Potential Effects of Contaminants on Fraser River Sockeye Salmon

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including cessation <strong>of</strong> egg-laying behaviour and reduction in mature sperm. Similarly,spawning success was reduced by 80% in three-spined sticklebacks (Gasterosteusaculeatus) fed high doses <strong>of</strong> a commercial PBDE mixture (Bromkal 70-5DE) for a 3.5month period (the tissue concentration was 1630 µg/kg lipid; Holm et al. 1993).Importantly, juvenile lake trout (Salvelinus namaycush) fed diets containing high (25ng/g per PBDE congeners) or low (2.5 ng/g per PBDE congeners) levels <strong>of</strong> 13 PBDEcongeners had lower levels <strong>of</strong> plasma thyroxine than did control fish, indicating thatthese contaminants may influence thyroid homeostatis in fish (Tomy et al. 2004). Inrainbow trout, dietary exposure to PBDE-47 for six or more days resulted in a 75%reduction in ethoxyresorufin-O-deethylase (EROD) activity, indicating that ERODactivity may be a good indicator <strong>of</strong> exposure <strong>of</strong> salmonid fishes to PBDEs (Tjarnlundet al. 1998).In mammals, PBDEs are known to be neurotoxic, thyrotoxic, estrogenic, and possiblycarcinogenic. However, the data needed to identify the concentrations <strong>of</strong> PBDEs inwater, diet, or fish tissues that are sufficient to cause developmental dysfunctions,thyroid hormone imbalances, vitellogenin induction, or tumour induction/promotionhave not been established. Therefore, it is possible that PBDEs could cause adverseeffects in fish at concentrations lower than those associated with larval mortality orspawning success.No data were located on the toxicity <strong>of</strong> PBBs to fish. However, the results <strong>of</strong> studieson mammalian species indicate that these chemicals cause reproductive effects inmonkeys and elicit carcinogenic effects in other species (Siddiqi et al. 2003). Reducedgrowth, egg production, and egg hatchability were observed in chickens exposed toPBBs in dietary exposure studies (Darnerud 2003). A tolerable daily intake <strong>of</strong> 0.15µg/kg body weight (BW) has been established for PBBs in humans to protect againstcarcinogenic effects (based on a no observed adverse effect level <strong>of</strong> 0.15 mg/kg BW;IPCS 1994).Given the relative dearth <strong>of</strong> information on PBDEs and PBBs, it is clear that furtherinvestigations are needed to establish toxicity thresholds <strong>of</strong> these substances forsockeye salmon utilizing habitats within the Fraser River and its tributaries.Legacy Organochlorine and Other Pesticides - A number <strong>of</strong> organochlorine pesticideshave been identified as endocrine disrupting compounds. Some <strong>of</strong> these chemicalsappear to the antiestrogenic (i.e., endosulfan), while others appear to be capable <strong>of</strong>inducing vitellogenesis in male fish (DDTs and methoxychlor). For example91
Chakravorty et al. (1992) observed declines in plasma vitellogenin levels in femalecatfish (Clarias batrachus) exposed to endosulfan (nominal concentration <strong>of</strong> 1.5 µg/L)for 16 days. Similarly, male sheephead minnows exposed to endosulfan atconcentrations <strong>of</strong> 0.28 to 0.79 µg/L for 40-d did not accumulate detectable levels <strong>of</strong>vitellogenin in their plasma (Hemmer et al. 2001).Hemmer et al. (2001) also evaluated vitellogenin induction in male sheepsheadminnows exposed to methoxychlor at concentrations <strong>of</strong> 5.6 and 12.1 µg/L. Theresults <strong>of</strong> this experiment indicated that the parent compound was not estrogenic.However, the demethylated metabolites can bind to the estrogen receptor. At bothexposure levels, plasma vitellogenin levels increased rapidly, reaching 120 mgvitellogenin/mL <strong>of</strong> plasma in the high exposure group by day 35.Reproductive effects have been observed in fish exposed to the carbamate insecticidecarb<strong>of</strong>uran. In female dwarf gourami (Colisa lalia), 20-d aqueous exposures to thissubstance (i.e., at 0.7 µg/L) resulted in the production <strong>of</strong> fewer mature oocytes and ahigher incidence <strong>of</strong> atresia <strong>of</strong> mature oocytes (oocycte absorption; Sukumar andKarpagaganapathy 1992).Exposure to DDTs is also known to cause reproductive effects in fish. Cheek et al.(2001) exposed Japanese medaka to nominal concentrations <strong>of</strong> 2,4'-DDT rangingfrom 0 to 7.5 µg/L for two or eight weeks after hatching. The results <strong>of</strong> this studyshowed that 8-week exposures to this substance induced vitellogenin production in all<strong>of</strong> the treatment groups. Female-skewed sex ratios were observed at the two highestdoses, while an increased incidence <strong>of</strong> ovotestis was observed in fish exposed to 1.94µg/L <strong>of</strong> 2,4'-DDT for eight weeks. Dietary exposure <strong>of</strong> Atlantic croakers(Micropogonias undulatus) to 0.02 or 0.1 µg 2,4'-DDT/g BW/day for three or sevenweeks resulted in increased plasma gonadotropin hormone levels and increased ovarysize (as indicated by gonadosomatic index scores; Khan and Thomas 1998).In chinook salmon, short-term exposure to 2,4'-DDT (at 10 mg/L) at fertilization (1-hexposure) and at hatch (2-h exposure) did not adversely affect mortality rate, time tohatch, fish length, or fish weight at one month following first feeding (Milston et al.2003). Similarly, sex ratios, gonadal development, and concentrations <strong>of</strong> plasmaestradiol and 11-ketotestosterone were unaffected by the treatment. However, earlylife stage exposure to this substance resulted in long-term humoral immuneincompetence (i.e., immunosuppression) in chinook salmon, which could increase92
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February 2011technical report 2<str
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thresholds), which represent lowest
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Table of ContentsE
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5.5 Summary of the
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List of TablesTabl
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Table 4.17Table 4.18Table 4.19Table
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Table 4.47Table 4.48Table 4.49Table
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Table 6.4Table 8.1Compounds for Nat
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Figure 3.17 Map of
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Figure 5.20 Late Stuart Sockeye Sal
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List of Acronyms2,
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AcknowledgementsThe authors would l
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To assist it in fulfilling this man
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• Development of
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Chapter 2 Geographic and Temporal S
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life history of th
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• Pitt River Area of</str
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Chapter 3 Inventory of</str
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and Paper Mills - Canfor Pulp Limit
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3.1.1.2 Sawmills, Plywood Mills and
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(ENKON Environmental Ltd. 2001). Co
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Effluent toxicity was also included
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2011 for more information on the lo
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facilities identified in Table 3.11
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Inc.), poultry processing facilitie
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• Polycyclic aromatic hydrocarbon
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3.1.1.11 Municipal Wastewater Treat
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• Personal care products (fragran
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with oxytetracycline, ormetoprim, a
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In summary, the contaminants that c
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insecticides, such as phorate, terb
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Page 77 and 78: • Data collected for migration co
Page 79 and 80: Hazard quotients were calculated fo
Page 81 and 82: Many other substances have the pote
Page 83 and 84: Chapter 5 Evaluation of</st
Page 85 and 86: For surface water and sediment, the
Page 87 and 88: 3. For hardness-dependent water qua
Page 89 and 90: • 2,3,7,8-TCDD toxic equivalents
Page 91 and 92: concern by area of
Page 93 and 94: 0.05 mg/L; Glew and Hames 1971). As
Page 95 and 96: least time rearing in freshwater ha
Page 97 and 98: The results of thi
Page 99 and 100: Interest and in the South Thompson
Page 101 and 102: • Polychlorinated dibenzo-p-dioxi
Page 103 and 104: glycoproteins, polypeptides, peptid
Page 105 and 106: In-use herbicides in the Fraser Riv
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Page 109 and 110: Pulp and paper mills, saw mills, an
Page 111 and 112: salinity tolerance were significant
Page 113 and 114: and gonadosomatic index scores were
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Page 117: Spitsbergen et al. (1991) reported
Page 121 and 122: observed in saltwater gobies (Chasm
Page 123 and 124: (See Chapters 4 and 5 for further i
Page 125 and 126: emoval efficiency of</stron
Page 127 and 128: point and non-point source discharg
Page 129 and 130: Location of NatalS
Page 131 and 132: Nevertheless, it is possible that e
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Page 135 and 136: these substances to aquatic ecosyst
Page 137 and 138: • Alkylphenol ethoxylates (APEOs;
Page 139 and 140: chemicals of poten
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Page 143 and 144: • Sufficiency - For a cause and e
Page 145 and 146: infection by various disease agents
Page 147 and 148: magnitude, and spatial extent <stro
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Page 151 and 152: pathways and the intensity and exte
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Page 155 and 156: • The majority of</strong
Page 157 and 158: 7.4.6 Information on Interactive <s
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Page 161 and 162: 8.4 Preliminary Evaluation
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Page 167 and 168: 8.9 RecommendationsThis evaluation
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Chapter 9 References CitedAdams, R.
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Braune, B., D. Muir, B. DeMarch, M.
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EIP Associates. 1997. Polychlorinat
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Gallaugher, P. and L. Wood (Eds). P
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Hinch, S.G. and E.G. Martins. 2011.
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Kemble, N.E., D.K. Hardesty, C.G. I
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MacLatchy, D., L. Peters, J. Nickle
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Milston, R.H., M.S. Fitzpatrick, A.
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Peterman, R.M., D. Marmorek, B. Bec
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Smith, D.B., R.A. Zielinski, H.E. T
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USACE (U.S. Army Corps of</
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Walker, M.K., J.M. Spitsbergen, J.R
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Table 2.1. Overview of</str
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Table 2.2. Sampling sites for Early
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Table 2.3. Sampling sites for summe
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Table 2.4. Sampling sites for river
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Table 3.1. Listing of</stro
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Table 3.2. Chemicals of</st
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Table 3.8. Major pipelines transpor
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Table 3.10. Locations of</s
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Table 3.11. Listing of</str
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Table 3.16. List of</strong
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Table 3.17. List of</strong
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Table 3.18. Location of</st
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Table 3.20. Summary of</str
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Table 3.23. Estimated annual contam
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Table 3.28. Inventory of</s
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Table 4.1. Selected toxicity screen
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Table 4.2. Selected toxicity screen
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Table 4.3. Summary of</stro
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Table 4.19. Evaluation of</
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Table 4.32. Frequency of</s
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Table 4.53. Identification
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Table 5.1. Selected toxicity refere
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Table 5.2. Selected toxicity refere
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Table 5.3. Exposure point concentra
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Table 5.9. Hazard quotients <strong
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Table 5.11. Hazard quotients <stron
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Table 5.19. Hazard quotients <stron
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Table 5.23. Mean concentrations <st
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Table 6.2. Effects
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Table 6.3. Field studies of
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Table 6.4. Compounds for National r
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Table 8.1. Inventory of</st
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Figures
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Figure 5.1. Water Quality Index sco
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Figure 5.3. Fraser River Sockeye Sa
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Figure 5.5. Pitt Sockeye Salmon Pro
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Figure 5.7. Weaver Sockeye Salmon P
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Figure 5.9. Cultus Sockeye Salmon P
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Figure 5.11. Portage Sockeye Salmon
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Figure 5.13. Fennell Sockeye Salmon
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Figure 5.15. Late Shuswap Sockeye S
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Figure 5.17. Chilko Sockeye Salmon
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Figure 5.19. Early Stuart Sockeye S
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Figure 5.21. Stellako Sockeye Salmo
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Figure 5.23. Bowron Sockeye Salmon
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Appendices
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SW4 Deliverables4.1 The Contractor
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obtained on one species, sometimes
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• For substances for which the se
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WeaknessesThere is a lot of
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Pg 110 Ln 4189 - now called Listene
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the potential effects of</s
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A-14
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4. Fish processing plants are fewer
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Appendix 3. Environmental Data Sour
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4. Keyword searches for water quali
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A3.5 Contaminant Spill ReportsData
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River Pulp, Kamloops Cellulose Fibr
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Table A3.1. Water quality stations
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Table A3.1. Water quality stations
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Appendix 4. Data Treatment and Meth
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when multiple samples were reported
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$ Early rearing of
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i) The number of t
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In addition, some sockeye salmon (e
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• Selecting probable effect conce
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deBruyn, A.M., H. deBruyn, M.G. Iko
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Appendix 5. Data description and so
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