/Steven A. Fischer, Lenwood W. Hall and John A. Sullivan. Fischer, Steven A. Sullivan, John A. Hall, Lenwood W. [Shady Side, Md.:Johns Hopkins University,1989] Fish-culture Environmental aspects Chesapeake Bay (Md. and Va.) Water quality management Chesapeake Bay (Md. and Va.) Fisheries Environmental aspects Chesapeake Bay ((Md. and Va.) Yellow perch Chesapeake Bay (Md. and Va.) A SYNTHESIS OF WATER QUALITY AND CONTAMINANTS DATA FOR YELLOW PERCH, PERCA FLAVESCENS FINAL DRAFT Sep 1989 COASTAL ZONE INFORIvIATION Cr,-NTER SH 171 S96 1989 (71 5% FINAL DRAFT A SYNTHESIS OF WATER QUALITY AND CONTAMINANTS DATA FOR YELLOW PERCH, PERCA FLAVESCE.NS Steven A. Fischer -Lenwood W. Hall, Jr. and John A. Sullivan -The Johns Hopkins University Applied Physics Laboratory Aquatic Ecology Section Shady Side, Maryland COASTAL ZONE 'NFORMATION CENTEF, September, 1989 Preparation of this report was funded by the Coastal Resources Division, Tidewater Administration, Maryland Department of Natural Resourcesi through a CZM Program Implementation Grant from the Office of ocean and Coastal Resource Management, NOAA. 'T INTRODUCTION The unique physical, chemical and biological parameters of the Chesapeake Bay create a suitable environment for numerous fish species. The abundance and distribution of resident and migratory f ish species which utilize the Bay, as well as the recruitment potential of estuarine-reared oceanic fish species, are influenced by variables such as climate, reproductive potential, parasites, disease, natural population cycles, food availability and suitable habitat. overharvesting of commercial and recreational f ish@ species and habitat destruction (water quality and contaminants) are 'the primary factors resulting in dramatic and prolonged fish stock declines (Wohlfarth, 1986; Setzler-Hamilton, 1987; Speir, 1987). Habitat degradation resulting from adverse water quality and chemical contaminants have been suspected recently of reducing several Chesapeake Bay fish species populations (Hendrey, 1987; Klauda and Bender, 1987). The extent and degree of spawning and nursery habitat degradation resulting from deleterious contaminant and water quality conditions within the Chesapeake Bay and related tributaries are major considerations when attempting to manage particular fish species. Populations of anadromous and resident fish species, including the yellow perch (Perca flavescens), have recently declined within the Chesapeake Bay (Hendrey, 1987; Klauda and Bender, 1987). Due to such drastically low yellow perch stocks in the Chesapeake Bay, the state of Maryland instituted a partial ban effective in 1989. The ban prevents the collection of yellow perch by any method from 11 river systems around the Bay. The new regulation also prohibits the sale of yellow perch during the entire month of February. In addition, a creel limit of 5 yellow perch per person per day with a minimum length limit of 216 mm was implemented. Yellow perch are residents of the Bay and spawn within the poorly buffered coastal plain freshwater tributaries. Yellow perch eggs and larvae are exposed to potentially detrimental acidic pulses. More definitive data concerning water quality and contaminant effects on the early life history stages of yellow perch are required if adequate management plans are to be implemented. Synthesis of the data can also be used to identify suitable habitat requirements. This document was developed to provide a compilation and review of both water quality and contaminants data on various life stages of yellow perch. 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 yeliow perch will be prepared by other investigators and merged with this document to provide a complete review of the species. 2 TOXIC WATER-QUALITY COI@DITIONS Toxic water quality conditions adversely affecting various life stages of yellow perch are presented in Table .1. Each parameter is discussed separately in the following sections. Temperature Temperature effects on yellow perch embryos, larvae, juveniles and adults were evaluated in 19 different studies. Hokanson (1977a) reported that yellow perch require increased temperatures during early ontogenetic development. Hokanson and Kleiner (1974) and Hokanson (1977b) indicated minimum and maximum median tolerance limits (TLSO) for yellow perch egg stages were 6.8 and 19.9 C, respectively. Hatching varied from 2 d at 18.2 C to 30.5 d at 3.3 C according to Hokanson and Kleiner (1974). Hardy (1978) indicated that hatching occurred in 11 - 13 d at 15 C in freZ:@water, wh---)e 13 - 15 d were required at 1.55 C in 5.8 ppt salinity. Yellow perch larvae exhibited a temperature preference of 21.7 - 24.3 C when acclimated at 20 - 25 C (Ross et al. 1977). Hale and Carlson (1972) reported a 63% survival rate for larvae fed at 20 - 21 C, which is similar to the preference range reported by Ross et al. (1977). A temperature tolerance range of 10 - 30 C for feeding larvae was reported by Hokan'son (1977b), while Hubbs (1971) reported that larvae fed when temperatures 3 were as low as 9.5 C. Significant mortality to larvae, acclimated between 13.5 - 17 C, occurred only as a result of a 15 C temperature increase in an experiment designed to simulate primary entrainment with pressure-temperature shock (PSE&G, 01 1978). They also reported no significant difference in mortality between control and treatment groups when larvae, acclimated at 16.5 C, were exposed to test temperatures of 19.0 - 24.5 C for 0.5 - 4 h. McCauley and Read (1973) and Cherry et al. (1977) reported juvenile yellow perch selected a temperature range of 19 - 23 C when acclimated at 24 C and 15 - 24 C, respectively. Neill and Magnuson (1974) reported young-of-the-year (YOY) pe-rch selecteda similar temDerature (23 C) during a laboratory thermal preference experiment. Reynolds and Casterlin (1979) reported that age-0 yellow perch exhibited a diel rhythum of preferred temperature, with a predawn minimum of 16.7 C and a dusk maximum of 23.8 C. Optimum growth conditions for juvenile yellow perch were approximately equal to the preferred temperature (22 C) with 16 h of light (Huh et al., 1976). Conversely, McCormick (1976) reported significantly greater growth rates at 26 - 30 C when held at constant temperatures. He also reported little to no growth at 8 C and total mortality within 7 d at 34 C. Growth of juvenile yellow perch occurred within a temperature range of 6 - 31 C (Hokanson, 1977b). Barans and Tubb (1973) collected YOY and adult yellow perch seasonally to compare temperature preference ranges between the two life stages. They reported that YOY 4 yellow perch selected temperature ranges 4 C greater than those selected by adults during spring, summer, and fall, but YOY selected a temperature range 2 C lower than adults during the winter. Hokanson and Kleiner (1974) also reported the juvenile stage was more thermally tolerant than the adult stage.. Hokanson and Kleiner (1974) reported that 24.7 C was the physiological optimum temperature for adult yellow perch. Ross and Siniff (1982) reported that adult yellow perch preferred a median temmerature of 6.3 C when exposed to a winter thermal effluent of 0 - '15 C. This winter temperature preference differs from that of Barans and Tubb (1973) who collected adult yellow perch during the winte.--- in the range of 12 - 16 C. Meldrim and Gift (1971) reported that adult perch acclimated at 15 C (6 ppt salinity) and 25 C (freshwater) preferred 23.5 C and 22.5 C, respectively. Thermal avoidance tests were also conducted by Meldrim and Gift (1971). Two groups of adult yellow perch acclimated at 25 C and different light levels avoided temperatures greatr--r than 33 C. PSE&G (1978) reported a similar avoidance range (31 - 34 C) when acclimated at 25 C in freshwater. PSE&G (1978) data also indicated that saltwater increased the upper avoidance temperature in adult yellow perch. Avoidance temperatures of 14 - 18 C and 27 C were reported when adult yellow perch were acclimated at 6 C in freshwater and saltwater (1.5 ppt salinity) environments, respectively. Two investigators reported that rheotactic responses were the cause of behavioral changes exhibited by adult yellow perch 5 encountering heated thermal effluent (Kelso, 1976; MacLean, 1982). salinity Salinity effects on yellow perch eggst larvae, YOY and adults were evaluated in four studies. Muncy (1962) reported that spawning occurred in freshwater and in brackish areas with less than 2.5 ppt salinity. Hatching success of yellow perch eggs decreased with increased salinity ranging from 0 - 11.7 ppt (Muncy, 1962). He also reported a 2 d hatching delay in saltwater (5.8 ppt) versus freshwater at 15 C. Muncy (1962) also reported hatching success ranged from 65 - 42% when salinity conditions varied from 0 - 2.43 ppt. Klauda et al. (1988) conducted a preliminary salinity tolerance laboratory experiment of 8 and 26 d old yellow perch larvae. Mortality estimates for 8 and 26 d old larvae at 3 ppt salinity were 40% and 28%, respectively. Mortality estimates for 8 and 26 d old larvae at 6 ppt salinity were 25% and 18%, respectively. Neither age-group survived longer than 48 h in 12 and 24 ppt salinity. Muncy (1962) reported that YOY perch were collected in salinities ranging from 0.5 - 9.5 ppt. Seine hauls from the Severn River (Annapolis, MD) indicated that YOY yellow perch were most abundant in 5 - 7 ppt salinity (Muncy 1962). Actual field data represents the only salinity information regarding adult yellow perch since no laboratory salinity 6 preference experiments have been conducted. Driver and Garside (1966) and Muncy (1962) both reported that adult yellow perch inhabit salinities ranging from 0.0 - 10.3 ppt, while Hardy (1978) reported that adult yellow perch were collected from waters with salinities up to 15 ppt. Dissolved Oxygen The effects of low dissolved oxygen (D.O.) on larval and juvenile yellow'perch were examined in two studies. Petit (1973) reported a lethal D.O. concentration of 0.84 mg 02/L for yellow perch larvae at 23 C. This D.O. concentration was not lethal for YOY tested at 15.1 C, which may have been the result of a lowered metabolic rate. Carlson et al. (1980) indicated that growth of juvenile yellow perch was not significantly affected when mean D.O. concentrations were > 3.5 mg 02/L, while growth was significantly reduced when D.O. concentrations were < 2.0 mg 02/L. IDH Eight studies were conducted to evaluate the effects of pH on various life history stages of yellow perch. Yellow perch eggs were exposed to four pH levels (5.0 - 7.0) an'd five nominal aluminum concentrations (0 - 400 ug/L) during a series of flow- through experiments (janicki and Greening, 1988). They reported that mean egg mortality (62%) was significantly greater at pH 5.0 with no aluminum during a 15 d exposure than in the less acidic test conditions (40 -45%). The addition of aluminum did not significantly influence mortality rates. Klauda et al. (1988) reported that yellow perch larvae could tolerate 12 - 24 h acidic pulses of pH 5.0. These investigators also reported that 17 d old feeding larvae were more sensitive to acid pulses of pH 4.0 than were pre@-feeding larvae. They concluded that yellow perch is a relatively acid tolerant species that can sustain reproducing populations when mean pH is 5.0. Correll et al. (1987) indicated that significant differences in the survival of newly hatched (12 h old) yellow perch larvae existed between pH 5 and 7 even though greater than 50% of the larvae survived at pH 5.0. The addition of 100 ug/L of nominal inorganic monomeric aluminum at pH 5.0 reduced survival of yellow perch larvae. from > 50% (pH 5.0 with no aluminum) to 5% (Swenson et al. 1989). Klauda (1989) proposed that critical acidic conditions for early life history stages of yellow perch occur between pH 4.5 - 5.5, and includes inorganic monomeric aluminum concentrations between 50 - 150 ug/L with dissolved calcium levels at least 2 mg/L. The acid tolerance of YOY and adult yellow perch collected from lakes with ambient pH > 6.0 was tested under laboratory conditions (Rahel and Magnuson, 1983). It was reported that both YOY and adults survived longer than 10 d at pH 3.05 in 19 C 8 water. Lyons (1982) examined blood sodium concentrations in adult yellow perch from a naturally acidic (pH 4.6) and a naturally alkaline lake (pH 7.9). He reported that exposure to lethal acidity (ph 3.2) for 48 h resulted in significant but similar decreases in plasma sodium levels in both populations. Factors other than significant decreases in blood sodium levels were assumed responsible for mortality in the yellow perch populations. Rahel (1983) reported that adult yellow perch from acidic lakes (pH 4.5) survived longer than adults from alkaline lakes (pH 7.6) when exposed to pH 3.2 for 21 d. This suggests possible genetic adaptations to low pH conditions. The survival of adult yellow perch at pH 10.4 was similar for organisms previously exposed to acidic and alkaline lakes (Rahel, 1983). Susnended Sediment Several studies designed to evaluate the effects of suszended solids an yellow perch eggs and larvae in the Chesapeake Bay have been conducted. Schubel and Wang (1973) reported fine-grained suspended sediment in concentrations <500 mg/L had no significant effect on hatching success of yellow perch eggs. However, they did report a 6 - 12 h delay in hatching at 100 and 500 mg/L suspensions. Schubel et al. (1973) conducted additional tests and reported that a 1000 mg/L suspension significantly reduced hatching success 'of yellow perch eggs. Conversely, Auld and Schubel (1974) exposed eggs to the 9 same conditions and found no significant reduction in hatching success. Minimal information exists concerning the effect of suspended solids on yellow perch larvae. survival was significantly reduced when yellow perch larvae were exposed for 96 h to concentrations of suspended solids > 500 mg/L (Auld and Schubel, 1974). TOXICITY TO SINGLE CHEMICALS Acute toxicity data for larval and juvenile yellow perch exposed to 56 single chemicals are presented in Tables 2 and 3, respectively. The majority of the acute toxicity research for yellow perch was conducted at the Columbia National Fisherids Research Laboratory (Mayer and Ellersieck, 1986). The deleterious effects of total residual chlorine (TRC) to yellow perch larvae were greatly enhanced in saltwater versus freshwater. PSE&G (1978) reported 50% mortality when larvae were exposed to 0.55 mg/L TRC for 0.5 h in 3.5 ppt salinity at 16 C. Seegert et al. (1977) reported a 24 h LC50 value of 4.0 mg/L TRC when larvae were exposed for 0.5 h in a freshwater environment at 15 C. The acute toxicity of one inorganic compound on yellow perch larvae was investigated by Fung and Bewick (1980). They reported 1 h LC50 values of 1.55 and 0.046 mg/L hydrogen sulfide at 10 and 20 C, respectively. Acute toxicity datd for larvae exposed to 42 organic compounds are presented in Table 2. The 10 most toxic substances (expressed as 96 h LC501s) were the pesticides Antimycin A (0. 040 ug/L) , S-bioallethrin (7.8 ug/L) DDT (9. 0 ug/L) and toxaphene (12 ug/L) (Mauck et al., 1976; Mayer and Ellersieck, 1986). Toxicity data for yellow perch juveniles were available from six studies (Table 3). Brooks and Seegert (1977) reported 24 h LC50 values of TRC for YOY yellow perch were inversely related to temperature. A study by Marking and Olsen (1975) indicated 3- trifluoromethyl-4-nitrophenol (TFM) was more toxic to juvenile yellow perch than to older age-0 yellow perch. Toxicity data from three inorganic compounds (hydrogen cyanide, hydrogen sulfide and potassium permanganate) are list-ad in 7able 3. Hydrogen sulfide was the most toxic to juvenile yellow perch with a 96 h LC50 value of 8 ug/L (Fung and Bewick, 1980). Acute toxicity data for juveniles exposed to 7 organic compounds are presented in Table 3. The most toxic chemicals (expressed as 96 h LC50's) were RU-11679 (0.06 ug/L), endrin (0.15 ug/L) and resmethri.n. (0.51 ug/L) (Mayer and Ellersieck, 1986). TOXICITY'TO CHEMICAL MIX=ES One acute toxicity chemical mixture experiment was conducted with juvenile yellow perch., Seeyle et al. (1988) graphically presented 24 h LC25 values for numerous combinations of the piscicides TFX and Bayer-73 at 33 different alkalinities (40 - 11 200 mg/L CaC03)- Juvenile yellow perch sensitivity to TFM and mixtures of TFM and Bayer-73 decreased as alkalinity increased. IN-SITU STUDIES Four in-situ contaminant studies have been conducted with yellow perch eggs, larvae, YOY and adults (Table 4). Schofield and Driscoll (1987) reported that only 3.8% of the yellow perch eggs collected in a near-neutral lake.(pH 6.6), with 0 - 30 ug/L total monomeric aluminum, hatched when placed in an acidic lake (PH 5.0 with 190 - 230 ug/L total monomeric aluminum) . Hatching success for eggs spawned and hatched in the neutral lake was 86.2%. A hatching success rate of 43.5% was reported for eggs deDosited and hatched in the acidic lake (PH 5.0) (Schofield and Driscoll, 1987). Similar to Rahel (1983), Schofield and Driscoll (1987) concluded that yellow perch exhibited genetic adaptation to acid stress. In-situ tests.were also conducted in two Maryland coastal plain streams by Janicki and Greening (1988). They reported an 8.4% egg mortality rate as PH decreased to 6.0 and total monomeric aluminum peaked at 55 ug/L during a 4 d storm event in Mattawoman Creek. In Bacon Ridge Creek, egg mortality rates ranged from 0.3 - 50.0% as pH decreased to 6.4 and total monomeric aluminum peaked at 20 ug/L. Janicki and Greening (1988) did not offer any suggestions as to why higher mortalities were observed in the less acidic system, although Klauda (1989) suggested that suspended sediments, turbulence, and 12 current velocity may have affected the mortality rates. Greening et al. (1989) reported that yellow perch eggs were relatively insensitive to chemical changes during four storm events in the same two streams studied by Janicki and Greening (1988). They recorded egg mortality rates of 0 - 23.7% in Mattawoman Creek at pH minimums of 5.8 - 6.0, dissolved calcium concentrations of 3.1 - 5.6 mg/L, and total monomeric aluminum maxima of 69 ug/L. Mortality rates ranged from 2.5 - 12.5 % in Bacon Ridge Creek as pH ranged from 5.8 - 6.0, dissolved calcium concentrat" ions were 5.7 - 8.2 mg/L, and total monomeric aluminum peaked at 52 ug/L. Greening e"-* al. (1988) also examined mor-tality rates of larval yellow perch. They reported that larvae were more sensitive than eggs when exposed to acidic storm events. Mortality rates for yellow perch larvae in Mattawoman Creek ranged from 51.5 - 100% as pH minima ranged from 5.8 - 6.3, with total monmeric aluminum maxima at 69 ug/L and dissolved calcium between 3.1 - 7.3 mg/L. At Bacon Ridge Creek, a 92.3% larval mortality rate was recorded at a pH minima of 5.8, with total monomeric aluminum of 52 ug/L and dissolved calcium between 5.7 8.2 mg/L. Schofield and Driscoll (1987) reported a 72% survival rate when YOY perch were transferred from a neutral lake (pH 6.9) to an acidic lake (pH 4.6) for a 28 d in-situ experiment. They concluded that non-native species (yellow perch) exhibited greater acid tolerance than native cyprinids. 13 Adult yellow perch were placed into wire' mesh cages in the Hudson River (below a suspected contaminant source) for 14 d to show the rapid bioaccumulation of the polychlorinated biphenyl (PCB), Aroclor 1016 (Skea et al., 1979). Control groups were located upstream of the suspected contaminant source. The PCB concentration was calculated daily from the river water below the contaminant source. Concentrations of Aroclor 1016 found within the exposed adult yellow perch were greater than 10,000 times the concentrations present in the water. CONCLUSIONS 1. Yellow perch populations within the Chesapeake Bay have 01 declined in recent years. Spawning occurs in poorly buffered coastal plain freshwater tributaries of the Chesapeake Bay. Eggs and larve are thus exposed to potentially deleterious acidic pulses. 2. Hatching occurred in 2 d at 18.2 C, while 30.5 d were required at 3.3 C. Median thermal tolerance limits for yellow perch eggs were 7 20 C. Feeding larvae tolerated a temperature range of 10 30 C, while 20 - 24 C appears to be the optimum range. optimum growth conditions for juveniles occurred at 22 C with 16 h of light. A diel temperature preferenda was reported for age-O yellow perch; maximun 14 preferred temperature occurred at dusk. The physiological optimum temperature for adult yellow perch is 24.7 C. 3. Spawning occurs in freshwater and brackish water with less than 2.5 ppt salinity. Hatching success of yellow perch decreased as salinity increased from 0 - 2.4 ppt salinity. Larvae survived for 72 h at salinities < 6 ppt, but no survival was observed after 48 h exposure to salinities > 12 ppt. Adults have been collected in salinities ranging from 0 15 ppt. 4. A dissolved oxygen (D.O.) concentration of 0.84 mg/L was lethal to larval yellow perch exposed at 23 C, but was not lethal after exposure at 15 C. Growth of age-O yellow perch was significantly reduced when D.O. concentrations were < 2.0 mg/L. 5. Yellow perch is considered a relatively acid tolerant species, however, the data suggests adults can survive and spawn in acidic waters that are potentially detrimental to fertilized eggs. Mortality of yellow perch eggs was significantly greater at pH 5.0 than at other less acidic conditions. Larvae tolerated a 12 - 24 h exposure to an acid pulse of > pH 5.0, while survival decreased from > 50% to 5% with the addition of 100 ug/L aluminum at pH 5.0. A proposed critical acidic condition exists for early life stages of 15 yellow perch exposed to pH 4.5 - 5.5, with inorganic monomeric aluminum concentrations between 50 - 150 ug/L and dissolved calcium levels at least 2 mg/L. Adult yellow perch collected from naturally acidic waters (pH 4.5) exhibit a possible genetic adaptation to low pH conditions over adults from alkaline lakes (pH 7.6). 6. Concentrations of 100 - 500 mg/L suspended solids caused a 6 - 12 h delay in hatching of yellow perch eggs. Survival of larvae was significantly reduced when exposed for 96 h to concentrations > 500 mg/L suspended solids. 7. Acute toxicity data for larval yellow perch exposed to 44 single chemicals indicated that the pesticides Antimycin- A, S-bioallethrin, DDT and toxaphene were most toxic. Toxicity data for juveniles exnosed to 13 single chemicals indicated the insecticides RU-11679, endrin, and resmethrin were most toxic. 8. An inverse relationship existed between alkalinity and the sensitivity of juvenile yellow perch to 3-trifluoromethyl-4- nitrophenol (TFM) and mixtures of TFM and Bayer-73. 9. 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Effects of dissolved oxygen on survival and behavior of selected f ishes of western Lake Erie. Ohio Bio. Sur. Bull. 4; 1973, 80 p. Public Service Electric and Gas company (PSE&G). Annual Environmental operating Report (Nonradiological) ; Salem Nuclear Generating Station - Unit 1; 1977 Report, Vol. 3; Newark, NJ; 1978. Rahel, F. J. Population differences in acid tolerance between yellow perch, Perca flavescens, from naturally acidic and alkaline lakes. Can. J. Zool. 61:147-152; 1983. Rahel, F. J. and Magnuson, J. J. Low pH and the absence of fish species in naturally acidic Wisconsin lakes: inferences for cultural acidification. Can. j. Fish. Aquat. Sci. 40:3-9; 1983. Reynolds, W. W. and Casterlin, M. E. Behavioral thermoregulation and locomotor activity of Perca flavescens. Can. J. Zool. 57:2239-2242; 1979. Ross, J.; Powles, P. M. and Berrill, M. Thermal selection and related behavior in larval yellow perch. Can. Field Nat. 91:406-410; 1977. Ross, M. J. and Siniff, D. B. Temperatures selected in a power plant thermal effluent by yellow perch (Perca flavescens) in winter. Can. J. Fish. Aquat. Sci. 39:346-349; 1982. Schofield, C. L. and Driscoll, C. T. Fish species distribution in relation to water quality gradients in the north branch of the Moose River basin. Biogeochem.. 3:63-85; 1987. 22 Schubel, J. R.; Auld, A. H. and Schmidt, G. M. Effects of suspended sediment on the development and hatching success of yellow perch and striped bass eggs. Proc. Annu. Conf. Southeast. Assoc. Game Fish Comm. 27:689-694; 1973. Schubel, J. R. and Wang, J. C. S. The effects of suspended sediment on the hatching success of Perca flavescens (yellow perch), Morone americana (white perch), Morone saxatilis (striped bass), and Alosa pseudcharencrus (alewife) eggs. Spec. Rep. 30, Chesapeake Bay Institute, Johns Hopkins Univ., Ref.' 73-3; 1973, 77 p. Seegert, G. L.; Brooks, A. S. and Latimer, D. L. The effects of a 30-minute exmosure of selected Lake Ylich-4gan fishes and invertebrates to residual chlorine. In: L. D. Jensen (ed) Biofouling Control Procedures Technology and Ecological Effects, Marcel Dekker, Inc., New York, NY; 1977, p. 91-100. Seeyle, J. G.; Johnson, D. A.; Weise, J. G. and King, E. L., Jr. Guide for determining application rates of lampricides for control of sea lamprey ammocetes. Great Lakes Fish. Comm. Tech. Rep. 52; 1988, 23 p. Setzler-Hamilton, E. M. Utilization of Chesapeake Bay by early life history stages of fishes. In: Majumdar, S. K.; Hall, L. W., Jr. and Austin, H. M. (eds) Contaminant Problems and Management of Living Chesapeake Bay Resources, p. 63-93. Penn. Acad. Sci., Easton, PA; 1987. Skea, J. C.; Simonin, H. A.; Dean, H. J.; Colquhoiin, J. R.; Spagnoli, J. J. and Veith G. D. Bioaccumulation of Aroclor 23 1016 in Hudson River fish. Bull. Environm. Contam. Toxi@ol. 22:332-336; 1979. Smitht L. L.; Broderius, S. J.; Oseid, D. M.; Kimball, G. L. and Koenst, W. M. Acute toxicity of hydrogen cyanide to freshwater fishes. Arch. Environm. Contam. Tox'icol. 7:325- 337; 1978. Speir, H. J. Status of some finfish stocks in the Chesapeake Bay. Water Air Soil Pollut. 35:49-62; 1987. Swenson, W. A.; McCormick, J. H.; Simonson, T. D.; Jensen, K. M. and Eaton, J. G. Experimental acidification of Little Rock Lake (Wisconsin): fish research approach and early responses. Arch. Environ. Contam. Toxicol. 18:167-174; 1989. Wohlfarth, G. W. Decline in natural fisheries - a genetic analysis and suggestions for recovery. Can. J. Fish. Aquat. Sci. 43:1298-1306; 1986. 24 Table I. Toxic water quality parameters adversely affecting various life stages of yellow perch. Parameter Life Stage Data Reference Temperature Egg Tolerance range of 7 - 20C Hokanson, 1977 Temperature Egg LC50 range of 6..8 - 19.9C Hokanson and Kleiner, 1974 Temperature Larvae Primary entrainment was PSE&G, 1978 simulated. Significant mortality occurred only as the result of a 15C temperature increase when acclimated between 13.5 - 17C. Ln Temperature Larvae A preference range of 21.7 - Ross et al, 24.3C was reported when 1977 acclimated between 20 - 25C. Temperature Larvae No significant difference PSE&G, 1978 occurred in mortality between controls and expe'rimental treatments when exposed to a 2.5 - 8.OC temperature increase for 0.5 - 411. Acclimation was 16.5C. Temperature Larvae 63% survival occurred during Hale and a feeding study after 3 weeks Carlson, 1972 at 20 - 21C. Table 1. (Continued) Parameter Life Stage Data Reference Temperature Larvae At 12.5C three of seven groups Hubbs, 1971 fed, while one of nine fed at 9.5C. Temperature Larvae Tolerance range for feeding Hokanson, 1977 larvae was 10 30C. Temperature Juvenile Temperature preference ranged Cherry et al, from 19.2 - 22.4C when 1977 acclimated at 15, 18, 21, and 24C. Temperature Juvenile Growth tolerance range was Hokanson, 1977 6 - 31C. Temperature Juvenile A temperature range of 20 - McCauley and 23.3C was selected when Road, 1973 acclimated at 24. Temperature Juvenile Greatest weight gain occurred Huh et al, at 22C with 16h of light. 1976 Data suggests photoperiod influences growth much more than temperature. Temperature Age-O Diel preferred temperatures Reynolds of 16.7C (predawn) and and Casterlin, 23.8C (dusk) were exhibited 1979 when acclimated at 20C. Table 1. (Continued) Parameter Life Stage Data Reference Temperature Age-O and Fish were collected seasonally Hokanson and Adults from Lake Erie. Age-0 fish Kleiner, preferred temperatures 4C or 1974 greater than those preferred by adults during spring, summer and fall, but preferred water 2C lower than adults during winter. Temperature Adults A temperature of 6.3C was Ross and perferred when exposed to a Siniff, winter thermal plume 1982 considting of a 0 - 15C thermal gradient. Temperature Adults Selected a temperature range McCauley of 17.6 - 20.1C when and Reed, acclimated to 24C. 1973 Temperature. Adults Preferred 23.5C when Meldrim and acclimated at 15C in 6 ppt Gift, 1971 salinity. Preferred 22.5C when acclimated at 25C in freshwater. Similar avoidance temperatures (33.3 - 33.9C) were selected when acclimated at 25C but different light levels (2 and 20 ft. - candles). Table 1. (Continued) Parameter Life Stage Data Reference Temperature Adults Fish acclimated in freshwater PSE&G, 1978 to 25C avoided areas 31 - 34C, while those acclimated to 6C avoided 14 - 18C. Fish acclimated to 6C in 1.5 ppt salinity avoided.27C. Salinity Egg Hatching success was: Muncy, 1962 65-68% in freshwater 56% in 0.47 2.43 ppt salinity 42% in 0.1 0.94 ppt salinity 55% in 5.8 ppt salinity 0% in 11.7 ppt salinity tI3 Salinity Larvae. 8 and 26d, old larvae were Klauda at al, CO exposed to 3, 6, 12 and 24 1988 ppt salinity for 72h. No survival occurred in either group after 48h exposure in 12 - 24 ppt salinity. Mortality for Od old larvae ranged from 40 - 25% after 72h exposure to 3 - 6 ppt salinity. Mortality of 26d old larvae ranged from 28 - 18% after 72h exposure to 3 - 6 ppt salinity. Table 1. (Continued) Parameter Life Stage Data Reference Dissolved Oxygen Juvenile Exposed for 67d to five Carlson et al, concentrations of 1980 dissolved oxygen (2.0 - 6.5 mg/L). Growth was not reduced when mean constant dissolved oxygen level was @-- 3.5mg/L. Growth was not affected at fluctuations of 1.4 - 3.8 mg/L. Dissolved Oxygen Age-0 Fish at 22.95C were exposed Petit, 1973 to disolved oxygen concentrations between 1 - 5 mg/L. At 5 mg/L opercular movements increased; 4 mg/L there was loss of normal coloration; 2 mg/L cessation of feeding; loss of equilibrium at 1 mg/L. Lethal level occurred at 0.895 mg/L for individuals and 0.839 mg/L for groups of four. No lethal level found when acclimated at,15.1C. pH Egg Exposed to p1l 5, 5.5, 6 and 7 Janicki and and nominal aluminum (0 - 400 Greening, pg/L). 62% mortality after 1988 15d exposure to pH 5.0 with no altii-inum. Mortality in less acidic conditions (40 45%) was significantly less than at p1l 5.0. Addition of aluminum did not significantly affect mortality. Temp = 12 - 15C. Table 1. (Continued) Parameter Life Stage Data Reference P11 Larvae At p1l 5.0 with 100 Mg/L Swenson et al, aluminum (Al) survival 1989 declined significantly to 5% compared to > 50% survival in the other pil 5.0 treatments. The addition of 100 pg/L Al at p1l 4.5 resulted in total mortality. pH Larvae 17d old feeding larvae were Klauda et al, more sensitive to acid 1988 pulses of p1l 4.0 than pre- feeding larvae. Mean mortalities of feeding larvae during a 12h pulse were 98% at pil 4, 4% at pH 5 and 8% at p1l 6. Mean mortalities of pre-feeding larvae during a 12h pulse were 22% at pli 4, 2% at pil 5 and 0% at pff 6. Pulse durations did not affect larval mortality at p1l 5 or 6. pit Larvae >50% survival occurred at p1l Correll et al, 5.0. significant difference 1987 in survival occurred between pil 5 and 7, while both significantly reduced overall survivability. Table 1. (Continued) Parameter Life Stage Data Reference pit Adult Exposure to lethal-acidity Lyons, 1982 (pit 3.2) for 48h resulted in significant but similar decreases in blood plasma sodium levels in both populations. Fish were from a naturally acidic lake (pit 4.6) and a naturally alkaline lake (pit 7.9). pH Adult Fish from acidic lakes (pit 4.5) Rahel, 1983 survived longer than fish from alkaline lakes (pit 7.6) when exposed to pit 3.2 at 18 - 20C Li in a laboratory. Acclimation to sublethal pit (4.6) for 21d did not affect acid tolerance. Suscepti- bility to lethal high pH (10.4) was shnilar for acidic and alkalini-.! acclimated fish. pit Adult Survived longer than 10d in a Rahel and lab experiment at pit 3.05 and Magnuson, 19C. Collected from wild in 1983 lakes with ambient pit > 6.0. Suspended Solids Egg Exposures of 50, 100, 500 Schubel et al, and 1000 mg/L were used. @1973 A significant decrease in hatching success occurred when exposed to 1000 mg/L Table 1. (Continued) Parameter Life Stage Data Reference Suspended Solids Egg Hatching success was not Sdwbel and Wang, affected by concentrations 1973 :5 500 mg/L. A 6 - 12h hatching delay occurred at 100 and 500 ing/L suspensions. Suspended Solids Egg Exposures of 50, 100, 500 Auld and and 1000 mg/L were used. Schubel, No significant reduction in 1974 hatching success was reported. Suspended Solids Larval Suspensions ?-- 500 mg/L Auld and significantly reduced survival Schubel, when exposed for 96h. 1974 Table 2. Toxicity data for yellow perch larvae exposed to various single chemicals. All studies were static unless otherwise noted. (FT flow through) Water Quality Water Temp. Hardness chemical Type (CO) PH (mg/L) Data References (CaC03) Acephate (Insecticide) Fresh Mayer and 94% Tech material 12 7.5 42 96h LC50 > 50000 jug/L Ellersieck, 75% Wettable powder 12 7.5 42 96h LC50 > 100000 pg/L 1986 75% Wettable powder 12 6.5 42 96h LC50 > 100000 pg/L 75% Wettable powder 12 9.0 42 96h LC50 > 100000 pg/L 75% Wettable powder 12 8.0 12 96h LC50 > 100000 pg/L 75% Wettable powder 12 8.0 44 96h LC50 > 100000 pg/L 75% Wettable powder 12 8.0 300 96h LC50 > 100000 pg/L Aninocarb (Herbicide) Fresh 98% Tech 12 7.5 40 96h LC50 = 6400 Ag/L 98% Tech 12 7.5 40 96h LC50 = 230 pg/L 17% Oil soluble 12 7.5 40 96h LC50 = 11700 jjg/L 98% Tech 7 7.5 40 96h LC50 = 5600 pg/L 98% Tech 12 7.5 40 96h LC50 - 4700 Mg/L 98% Tech 17 7.5 40 96h LC50 = 1700 pg/L 98% Tech 22 6.5 40 96h LC50 - 6400 pg/L 98% Tech 12 7.5 40 96h LC50 - 7000 pg/L 98% Tech 12 8.5 40 96h LC50 = 1430 pg/L 98% Tech 12 9.0 40 96h LC50 = 425 pg/L 98% Tech 12 8.0 40 96h LC50 = 5400 pg/L 98t Tech 12 8.0 40 96h LC50 = 6200 pg/L 98% Tech 12 8.0 1.60 96h LC50 = 7400 pg/L 98% Tech 12 8.0 280 96h LC50 = 5600 Mg/L Antimycin A (Piscicide) Fresh 95.5% Tech 12 7.4 44 96h LC50 0.040 gg/L Table 2. (Continued) Water Quality Chemical Water Temp. Hardness Type (C-) P11 (mg/L) Data References (CaCO 3) Azinphos-methyl (Insecticide) Fresh 93t Tech 16 7.1 44 96h LC50 = 15 Ag/L 93% Tech 7 7.5 44 96h LC50 - 40 Ag/L 93% Tech 17 7.5 44 96h'LC50 = 5.6 pg/L 93% Tech 22 7.5 44 96h LC50 = 2.4 Ag/L 93% Tech 12 6.5 44 96h LC50 = 17 Ag/L 93% Tech 12 7.5 44 96h LC50 = 29 jig/L 93% Tech 12 8.5 44 96h LC50 = 8.5 Ag/L 93% Tech 12 9.0 44 96h LC50 = 29 Mg/L 93% Tech 12 B.0 12 96h LC50 = 18 Mg/L 93% Tech 12 8.0 44 96h LC50 = 36 Ag/L 93% Tech 12 8.0 170 96h LC50 = 11 Ag/L 93% Tech 12 8.0 300 9 611 LC50 = 27 Ag/L 93% Tech (FT) 12 7.5 314 96h LC50 = 6.5 Mg/L Captan (Fungicide) Fresh 90% (FT) 17 7.5 314 96h LC50 = 120 pg/L- Carbaryl, (Insecticide) Fresh 99.5% Tech 18 7.1 40 96h LC50 = 745 pg/L 99.5% Tech 12 7.5 42 96h LC50 = 5100 pg/L 99.5% Tech 7 7.5 42 96h LC50 = 13900 pg/L 99.5% Tech 12 7.5 42 96h LC50 = 5400 pg/L 99.5% Tech 17 7.5 42 .96h LC50 = 3400 pg/L 99.5% Tech 22 7.5 42 96h LC50 = 1200 pg/L 99.5% Tech 12 6.5 42 96h LC50 = 4000 pg/L 99.5% Tec 12 7.5 42 96h LC50 = 4200 pg/L 99.5% Tech 12 8.5 42 96h LC50 = 480 Ag/L 99.5% Tech 12 9.0 42 96h LC50 = 350 Ag/L 99.5% Tech 12 .8.0 42 9 6h LC50 = 3BOO pg/L 99.5% Tech 12 8.0 170 96h LC50 = 5000 Mg/L 99.5% Tech 12 8.0 300 96h LC50 = 3750 jig/L Table 2. (Continued) Water Quality Water Temp. flardness Chemical Type (C*) P11 (mg/L) Data References (CaC03) Carbaryl (Insecticide) Fresh 99% Tech 12 7.5 44 96h LC50 = 240 Ag/L 99% Tech 12 9.5 42 96h LC50 = 120 pg/L 99% Tech 12 7.5 44 96h.LC50 - 400 pg/L Chlordane (Insecticide) Fresh 100% Tech (FT) 12 7.1 44 96h LC50 = 9.6 Mg/L DDT (Insecticide) Fresh, 99% Tech 18 7.1 44 96h LC50 = 9.0 pg/L Diflubenzuron (Insecticide) Fresh 12 7.4 44 96h LC50 > 50000 Mg/L Lj 95% Tech 12 7.4 40 96h LC50 > 25000 Ag/L V1 95% Tech Dimethrin (Insecticide) Fresh 100% Tech 12 7.5 44 96h LC50 - 28 Mg/L Dinitramine (Herbicide) Fresh 99.2% Tech 12 7.5 44 96h LC50 = 1000 pg/L 99.2% Tech (FT) 12 7.5 314 96h LC50 = 780 pg/L Diquat (Herbicide) Fresh 35.3% Liquid Concentrate 12 7.5 44 96h LCSO = 60000 pg/L 35.3% Liquid Concentrate 12 9.5 44 96h LC50 = 23500 pg/L Table 2. (Continued) Water Quality Water Temp. Hardness Chemical Type (CO) PH (mg/L) Data References (CaCO 3) Fenitrothion (Insecticide) Fresh 95% Tech 12 7.5 40 96h LC50 = 5800 pg/L 40% Wettable Powder 12 7.5 42 96h LC50 = 2700 pg/L 40% Wettable Powder 12 7.5 42 96h LC50 = 4700 Mg/L 40% Wettable Powder 7 7.5 42 96h LC50 = 2600 Ag/L 40% Wettable Powder 12 7.5 42 96h LC50 = 3500 Mg/L 40% Wettable Powder 17 7.5 42 96h LC50 = 3000 pg/L 40% Wettable Powder 12 6.5 42 96h LC50 = 4800 Mg/L 40% Wettable Powder 12 7.5 42 96h LC50 - 2900 pg/L 40% Wettable Powder .12 8.5 42 96h LC50 - 3500 pg/L 40% Wettable Powder 12 9.0 42 96h LC50 = 3200 pg/L 40% Wettable Powder 12 8.0 44 96h LC50 = 3900 pg/L 40% Wettable Powder 12 8.0 170 96h LC50 - 2000 pg/L 40% Wettable Powder 12 8.0 300 96h LC50 = 3700 pg/L Fenthion (Insecticide) Fresh 46% spray concentrate 18 7.1 44 96h LC50 = 1650 pg/L Folpet (Fungicide) Fresh 88% Tech 12 7.5 44 96h LC50 = 177 pg/L Houghto - Safe 1120 (Hydraulic fluid) 100% liquid 12 7.5 314 96h LC50 = 500 pg/L Table 2. (Continued) Water Quality Water Temp. Hardness chemical Type (CO) P11 (mg/L) Data References (CaCO,) Leptophos (Insecticide) Fresh 87.2% Tech 12 7.4 44 96h LC50 = 2000 Mg/L 87.2% Tech 12 7.4 44 96h LC50 = 1320 Mg/L 87.2% Tech 7 7.4 44 96h LC50 = 3750 pg/L 87.2% Tech 12 7.4 44 96h*LC50 < 500 pg/L 87.2% Tech 22 7.4 44 96h LC50 < 25 Mg/L 87.2% Tech 12 9.0 44 96h LC50 = 680 pg/L 87.2% Tech 12 8.5 44 96h LC50 = 150 pg/L 87.2% Tech 12 7.5 44 96h LC50 = 690 jig/L 87.2% Tech 12 6.5 44 96h LC50 - 140 pg/L 87.2% Tech 12 8.0 12 96h LC50 = 270 pg/L 87.2% Tech 12 8.0 44 96h LC50 = 2500 gg/L 87.2% Tech 12 8.0 170 96h LC50 - 950 pg/L 87.2% Tech 12 8.0 300 96h LC50 - 880 fig/L 87.2% Tech 12 8.0 44 96h LC50 - 2050 14g/L 87.2% Tech (FT) 12 7.6 314 96h LC50 = 7.0 pg/L Malathion (Insecticide) Fresh 95% Tech 18 7.1 44 96h LC50 - 263 Mg/L Methoxychlor (Insecticide) Fresh 98% Tech 12 7.5 40 96h LC50 = 30.0 14g/L 50% Granular 12 7.5 40 96h LC50 = 17.5 jig/L 98% Tech 12 7.5 42 96h LC50 > 50 pg/L 98% Tech (FT) 12 7.5 314 .96h LC50 > 20 pg/L Methyl Parathion (Insecticide) Fresh 90% Tech 18 7.1 44 96h LC50 3060 pg/L Table 2. (Continued) Water Quality Water Temp. Hardness Chemical Type (CO) PH (mg/L) Data References (CaC03) Mexacarbate (Insecticide) Fresh 90% Tech 12 7.5 44 96h LC50 - 16200 gg/L 90% Tech 17 7.5 44 96h LC50 = 16900 gg/L 90% Tech (FT) 12 7.5 314 96h LC50 = 8300 pg/L Mirex (Insecticide) Fresh 98% Tech 15 7.4 40 96h LC50 > 100000 gg/L Paroil 1032 (Plasticizer) Fresh 100% liquid (FT) 12 7.5 314 96h LC50 > 5000 pg/L Paroil, 10@B (Plasticizer) Fresh Li 100% liquid (FT) 12 7.5 314 96h LC50 > 10000 gg/L Paroil 160 (Coolant) Fresh 100% liquid (FT) 12 7.5 314 96h LC50 > 10700 gg/L PCB Arochlor (Industrial) Fresh 1016 100% Tech 12 7.4 44 96h LC50 = 240 Mg/L 1242 100% Tech (FT) 17 7.6 314 96h LC50 > 150 Mg/L 1248 100% Tech (FT) 17 7.6 314 96h LC50 > 100 pg/L 1254 100% Tech (FT) 17 7.6 314 96h LC50 > 150 pg/L 1260 100% Tech (FT) 17 7.6 314 96h LC50 > 200 pg/L Phthalate Dibutyl (Plasticizer) Fresh 1001 liquid (FT) 12 7.6 314 96h LC50 350 gg/L Pydraul 50E (Hydraulic fluid) Fresh 100% liquid (FT) 12 7.8 300 96h LC50 540 gg/L Table 2. (Continued) Water Quality Water Temp. Hardness Chemical Type (CO) P11 (mg/L) Data References (CaC03) S-Bioallethrin (Insecticide) Fresh 98% Tech 12 7.5 44 96h LC50 m 7.8 Ag/L Toxaphene (Insecticide) Fresh 100% Tech 18 7.4 44 9 611 LC50 = 12 Mg/L Trichlorfon (Insecticide) Fresh 98% Tech 12 7.5 40 96h LC50 > 10000 gg/L Tricresyl Phosphate (Industrial) Fresh 100% Tech (FT) 12 7.4 242 96h LC50 = 500 pg/L Xylenol Dimethylamino (metabolite) Fresh 99% Tech 12 7.5 44 96h LC50 = 3400 gg/L 99% Tech 12 9.5 44 96h LC50 - 100 gg/L Dinitramine (lierbicide) Fresh 12 7.5 42 96h LC50 = 1000 gg/L Olson et al, 1975 Pyrethrum, extract Fresh Mauck et al, 20% (FT) 12 96h LC50 = 44.5 gg/L 1976 Dimethrin Fresh 96% Tech 12 96h LC50 = 28 jig/L d-Trans allethrin Fresh 90% Tech (FT) 12 96h LC50 = 9.9 pg/L RU-11679 Fresh 12 96h LC50 = 0.06 pg/L Table 2. (Continued) Water Quality Water Temp. 11ardness Chemical Type (CO) PH (mg/L) Data References (CaCO,) S-bioallethrin Fresh 12 96h LC50 = 7.8 pg/L SBP-1382 Fresh 89t Tech (FT) 12 96h LC50 = 0.5 Mg/L Total Residual saline 16 Approximately 50t PSE&G, 1978 Chlorine (TRC) (3.50/oo) mortality after 0.5h exposure to 550 pg/L TRC. No survival after 0.5h exposure to 2300 pg/L TRC. 46 TRC Fresh 10 24h LC50 = 7700 pg/L Seegert 0 15 24h LC50 = 4000 pg/L et-al, 1977 20 96h LC50 = 1100 Mg/L 25 96h LC50 = 1100 pg/L Hydrogen Sulfide Fresh 10 7.5 96h LC50 = 2 Mg/L Fung and 20 8.0 96h LCSO < 2 Mg/L Bewick, 1980 1111 MINE 0 1 IN@ 11 11 1 1 1 1 Table 3. Toxicity data for juvenilq yellow perch exposed to various single chemicals. All studies were static unless otherwise noted. (FT = flow through) Water Quality Water Temp. Hardness chemical Type (CO) P11 (mg/L) Data References (CaCO 3) Carbaryl (Insecticide) Fresh Mayer and 99.5% Tech (FT) 12 7.5 314 96h-LC50 = 1420 Ag/L Ellersieck, 1986 D-trans Allethrin (Insecticide) Fresh 90% Tech (FT) 12 7.5 314 96h LC50 = 9.9 pg/L Endrin (Insecticide) Fresh 99A Tech (FT.) 12 7.6 314 96h LC50 = 0.15 pg/L Phoxim (Insecticide) Fresh 89% Tech 12 7.5 44 96h LC50 - 605 pg/L 89% Tech 17 7.5 44 96h LC50 = 563 pg/L 89% Tech (FT) 12 7.5 314. 96h LC50 = 710 jig/L Pyrethrum (Insecticide) Fresh 20% liquid (FT) 12 7.6 314 96h LC50 = 33 pg/L Resmethrin (Insecticide) Fresh 84% Tech (FT) 12 7.6 314 96h LC50 = 0.51 pg/L RU-11679 (Insecticide) Fresh 96W Tech (FT) 12 7.6 314 96h LC50 = 0.06 jug/L Table 3. (Continued) Water Quality Water Temp. Hardness Chemical Type (CO) P11 (mg/L) Data References (CaC03) TRC Fresh Effects of one 0.5h Brooks and exposure Seegert, 10 24h LC50 - 6000 Mg/L 1977 15 24h'LC50 - 3900 Ag/L 20 24h LC50 = 1100 pg/L .25 24h LC50 = 1000 Mg/L 30 24h LC50 = 700 pg/L Effects of three 5 min. exposures 3 h apart 10 24h LC50 = 22600 pg/L 20 24h LC50 - 9000 Mg/L Hydrogen Sulfide Fresh 10 7.5 96h LC50 - 36 Mg/L Fung and 20 8.0 96h LC50 = 8 Mg/L Bewick, 1980 Hydrogen Cyanide Fresh 15 96h LC50 = 90.4 pg/L Smith, 1978 (HCN) 21 96h LC50 = 108 Ag/L An inverse relationship existed between organism sensitivity to HCH and dissolved oxygen concentration at 21C. Potassium Permanganate Fresh 12 7.5 44 96h LC50 = 2830 pg/L Marking and Bills, 1975 3-trifluoromethyl- Fresh 12 96h LC50 = 9400 pg/L Marking and 4-nitrophenol (TFM) (FT) 12 96h LC50 = 4400 pg/L Olsen, 1975. M mill I II I Table 4. In-situ water quality and contaminant studies conducted with various life stages of yellow perch. Parameter Life @7tiqe Data Reference PH Egg Temp = 10.3 - 10.9.C. Schofield and Poor hatching success occurred Driscoll, as a result of alterations in 1987 egg membrane structure inhibiting process. This suggests possible genetic adaptation to acid stress. Mortality rates: Egg Source Incubation Moose Mos Site __Lpff 5. 0) (01 6. 6) Moose 43.5% 3.8 Moss 77.0% 86.2 PH YOY YOY were transferred from an Schofield and alkaline lake (pH 6.9) to an Driscoll, acidic lake (PH 4.6) where 1987 cages were monitored for 28 d. 72% survival rate was recorded.. Table 4. (Continued) Parameter Life Stage Data Reference pH and Aluminum Egg Mattawoman_free%: Janicki and (Al) egg mortality = 8.4% Greening, P11 minima = 5-8 7 6.0 1988 Total monomeric Al maxima 55 Ag/L Dissolved calcium @-- 4.8 mg/L Bacon Ridge Creek: egg mortality = 50% p1l minima = 5.8 - 6.0 Total monomeric Al maxima = 52 Mg/L Dissolved calcium = 5.7 - 8.2 mg/L pH and Al Larvae Mattawoman Creek: Greening et Larval mortality - 51.5 - 100% al., 1989 p1l minima - 5.8 - 6.3 Total monomeric Al maxima - 69 Mg/L Dissolved calcium 3.1 - 7.3 mg/L Bacon-Rid e Creek: Larval mortality = 92.3% p1l minima = 5.8 Total monomeric Al maxima = 52 pg/L Dissolved calcium 5.7 mg/L -M @M AM. IM 'M ''M -'M. M M Table 4. (Continued) Parameter Life Stage Data Reference Archlor 1016 (PCB) Adult Fish were collected from a nearby Skea et al., nearby lake and.exposed for 14d 1979 to Hudson River water. Fish had bioacctimulated 1.8 jig/g of Arochlor 101(,. ,Iiile controls (up river) had residues < 0.02 pg/g. Perch bioaccumulated approximately 10400 times the concentration present within the water (0.17 Mg/L). U L. -- 3 6668 14100 9953 @&