosens cemented (compacted) gravel areas used by spawning salmon (e.g., 23 (Montgomery et al. 1996). The act of spawning also coarsens gravel in spawning reaches,
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1 removing fine material that blocks interstitial gravel flow and reduces the survival of incubating 2 eggs in egg pockets of redds. 3 4 The added spawner density resulting from hatchery-origin fish spawning in the wild can have 5 negative consequences at times. In particular, the potential exists for hatchery-derived fish to 6 superimpose or destroy the eggs and embryos of ESA-listed species when there is spatial overlap 7 between hatchery and natural spawners. Redd superimposition has been shown to be a cause of 8 egg loss in pink salmon and other species (e.g., Fukushima et al. 1998). 9 10 Adult Collection Facilities
11 The analysis also considers the effects from encounters with natural-origin fish that are 12 incidental to broodstock collection. Here, NMFS analyzes effects from sorting, holding, and 13 handling natural-origin fish in the course of broodstock collection. Some programs collect their 14 broodstock from fish voluntarily entering the hatchery, typically into a ladder and holding pond, 15 while others sort through the run at large, usually at a weir, ladder, or sampling facility. 16 Generally speaking, the more a hatchery program accesses the run at large for hatchery 17 broodstock – that is, the more fish that are handled or delayed during migration – the greater the 18 negative effect on natural-origin and hatchery-origin fish that are intended to spawn naturally 19 and on ESA-listed species. The information NMFS uses for this analysis includes a description 20 of the facilities, practices, and protocols for collecting broodstock, the environmental conditions 21 under which broodstock collection is conducted, and the encounter rate for ESA-listed fish. 22 23 NMFS also analyzes the effects of structures, either temporary or permanent, that are used to 24 collect hatchery broodstock, and remove hatchery fish from the river or stream and prevent them 25 from spawning naturally, on juvenile and adult fish from encounters with these structures. NMFS 26 determines through the analysis, for example, whether the spatial structure, productivity, or 27 abundance of a natural population is affected when fish encounter a structure used for broodstock 28 collection, usually a weir or ladder. 29 30 Factor 3. Hatchery fish and the progeny of naturally spawning hatchery fish in 31 juvenile rearing areas
32 NMFS also analyzes the potential for competition and predation when the progeny of naturally 33 spawning hatchery fish and hatchery releases share juvenile rearing areas. The level of effect for 34 this factor ranges from neutral or negligible to negative. 35 36 Competition
37 Generally speaking, competition and a corresponding reduction in productivity and survival may 38 result from direct or indirect interactions. Direct interactions occur when hatchery-origin fish 39 interfere with the accessibility to limited resources by natural-origin fish, and indirect 40 interactions occur when the utilization of a limited resource by hatchery fish reduces the amount 41 available for fish from the natural population (Rensel et al. 1984). Natural-origin fish may be 42 competitively displaced by hatchery fish early in life, especially when hatchery fish are more 43 numerous, are of equal or greater size, take up residency before naturally produced fry emerge 44 from redds, and residualize. Hatchery fish might alter natural-origin salmon behavioral patterns
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1 and habitat use, making natural-origin fish more susceptible to predators (Hillman and Mullan 2 1989; Steward and Bjornn 1990). Hatchery-origin fish may also alter natural-origin salmonid 3 migratory responses or movement patterns, leading to a decrease in foraging success by the 4 natural-origin fish (Hillman and Mullan 1989; Steward and Bjornn 1990). Actual impacts on 5 natural-origin fish would thus depend on the degree of dietary overlap, food availability, size- 6 related differences in prey selection, foraging tactics, and differences in microhabitat use 7 (Steward and Bjornn 1990). 8 9 Specific hazards associated with competitive impacts of hatchery salmonids on listed natural- 10 origin salmonids may include competition for food and rearing sites (NMFS 2012b). In an 11 assessment of the potential ecological impacts of hatchery fish production on naturally produced 12 salmonids, the Species Interaction Work Group (Rensel et al. 1984) concluded that naturally 13 produced coho and Chinook salmon and steelhead are all potentially at “high risk” due to 14 competition (both interspecific and intraspecific) from hatchery fish of any of these three species. 15 In contrast, the risk to naturally produced pink, chum, and sockeye salmon due to competition 16 from hatchery salmon and steelhead was judged to be low. 17 18 Several factors influence the risk of competition posed by hatchery releases: whether competition 19 is intra- or interspecific; the duration of freshwater co-occurrence of hatchery and natural-origin 20 fish; relative body sizes of the two groups; prior residence of shared habitat; environmentally 21 induced developmental differences; and density in shared habitat (Tatara and Berejikian 2012). 22 Intraspecific competition would be expected to be greater than interspecific, and competition 23 would be expected to increase with prolonged freshwater co-occurrence. Hatchery smolts are 24 commonly larger than natural-origin fish, and larger fish usually are superior competitors. 25 However, natural-origin fish have the competitive advantage of prior residence when defending 26 territories and resources in shared natural freshwater habitat. Tatara and Berejikian (2012) 27 further reported that hatchery-influenced developmental differences from co-occurring natural- 28 origin fish are variable and can favor both hatchery- and natural-origin fish. They concluded that 29 of all factors, fish density of the composite population in relation to habitat carrying capacity 30 likely exerts the greatest influence. 31 32 En masse hatchery salmon smolt releases may cause displacement of rearing natural-origin 33 juvenile salmonids from occupied stream areas, leading to abandonment of advantageous feeding 34 stations, or premature out-migration by natural-origin juvenile salmonids. Pearsons et al. (1994) 35 reported small-scale displacement of juvenile naturally produced rainbow trout from stream 36 sections by hatchery steelhead. Small-scale displacements and agonistic interactions observed 37 between hatchery steelhead and natural-origin juvenile trout were most likely a result of size 38 differences and not something inherently different about hatchery fish. 39 40 A proportion of the smolts released from a hatchery may not migrate to the ocean but rather 41 reside for a period of time in the vicinity of the release point. These non-migratory fish 42 (residuals) may directly compete for food and space with natural-origin juvenile salmonids of 43 similar age. Although this behavior has been studied and observed, most frequently in the case of 44 hatchery steelhead, residualism has been reported as a potential issue for hatchery coho and 45 Chinook salmon as well. Adverse impacts of residual hatchery Chinook and coho salmon on 46 natural-origin salmonids can occur, especially given that the number of smolts per release is
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1 generally higher; however, the issue of residualism for these species has not been as widely 2 investigated compared to steelhead. Therefore, for all species, monitoring of natural stream areas 3 in the vicinity of hatchery release points may be necessary to determine the potential effects of 4 hatchery smolt residualism on natural-origin juvenile salmonids. 5 6 The risk of adverse competitive interactions between hatchery- and natural-origin fish can be 7 minimized by: 8 9 • Releasing hatchery smolts that are physiologically ready to migrate. Hatchery fish 10 released as smolts emigrate seaward soon after liberation, minimizing the potential for 11 competition with juvenile naturally produced fish in freshwater (California HSRG 2012; 12 Steward and Bjornn 1990) 13 • Operating hatcheries such that hatchery fish are reared to a size sufficient to ensure that 14 smoltification occurs in nearly the entire population 15 • Releasing hatchery smolts in lower river areas, below areas used for stream-rearing by 16 naturally produced juveniles 17 • Monitoring the incidence of non-migratory smolts (residuals) after release and adjusting 18 rearing strategies, release location, and release timing if substantial competition with 19 naturally rearing juveniles is determined likely 20 21 Critical to analyzing competition risk is information on the quality and quantity of spawning and 22 rearing habitat in the action area,23 including the distribution of spawning and rearing habitat by 23 quality and best estimates for spawning and rearing habitat capacity. Additional important 24 information includes the abundance, distribution, and timing for naturally spawning hatchery fish 25 and natural-origin fish; the timing of emergence; the distribution and estimated abundance for 26 progeny from both hatchery and natural-origin natural spawners; the abundance, size, 27 distribution, and timing for juvenile hatchery fish in the action area; and the size of hatchery fish 28 relative to co-occurring natural-origin fish. 29 30 Predation
31 Another potential ecological effect of hatchery releases is predation. Salmon and steelhead are 32 piscivorous and can prey on other salmon and steelhead. Predation, either direct (consumption by 33 hatchery fish) or indirect (increases in predation by other predator species due to enhanced 34 attraction), can result from hatchery fish released into the wild. Considered here is predation by 35 hatchery-origin fish, the progeny of naturally spawning hatchery fish, and avian and other 36 predators attracted to the area by an abundance of hatchery fish. Hatchery fish originating from 37 egg boxes and fish planted as non-migrant fry or fingerlings can prey upon fish from the local 38 natural population during juvenile rearing. Hatchery fish released at a later stage, so they are 39 more likely to emigrate quickly to the ocean, can prey on fry and fingerlings that are encountered 40 during the downstream migration. Some of these hatchery fish do not emigrate and instead take 41 up residence in the stream (residuals) where they can prey on stream-rearing juveniles over a 42 more prolonged period, as discussed above. The progeny of naturally spawning hatchery fish 43 also can prey on fish from a natural population and pose a threat. In general, the threat from
23 “Action area” means all areas to be affected directly or indirectly by the action in which the effects of the action can be meaningfully detected and evaluated.
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1 predation is greatest when natural populations of salmon and steelhead are at low abundance, 2 when spatial structure is already reduced, when habitat, particularly refuge habitat, is limited, 3 and when environmental conditions favor high visibility. 4 5 (Rensel et al. 1984) rated most risks associated with predation as unknown because there was 6 relatively little documentation in the literature of predation interactions in either freshwater or 7 marine areas at the time. More studies are now available, but they are still too sparse to allow 8 many generalizations to be made about risk. Newly released hatchery-origin yearling salmon and 9 steelhead may prey on juvenile fall Chinook and steelhead and other juvenile salmon in the 10 freshwater and marine environments (Hargreaves and LeBrasseur 1986; Hawkins and Tipping 11 1999; Pearsons and Fritts 1999). Low predation rates have been reported for released steelhead 12 juveniles (Hawkins and Tipping 1999; Naman and Sharpe 2012). Hatchery steelhead release 13 timing and protocols used widely in the Pacific Northwest were shown to be associated with 14 negligible predation by migrating hatchery steelhead on fall Chinook fry, which had already 15 emigrated or had grown large enough to reduce or eliminate their susceptibility to predation 16 when hatchery steelhead entered the rivers (Sharpe et al. 2008). Hawkins (1998) documented 17 hatchery spring Chinook salmon yearling predation on naturally produced fall Chinook salmon 18 juveniles in the Lewis River. Predation on smaller Chinook salmon was found to be much higher 19 in naturally produced smolts (coho salmon and cutthroat, predominately) than their hatchery 20 counterparts. 21 22 Predation may be greatest when large numbers of hatchery smolts encounter newly emerged fry 23 or fingerlings, or when hatchery fish are large relative to naturally produced fish (Rensel et al. 24 1984). Due to their location in the stream or river, size, and time of emergence, newly emerged 25 salmonid fry are likely to be the most vulnerable to predation. Their vulnerability is believed to 26 be greatest immediately upon emergence from the gravel and then their vulnerability decreases 27 as they move into shallow, shoreline areas (USFWS 1994). Emigration out of important rearing 28 areas and foraging inefficiency of newly released hatchery smolts may reduce the degree of 29 predation on salmonid fry (USFWS 1994). 30 31 Some reports suggest that hatchery fish can prey on fish that are up to 1/2 their length (HSRG 32 2004; Pearsons and Fritts 1999), but other studies have concluded that salmonid predators prey 33 on fish 1/3 or less their length (Beauchamp 1990; Cannamela 1992; CBFWA 1996; Hillman and 34 Mullan 1989; Horner 1978). Hatchery fish may also be less efficient predators as compared to 35 their natural-origin conspecifics, reducing the potential for predation impacts (Bachman 1984; 36 Olla et al. 1998; Sosiak et al. 1979). 37 38 There are several steps that hatchery programs can implement to reduce or avoid the threat of 39 predation: 40 41 • Releasing all hatchery fish as actively migrating smolts through volitional release 42 practices so that the fish migrate quickly seaward, limiting the duration of interaction 43 with any co-occurring natural-origin fish downstream of the release site. 44 • Ensuring that a high proportion of the population have physiologically achieved full 45 smolt status. Juvenile salmon tend to migrate seaward rapidly when fully smolted,
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1 limiting the duration of interaction between hatchery fish and naturally produced fish 2 present within, and downstream of, release areas. 3 • Releasing hatchery smolts in lower river areas near river mouths and below upstream 4 areas used for stream-rearing young-of-the-year naturally produced salmon fry, thereby 5 reducing the likelihood for interaction between the hatchery and naturally produced fish. 6 • Operating hatchery programs and releases to minimize the potential for residualism. 7 8 Disease
9 The release of hatchery fish and hatchery effluent into juvenile rearing areas can lead to 10 transmission of pathogens, contact with chemicals or altering of environmental parameters (e.g., 11 dissolved oxygen) that can result in disease outbreaks. Fish diseases can be subdivided into two 12 main categories: infectious and non-infectious. Infectious diseases are those caused by pathogens 13 such as viruses, bacteria, and parasites. Noninfectious diseases are those that cannot be 14 transmitted between fish and are typically caused by genetic or environmental factors (e.g., low 15 dissolved oxygen). Pathogens can also be categorized as exotic or endemic. For our purposes, 16 exotic pathogens are those that have no history of occurrence within state boundaries. For 17 example, Oncorhynchus masou virus (OMV) would be considered an exotic pathogen if 18 identified anywhere in Washington state. Endemic pathogens are native to a state, but may not be 19 present in all watersheds. 20 21 In natural fish populations, the risk of disease associated with hatchery programs may increase 22 through a variety of mechanisms (Naish et al. 2008), including: 23 • Introduction of exotic pathogens 24 • Introduction of endemic pathogens to a new watershed 25 • Intentional release of infected fish or fish carcasses 26 • Continual pathogen reservoir 27 • Pathogen amplification 28 29 The transmission of pathogens between hatchery and natural fish can occur indirectly through 30 hatchery water influent/effluent or directly via contact with infected fish. Within a hatchery, the 31 likelihood of transmission leading to an epizootic (i.e., disease outbreak) is increased compared 32 to the natural environment because hatchery fish are reared at higher densities and closer 33 proximity than would naturally occur. During an epizootic, hatchery fish can shed relatively 34 large amounts of pathogen into the hatchery effluent and ultimately, the environment, amplifying 35 pathogen numbers. However, few, if any, examples of hatcheries contributing to an increase in 36 disease in natural populations have been reported (Naish et al. 2008; Steward and Bjornn 1990). 37 This lack of reporting is because both hatchery and natural-origin salmon and trout are 38 susceptible to the same pathogens (Noakes et al. 2000), which are often endemic and ubiquitous 39 (e.g., Renibacterium salmoninarum, the cause of Bacterial Kidney Disease). 40 41 Adherence to a number of state, federal, and tribal fish health policies limits the disease risks 42 associated with hatchery programs (IHOT 1995; NWIFC and WDFW 2006; ODFW 2003; 43 USFWS 2004). Specifically, the policies govern the transfer of fish, eggs, carcasses, and water to 44 prevent the spread of exotic and endemic reportable pathogens. For all pathogens, both 45 reportable and non-reportable, pathogen spread and amplification are minimized through regular
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1 monitoring (typically monthly) removing mortalities, and disinfecting all eggs. Vaccines may 2 provide additional protection from certain pathogens when available (e.g., Vibrio anguillarum). 3 If a pathogen is determined to be the cause of fish mortality, treatments (e.g., antibiotics) will be 4 used to limit further pathogen transmission and amplification. Some pathogens, such as 5 infectious hematopoietic necrosis virus (IHNV), have no known treatment. Thus, if an epizootic 6 occurs for those pathogens, the only way to control pathogen amplification is to cull infected 7 individuals or terminate all susceptible fish. In addition, current hatchery operations often rear 8 hatchery fish on a timeline that mimics their natural life history, which limits the presence of fish 9 susceptible to pathogen infection and prevents hatchery fish from becoming a pathogen reservoir 10 when no natural fish hosts are present. 11 12 In addition to the state, federal and tribal fish health policies, disease risks can be further 13 minimized by preventing pathogens from entering the hatchery facility through the treatment of 14 incoming water (e.g., by using ozone) or by leaving the hatchery through hatchery effluent 15 (Naish et al. 2008). Although preventing the exposure of fish to any pathogens prior to their 16 release into the natural environment may make the hatchery fish more susceptible to infection 17 after release into the natural environment, reduced fish densities in the natural environment 18 compared to hatcheries likely reduces the risk of fish encountering pathogens at infectious levels 19 (Naish et al. 2008). Treating the hatchery effluent would also minimize amplification, but would 20 not reduce disease outbreaks within the hatchery itself caused by pathogens present in the 21 incoming water supply. Another challenge with treating hatchery effluent is the lack of reliable, 22 standardized guidelines for testing or a consistent practice of controlling pathogens in effluent 23 (LaPatra 2003). However, hatchery facilities located near marine waters likely limit freshwater 24 pathogen amplification downstream of the hatchery without human intervention because the 25 pathogens are killed before transmission to fish when the effluent mixes with saltwater. 26 27 Noninfectious diseases are those that cannot be transmitted between fish and are typically caused 28 by genetic or environmental factors (e.g., low dissolved oxygen). Hatchery facilities routinely 29 use a variety of chemicals for treatment and sanitation purposes. Chlorine levels in the hatchery 30 effluent, specifically, are monitored with a National Pollutant Discharge Elimination System 31 (NPDES) permit administered by the Environmental Protection Agency. Other chemicals are 32 discharged in accordance with manufacturer instructions. The NPDES permit also requires 33 monitoring of settleable and unsettleable solids, temperature, and dissolved oxygen in the 34 hatchery effluent on a regular basis to ensure compliance with environmental standards and to 35 prevent fish mortality. In contrast to infectious diseases, which typically are manifest by a 36 limited number of life stages and over a protracted time period, non-infectious diseases caused 37 by environmental factors typically affect all life stages of fish indiscriminately and over a 38 relatively short period of time. One group of non-infectious diseases that are expected to occur 39 rarely in current hatchery operations are those caused by nutritional deficiencies because of the 40 vast literature available on successful rearing of salmon and trout in aquaculture. 41 42 Acclimation
43 One factor the can affect hatchery fish distribution and the potential to spatially overlap with 44 natural-origin spawners, and thus the potential for genetic and ecological impacts, is the 45 acclimation (the process of allowing fish to adjust to the environment in which they will be
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1 released) of hatchery juveniles before release. Acclimation of hatchery juvenile before release 2 increases the probability that hatchery adults will home back to the release location, reducing 3 their potential to stray into natural spawning areas. Acclimating fish for a period of time also 4 allows them to recover from the stress caused by the transportation of the fish to the release 5 location and by handling. (Dittman and Quinn 2008) provide an extensive literature review and 6 introduction to homing of Pacific salmon. They note that, as early as the 19th century, marking 7 studies had shown that salmonids would home to the stream, or even the specific reach, where 8 they originated. The ability to home to their home or “natal” stream is thought to be due to odors 9 to which the juvenile salmonids were exposed while living in the stream (olfactory imprinting) 10 and migrating from it years earlier (Dittman and Quinn 2008; Keefer and Caudill 2013). 11 Fisheries managers use this innate ability of salmon and steelhead to home to specific streams by 12 using acclimation ponds to support the reintroduction of species into newly accessible habitat or 13 into areas where they have been extirpated (Dunnigan 1999; Quinn 1997; YKFP 2008). 14 15 (Dittman and Quinn 2008) reference numerous experiments that indicated that a critical period 16 for olfactory imprinting is during the parr-smolt transformation, which is the period when the 17 salmonids go through changes in physiology, morphology, and behavior in preparation for 18 transitioning from fresh water to the ocean (Beckman et al. 2000; Hoar 1976). Salmon species 19 with more complex life histories (e.g., sockeye salmon) may imprint at multiple times from 20 emergence to early migration (Dittman et al. 2010). Imprinting to a particular location, be it the 21 hatchery, or an acclimation pond, through the acclimation and release of hatchery salmon and 22 steelhead is employed by fisheries managers with the goal that the hatchery fish released from 23 these locations will return to that particular site and not stray into other areas (Bentzen et al. 24 2001; Fulton and Pearson 1981; Hard and Heard 1999; Kostow 2009; Quinn 1997; Westley et al. 25 2013). However, this strategy may result in varying levels of success in regards to the proportion 26 of the returning fish that stray outside of their natal stream. (e.g., (Clarke et al. 2011; Kenaston et 27 al. 2001). 28 29 Having hatchery salmon and steelhead home to a particular location is one measure that can be 30 taken to reduce the proportion of hatchery fish in the naturally spawning population. By having 31 the hatchery fish home to a particular location, those fish can be removed (e.g., through fisheries, 32 use of a weir) or they can be isolated from primary spawning areas. Factors that can affect the 33 success of homing include: 34 • The timing of the acclimation, such that a majority of the hatchery juveniles are going 35 through the parr-smolt transformation during acclimation 36 • A water source unique enough to attract returning adults 37 • Whether or not the hatchery fish can access the stream reach where they were released 38 • Whether or not the water quantity and quality is such that returning hatchery fish will 39 hold in that area before removal and/or their harvest in fisheries. 40 41 Factor 4. Research, monitoring, and evaluation that exists because of the hatchery 42 program
43 NMFS also analyzes proposed RM&E for its effects on listed species and on designated critical 44 habitat. The level of effect for this factor ranges from positive to negative. 45
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1 Generally speaking, negative effects on the fish from RM&E are weighed against the value or 2 benefit of new information, particularly information that tests key assumptions and that reduces 3 uncertainty. RM&E actions can cause harmful changes in behavior and reduced survival; such 4 actions include, but are not limited to: 5 • Observation during surveying 6 • Collecting and handling (purposeful or inadvertent) 7 • Holding the fish in captivity, sampling (e.g., the removal of scales and tissues) 8 • Tagging and fin-clipping, and observing the fish (in-water or from the bank) 9 10 Observing/Harassing
11 For some parts of the proposed studies, listed fish would be observed in-water (e.g., by snorkel 12 surveys, wading surveys, or observation from the banks). Direct observation is the least 13 disruptive method for determining a species’ presence/absence and estimating their relative 14 numbers. Its effects are also generally the shortest-lived and least harmful of the research 15 activities discussed in this section because a cautious observer can effectively obtain data while 16 only slightly disrupting fishes’ behavior. Fry and juveniles frightened by the turbulence and 17 sound created by observers are likely to seek temporary refuge in deeper water, or behind/under 18 rocks or vegetation. In extreme cases, some individuals may leave a particular pool or habitat 19 type and then return when observers leave the area. At times, the research involves observing 20 adult fish, which are more sensitive to disturbance. These avoidance behaviors are expected to be 21 in the range of normal predator and disturbance behaviors. Redds may be visually inspected, but 22 would not be walked on. 23 24 Capturing/handling
25 Any physical handling or psychological disturbance is known to be stressful to fish (Sharpe et al. 26 1998). Primary contributing factors to stress and death from handling are excessive doses of 27 anesthetic, differences in water temperatures (between the river and holding vessel), dissolved 28 oxygen conditions, the amount of time fish are held out of the water, and physical trauma. Stress 29 increases rapidly if the water temperature exceeds 18ºC or dissolved oxygen is below saturation. 30 Fish transferred to holding tanks can experience trauma if care is not taken in the transfer 31 process, and fish can experience stress and injury from overcrowding in traps if the traps are not 32 emptied regularly. Decreased survival can result from high stress levels because stress can be 33 immediately debilitating, and may also increase the potential for vulnerability to subsequent 34 challenges (Sharpe et al. 1998). Debris buildup at traps can also kill or injure fish if the traps are 35 not monitored and cleared regularly. 36 37 Fin clipping and tagging
38 Many studies have examined the effects of fin clips on fish growth, survival, and behavior. The 39 results of these studies are somewhat varied, but fin clips do not generally alter fish growth 40 (Brynildson and Brynildson 1967; Gjerde and Refstie 1988). Mortality among fin-clipped fish is 41 variable, but can be as high as 80 percent (Nicola and Cordone 1973). In some cases, though, no 42 significant difference in mortality was found between clipped and un-clipped fish (Gjerde and 43 Refstie 1988; Vincent-Lang 1993). The mortality rate typically depends on which fin is clipped. 44 Recovery rates are generally higher for adipose- and pelvic-fin-clipped fish than for those that
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1 have clipped pectoral, dorsal, or anal fins (Nicola and Cordone 1973), probably because the 2 adipose and pelvic fins are not as important as other fins for movement or balance (McNeil and 3 Crossman 1979). However, some work has shown that fish without an adipose fin may have a 4 more difficult time swimming through turbulent water (Buckland-Nicks et al. 2011; Reimchen 5 and Temple 2003). 6 7 In addition to fin clipping, PIT tags and CWTs are included in the Proposed Action. PIT tags are 8 inserted into the body cavity of the fish just in front of the pelvic girdle. The tagging procedure 9 requires that the fish be captured and extensively handled, so it is critical that researchers ensure 10 that the operations take place in the safest possible manner. Tagging needs to take place where 11 there is cold water of high quality, a carefully controlled environment for administering 12 anesthesia, sanitary conditions, quality control checking, and a recovery holding tank. 13 14 Most studies have concluded that PIT tags generally have very little effect on growth, mortality, 15 or behavior. Early studies of PIT tags showed no long-term effect on growth or survival (Prentice 16 et al. 1987; Prentice and Park 1984; Rondorf and Miller 1994). In a study between the tailraces 17 of Lower Granite and McNary Dams (225 km), (Hockersmith et al. 2000) concluded that the 18 performance of yearling Chinook salmon was not adversely affected by orally or surgically 19 implanted sham radio tags or PIT tags. However, (Knudsen et al. 2009) found that, over several 20 brood years, PIT tag induced smolt-adult mortality in Yakima River spring Chinook salmon 21 averaged 10.3 percent and was at times as high as 33.3 percent. 22 23 Coded-wire tags are made of magnetized, stainless-steel wire and are injected into the nasal 24 cartilage of a salmon and thus cause little direct tissue damage (Bergman et al. 1968; Bordner et 25 al. 1990). The conditions under which CWTs should be inserted are similar to those required for 26 PIT tags. A major advantage to using CWTs is that they have a negligible effect on the biological 27 condition or response of tagged salmon (Vander Haegen et al. 2005); however, if the tag is 28 placed too deeply in the snout of a fish, it may kill the fish, reduce its growth, or damage 29 olfactory tissue (Fletcher et al. 1987; Peltz and Miller 1990). This latter effect can create 30 problems for species like salmon because they use olfactory clues to guide their spawning 31 migrations (Morrison and Zajac 1987). 32 33 Mortality from tagging is both acute (occurring during or soon after tagging) and delayed 34 (occurring long after the fish have been released into the environment). Acute mortality is caused 35 by trauma induced during capture, tagging, and release—it can be reduced by handling fish as 36 gently as possible. Delayed mortality occurs if the tag or the tagging procedure harms the animal. 37 Tags may cause wounds that do not heal properly, may make swimming more difficult, or may 38 make tagged animals more vulnerable to predation (Howe and Hoyt 1982; Matthews and Reavis 39 1990; Moring 1990). Tagging may also reduce fish growth by increasing the energetic costs of 40 swimming and maintaining balance. 41 42 NMFS has developed general guidelines to reduce impacts when collecting listed adult and 43 juvenile salmonids (NMFS 2000b; NMFS 2008a) that have been incorporated as terms and 44 conditions into section 7 opinions and section 10 permits for research and enhancement. 45 Additional monitoring principles for supplementation programs have been developed by the 46 (Galbreath et al. 2008).
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1 The effects of these actions should not be confused with handling effects analyzed under 2 broodstock collection. In addition, NMFS also considers the overall effectiveness of the RM&E 3 program. There are five factors that NMFS takes into account when it assesses the beneficial and 4 negative effects of hatchery RM&E: (1) the status of the affected species and effects of the 5 proposed RM&E on the species and on designated critical habitat, (2) critical uncertainties 6 concerning effects on the species, (3) performance monitoring and determining the effectiveness 7 of the hatchery program at achieving its goals and objectives, (4) identifying and quantifying 8 collateral effects, and (5) tracking compliance of the hatchery program with the terms and 9 conditions for implementing the program. After assessing the proposed hatchery RM&E and 10 before it makes any recommendations to the action agency(s) NMFS considers the benefit or 11 usefulness of new or additional information, whether the desired information is available from 12 another source, the effects on ESA-listed species, and cost. 13 14 Hatchery actions also must be assessed for masking effects. For these purposes, masking is when 15 hatchery fish included in the Proposed Action mix with and are not identifiable from other fish. 16 The effect of masking is that it undermines and confuses RM&E and status and trends 17 monitoring. Both adult and juvenile hatchery fish can have masking effects. When presented 18 with a proposed hatchery action, NMFS analyzes the nature and level of uncertainties caused by 19 masking and whether and to what extent listed salmon and steelhead are at increased risk. The 20 analysis also takes into account the role of the affected salmon and steelhead population(s) in 21 recovery and whether unidentifiable hatchery fish compromise important RM&E. 22 23 Factor 5. Construction, operation, and maintenance, of facilities that exist because of 24 the hatchery program
25 The construction/installation, operation, and maintenance of hatchery facilities can alter fish 26 behavior and can injure or kill eggs, juveniles, and adults. These actions can also degrade habitat 27 function and reduce or block access to spawning and rearing habitats altogether. Here, NMFS 28 analyzes changes to: riparian habitat, channel morphology, habitat complexity, in-stream 29 substrates, and water quantity and quality attributable to operation, maintenance, and 30 construction activities. NMFS also confirms whether water diversions and fish passage facilities 31 are constructed and operated consistent with NMFS criteria. The level of effect for this factor 32 ranges from neutral or negligible to negative. 33 34 Factor 6. Fisheries that exist because of the hatchery program
35 There are two aspects of fisheries that are potentially relevant to NMFS’ analysis of the Proposed 36 Action in a section 7 consultation. One is where there are fisheries that exist because of the 37 HGMP that describes the Proposed Action (i.e., the fishery is an interrelated and interdependent 38 action), and listed species are inadvertently and incidentally taken in those fisheries. The other is 39 when fisheries are used as a tool to prevent the hatchery fish associated with the HGMP, 40 including hatchery fish included in an ESA-listed salmon ESU or steelhead DPS, from spawning 41 naturally. The level of effect for this factor ranges from neutral or negligible to negative. 42 43 “Many hatchery programs are capable of producing more fish than are immediately useful in the 44 conservation and recovery of an ESU and can play an important role in fulfilling trust and treaty 45 obligations with regard to harvest of some Pacific salmon and steelhead populations. For ESUs
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1 listed as threatened, NMFS will, where appropriate, exercise its authority under section 4(d) of 2 the ESA to allow the harvest of listed hatchery fish that are surplus to the conservation and 3 recovery needs of the ESU, in accordance with approved harvest plans” (NMFS 2005c). In any 4 event, fisheries must be strictly regulated based on the take, including catch and release effects, 5 of ESA-listed species. 6 7 Araki, H., W. R. Ardren, E. Olsen, B. Cooper, and M. S. Blouin. 2007. Reproductive success of 8 captive-bred steelhead trout in the wild: Evaluation of three hatchery programs in the 9 Hood River. Conservation Biology 21(1):181-190. 10 Araki, H., B. A. Berejikian, M. J. Ford, and M. S. Blouin. 2008. Fitness of hatchery-reared 11 salmonids in the wild. Evolutionary Applications 1:342-355. 12 Ayllon, F., J. L. Martinez, and E. Garcia-Vazquez. 2006. Loss of regional population structure in 13 Atlantic salmon, Salmo salar L., following stocking. ICES Journal of Marine Science 14 63:1269-1273. 15 Bachman, R. A. 1984. Foraging behavior of free-ranging wild and hatchery brown trout in a 16 stream. Transactions of the American Fisheries Society 113(1):1-32. 17 Beacham, T. D., and coauthors. 2006. Pacific Rim population structure of Chinook salmon as 18 determined from microsatellite analysis. Transactions of the American Fisheries Society 19 135(6):1604-1621. 20 Beauchamp, D. A. 1990. Seasonal and diet food habit of rainbow trout stocked as juveniles in 21 Lake Washington. Transactions of the American Fisheries Society 119:475-485. 22 Beckman, B. R., and coauthors. 2000. Physiological status of naturally reared juvenile spring 23 Chinook salmon in the Yakima River: Seasonal dynamics and changes associated with 24 smolting. Transactions of the American Fisheries Society 129:727-753. 25 Beechie, T., and coauthors. 2013. Restoring Salmon Habitat for a Changing Climate. River 26 Research and Applications 29(8):939-960. 27 Bell, E. 2001. Survival, Growth and Movement of Juvenile Coho Salmon (Oncorhynchus 28 kisutch) Over-wintering in Alcoves, Backwaters, and Main Channel Pools in Prairie 29 Creek, California. September, 2001. A Thesis presented to the faculty of Humboldt State 30 University. 85p. 31 Bentzen, P., J. B. Olsen, J. E. McLean, T. R. Seamons, and T. P. Quinn. 2001. Kinship analysis 32 of Pacific salmon: Insights into mating, homing, and timing of reproduction. Journal of 33 Heredity 92:127-136. 34 Berejikian, B. A., and M. J. Ford. 2004. Review of Relative Fitness of Hatchery and Natural 35 Salmon. U.S. Dept. Commer., NOAA Tech. Memo., NMFS-NWFSC-61. 43p. 36 Bergman, P. K., K. B. Jefferts, H. F. Fiscus, and R. C. Hager. 1968. A preliminary evaluation of 37 an implanted, coded wire fish tag. Fisheries Research Papers, Washington Department of 38 Fisheries 3(1):63-84. 39 Berntson, E. A., R. W. Carmichael, M. W. Flesher, E. J. Ward, and P. Moran. 2011. Diminished 40 reproductive success of steelhead from a hatchery supplementation program (Little Sheep 41 Creek, Imnaha Basin, Oregon). Transactions of the American Fisheries Society 140:685- 42 698. 43 Bigg, M. 1982. An assessment of killer whale (Orcinus orca) stocks off Vancouver Island, 44 British Columbia. Report of the International Whaling Commission 32(65):655-666.
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