Document N2OJkZDwy9Nvn01dwn9dw2vB8

-1 DRAFT POLYCHLORINATED BIPHENYLS CRITERIA: Aquatic Life - 0.001 ug/1 In freshwater; 0.01 ug/1 4n marine water INTRODUCTION: Polychlorinated biphenyls (PCB's) are a class of compounds produced by the chlorination of biphenyls and are known In the United States commercially as Aroclors ^. The degree of chlorination determines their Chemical properties and generally their composition can be Identified by the numerical nomenclature, e.g., Arodor 1242, Arodor 1254, etc. The first two digits represent the molecular type and the last two digits the average percentage by weight of chlorine (NTIS, 1972). Identification of PCB's In the presence of orgartochlorlne pesticides such as DDT and DDE has been difficult In the past because of their similar chroma tographic characteristics (Rlsebrough et al_., 1968}. In PCB analysis today, the Interference of organochlorlne hydrocarbons 1$ overcome by sequential column chromatography on Florsll and silica gel (Armour and Burke, 1970; FDA, 1971). Gas-liquid chromatography with highly sensitive and selective detectors has been employed successfully In their detection at low levels (Nebecker and Puglisl, 1971). PCB compounds are slightly soluble In water; soluble In fats, oils, and organic solvents, and Typically, the specific gravity, boiling point, and^jy^Pii^|of PCB's Increase with their chlorine content. PCB's are relatively non-flamnable MONS 201691 2- - have useful cooling. Insulating, and dielectric properties, and principally are used In the electrical Industry In capacitors and transformers. RATIONALE: .lvV ' Exposure to PCB Is known to cause skin lesions (Schwartz and Peck, and to increase liver enzyme activity that may have a secondary effect on reproductive processes (Rlsebrough, 1969; Street et^al_., 1968; Wasserman at al_., 1970). It Is not clear whether the effects are due to the PCB's or their contaminants, the chlorinated dlbenzofurans, that are highly toxic (Bauer et al_. ,<1961; Schultz, 1968; Varrett, 1970). While chlorinated dlbenzofurans are a byproduct of PCB production. It Is n>t known whether they are also produced by the degradation of PCB's (NAS, 1974). . Analyses of 40 fish from the 1970 National Pesticide Monitoring Program Indicated only one fish to contain less than 1 ug/g PCB with the ten highest residues ranging from 19 ug/g to 213 ug/gjyljOle body wHaht (Stalling and Mayer, 1972). Studies of the Milwaukee River revealed ambient water concentrations of 2.0 to 2.8 ug/1 and residues In fish as high as 405 ug/g (Velth and Lee, 1971). Open water Lake Michigan concentrations have been reported to be less Pt> b / rpra'" than 0.01 ug/1 with mean residues In coho salmon of about 15 ug/g (Velth, 1973), r - t The Food and Drug Administration guideline for protecting the health of human j> -i.f & consumers of fish Is 5 ug/g in tissue residues of fish, fated on Like Michigan i- r i 4 r----------------- -- -- -- , r'- ' r 4j#ta. which Indicate that et a concentration of 41.01 og/1 b illltnoY * r r the flah tissue /luhw' \y>rc--v-y-^' 1-------------------------------------------------- ------------- --------------------------------------------------------:--------------1\ jot b o1 r nrresidues exoeed e level found to be non-ftezardous to man,m criterion of 0.601 ( *8/1 in freshwater is warranted. * Blueglll sunflsh exposed to Aroclors 1248 and (M|r 1254, exhibited vb1oaccumi -cion factor of 7.1 x 10* (Stalling and Mayer, 1972). fa y V ' >o The bloaccumulatlon factor for gizzard shad In the Saginaw River (Michigan) , 'Pt>T ^ ^ '1^ /1* bej/j MQNS 201692 ; -3- varled between 0.6 x 105 and 1.5 x 105 for Aroclor 1254 (Michigan Water Res. Conri., 1973). A residue level of 2 ug/g In fish consumed bypufterclal ranch been shown to prevent survival of offspring (Ringer 1972). Reproduction was almost totally eliminated In ranch mink fed a beef diet containing 0.64 ug/g of Aroclor 1254 (Platonow and Kalstad, 1973). This suggests that a mink-food tissue level of not more than 0.5 ug/g would be required to protect the wildlife consumer. Median PCB concentrations In whole fish of eight species from Long Island ft W Sound obtained In 1970 were reported to be In the order of 1 ug/g, as were comparable concentrations off the coast of Sguthern California. (Hays and Risebrough, 1972; Rlsebrough, 1969). Generally, residues In ocean fish have been below 1 ug/g (Rlsebrough, 1970). Surveys of Escambia Bay (Florida) during the period September 1969 to December 1971 have produced data on the pathways and effects of PCB's In the estuarine and marine environments. Although the major PCB source, accidental leakage from a PCB manufacturing plant has been terminated, residues continue to be observed In aquatic organisms of the bay foiko, \974). The sediment C reservoir of Aroclor 1254$$ thought,,$01*0' tafttlnulng source of ?CB to biota. The Initial survey of Escambia Bey biota revealed fish, shrimp, and crabs with levels as high as 12 ug/g. Higher levels were detected In higher trophic levels than shrimp, which could implicate a chain transfer from sediment to large animals. . From the Escambia Bay data, which Include flow-through bioassays with residue analyses where possible, the following conclusions were reached: (1) all of the Aroclors tested are acutely toxic for certain estuarine organisms; MONS 201693 -4- V (2) bioassays lasting longer than 96 hours demonstrated that Aroclor 1254 Is toxic to commercial shrimp at less than 1 ug/1; (3) fish, particularly sheep- head minnows, are extremely sensitive to Aroclor 1254 with 0.1 ug/1 being lethal to fry; and, (4) acute toxicity of Aroclor 1016 to estuarine organisms Is similar to the toxicity of other Arodors but appears less toxic to fish In long-term exposures than does Aroclor 1254 (Duke, 1974). odc ' r.< - Oysters were sensitive to Aroclor 1260 with growth diminished by 44 percent /oppb io?fpb In 10 ug/1 and by 52^percent In 100 ug/1. Approximately 10 percent of the pink shrimp died In lol)^ug/l, but no apparent effects on plnflsh were noted at 100 ug/1. Aroclor 1254 had no apparent effect on Juvenile plnflsh at 100 ug/1 * In 48-hour flow-through tests, but killed 100 percent of the pink shrimp. At ppY) . 100 ug/1 of Aroclor 1254 for 96 hours, shell growth of oysters was Inhibited v and decreased only 41 percent at levels of 10 ug/1. The toxicity of Aroclor 1248 and 1242 to shrimp and plnflsh was similar to that of Aroclor 1254. Aroclor 1242 was toxic to oysters at 100 ug/1. Klllflsh exposed to 25 mg/1 of Aroclor 1221 suffered an B5 percent mortality. In 96-hour bioassays, Aroclor 1016 was toxic to an estimated 50 percent of the oysters, brown shrimp, and grass shrimp at 10 ug/1; It was toxic to 18 percent of the plnflsh at 100 ug/1 *Duke, 1974). Young oysters exposed to Aroclor 1254 In flowing sea water for 24 weeks experienced reduction In growth rates at 4.0 ug/1, but apparently were not affected by 1.0 ug/1. Oysters accumulated as much as 100,000 times the testwater concentration of 1.0 ug/1. General tissue alterations In the vesicular around the diverticula.of the >atopancreas were noted In the oysters exposed to 5.0 ug/1. No significant mortality was observed In oysters exposed continu ously to 0.01 ug/1 of Aroclor 1254 for 56 weeks {fluv -ke* IfM), MONS 201694 V -5- Blue crabs apparently were not affected by 20 days' exposure to 5.0 ug/1 of Aroclor 1254. Pink shrimp exposed under similar conditions experienced a 72 percent mortality. In subsequent flow-through bioassays, 51 percent of the juvenile shrimp were killed by Aroclor 1254 In li days and 50 percent of the adult shrimp were killed at 3.0 ug/1 In 35 days. From pathological examinations of the exposed pink shrimp. It appears that Aroclor 1254 facilitates or enhances the expression of latent viral Infections. Aroclor 1254 was lethal to grass shrimp at 4.0 ug/1 In 16 days, to amphlpods at 10 ug/1 In 30 days, and to juvenile spot at 5.0 ug/1 after 20 to 45 days. Sheephead minnows were the most sensitive estuarine organisms to Aroclor 1254 with 0.3 ug/1 being lethal to the fry within 2 weeks. Aroclor 1016 In two different 42-day flow-through bioassays caused significant mortalities of plnflsh at ISaig/l and 21 ug/1. Pathological examination of those exposed to 32 ug/1 revealed several liver and pancreatic alterations. Sheephead minnows In 28-day Aroclor 1016 flow-through bioassays were not affected by concentrations of 10 ug/1 or less, but died at 32 and 100 ug/1 |Duke, 1974). The bloaccumulatlon factors for the different flow through bioassays are: Aroclor 1254 1254 1254 1254 1254 1016 Organlsm Oyster Blue Crab Grass Shrimp Spot Plnflsh vPinf1 sh Time 30 days 20 days 7 days 1 -26 days 35 days 42 days Accumulatlon Facts (as a multiplier of test water concentrations) ' 1.01 x 105 1' V' 4 x 103 u'( C 3.2 x 103 to 11 x 103 37 x 103 21.8 x 103 11 x 103 to 24 x 103 1016 Sheephead Minnow 2.5 x 103 to 8.1 x 103 HONS 201695 6- Based upon an accumulation factor of 100,000 In the oyster. It Is necessary Olppt> to limit the marine water concentration of PCB's to a maximum of ,0.01 ug/1 to protect the human consumer. Evidence Is accumulating that PCB's do not contribute to shell thinning of bird eggs (NAS, 1974). Dietary PCB's produced no shell thinning In eggs of Mallard ducks (Heath et a^., 1972). PCB's may Increase susceptibility to Infectous agents such as viral diseases (Friend and Trainer, 1970), and increase the activity of liver enzymes that degrade steroids. Including sex hormones (Rlsebrough et aK, 1968; Street et aK, 1968). Laboratory studies have Indi cated that PCB with Its derivatives or metabolites, cauaes embryonic death of birds (Voss and Koeman, 1970). MOMS 201696 -7- REFERENCES CITED: Armour, J.A., and J.A. Burke, 1970. Method for separating polychlorinated biphenyls from DDT and Its analogs. Assoc. Official Anal. Cham. 53:761. Bauer, H., et al_., 1961. Occupational poisonings In the production of compounds. Arch. Gewerbepath 18:538. jaWHiMHi Testimony In the matter of proposed toxic pollutant effluent standards for Aldi*1 n-Dleldrln et^aK FWPCA (307) Docket f 1. FDA, 1971. U.S. Dept, of H.E.W. Pesticide Analytical Manual, Vol. I and II. Friend, H., and D.O. Trainer, 1970. Polychlorinated biphenyl Interaction with duck hepatitis virus. Science, 170:1314. Hays, H.. and R.W. Rlsebrough, 1972. Pollutant concentrations In abnormal spring tern from Long Island Sound. AUK 89:19. Heath, R.G. et al_., 1972. Effects of polychlorinated biphenyls on birds. Proceedings IV International Ornithological Congress Michigan Water Res. Come., 1973. Monitoring for polychlorinated biphenyls In the aquatic environment. National Academy of Sciences, 1974. Water quality criteria, 1972. iMBHNP* L, and F.A. Pugllsl, 1971. PCB Newsletter, p. 19. and F.A. Pugllsl. 1974. Effect of polychlorinated biphenyls (PCB's) on survival and reproduction of Daphnla gammarus and Tanytorsus. Trans. Amer. Fish. Soc. (In Press). MOMS 201697 8- - National Technical Information Service, 1972. Polychlorinated biphenyls and tne environment. RTIS Interdepartmental Task Force, Washington, D.C. Platonow, N.8. and L.H. Kalstad, 1973. Dietary effects of polychlorinated biphenyls on mink. Can. Jour- Comp. Med. 37:391. Ringer, R.K. et al_., 1972. Effect of dietary polychlorinated biphenyls on growth and reproduction of mink. Amer. Chem. Soc. National Meeting Reprints of Papers, 12:149. Risebrough, R.W., 1969. Chlorinated hydrocarbons In marine ecosystems. In: Chemical Fallout, M.W. Miller and G.G. Berg, eds., C.C. Thomas, Springfield. Risebrough, R.W., 1970. More letters In the world. Environ. 12:16. Risebrough, R.W. et aK, 1968. Polychlorinated biphenyls In the global eco system. Nature, 220:1096. Schulz, K.H., 1968. Clinical picture and etiology of chloracne. Arbeltsmed. Soziaimed. Arbeltshgy. 3:25. Reprinted In translation In U.S., Congress. Senate, Committee on Commerce, Effects of 2, 4, 5-T on man and the environ ment: Hearings, 91st Cong., 2nd sess., pp. 336*341. Schwartz, L. and S.M. Peck, 1943. Occupational acne. New York State Med. 43:1711 Stalling, D.L.,and F.L. Mayer, Jr., 1972. Toxlcltles of PCB's to fish and environmental residues. Env. Health Perspectives, 1:54. Street, J.C. et al_., 1968. Comparative effects of polychlorinated biphenyls and organochlorlne pestlwides In Induction of hepatic microsomal enzymes. Amer. Chem. Soc., 158th National Meeting, Sept. 8-12, 1968. HONS 201*98 -9Varrett, J., 1970. Statement In U.S. Congress, Senate, Cormlttee on Comerce, Effects of 2, 4, 5-T on man and the environment: Hearings, 91st Cong., 2nd sess., pp. 190-360. i&m Chlorinated hydrocarbons In fish from lake fish. Final report, EPA Grant 1602 PBE. end G.F. Lee, 1971. Chloroblphenyls (PCB's) In the Milwaukee River. Water Res. 5:1107. Voss, J.G. and J.H. Koeman, 1970. Comparative toxlcoyog1c study with poly chlorinated biphenyls In chickens with special reference to porphyria, edema, formation, liver nebrosls, and tissue residues. Toxicol. Appl. Pharmacol. 17:656. Wasserman, M. et al_., 1970. The effect of organochlorlne Insecticides on serum colesterol level In people occupationally exposed. Bull. Environ. Contam. Toxicol. 5:368. HONS 201*99