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A SYNTHESIS OF WATER QUALITY AND CONTAMINANTS DATA FOR THE SPOT, LEIOSTOMUS XANTHURUS FINAL DRAFT SEP, 1989 COASTAL ZONE INFORMATION CE-14TER SH 171 S" 1989 6, 7 1 FINAL DRAFT A SYNTHESIS OF WATER QUALITY AND CONTAMINANTS DATA FOR THE SPOT, LEIOSTOMUS XANTHURUS Lenwood W. Hall, Jr. Steven J. Bushong Steven A. Fischer and john A. Sullivan The Johns Hopkins University Applied Physics Laboratory Aquatic Ecclogy Section Shady Side, Maryland 20764 COASTAL ZONE INFO.'LrxMATION CENTER September, 1989 Preparation of this report was funded by the Coastal Resources Division, Tidewater Administration, Maryland Department of Natural Resources, through a CZM Program Implementation Grant f rom the Office of ocean and Coastal Resource Management, NOAA. MD W. P.' DRAFT INTRODUCTION The Chesapeake Bay is one of the largest and most productive estuaries in the world. This estuary provides spawning and nursery habitat for numerous species of fish. The abundance and distribution of fish species within the Bay are related to many variables such as climate, natural population cycles, reproductive potential, disease, predation, food and suitable habitat. Wohlfarth (1986) reported that overfishing and/or deterioration of habitat quality (contaminant and water quality problems) are usually the prime causes of dramatic and extended fish stock declines. In recent years, degrading habitat conditions resulting from adverse water quality and chemical contaminants in nursery or spawning areas have been suspected in reducing populations of various Chesapeake Bay fish species (Klauda and Bender, 1987). Various resident and anadromous fish species have declined in Chesapeake Bay while stocks of oceanic spawners--such as spot, Leiostomous xanthurus, have remained stable (Klauda and Bender, 1987). Spot spawn in nearshore marine waters in the winter but older larvae use the Chesapeake Bay as nursery areas in the spring. Juvenile spot are dominant in the Bay during the summer months. The vulnerable early life stages of spot (eggs and young larvae) are not exposed to potentially toxic Chesapeake Bay aquatic habitat conditions. Although contaminant and water quality problems have not caused a decline of spot in Chesapeake DRAFT Bay, it is important to identify adverse conditions that may affect the survival of the species if adequate management plans are to be implemented. Synthesis of these data can also be used to identify suitable habitat requirements. This document was developed to provide a synthes is and review of both water quality and contaminants data on various life stages of spot. Data contained in this document will be useful in the Toxics Reduction Strategy for the Chesapeake Bay program effort. A life history and ecology section on spot will be prepared by'other investigators and merged with this document to provide a complete review on the species. SUITABLE WATER QUALITY PARAMETERS Several water quality parameters suitable for survival of various life stages of spot are presented in Table 1. Various life stages may live outside of the parameters listed in Table 1; however, such conditions would be stressful. Data in Table 1 were obtained from Hettler and Clements (1978), Bridges (1971), Stickney and Cueneo (1982), Johnson (1978), PSE&G (1978), Ogren and Brusher (1977) and Tsai et al. (1979). Toxic water quality conditions are presented in a separate section of this document (Table 2). Suitable temperature ranges for eggs, larvae, juveniles and adults were > 14 C (upper limit not known), 10 - 37 C, 6 - 20 C and 6-36.7 C. The upper lethal limit for larvae (37 C) is 1 C below the Critical Thermal Maximum (CTM) at an acclimation 2 DRAFT temperature of 30 C. The 6 - 20 C range reported for juveniles is a preferred range; temperatures of 1.2 to 35.5 C can be tolerated. Suitable salinity conditions for juvenile,and adult spot were > 2 ppt. Dissolved oxygen concentrations > 5.0 mg/L were reported suitable for all life stages. Suspended solids concentrations below 50.6 g/L were suitable for juveniles. TOXIC WATER QUALITY CONDITIONS Toxic water quality conditions adversely affecting various life stages of spot are presented in Table 2. Each parameter is discussed separately in the following sections. TemRerature Temperature effects on various life stages of spot were evaluated in 15 different studies. Hettler and Clements (1978) reported that spot embryos will not develop at temperatures below 14 C. These investigators reported that pre-gastrula embryos suffered 50% mortality or greater when exposed to temperature increases of 8 to 14 C; older embryos were not affected by these thermal increases. Post-fertilized eggs exposed to a 12 C thermal increase above ambient temperatures for 30 min. suffered approximately 20% greater mortality than controls (Hettler and Clements, 1978). An 8 C thermal shock above ambient temperature caused no significant effect. Hettler and Clements (1978) reported that spot larvae can tolerate temperatures as low as 5 C. Although this temperature 3 DRAFT can be tolerated, other investigators have reported that feeding was reduced at 10 C and ceased completely at 6 C (Hoss et al., 1974). These investigators also reported unexpectedly high respiration rates at 10 C thus indicating cold stress at this temperature. Hettler and Clements (1978) reported that exposure time was a critical factor in determining mortality of I to 20 d old larvae exposed to temperature increases of 12 C above ambient. sixty pin. exposures were lethal to larvae while exposures of less than 15 min. had minimal effect. Hoss et al., (1974) reported that 12 C increases for 40 min. did not reduce survival or effect weight gain after 14 d. Bridges (1971) reported critical thermal maximum (CTM) values of 30, 34 and 38 C for spot larvae acclimated to 10, 20 and 30 C, respectively. CTM values increased with increasing fish size and increased salinity. other investigators reported CTM values of 28.4, 30.4 and 31..1 C for larvae acclimated to 5, 10 and 15 C, respectively (Hoss et al., 1974). Middaugh et al., (1975) determined a CTM value of 35 C using a temperature increase of 1 C / 5 min above ambient temperatures of 20 C. A lower CTM of 31.1 C was reported for larval spot at acclimation temperatures of 15 C (Hoss et al., 1971). An ultimate upper incipient lethal temperature of 35.2 C has also been reported for postlarval and juvenile spot (Hodson et al., 1981). Juvenile spot were reported to tolerate temperzitures ranging from 1.2 to 35.5 C but preferred temperatures of 6 to 20 C (Stickney and Cuenco, 1982). A lower lethal temperature of 4 to 4 DRAFT 5 C was reported by these investigators. Public Service Electric and Gas Company (1978) reported 96 h LT50 temperatures of 10 and 4.5 C for juveniles acclimated to 25 and 10 C, respectively. A preferred temperature of 25 C was reported for juveniles by these investigators. Peters et al., (1972) reported that optimum feeding occurred at 24 C, which was approximately equal to the preferred temperature (25 C) reported by Public Service Electric and Gas (1978). Meldrim and Gift (1974) reported that juvenile (subadult) spot avoided 26 and 30 C when acclimated to 20 and 27 C, respectively, at 20 foot candles. Spot acclimated to 26 C and 2 foot candles avoided 33 C. Burton (1979) reported 5 C increases in temperature above acclimation temperatures of 15 and 25 C caused significant increases in ventilation rate of juvenile spot. Increased ventilation rate was also reported after a 2.5 C increase in temperature above a 30 C acclimation temperature. This investigator also reported ventilation rates indicative of cold stress occurred at 5 C. 'Field studies conducted by Galloway and Strawn (1974) demonstrated that spot (unknown age) were attracted,to heated effluent during the cool winter months in Galveston Bay, Texas. Spot were most abundant at temperatures of 25 to 34 C but avoided temperatures greater than 37.5 C. SALINITY Salinity effects on juvenile and adult spot were evaluated 5 DRAFT in three studies. Juvenile spot were reported to tolerate large reductions in salinity (34 to 0 ppt) in one hour.-although oxygen consumption was reduced (Moser and Gerry, 1989). After 8 h of expos ure to freshwater, salinity was raised to 34 ppt and the oxygen consumption returned to normal. Public Service Electric and Gas Company (1978) conducted salinity tolerance tests using a wide range of salinity and temperature combinations and determined that survival of juvenile and adult spot was very low at salinity conditions less than 2 ppt. Perez (1969) showed that spot move faster in changing salinity regimes of 10 ppt but not 5 ppt. This investigator interpreted the increased swimming speed as avoidance behavior and suggested that rate of salinity change (not actual salinity) may limit the distribution of spot in estuaries. DISSOLVED OXYGEN Dissolved oxygen (D. 0.) effects on spot were evaluated in 5 different studies. Middaugh et al. (1975) reported 29% mortality to spot larvae after 24 h exposures to 1.6 mg/L. Similar 24 h exposures to 3.5 and 6.5 mg/L did not cause mortality. Burton et al. (1980) reported a 96 h LC50 of 0.7 mg/L D. 0. for juvenile and/or adult spot. Slightly lower LD50 values of 0.4 mg/L were reported for this species by Thorton (1975). This investigator reported that spot exhibited increased ventilation 'rates at less than 2.0 mg/L D. 0. with maximum respiratory compensation at 0.94 mg/L D. 0. Ogren and Brusher (1977) reported that juvenile spot 6 DRAFT inhabit waters with D. 0. concentrations as low as 1.3 to 5.4 * "0 mg/L. However, dissolved oxygen values above 5.0 mg/L were preferred. SUSPENDED SOLIDS The effects of suspended solids on spot were assessed in one study. Tsai et al. (1979) reported 24 and 48 h TLm. values of 50.61 g/L for juvenile spot using fullers earth as a clean sediment source. TOXICITY TO SINGLE CHEMICALS Toxicity data for various life stages of spot exposed to eighty-three single chemicals in saline water are presented in Table 3. Most of these data were generated from acute flow- through tests with pesticides. Limited toxicity data were available with early life stages of spot (eggs and larvae). Engle and Sunda (1979) evaluated the effects of copper (measured as cupric ion activity pCu) on spot eggs. An equation was used to calculate the cupric ion activity with pH-dependent, conditional and apparatus-stability constants for copper-tris complex. Conversion to standard ug/L units was therefore not possible. These investigators reported that survival of spot eggs was reduced by 50 % in 24 h at pCu of 8.8 (0.1 mM Cu). Percent hatch was inhibited after 4 d at less than b.4 pCu (greater than 0.02 mM Cu). Two acute toxicity studies were available for spot larvae. 7 DRAFT Foster (1987) reported a 96 h LC50 of 31 Ug/L (nominal concentration) for spot larvae exposed to hexachloro- cyclopentadiene. Middaugh et al. (1975) reported a 120 h LC50 of 600 ug/L for spot larvae exposed to cadmium. No mortality was reported at 100 ug/L Cd after 200 h of exposure. These investigators also reported that exposure of spot larvae to Cd concentrations greater than 500 ug/L for 96 h decreased the critical thermal maximum and reduced resistence to low dissolved oxygen stress. Toxicity data for juvenile and adult spot were grouped together and arranged alphabetically in Table 3. The most toxic chemicals to juvenile and adult s pot based on acute toxicity values were Endosulf an (96 h LC50 = 0. 09 ug/L) , Antimycin A (48 h LC50 = 0. 23 ug/L) , Endrin (48 h LC50 = 0. 3 ug/L) and Toxaphene (96 h LC50 = 0.92 ug/L). The least toxic chemicals to juvenile spot and adult spot were Mirex (48 h LC50 > 2000 ug/L) , Ametryn (48 h LC50 > 1000 ug/L) and Atrasine (96 h LC50 = 8,500 ug/L) . CONCLUSIONS 1. Populations of spot have remained stable in Chesapeake Bay in recent years. Spot spawn in nearshore marine waters in the winter therefore the vulnerable egg and young larvae are not exposed to potentially toxic Chesapeake Bay aquatic habitat conditions. 8 DRAFT 2. Suitable temperature ranges for egg, larval juvenile and adult spot were > 14 C, 10 - 37, 6 - 20 and 6 36.7 C. Salinity ranges > 2 ppt were considered suitable for juveniles and.adults. Suitable D. 0. conditions for all four life stages were > 5 mg/L. Suspended solids concentrations much less than 50.6 g/L were suitable for juvenile spot. 3. Spot embryos will not develop at temperatures below 14 C. Larvae can tolerate temperatures as low as 5 C although feeding is completely reduced at 6 C. Exposure time was a critical factor in determining mortality of 1 - 20 d old larvae exposed to temperature increases of 12 C above ambient; sixty min. exposures were lethal to larvae while exposures less than 15 min. had minimal effect. 4. Critical thermal maximum (CTM) of 30, 34, and 38 C were reported for spot larvae acclimated to 10, 20 and 30 C, respectively. Juvenile spot were reported to tolerate temperatures ranging from 1.2 to 35 .5 C but preferred temperatures of 6 to 20 C. Lower lethal temperatures of 4 to 5 C were reported for juvenile spot. ventilation rates indicative of cold stress were also reported at 5 C. 5. Juvenile spot can tolerate large reductions in salinity (34 ppt to 0 ppt) although survival is significantly reduced below 2 ppt. 9 DRAFT 6. Dissolved oxygen concentrations of 1.6 mg/L caused 29% mortality to spot larvae in 24 h. Dissolved oxygen concentrations of 0.4 to 0.7 mg/L were lethal to juve nile spot. 7. Toxicity data were available for various life stages of spot exposed to eighty-three chemicals in saline water. Limited toxicity data were available for spot eggs and larvae. A 96 h LC50 of 31 ug/L was reported for spot larvae exposed to hexachloro-cyclopentadiene. A 120 h LC50 of 600 ug/L was reported for spot larvae exposed to cadmium. The most acutely toxic chemicals to juvenile and adult spot were Endosulfan (96 h LC50 = 0. 09 ug/L) , Antimycin A (48 h LC50 = 0. 23 ug/L) Endrin (48 h LC50 = 0. 3 ug/L) and Toxaphene (96 h LC50 = 0. 92 ug/L) . REFERENCES Bellanca, M. A. and Bailey, D. S. Effects of chlorinated effluents on aquatic ecosystems in the lower James River. J. Water Poll. Control Fed. 49:639-645; 1977. Bridges, D. W. The critical thermal maximum of juvenile spot, Leiostomus xanthurus. Lacepede, Raleigh, North Carolina; Water Resources Research Institute, University of North Carolina, Report No. 43; 1971:39p. Burton, D. T. Ventilation frequency compensation r6sponses of three eurythermal estuarine fish exposed to moderate temperature increases. J. Fish Biol. 15:589-600; 1979. 10 DRAFT Burton, D. T. Evaluation of Pentron D-900 toxicity to juvenile estuarine fish and blue crabs. Bull Environ'm. Contam. Toxicol. 25:470-476; 1980. Burton, D. T.; Richardson, L. B. and Moore, C. J.. Effect of oxygen reduction rate and constant low dissolved oxygen concentrations on two estuarine fish. Trans. Amer. Fish Soc. 109:552-557; 1980. Engel, D. W. and Sunda W. G. Toxicity of cupric ion to eggs of the spot Leiostomu's xanthurus and the Atlantic silverside Menidia menidia. Mar. Biol. 50:121-126; 1979. Foster, L. M., Jr. Acute toxicity handbook of chemicals to estuarine organisms. Gulf Breeze, FL; United States Environmental Protection Agency, Environmental Research Laboratory, EPA/600/8-87/017; 1987:274p. Gallaway, B. J. and Strawn, K. Seasonal abundance and distribution of marine fishes at a hot-water discharge in Galveston Bay, Texas. Contrib. Mar. Sci. 18:71-137; 1974. Harder, H. W.; Carter, T. V. and Bidleman, T. F. Acute effects of toxaphene and its sediment-degraded products on estuarine fish. Can. J. Fish Aquat. Sci. 40:2119-2125; 1983. Hargis, W. J., Jr.; Roberts, M. H., Jr. and Zwerner, D. E. Effects of contaminated sediments and sediment-exposed effluent water on an estuarine fish: acute toxicity. Mar. Environ. Res. 14:337-354; 1984. Hartwell, S. I. and Hoss, D. E. Thermal shock resistance of spot (Leiostomus xanthurus) after acclimation to constant or 11 'DRAFT cycling temperature. Trans. Amer. Fish Soc. 108:397-400; 1979. Hawkins, W. E.; Tate, L. G. and Sarphie, T. G. Acute effects of cadmium on the spot Leiostomus xanthurus (Teleostei): tissue distribution and renal ultrastructure. J. Toxicol Environ. Health 6:283-295; 1980. Hettler, W. F. and Clements, L. C. Ef f ects of acute thermal stress on marine fish embryos and larvae. IN: L. D. Jensen (ed.) Fourth National Workshop on Entrainment and Impingement, p. 171-190, E. A. Communications, Ecological Analysts, Inc., Melville, N.Y.; 1978. Hodson, R. G.; Fechhelm, R. G. and Monroe, R. J. Upper temperature tolerance of spot, Leiostomus xanthurus, from the Cape Fear River Estuary, North Carolina.. Estuaries 4:345-356; 1981. Holland, H. T. and Lowe, J. 1. Malathion: Chronic effects on estuarine fish. Mosquito News, 26:383-385; 1966. Hoss, D. E.; Coston, L. C. and Hettler, W. F, Jr. Effects of increased temperature on post-larval and juvenile estuarine fish. Proc. 25th Ann. Conf. S. E. Assoc. Game Fish Comm., pp. 635-642; 1971. Hoss, D. E.; Coston-Clements, L.; Peters, D. S. and Tester, P.A. Metabolic responses of spot, Leiostomus xanthurus and Atlantic croaker, Micropogonias undulatus, larvae to cold temperatures encountered following recruitment to estuaries. Fish Bull. 86:483-488; 1988. 12 DRAFT Hoss, D. E.; Hettler, W. F., Jr.; and Coston, L. C. Effect of thermal shock on larval estuarine fish-ecol ogical implications with respect to entrainment in power plant cooling systems. -In: J.H.S. Blaxter (ed.) The early life history of fish. p. 357-371. Springer-Verlag, New York; 1974. Johnson, D. G. Development of Fishes of the Mid-Atlantic Bight. Vol 4. U. S. Fish Wildl. Serv. Biol. Serv. Prog. FWS/OBS 78/12; 1978. Klauda, R. J. and Bender, M. Contaminant effects on Chesapeake Bay finfishes. IN: S. K. Majumdar, L. W. Hall, Jr. and H. M. Austin (eds). Contaminant Problems and Management of Living Chesapeake Bay Resources. p. 321-372; Pennsylvania Academy of Science, Easton, PA; 1987. Liden, L. H. and Burton, D. T. Survival of juvenile Atlantic menhaden (Brevoortia tyrannus) and spot (Leiostomus xanthurus) exposed to brominechloride and chlorine-treated estuarine waters. J. Environ. Sci. Health. A12:375-388; 1977. Liden, L. H.; Burton, D. T.; Margrey, S. L.; Block, R. M. and Thoderick, J. C. Effects of chlorinated and bromochlorinated powerplant condenser cooling waters on survival and blood pH of Atlantic menhaden (Brevoortia tyrannus) and spot (Leiostomus xanthurus). ASB Bulletin 24:66; 1977. Lowe, J. I. Chronic exposure of spot, Leiostomus xanthurus, to 13 DRAFT sublethal concentrations of toxaphene in seawater. Tran. Am. Fish Soc. 93:396-399; 1964. Lowe, J. I. Some ef f ects of Endrin on . estuarine f ishes., Proc. Annu. Conf. Southeast. Assoc. Game and Fish Comm., 63:271- 276; 1965. Meldrim, J. W.; Gift, J. J. and Petrosky, B. R. The effect of temperature and chemical pollutants on the behavior of several estuarine organisms. Ichthyological Associates, Inc., Middletown, Delaware, Bulletin No. 11; 1974. Middaugh, D. P.; Crane, A.*M. and Couch, J. A. Toxicity of chlorine to juvenile spot, Leiostomus xanthurus. Water Res. 11:1089-1096; 1977. Middaugh, D. P.; Davis, W. R. and Yoakum, R. L. The response of larval fish, Leiostomus xanthurus, to environmental stress following sublethal cadmium exposure. Mar. Sci. 19:13-19; 1975. Moser, M. L. and Gerry, L. R. Differential effects of salinity changes on two estuarine fishes, Leiostomus xanthurus and Micropogonias undulatus. Estuaries 12:35-41; 1989. Ogren, L. H. and Brusher, H. A. The distribution and abundance of fishes caught with a trawl in the St. Andrews Bay system, Florida. Northeast Gulf Sci. 1:83-105; 1977. Parrish, P. R.; Couch, J. A.; Forester, J.; Patrick, J. M., Jr. and Cook, G. H. Dieldrin : effects on several bstuarine organisms. Proceedings 27th Annual Conf. Southeastern Assoc. Game and Fish Comm., pp. 427-434; 1973. 14 DRAFT Peters, D. S.; Kjelson, M. A. and Boyd, M. T.' The effect of temperature on food evacuation rate in the pinfish (Lagodon Rhomboides), spot (Leiostomus xanthurus) and silverside (Menidia -menidia). Proc. 26th Ann. Conf. Southeastern Assoc. Game and Fish Comm., pp. 638-643; 1972. Perez, K. T. An orthokinetic response to rates of salinity change in two estuarine fishes. Ecology, 50:454-457; 1969. Public Service Electric and Gas Company. Annual Environmental Operating Report (Nonradiological), Salem Nuclear Generating Station - Unit No. 1; Newark, N. J., Vol. 3; 1978. Richardson, L. B.; Burton, D. T. and Rhoderick, J. C. Toxicity of bromate to striped bass ichthyoplankton (Morone saxatilis) and juvenile spot (Leiostomus xanthurus). J. Toxicol. Environ. Health 8:687-695; 1981. Roberts, M. H., Jr. Survival of juvenile spot (Leiostomus xanthurus) exposed to bromochlorinated and chlorinated sewage in estuarine waters. Mar. Environ. Res. 3:63-80; 1980. Roberts, M. H., Jr. and Gleeson, R. A. Acute toxicity of bromochlorinated seawater to selected estuarine species with a comparison to chlorinated seawater toxicity. Marine Environ. Res. 1:19-30; 1978. Schimmel, S. C.; Patrick, J. M., Jr. and Forester, J. Heptachlor: Toxicity to and uptake by several estuarine organisms. J. Toxicol. Environ. Health, 1:955-965; 1976a. Schimmel, S. C.; Patrick, J. M. and Forester, J. Heptachlor: 15 DRAFT uptake, depuration, retention, and metabolish by spot, Leiostomus xanthurus. J. Toxicol. Environ. Health, 2:169- 178; 1976b. Schimmel, S. C.; Patrick, J. M., Jr. and Wilson, A. J., Jr. Acute toxicity to and bioconcentration of endosulfan by. estuarine animals. IN: F. L. Mayer and J. L. Hamelink (eds). Aquatic Toxicology and Hazard Evaluation, ASTM STP 634, pp. 241-253. American Society for Testing and Materials, Philadelphia, PA; 1977. Schimmel, S. C. and Wilson, A. J., Jr. Acute toxicity of kepone to four estuarine animals. Chesapeake Science, 18:224-227; 1977. Stehlik, L. L. and Merriner, J. V. Effects of accumulated dietary kepone on spot (Leiostomus xanthurus). Aquat. Toxicol. 3:345-358; 1983. Stickney, R. R. and Cuenco, M. L. Habitat suitability index models: Juvenile spot. U. S. Dept. Int. Fish Wildl. Serv. FWS/OBS-82/10.20; 1982, 12p. Subrahmanyam, C. B. Oxygen consumption of estuarine fish in relation to external oxygen tension Comp. Biochem. Physiol. 67A:129-133; 1980. Thornton, L. L. Laboratory experiments on the oxygen consumption and resistence to low oxygen levels of certain estuarine fishes. Newark, Delaware; University of Delaware; 1975. MS Thesis. Tsai, C.; Welch, J.; Chang, K. and Shaeffer, J. Bioassay of 16 DRAFT Baltimore harbor sediments. Estuaries 2:141-153; 1979. Ward, G. S. and Ballantine, L. Acute and chronic toxicity of atrazine to estuarine fauna. Estuaries 8:22-27; 1985. Weeks, B. A. and Warinner, J. E. Effects of toxic chemicals on macrophage phagocytosis in two estuarine fishes. mar. Environm. Res. 14:327-335; 1984. Wohlfarth, G. W. Decline in natural fisheries a genetic analysis and suggestion for recovery. Can J. Fish Aquatic Sci. 43:1298-1306; 1986. 17 Table 1. Suitable water quality parameters f or various life stages of the spot (NA not available). Life Temperature Salinity pH Dissolved Suspended Stage (C) (ppt) Oxygen Solids mg/L g/L Egg > 14a NA NA > 5 NA Larvae 10 - 37b NA NA > 5 NA Juvenile 6 - 20c > 2 ppt NA > 5 < 50.6d Adult 6 - 36.7 > 2 ppt NA > 5 NA Co Upper limit is not known b = 1 C below the CTM at an acclimation temperature of 30 C = Preferred temperature range but can tolerate 1.2 to 35.5 C .d = The 24 and 48 h TLM was 50.61 g/L. Suitable ranges of survival would be much less-. Table 2. Toxic water quality parameters adversely affecting various life stages of spot. (NA not available). Parameter Life Stage Data Reference Temperature Embryos and larvae Spot embryos did not develop at Hettler and temperatures below 14C. Larvae Clements, tolerated temperatures as low 1978 as 5C. Pregastrula embryos Suffered 50% mortality or greater at shock temperatures of -8C delta to 14C delta T. Early embryos z 50% mortality at a delta T of 14C. Mid-development Very little effect at temperature embryos shocks as great as -delta T of 14C. Post fertilized eggs Eggs receiving a -delta T of 12C shock above ambient temperatures for 30 min. suffered z 20% greater mortality than controls; 8C thermal shock showed no significant effect. Larvae 60 min. exposures to -delta T of 12C caused high mortalities (68-100%) in larvae of different ages (1-21d old). Exposures of :5 15 min. to -delta T of 12C had little impact. Table 2. (Continued) Parameter Life Stage Data Reference Temperature Larvae Critical thermal maximum was Middaugh determined to be z 35C using et al., a temperature increase rate 1975 of I.OC/5 min. Acclimation temperature was 20C. Temperature Larvae A 12C increase in temperature Hoss et al., (15C acclimation) for 40 1974 min. did not reduce survival or effect weight gain after- 14d. CTM values of 31.1, 30.4 and 28.40C were reported for fish acclimated at 15, 10 and 5C. respectively. Temperature Larvae Feeding ceased at 6C and was Hoss et al., reduced at 10C. Mortality was 1988 also evident at :5 10C. Unexpectedly high respiration rates at IOC also indicates cold stress in spot larvae at :5 10C. Temperature Post larvae and Ultimate upper incipient Hodson et Juveniles lethal temperature estimated al., 1981 at 35.2C. Increases in salinity increased resistance time but decreased lethal temperature estimates. Table 2. (Continued) Parameter Life Stage Data Reference Temperature Post larvae (19mm) Fish acclimated to 10, 20 and Bridges, 30C had CTM values of 30, 34 1971 and 38C, respectively, using a temperature increase of 1C per min. CTM values increased with increasing fish size, age and increased salinity. Temperature Post larvae Critical Thermal Maximum Hoss et al., 31.1C using fish acclimated 1971 at 15C and 30ppt salinity (temperature increase IC per min.) Fa A 5C thermal shock (15C to 20C) caused increased 02 consumption. A IOC thermal shock (15C to 25C) killed 50% of the spot in 4h. Temperature Post yolk-sac Fish acclimated to constant Hartwell and larvae temperatures were equally Hoss, 1979 sensitive to thermal shock as fish acclimated at cycling temperature � 4C). Fish acclimated at base temperatures of 10, 15, and and 20C suffered 50% mortality at instantaneous 20 min. temperature increases of 18.5, 16 and 12C, respectively. Table 2. (continued) Parameter Life Stage Data Reference Juveniles As with larvae, there was no difference between cycling and constant acclimation temperatures. Fish acclimated at base temperatures of 15, 20 and 25C suffered 50% mortality at instantaneous 20 min. temperature increases of 19, 15 and 10.5C, respectively. Temperature Juvenile Tolerate 1.2 - 35.5C, but Stickney and prefer 6 - 20C. Lower lethal Cuenco, 1982 temperature was between 4 - 5C. Temperature Juveniles 5C increases in temperature Burton, 1979 above acclimation temperatures of 15 and 25C caused significant increases in ventilation rate. A 2.5C increase in temperature above a 30C acclimation also caused increased ventilation rate. No mortality was observed after these 15 min. thermal shock exposures. Ventilation rates indicative of cold stress occurred at 5C. Temperature Juvenile and Adults Spot acclimated to 20 (4.5 ppt. Meldrim et salinity) and 27C (7.0 ppt. al., 1974 salinity avoided temperatures of 26 and 30C, respectively, when the light level was 20 foot- candles. Spot acclimated at 2 foot-candles light intensity. Table 2. (Continued) Parameter Life'Stage Data Reference Temperature Juveniles and Adults Fish were acclimated to a Public temperature range of 6 - 27C. service At an acclimation of 6CF Electric fish showed preference for and Gas 15C; at an acclimation of Company, 27C, fish showed preference 1978 for 250C. The = preferred temperature was 25C. Fish acclimated to 10C avoided temperatures of 19 - 24C. Fish acclimated to 30C avoided 34C. Juveniles and Adults 96 h LT50 temperatures for fish acclimated at 25C and 10C was 10C and 4.5C, respectively, in cold shock experiments. Temperature NA (wt 15-40g) Optimum feeding occurred at Peters et 24C with decreased feeding al., 1972 as temperatures deviated from the optimum. Temperature NA Fish sampling in Galveston Bay Gallaway and showed that spot were attracted Straw'n, 1974 to'heated effluents during cool months. Spot were most abundant at temperatures of 25 - 34C but avoided temperatures @t 37.5C. MM MM ,Table 2. (Continued) Parameter Life Stage Data Reference salinity Juvenile Spot demonstrated no aversion to Moser and crossing salinity gradients of Gerry, 1989 5 ppt. and 10 ppt. A drop in salinity from 34 ppt. to 0 ppt. in 1 hour caused a drop in oxygen consumption; however, after 8h the salinity was raised back to 34 ppt. and oxygen consumption returned to normal. Salinity Juveniles and Adults Low salinity tolerance tests Public were conducted over a range of Service of temperature and salinity Electric acclimation. Overall, survival and Gas of spot was very poor at < 2 ppt. Company, salinity. 1978 salinity Juvenile and Adults Spot demonstrated increased Perez, 1969 swimming speed during times of salinity change (10 ppt. change per hour; 12 ppt. - 17 ppt). Salinity changes of 5 ppt. per h did not elicit the same response. The increased swimming speed was interpreted as avoidance behavior. Dissloved Oxygen larvae Exposure to 1.6 mg/L D.O. Middaugh et (D.O.) (at 20 � IC) caused 29% al., 1975 mortality in 24 h. Equal exposures to 3.5 and 6.5 mg/L D.O. had no effect on survival. Table 2. (Continued) Parameter Life Stage Data Reference Dissolved oxygen Juvenile Inhabit waters with D.O. Ogren and concentrations as low as and Brusher, 1.3 - 5.4 mg/L, but most 1977 prefer concentrations > 5.0 mg/L. Dissolved oxygen Juvenile and Adults 96 h LC5 0.81 mg/L 02 Burton et 96 h LC50 0.7 mg/L 02 al., 1980 96 h LC95 0.6 mg/L 0, The lethal threshold conc. is approximately 0.7 mg/L 02 Dissolved oxygen NA Spot died at a critical Subrahmanyam, (length 85-87 mm) oxygen tension of P02 1980 Ln 24mmHg Dissolved oxygen NA LD50 = 0.4 ml/L D.O. Thornton, Spot exhibited increased 1975 ventilation rate at 5 2.0 m/L D.O. and maximum respiratory compensation at 0.94 m/L D.O. Suspended Solids Juvenile 24 h and 48 h TLM value Tsai et al., 50.61 g/L using fullers 1979 earth as a clean sediment source. Table 3. Toxicity data for Spot exposed to various single chemicals (NA = Not Available). All toxicity tests were conducted using flow-through conditions unless otherwise indicated as static. Life Chemical Water Test Data Reference Stage Type Temperature (C) Eggs Copper measured Saline 17 Survival of eggs was Engel and Sunda, as Cupric ion reduced 50% in 24 h in 1979 activity static conditions at pCu = 8.8 (O.lmMCu)(Cupric ion activity). Percent hatch was inhibited after 4 d at < 9.4,pCu (> 0.02mMCu). Larvae Hexachloro- Saline 25 96h LC50 = 31 ug/L (static) Foster, 1987 cyclopentadiene (22ppt) (Nominal) Larvae Cadmium Saline 15-22 Approx. 120 h LC50 600 Middaugh et al., (16-19ppt) ug/L incipient LC50 1975 200-300 ug/L. No mortality in 200 h at 100 ug/L. Larvae Cadmium Saline 17-20 Critical Thermal Maximum Middaugh et al., (17-20ppt) significantly decreased 1975 in fish preexposed to > 500 ug/L Cd for 96h. significant reduction in resistance to low dissolved oxygen stress in fish preexposed to @: 500 ug/L Cd for 96h. Adult Acephate Saline 25 96h LC50 > 100,000 ug/L Foster, 1987 (20ppt) (Static) (Nominal) @ M"M M M Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Adult Aldicarb saline 25 96h LC50 200 ug/L (20ppt) (static) (Nominal) Juvenile Aldrin saline 24 48h LC50 = 3.2 ug/L (28ppt) (Nominal) Juvenile Ametryn saline 28 48h LC50 > 1000 ug/L (29ppt) (Nominal) Juvenile Anilazine (Saline 29 48h LC50 8.5 ug/L (23ppt) (Nominal) Juvenile Antimycin A Saline 25 48h LC50 0.23 Mg/L (28ppt) (Nominal) Juvenile Atrazine Saline 28 48h LC50 > 1000 ug/L (29ppt) (Nominal) NA Atrazine Filtered 22 1 96h LC50 = 8500 ug/L Ward and seawater (Nominal) (Static) Ballantine, (12ppt) 1985 Juvenile Azinphos- saline 21 48h LC50 = 28 ug/L Methyl (21ppt) (Nominal) Adult Bensolide saline 25 48h LC50 = 320 ug/L (23-ppt) (Nominal) Juvenile Bromacil saline 13 48h LC50 > 1000 ug/L (18ppt) (Nominal) Juvenile Bromate Renewed 20.1 0.25 lod LC50 = 278,600 ug/L Richardson et Saline al., 1981 (5.1 � 1-Oppt) Ta% 1 eM3. Wco n t i! M M M M M M M M M M M. M Life Chemical Water Test Data Reference Stage Type Temperature (C) Juveniles Bromine Saline 19 28 96h LC50 = 220 ug/L Roberts and chloride (20ppt) Gleeson, 1978 Adult Cadmium Saline 22 1 48h LC50 = 35,000 ug/L Hawkins et al., (15ppt) (Static) 1980 A dult Cadmium Saline 22 1 48h exposures to @! io,ooo (15ppt) ug/L Cd caused severe renal damage. Proximal tubule cells demonstrated increased heterogeneous bodies and epithelial desquamation at @: 10,000 ug/L Cd. Mitochondria. damage was also reported. IQ I Adult Carbophenothion Saline 250C 96h LC50 = 500 ug/L (20ppt) (Static) (Nominal) Adult Carbophenothion Saline 260C 96h LC50 > 210 ug/L (24ppt) (Measured) Juvenile Chlordecone Saline 220C 48h LC50 = 130 ug/L Foster, 1987 (26ppt) (Nominal) Adult Chlordecone Saline 250C 96h LC50 = 6.6 ug/L (18ppt) (Measured) Juvenile Chloropi@opylate Saline 1410C 48h LC50 = 320 ug/L (26ppt) (Nominal) Juvenile Chlorothalonil Saline IIOC 48h LC50 = 32 ug/L (22ppt) (Nominal) = M = = = M = M M = M = M M = M = M M Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) NA Total residual Saline 14.2 - 16 24h TLm = 140 ug/L TRC Bellanca and chlorine (TRC) 96h TLm, = 90 ug/L TRC Bailey, 1977 After 96h: 100% mortality at @: 160 ug/L TRC; 0% mortality at :5 40 ug/L TRC. NA TRC Saline 16 - 26 Avoidance reported at Public Service (length (3-8ppt) concentrations ranging Electric & Gas 33-115mm) from 30 - 300 ug/L Co., 1978 TRC depending upon variables such as temperature, salinity and light level. Juvenile TRC Saline 10 0.5 Incipient LC50 = 120 Middaugh et (20-24ppt) ug/L TRC. No mortality al., 1977 was observed at 40 ug/L after 8 d. Juvenile TRC Saline 15 0.5 Incipient LC50 = 60 (20-24ppt) ug/L TRC (No mortality observed at 40 ug/L after 8 d). No pathological effects were noted in fish exposed to 600 ug/L TRC; however, fish exposed to 1,570 ug/L TRC demonstrated gill damage after 95 min. exposure. M MM MMMM Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenile TRC saline 10, 15 and A TRC concentration of (19-22ppt) 20 � 0.5 50 ug/L caused significant avoidance behavior at 15 and 20C. At 10, avoidance behavior was measured at 180 ug/L TRC. Juvenile TRC NA 15 acclimation; Exposure to 50 - 70 ug/L test temperatures TRC increased sensitivity to of 15, 20, to thermal shock only in one 25 and 28 condition (15C declimation to 28C for 60 min). Exposure to 340 - 520 ug/L TRC increased sensitivity to all thermal shock exposures. Juvenile Chlorinated Saline 29 32.4 No significant mortality Liden and bromochlorinated (2.Oppt) reported at 20 - 81 ug/L Burton, 1977 condenser cooling total residual bromine water after 19 d. Significant mortality was observed after 20 d exposure to 14 - 62 ug/L TRC compared to controls. M M M M M M M M M M M M M M M M M M M Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenil e DDE saline 12 48h LC50 > 100 ug/L (26ppt) (Nominal) Juvenile DEF Saline 27 48h LC50 = 240 ug/L (26ppt) (Nominal) Adult DEF saline 25 96h LC50 = 160 ug/L (20ppt) (Static) (Nominal) Adult DEF Saline 26 96h LC50 = 130 ug/L (20ppt) (measured) Juvenile Demeton Saline 26 48h LC50 = 320 ug/L (27ppt) (Nominal) Juvenile Diamidfos saline 21 48h LC50 > 1000 ug/L Foster, 1987 (29ppt) (Nominal) Juvenile Dicamba Saline 30 48h LC50 > 1000 ug/L (29ppt) (Nominal) Juvenile Dichlofluanid Saline 13 48h LC50 = 32 ug/L (29ppt) (Nominal) Juvenile Dichlorvos saline 28 48h LC50 = 320 ug/L (25ppt) (Nominal) Juvenile Dieldrin. Saline 12 24h LC50 = 3.2 ug/L (25ppt) (Nominal) M M M M M M M M M M M M M M M M M M M Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenile Dieldrin Unfiltered NA After 4d exposure to Parrish et in acetone sea water 1.35 ug/L, fish showed al., 1973 degenerative changes in gill and visceral tissue. No effects were reported at 5 0.135 ug/L after 35 d. Juvenile Dimetilan Saline 12 48h LC50 > 1000 ug/L (25ppt) (Nominal) Juvenile Endothall Saline 27 48h LC50 > 1000 ug/L Aquathol (28ppt) (Nominal) Plus LJ LJ Juvenile Endrin Saline 12 48h LC50 = 0.3 ug/L (24ppt) (Nominal) Juvenile Endrin Saline 17 24h LC50 = 0.45 ug/L Lowe, 1965 (23ppt) Concentrations of Endrin < 0.05 ug/L were sublethal to juveniles after continuous exposure for 8 months. Adult Endosulfan Saline mean = 25.0 96h LC50 = 0.09 ug/L Schimmel et in acetone (mean (measured) al.., 1977 (ThiodanO) 18ppt) Adult EPN Saline 24 96h LC50- 26 ug/L Foster, 1987 (23ppt) (measured) @ M M M M M M M M M M M M M M M M M M Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenile Ethion Saline 27 48h LC50 = 70 ug/L (31ppt) (Nominal) Adult Ethoprop Saline 25 96h LC50 = 33 ug/L (20ppt) (static) (Nominal) Juvenile Fenac Saline 13 48h LC50 > 1000 ug/L Sodium Salt (23ppt) (Nominal) Juvenile Fenthion Saline 19 48h LC50 = 1200 Ug/L (23ppt) (Nominal) Juvenile Fenuron Saline 25 48h LC50 > 1000 ug/L Foster, 1987 (20ppt) (Nominal) Juvenile Fonofos Saline 24 48h LC50 = 240 ug/L (28ppt) (Nominal) Juvenile Heptachlor Saline 25 1.5 100% mortality after Schimmel et al., in acetone (20 � 1.5ppt) 6d at a measured 1976b concentration of 2.55 ug/L. Juvenile Technical- Saline 23 - 26 96h LC50 = 0.85 ug/L Schimmel et al.1 grade (20 - 21ppt) 1976a Heptachlor (65%) in acetone Juvenile Analytical Saline 24.5 25.5 96h LC50 0.86 ug/L grade (20 - 22ppt) Heptachlor (99.8%) in acetone Table 3. (Continued) Life Chemical Water Test. Data Reference stage Type Temperature (C) Adult Hexachloro- Saline 25 96h LC50 = 37 ug/L cyclopentadiene (24ppt) (Static) (Nominal) Juvenile Isobenzan Saline 13 48h LC50 = 0.32 ug/L (22ppt) (Nominal) Juvenile Yepone in Saline 23 - 28 Fish fed a.diet Stehlik and food source (17.7 - 18ppt) contaminated with Merriner, 1983 3.3 ug/g Kepone developed muscular tetany, fractured vertebral centra and abnormally thickened vertebrae over a 4 week period. Some mortalities occurred in 1 week. Juvenile Kepone in Saline 16 23 Fish fed diets of 0.59 food source (20.3 - 21.8ppt) and 0.3 ug/g Kepone for 56 d had increased incidence of vertebral and spinal fractures. Juvenile Kepone in Saline 25 96h LC50 = 6.6 ug/L Schimmel and acetone (mean = 18.Oppt) Wilson, 1977 Juvenile Leptophos Saline 22 96h LC50 = 4.1 ug/L (23ppt) (measured) low:* ME Table 3. (continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenile Lindane Saline 15 48h LC50 23 ug/L (23ppt) (Nominal) Juvenile Malathion Saline 19 48h LC50 320 ug/L (24ppt) (Nominal) Juvenile Malathion Saline 23 29 Exposed for 182d to Holland and (2-5 - 2.7ppt) 10 ug/L and no Lowe, 1966 significant differences in growth or mortality were observed. Brain ChE was significantly lower in exper. groups, but 1 week after termination of the experiment, the fish had regenerated near normal levels of the enzyme. Adult Mercuric Saline 26 96h LC50 = 36 ug/L Chloride (20ppt) (Static) (Nominal) Juvenile Methidathion Saline 12 48h LC50 = 32 ug/L (25ppt) (Nominal) Juvenile Methoxychlor .Saline 22 48h LC50 = 23 ug/L (26ppt) (Nominal) Adult Methyl Saline 22 96h LC50 = 59 ug/L Parathion (12ppt) (measured) Juvenile Mirex Saline 22 48h LC50 > 2000 ug/L Foster, 1987 (27ppt) (Nominal) Table 3. (Continued) Life Chemical Water Test Data Reference Stage Type Temperature (C) Juvenile Molinate saline 25 48h LC50 > 1000 ug/L (20ppt) (Nominal) Juvenile Naled saline 20 48h LC50 = 240 ug/L (20ppt) (Nominal) Juvenile Neburon Saline 25 48h LC50 = 320 ug/L (20ppt) (Nominal) Adult Nickel saline 26 96h LC50 = 70,000 ug/L Chloride (21ppt) (Static) (Nominal) Juvenile Nitrapyrin saline 16 48h LC50 > 1000 ug/L (20ppt) (Nominal) Juvenile Parathion saline 14 48h LC50 = 18 ug/L (22ppt) (Nominal) Juvenile Pentron D-90 Saline 25 � I No mortality after Burton, 1980 (6.8ppt) 96 hours at 5000 ug/L (Static) Adult Phorate saline 25 96h LC50 = 3.9 ug/L (18ppt) (measured) Juvenile Phosphamidon Saline 23 48h LC50 > 1000 ug/L (29ppt) (Nominal) Juvenile Phoxim saline 29 48h LC50 = 2.8 ug/L (29ppt) (Nominal) Adult Potassium Saline 26 96h LC50 = 27 mg/L dichromate (21ppt) (Static) (Nominal) Table 3. (Continued) Life Chemical Water Test, Data Reference Stage Typpe Temperature (C) Juvenile Prometryn Saline 28 48h LC50 > 1000 ug/L (29ppt) (Nominal) Juvenile Ronnel Saline 13 48h LC50 = 320 ug/L Foster, 1987 (24ppt) (Nominal) Juvenile Silvex Saline 16 48h LC50 = 360 ug/L Propylene (20ppt) (Nominal) glycol butylether ester (KuronO) Juvenile 2,4,5-T Saline 16 48h LC50 = 320 ug/L Propylene (20ppt) (Nominal) glycol butylether ester Juvenile Temephos Saline 23 48h LC50 > 1000 ug/L (23ppt) (Nominal) Juvenile Terpene Saline 25 48h LC50 = 3.2 ug/L Polychlorinates (27ppt) (Nominal) Juvenile Tetrachlor- Saline 17 48h LC50 > 1000 ug/L vinphos (25ppt) (Nominal) Juvenile Tetrasul Saline 16 48h LC50 > 1000 ug/L (29ppt) (Nominal) Juvenile Thanite Saline 14 48h LC50 = 32 ug/L (22ppt) (Nominal) Juvenile Toxaphene Saline 12 48h LC50 = 3.2 ug/L (25ppt) (Nominal) NO.M min -M M M aft.-M-M M M M M M M M Table 3. (Continued) Life chemical Water Test. Data Reference Stage Type Temperature (C) Juvenile Toxaphene Saline Ambient 96h LC50 = 0.92 ug/L Harder et al., (in acetone) (32 - 35ppt) (min. temp 1983 18) Degraded 96h LC50 = 1.10 ug/L Toxaphene in acetone (allowed to degrade anaerobically in sediment for 20d at room temp). NA contaminated Saline 25 48h TLm valves ranged Tsai et al., Baltimore (5ppt) from 0.06 q/L - 29-12 g/L 1979 Harbor (static tests) of sediments contaminated sediment from suspended different Baltimore Harbor in water locations suspended in water. A Min valve of 50.61 g/L was obtained with clean sediment. Baltimore harbor sediments contained high levels of metals, Hexane extracts and PCB's- =Now Table 3. (continued) Data Reference Life Chemical water Test Stage Type Temperature pit (C) IIA Fish captured NA NA Macrophage phagocytosis Weeks and was markedly reduced in Warinner, in Elizabeth fish from the polluted 1984 River which is Elizabeth River compared highly contaminated to a nonpolluted "control" with polynuclear River. Macrophage aromatic phayocytosis returned to hydrocarbons (PAH) "control" levels in Elizabeth River fish that were held in clean water for several weeks. NA Elizabeth saline 20 27.8 Spot developed penetrating Hargis et al., River (16.3 - 20.4ppt) integumental lesions 1964 sediments within 8 d and later heavily severe fin and gill contaminated erosion. Mortality was with PAH (2,500,000 evident by d 2 with 3,900,000 ug/L 30% mortality in 18 d. PAH per dry Pancreatic and liver weight of sediments). alterations were also of sediments). observed in treatment fish. 1 36 6814 9946