AMBIENT WATER QUALITY ADVISORY XYLENE U.S. ENVIRONMENTAL PROTECTION AGENCY OFFICE OF WATER REGULATIONS AND STANDARDS CRITERIA AND STANDARDS DIVISION WASHINGTON, D.C. ------- CONTENTS Page Notices ii Foreword iii Acknowledgments iv I. Advisories 1-1 II. General Information II-l A. Biological, Chemical and Physical Properties II-l B. Occurrence 11-2 C. Environmental Fate 11-2 Ill . Aquatic Toxicity 111 -1 IV. Referances IV-1 V. EPA Contacts V-l i ------- NOTICES This document has been reviewed by the Criteria and Standards Division, Office of Water Regulations and Standards, U.S. Environmental Protection Agency, and approved for distribution. Mention of trade names or commercial products does not constitute endorsement or recommendation for use. This document is available to the public through the Criteria and Standards Division, Office of Water Regulations and Standards, U.S. EPA, Washington, DC. ii ------- FOREWORD The Criteria and Standards Division of the Office of Water Regulations and Standards has instituted water quality advisories as a vehicle for transmitting the best available scientific information concerning the aquatic life and human health effects of selected chemicals in surface waters. Advisories are prepared for chemicals for which information is needed quickly, but for which sufficient data, resources, or time are not available to allow derivation of national ambient water quality criteria. Data supporting advisories are usually not as extensive as required for derivation of national ambient water quality criteria, and the strength of an advisory will depend upon the source, type, and reliability of the data available. We feel, however, that it is in the best interest of all concerned to make the enclosed information available to those who need it. Users of advisories should take into account the bases for their derivation and their intended uses. Anyone who has additional information that will supplement or substantially change an advisory is requested to make the information known to us. An advisory for an individual chemical will be revised if any significant and valid new data make it necessary. We invite comments to help improve this product. Edmund M. Notzon, Director Criteria and Standards Division iii ------- ACKNOWLEDGMENTS AQUATIC LIFE Mary D. Balcer, author University of Wisconsin-Superior, Superior, WI iv ------- SECTION I. ADVISORIES AQUATIC LIFE If the measured or estimated ambient concentration of xylene exceeds 21/uug/L in fresh or salt water, one or more of the following options must be completed within a reasonable period of time: 1. Obtain more measurements of the concentration. 2. Improve the estimate of the concentration. 3. Reduce the concentration. 4. Obtain additional laboratory and/or field data on the effect of xylene on aquatic life so that a new aquatic life advisory or a water quality criterion can be derived. After a reasonable period of time, unless a consideration of all the available data concerning the ambient concentration and the effects of xylene on aquatic life demonstrates that the ambient concentration is low enough, it must be reduced. 1-1 ------- SECTION II. GENERAL INFORMATION Biological, Chemical. and Physical Properties The following information on the properties of the three isomers of xylene (dimethylbenzene) and its persistence in the aquatic environment was obtained from the QSAR system on July 17, 1986. Density the exception, was obtained from the Handbook of Chemistry, and Physics, 67th Ed., CRC Press, Boca Raton, Florida, 1986-87. ^ Some of the values were calculated activity relationships. using structure- Property Molecular weight Density (20'C) Log P Melting Point Boiling Point Vapor Pressure Heat of Vaporiza- tion pKa Solubility in Water BCF Absorption Coef. [Log (Koc)] Value Ortho-xylene Meta-xylene Para-xylene Source 106.09 g/mol 0.8802 3.44 -25.00'C 144.00"C 6.69 mm Hg 8720 cal/mol (not applic- able ) 176. mg/L 208 3.21 106.09 g/mol 0.8642 3.44 -48.00" C 139.00"C 8.36 mm Hg 8620 cal/mol (not applic- able) 185. mg/L 208 3.21 106.09 g/mol 0.8611 3.44 13.00 *C 138.00"C 8.82 mm Hg 8600 cal/mol (not applic- able) 197 mg/L 208 3.21 Calc Calc CLogP Meas Meas Meas Calc Calc Calc Calc ortho-Xylene 1,2-dimethylbenzene meta-Xvlene 1,3-dimethylbenzene para-Xylene 1,4-dimethylbenzene Log 10 (Henry's constant) = -2.28 atm.m3/mol -2.20 atm.m3/mol -2.20 atm.m3/mol It could be concluded that a chemical with these properties will vaporize rapidly from and will not persist in open water. Neely 100-day Partitioning Pattern ortho-Xylene meta-Xvlene Air = Water = Ground = Hydrosoil = 52.01% 29.69% 9.46% 8.83% 56.37% 27.00% 8.60% 8.03% para-Xylene 56.05% 27.20% 8.67% 8.09% Information on the QSAR system, see: Hunter, R., L. Faulkner, F. Culver and J. Hill. Draft user manual for the QSAR system. Center for Data Systems and Analysis, Montana State University, November, 1985. II-l ------- All the xylenes are colorless liquids with a mild sweet odor. B. Occurrence Xylenes occur at low levels in drinking water, food and air. Xylenes occur in both ground and surface public water supplies, with higher levels occurring in surface water supplies (Keith et al. 1976, Otson et al. 1982). The EPA's Community Water Supply Survey (U.S. EPA, 1983) found 3% of all ground- water derived public drinking water systems sampled had levels greater than 0.5 ug/L. The highest level reported in groundwater was 2.5 ug/L. The survey reported that 6% of all surface water derived drinking water systems are contaminated at levels higher than 0.5 ug/L; however none of the systems were reported to contain levels higher than 5.2 ug/L. No information on the occurrence of xylene in foods has been identified. Xylenes are found in the air of urban and suburban areas at levels of approximately 2 ug/L. Because of the low levels of xylenes reported in water, air is likely to be the major source of exposure. While xylenes occur naturally as a component of petroleum oil, they are also produced in large amounts. For example, in 1982, 5 billion pounds of xylenes were produced (U.S. ITC, 1984). Gasoline refinement and associated operations indirectly produce large quantities of xylenes. Due to their volatile nature, the majority of releases of xylene to the environment are to the air with only smaller amounts to water and soil. Releases of the compound to water are due to spills or leaks of petroleum products and, to a lesser extent, the disposal of paints, inks and other industrial products which use xylenes as a solvent. Because of the widespread use of petroleum products, releases of xylenes occur nationwide. C. Environmental Fate Based on our EXAMS model (Burns et al. 1981), the dominant process for removal of xylenes in water will be volatilization. The predicted volatilization rates are as follows: Rates will vary depending on the type of environment, temperature, oxygen exchange rate and amount of organic matter in the sediments. Oxidation of xylenes does not appear to be significant Hendey et al., 1974). Xylenes are reported not to absorb light significantly at wave lengths of ultraviolet-visible spectrum Volatilization half-life (days) o-xylene m-xylene p-xylene 2.6 - 11 2.8 - 11 2.7 - 11 11-2 ------- (>300nm) that correspond to the environmentally relevant wavelengths reaching surface waters (Weast, 1972). Therefore, photolysis is unlikely to be a significant degradative pathway, if it occurs at all. Sorption to sediments varies depending on the percent of organic matter. Green et al. (1981) found that movement of o- and p-xylene was inversely related to the octanol/water partition coefficient and that movement increased as the bulk density of the soil decreased. Biodegradation of xylene may be significant, but varies considerably depending on the isomer the source of seed, the feed rate and whether or not it was acclimated (Dore et al., 1975, Marion and Malaney, 1964). m-Xylene was found to be toxic to microorganisms at high feed rates (500 mg/L) (Marion and Malaney, 1964). A poor to moderate degradation rate is indicated by results of these studies and the reports of xylenes in drinking water. 11-3 ------- SECTION III. AQUATIC TOXICITY Introduction Aquatic life advisory concentrations are conceptually different from national aquatic life water quality criteria. Because aquatic life advisories are intended to be used to identify situations where there is cause for concern and where appropriate action should be taken, the advisory concentration for a chemical is derived to be equal to or lower than what the Criterion Continuous Concentration (Stephan et al. 1985) would be if a national water quality criterion for aquatic life could be derived for the chemical. If the concentration of a chemical in a variety of surface waters is found to exceed the aquatic life advisory concentration, this may indicate that the U.S. EPA should consider deriving aquatic life water quality criteria for that chemical. The literature searching and data evaluation procedures used in the derivation of aquatic life advisories are identical to those . used in the derivation of water quality criteria for aquatic life (Stephan et al. 1985). However, advisories do not contain a section on "Unused Data" as in a criteria document. This aquatic life advisory concentration for xylene was derived using the procedures described in the "Guidelines for Deriving Ambient Aquatic Life Advisory Concentrations" (Stephan et al. 1986). A knowledge of these guidelines is necessary in order to understand the following text, tables, and calculations. The latest comprehensive literature search for information for this aquatic life advisory was conducted in February, 1987. Commercial xylene is a mixture of the three isomers of xylene and may contain traces of ethylbenzene. Although slight differences have been noted in the toxicity of the various isomers to aquatic organisms, these differences have been small (within a factor of 5) and the data have not consistently demonstrated that any one isomer is more toxic than the others. For the purpose of this advisory, it is assumed that the three isomers are equally toxic and that their toxicities are additive. Therefore, data on the toxicities of all forms of xylene were combined instead of developing advisories on each individual isomer. In static toxicity tests, the amount of xylene in the exposure chambers declines rapidly. Benville and Korn (1977) found that concentrations decreased by 19 to 35% in 24 hr and that <1% of the initial concentration was left in 96 hr. Brooke (1987) calculated a half-life of 15.6 hr for xylene in a static exposure. Brooke also ran a set of comparison tests to determine if the 96-hr LC50 for fathead minnows exposed to xylene was III-l ------- dependent on the exposure method. He reported that the LC50 from a measured flow-through exposure (8,870 ug/L) was similar to that derived from a static exposure that was measured at 48 hr intervals (8,400 ug/L). However, if the static 96-hr LC50 had been calculated using only the 0-hr measurement of the xylene concentrations in the exposure, the value (i.e. 22,400 ug/L) would have been 2.525 times larger than that obtained from the flow-through exposure. In order to allow a more direct comparison of the effects of xylene on different species of aquatic organisms, the results from the various types of exposures need to be standardized. Therefore, acute toxicity data in Table 1 that were obtained from static tests that were not measured, or were only measured initially, were divided by a factor of 2.525 to equate them with flow-through test results. Effects on Freshwater Organisms Acceptable data on the acute toxicity of xylene to freshwater organisms are available for two species of invertebrates and six fish (Table 1). The snail, Aplexa hyporum, is quite tolerant of exposure to xylene with an LC50 > 22,400 ug/L (Holcombe et al., manuscript). Daphnia magna, the other invertebrate tested, was the most sensitive freshwater organism with a Species Mean Acute Value (SMAV) of 3,820 ug/L. The SMAVs for the six fish species were similar and ranged from 8,050 ug/L for the rainbow trout (Salmo qairdneri) to 16,510 ug/L for the goldfish (Carassius auratus) (Table 2). No acceptable data are available on the chronic toxicity of xylene to freshwater organisms. However, Black et al. (1982) exposed the fertilized ova of rainbow trout and leopard frogs (Rana pipiens) to various concentrations of xylene in flow- through chambers and monitored embryo survival and development through hatching. The EC50 for rainbow trout at hatching (23 days) was, 950 ug/L while at 4 days post-hatch the EC50 declined to 3,770 ug/L (Table 3). For the leopard frog the EC50s at hatching in 5 days and at 4 days post-hatch were 4,060 and 3,530 ug/L, respectively. Additional data are available on the lethal and sublethal effects of xylene on freshwater organisms (Table 3). Although some- of these results are from static unmeasured exposures, the data were not adjusted to flow-through conditions and therefore may not be directly comparable to the values contained in Table 1. The effects of xylene on microorganisms have been determined through a variety of static tests (Table 3). Bacteria and protozoans were quite resistant to xylene with inhibition of survival and cell replication occuring at concentrations between 16,900 and 200,000 ug/L (Bringmann 1973, 1978; Bringmann and Kuhn 1977b, 1980, 1981; Bringmann et al. 1980; Rogerson et al. 1983). Algal photosynthesis and cell replication were reduced by 50% 111-2 ------- after exposure to xylene concentrations ranging from 46,000 to 105,000 ug/L (Hutchinson et al. 1979, 1980; Kauss and Hutchinson 1975). Maynard and Weber (1981) observed that juvenile coho salmon (Oncorhynchus kisutch) were able to detect and avoid xylene at levels as low as 680 ug/L. Concentrations of 2,000 ug/L affected the respiration rate of rainbow trout (Slooff 1979). Effects on Saltwater Organisms Acceptable data on the acute toxicity of xylene to saltwater organisms are available for four invertebrates and one species of fish (Table 1). The adjusted Species Mean Acute Values ranged from 1,815 ug/L for adult bay shrimp (Crangon franciscorum) to 154,300 ug/L for embryos of the Pacific oyster (Crassostrea gigas). The striped bass (Morone saxatilis)« with a SMAV of 5,090 ug/L, was slightly more sensitive to xylene exposure than the freshwater fish species (Table 2). No chronic data are available for saltwater animals exposed to xylene. Commercial xylene concentrations greater than 10,000 ug/L were found to inhibit algal growth (Dunstan et al. 1975) (Table 3), while the motility of barnacle nauplii was affected by 19,500 ug/L (Donahue et al. 1977; Winters et al. 1977). Calculation of Advisory Concentration Species and Genus Mean Acute Values are available for 13 organisms (Table 2) and range from 1,815 ug/L for the bay shrimp to 154,300 ug/L for the Pacific oyster. The lowest Genus Mean Acute Value (GMAV), 1,815 ug/L, is therefore divided by a factor of 3.4, in accordance with the advisory guidelines, resulting in an Advisory Acute Value (AAV) of 533.8 ug/L. Due to the lack of any acceptable data on the chronic toxicity of xylene to aquatic organisms, an empirical value of 25 is used as the Advisory Acute-Chronic Ratio (AACR). Division of the AAV (533.8 ug/L) by the AACR (25) results in an Advisory Concentration of 21 ug/L. III-3 ------- Table I. Acute Toxicity of Xylene to Aquatic Animals FRESHWATER SPECIES Spec i es Sna i I (odult), Ap|exa hvporuni CIadoceran (<48 hr), Dophn i a magna Clodoceron (<24 hr), Daphnia maana Rainbow trout <09 g). Sal mo ao i rdner i Rainbow trout (0 6 9), Sal mo ao i rdner i Rainbow trout (juvenile), SaImo aairdneri Go Idf ish (3 8-6.4 cm), CarossI us aurot us Method r. M S. U r. u s. u s, u r. m s. u Chemicol Techni col (I00Z) Techni cal (lOOZ) Hardness (mg/L as CaCOjl 44.7 44.7 40 44 44.7 20 LC50 or ECSO W-) > 22.400 14,300 3,820 13,500 8,200 8.050 36,810 Adj usted LC50 or EC50 5.660 5,350 3.250 14,580 Species Mean Acute Value lua/L) >22,400 3,820 8,050 Ref erences Hoi combe et al. manuscri pt Hermens et al 1984 Holcombe et al manuscr i pt Walsh et al. 1977; Mayer and Ellersieck 1986 Johnson ond Finley 1980; Mayer and Ellersieck 1986 Holcombe et al manuscr i pt Pickering and Henderson 1966 ------- Table I (continued) Hordness LC50 (mg/L as or EC50 Spec i es Method0 Chemical** CoCOjl (ua/l) Goldfish F. M Anolyticol 80 16,940 (1-1.5 yr), Caross i us auratus Goldfish r. M o 44.7 16,100 (juvenile), Carass i us auratus Fathead minnow S, U - 360 2B.770 (3.8-6.4 cm), Pimeohales promeI as Fathead minnow S, U - 20 26,700 (3.8-6.4 cm). Pimeohales promeIos Fathead minnow S, U Reagent - 42,000 (juvenile), Pimeohales oromelas Fathead minnow S, U p SI.I 21,200 (juvenile), (99Z) Pimenholes promeI as Adj usted LC50 or EC50 (iia/L)c Species Uean- Acute Volue fua/L) Ref erences Brennimon et al. 1976 16,510 Hoi combe et al. manuscr i pt 11,390 - Pi cker i ng and Henderson 1966 10,600 - Pickering and Henderson I 966 17,000 - klettson et al . 1976 8,400 Brooke 1987 ------- Table I. (cont inuedj Soec i es Fathead ainno« (juvenile). Pimecholes prowelas' Fathead minno* (j uven lie), Piaiephal es promelos Fathead minno* (juvenile), Pimeohales promelos Fathead minno* (juvenile), Pimepholes promelos White sucker (juveni1e). Cotostomus cowmersonl Guppy (6 mo). Poec ilia ret i culota Method" Chemi colb Hardness (ing/L os CoCOjl LC50 or ECSO S. U0 p SI I 22,400 (99*) S, H p - 8.400 (99*) F. U p - 8,870 F, y o 44.7 16,100 F, U o 44.7 16,100 S, U - 20 34,730 Adjusted LC50 or EC50 (uo/L)C Species Mean Acute Value Ltia/Ll References 8,870 - Brooke 1987 Brooke 1987 Ge i ger et a I. I 986 Brooke I 987 11,950 Holcombe et al . manuscri pt I 6,100 Hoi combe et a I . manuscr i pt 13,750 13,750 Pickering and Henderson 1966 ------- Toble I. (coot i nued) Spec i es Bluegi11, Lepomi s mocrochi rus BIuegi 11 , (3 8-6.4 cm), Lepomi s mocrochi rus Bluegi 11 (0 9 g). Lepomis mocrochi rus Bluegi11 (juvenile). Lepomi s mocrochi rus BIuegi11 (j uveniIe), Lepomi s mocrochi rus Bluegi 11 (juvenile), Lepomi s mocrochi rus Method" S. U S. U S. U S. M_ r, y r. m C h em i c a I Technicol (I00Z) Reagent x Reagent x Hardness (mg/L as CoCOjl_ 20 44 31.2 31 .2 LC50 or CCSO itiflM- 19,000 20,870 13,500 24,500 15,700 44.7 16,100 Adjusted Species Mean LC50 or EC50 Acute Value (iiq/L)c (WL) 7.500 8,265 5,350 9,700 References Cope 1965 Pickering and Henderson 1966 Johnson and finley 1980; Mayer and Ellersieck 1986 Ba iIey et a I. I 985 Bailey et a I. 1985 Holcombe et al manuscr i pt ------- Table I (continued) SALTWATER SPECIES LC5Q Adjusted Species Mean Salinity or EC50 LC50 or ECSO Acute Value Soec i es Method0 Chemi col ^ (o/Kol (uo/Ll (ua/L)C (mo/H References Pacific oyster S. U o 25.3-30.8 169.000 66,900 - Legore 1974 (embryo), Crossostreo ai oas Pocific oyster S. U x 25.3-30.8 602,000 238,000 - Legore 1974 (embryo), Crossostreo al oos Pocific oyster S, U p 25.3-30.8 584,000 231,000 154,300 Legore 1974 (embryo), Crossostreo oi oos Gross shrimp, S, U - 15 7,400 2,900 2,900 Totem et ol 1978 Poloemonetes puoi o Boy shrimp S. U o 25 1,100 - - Benville and (odult). (> 99*) 1977 Cronoon fronc iscorum ------- Table I. (cont i nued) LC50 Sali n i ty or CCSO Spec i es Method0 Cheroi col ^ (a/Kg) (tiq/L) Bay shrimp S, M n 25 3,200 (adult), (>99X) Cranaon franc i scorum Boy shrimp S, M p 25 1,700 (adult), (>99X) Cronoon f rone i scorum Oungeness crab f, U o 30 6,000 (1st zoea). Cancer waoister Oungeness crab F, 0 m 30 12,000 (1st zoea). Cancer mooi ster Striped bass S, U o 25 9,700 (juvenile), (> 99*) Uorone soxotiIi s Adjusted Species Mean LC50 or EC50 Acute Value (uo/LlC (ua/Ll References Benv i11e and Korn 1977 1,815 Benv iI Ie and Korn 1977 CoM.el I «t g|. 1977 8,500 Co I duel I et ol . 1977 Benv i11e and Korn 1977 ------- Tab Ie I. (cont i nued) Speci es Method Chemicol Soli ni ty h/*ql LC50 or EC50 (Wi.) Adj usted LC50 or ECSO Species Uean Acute Value [flll) Ref erences Striped bass (juvenile), Morone sonat ills S. M m (> 99Z) 25 6,000 Benv i11e and Horn 1977 Striped bass (juveni le), Morone saxot11i s S. U P (>99X) 25 I ,700 5.090 Benv i11e and Korn 1977 0 S = Static; f - Flow-through; M = Measured; Mo = measured only at 0-hr, U = Unmeasured. ^ m = meta-xylene; o = ortho-xylene; p = pora-xylene; * = nixed isomers; percent purity is listed in parentheses when available. 0 Static unmeasured and static 0-hr measured data were adjusted by dividing by a factor of 2.525. ------- Toble 2. Ranked Genus Mean Acute Values with Species Uean Acute-Chronic Ratios Genus Mean Species Mean Species Uean Acute Value Acute Value Acute-Chroni Ronk° (ua/L> Species (lia/Ll** Rot io 13 154,300 Pacific oyster. 154.300 Crassostrea aiaos 12 > 22.400 SnaiI. > 22,400 Aplexo hvoorum II 16,510 Goldfish, 16,510 Caross i us ourotus 10 16,100 White sucker, 16,100 Cotostomus comroersoni 9 15,900 Bluegill, 15,900 'Lepomis macrochi rus 8 13,750 Guppy, 13,750 Poec ilia ret i culata 7 11,950 Fathead minno«, 11,950 Plmepholes oromelas 6 8,500 Dungeness crab, 8,500 Cancer magi ster 5 8,050 Rai nbo» trout, Solmo gairdneri 8,050 ------- Table 2. (continued) Ronk Genus Uean Acute Value (/"l/l| Spec i es Species Mean Acute Value (Wl)b Species Mean Acute-Chron i c Rat i o 5,090 Striped bass, Morone soxot iI is 5,090 3,820 Ciadoceran, Daohni a maano 3,820 2,900 Grass shrimp Poloemonetes duoi o 2.900 I,815 Bay shrimp, Cranaon franciscorum I .815 a Ranked from most resistant to most sensitive based on Genus llean Acute Value ^ From Table I. Advisory Acute Value = (I ,815 /ig/L)/ 3.4 = 533.8 /jg/L. Advisory Acute-Chronic Ratio = 25 Advisory Concentration = (533.8 /ig/L)/ 25 = 21 /ig/L ------- Table 3. Other Data on Effects of Xylene on Aquatic Organisms FRESHWATER SPECIES Spec i es Bocteri iioi, Pseudomonos put ido 61ue-green alga, Anacvst i s aerua i nosa Green alga, Ch I amvdonionos onquloso Green alga, Chlorello vulgaris Green alga, Chlorello vulooris Green alga, Chlorello vulgaris Chemical Hgrdness (ng/L as CoCOj) Durot i on 16 hr B days 3 hr 24 hr 10 days 3 hr Effect Inci pient inhibit!on of cell repli cat i on Inc i pi ent inhibition of cell repli cat i on EC50 (photosynthesis) ECSO (cell replication) Reduced survival EC50 (photosynthesis) Concentrat ion fiiq/L) > 200,000 > 200.000 46,000 55,000 171 .000 105,000 Ref erence Bringmann 1973; Bringmann and Kuhn 1977b Bringmann and Kuhn I 978a.b Hutchinson et al 1979, 1980 Kauss and Hutchinson 1975 Kauss et al . 1972, 1973 Hutchinson et al 1979, 1980 ------- Table 3. (continued) Hardness (mg/L as Spec i es Chemlcol0 CoCOj) Durat i on Green alga, - - 8 days Scenedesmus otiadrlcouda Protozoan, - - 72 hr Entos i phon sulcatum Protozoan, - - 48 hr Chi Iomonas pgraaoeci um Protozoan, - - 20 hr Uronewa oarduczi Protozoan, m - 18 hr Col pi di um colpoda Protozoan, o - >.24 hr Tetrohvineno el Iiott i Effect Incipient inhibition of eel I repli cat i on Inc i pi ent inhibition of cell repli cat i on Inc i pi ent i nhi bi t i on of cell replication Inc i pi ent inhibition of call repli cat i on Inc i pi ent i nhibition of survival Concent rat i on LeaZU > 200,000 > 160,000 > 8D.OOO > 160,000 162,000 Ref erente Bringraann and Kuhn 1977b, 1978a,b Bringmann 1978; Bringraann and Kuhn 1981 Br i ngaionn and Kuhn I 981, Br ingmann et al. 1980 Bringmann and Kuhn 1980. 1981 Rogerson et al 1983 Inc i pi ent i nhi bi t i on of survival 18,500 Rogerson et al 1983 ------- Table 3. (continued) Soeci es Chewlcol" Protozoan, ¦ Tetrahvmena elliottl Protozoan, p Tetrohvmeno el Iiott i Clodoceron (24 hr). Dophnio magna Clodoceron, Dophnio woano Coho salmon o (juvenile), Oncorhvnchus kisutch Rainbow trout, £o]j#o on i rdneri Rainboa trout « (eabryo), So I bo oo i rdnerl Hardness (mg/L as CaCOjl Curat i on >24 hr >24 hr 24 hr 24 hr I hr 180 24 br 96.0 23 days (to hatch) Effect Concentration (/ia/L) Reference Inc i pi ent i nhi bi t i on of survival 55,700 Rogerson et al . I 983 Inc i pi ent inhibition of survival 16,900 Rogerson et al. I 983 EC50 (iwnobi I i zat ion) 150,000 Bringmann and Kuhn 1977a LC50 > 100.000 and Doaden and < I.000,000 Bennett 1965 EC50 680 yaynard and Weber (avoidance) 1981 Increased respi rat i on 2,000 SI oof f 1979 EC50 (death and deforai ty) 5,950 Black et al 1982 ------- Table 3. (continued) Spec Ies Chemi ca10 Rainbo* trout ¦ (embryo/larva), So I mo QolrdnTl Hardness (mg/L as CoCOjl Durot i on 96.0 27 days (4 days post-hatch) Goldfish o - 24 hr (6.2 cm). Corassius ourotus Goldfish m - 24 hr (6.2 en). Corossius ourotus Goldfish p - 24 hr (6.2 cm). Corossi us ourotus Guppy o 25 7 days (2-3 mo). PoeciIi o ret iculoto Concentrat i on tf f ec t (ua/L) Ref erence CCSO 3,770 Block et ol . 1982 (death and deformi ty) LCSO 13,000 Bridie et al. 1979 LCSO 16,000 Bridie et al. 1979 LC50 18,000 Bridie et al. 1979 LCSO 35,100 Konemann 1979, 1981 ------- Table 3. (continued) Spec i es Guppy (2-3 mo). Poec iIi o ret i cuIoto Chowicol Hardness (mg/L os CoCOjl 25 Ourot i on 14 days Guppy (2-3 mo). PoeciIi a rot iculata 25 7 dqys Leopard frog (embryo). Rang pinions Leopard frog (embryo/larva), Rono oipiens 105 4 105 4 5 doys (to hatch) 9 days (4 days post-hatch) Effect LC50 Concent rat i on fWL) 37.700 Reference Konemann 1979, 1981 LC50 35.100 Konemgnn 1979, 1981 EC50 (death and deformi ty) EC50 (death and deformi ty) 4.060 3,530 Block et ol. 1982 Black et al 1982 ------- Table 3. (continued) SALTWATER SPECIES Species Chemical Oi no- flagellate, x Amphldlnlum corterae Barnacle (naupliI), Bolanus owphitrite Coho solmon (5-40 9). Oncorhvnchus Iti sutch Soli n i ty (q/*g) 30 30 Durot i on 2-3 days I hr 24 hr Effect Croath i nhi bi t i on EC50 (mobiIi ty) Lethali ty Concentration LiaZU > 10.000 19,500 100,000 Reference Dunstan et al. 1975 Donahue et al 1977; Wi nters et al. I 977 Uorrow et al 1975 0 m * aeta-xylene; o = ortho-xylene; p = para-xylene; x = mixed isomers ------- SECTION IV.REFERENCES Bailey, H.C., D.H.W. Liu and H.A. Javitz. 1985. Time/toxicity relationships in short-term static, dynamic, and plug-flow bioassays. In: Bahner, R.C. and D.J. Hansen (Eds.). Aquatic Toxicology and Hazard Assessment: Eighth Symposium ASTM STP 891. American Society for Testing and Materials, Philadelphia, PA. pp. 193-212. Benville, P.E., Jr., and S. Korn. 1977. The acute toxicity of six monocyclic aromatic crude oil components to striped bass (Morone saxatilis)and bay shrimp (Crago franciscorum). Calif. Fish and Game 63:204-209. Black, J.A., W.J. Birge, W.E. McDonnell, A.G. Westerman, B.A. Ramey and D.M. Bruser. 1982. The aquatic toxicity of organic compounds to embryo-larval stages of fish and amphibians. PB82- 224601. National Technical Information Service, Springfield, VA. Brenniman, G., R. Hartung and W.J. Weber, Jr. 1976. A continuous flow bioassay method to evaluate the effects of outboard motor exhausts and selected aromatic toxicants on fish. Water Res. 10:165-169. Bridie, A.L., C.J.M. Wolff and M. Winter. 1979. The acute toxicity of some petrochemicals to goldfish. Water Res. 13:623- 626. Bringmann, G. 1973. Determination of the biological damage from water pollutants from the inhibition of glucose assimilation in the bacterium Psedomonas fluorescens. Gesund.-Ing. 94:366-369. Bringmann, G. 1978. Studies on the biological effects of waterborne pollutants in protozoans, I. Bacteriophagus flagellates (model organisms: Entosiphon sulcatum stein). Z. Wasser Abwasser Forsch. 11:210-215. Bringmann, G. and R. Kuhn. 1977a. Results of the damaging effect of water pollutants on Daphnia magna. Z. Wasser Abwasser Forsch. 10:161-166. Bringmann, G. and R. Kuhn. 1977b. Limiting values for the damaging action of water pollutants to bacteria (Pseudomonas putida) and green algae (Scenedesmus cruadricauda) in the cell multiplication inhibition test. Z. Wasser Abwasser Forsch. 10:87-98. IV-1 ------- Bringmann, G. and R. Kuhn. 1978a. Limiting values for the noxious effects of water pollutant material to blue algae (Microcystis aeruginosa) and green algae (Scenedesmus quadricauda) in cell propagation inhibition tests. Vom Wasser 50:45-60. Bringmann, G. and R. Kuhn. 1978b. Testing of substances for their toxicity threshold: Model organisms Microcystis (Diplocystis) aeruginosa and Scenedesmus quadricauda. Mitt. Int. Ver. Theor. Angew. Limnol. 21:275-284. Bringmann, G. and R. Kuhn. 1980. Determination of the biological effect of water pollutants on protozoa. II. Bacteriovorous ciliates. Z. Wasser Abwasser Forsch. 13:26-31. Bringmann, G. and R. Kuhn. 1981. Comparison of the effects of harmful substances on flagellates as well as ciliates and a holozoic bacteriophagus and saprozoic protozoan. Gas- Wasserfach, Wasser-Abwasser 122:308-313. Bringmann, G., R. Kuhn and A. Winter. 1980. Determination of the biological effect of water pollutants in protozoa. III. Saprozoic flagellates. Z. Wasser Abwasser Forsch. 13:170-173. Brooke, L.T. 1987. Center for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI. (Memorandum to L.J. Larson, Center for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI. August 31). Caldwell, R.S., E.M. Caldarone and M.H. Mallon. 1977. Effects of a seawater-soluble fraction of Cook Inlet crude oil and its major aromatic components on larval stages of the Dungeness crab (Cancer magister Dana). In: Fate and effects of petroleum hydrocarbons in marine ecosystems and organisms. Wolfe, D.A. (Ed.). Pergamon Press, New York, NY. pp. 210-220. Cope, O.B. 1965. Sport Fishery Investigations. U.S. Fish and Wildlife Service Circular 226:51-63. Donahue, W.H., R.T. Wang, M. Welch and J.A.C. Nicol. 1977. Effects of water-soluble components of petroleum oils and aromatic hydrocarbons on barnacle larvae. Environ. Pollut. 13:187-202. Dowden, B.F. and H.J. Bennett. 1965. Toxicity of selected chemicals to certain animals. J. Water Pollut. Control Fed. 37:1308-1316. Dunstan, W.M., L.P. Atkinson and J. Natoli. 1975. Stimulation and inhibition of phytoplankton growth by low molecular weight hydrocarbons. Mar. Biol.(Berl.) 31:305-310. IV-2 ------- Geiger, D.L., S.H. Poirier, L.T. Brooke and D.J. Call (Eds.). 1986. Acute toxicity of organic chemicals to fathead minnows (Pimephales promelas). Center for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI. Hermens, J., H. Canton, P. Janssen and R. DeJong. 1984. Quantitative structure-activity relationships and toxicity studies of mixtures of chemicals with anaesthetic potency: Acute lethal and sublethal toxicity to Daphnia magna. Aquat. Toxicol. 5:143-154. Holcombe, G.W., G.L. Phipps, A.H. Sulaiman and A.D. Hoffman, manuscript. Simultaneous/multiple species testing: Acute toxicity of 13 chemicals to 12 diverse freshwater families. U.S. Environmental Protection Agency, Environmental Research Laboratory-Duluth, Duluth, MN. Hutchinson, T.C., J.A. Hellebust, D. Mackay, D. Tam and P. Kauss. 1979. Relationship of hydrocarbon solubility to toxicity in algae and cellular membrane effects. J. Am. Petrol. Inst. 4308:541-547. Hutchinson, T.C., J.A. Hellebust, D. Tam, D. Mckay, R.A. Mascarenhas and W.Y. Shiu. 1980. The correlation of the toxicity to algae of hydrocarbons and halogenated hydrocarbons with their physical-chemical properties. Environ. Sci. Res. 16:577-586. Johnson, W.W. and M.T. Finley. 1980. Handbook of acute toxicity of chemicals to fish and aquatic invertebrates. Resource Publication 137. U.S. Fish and Wildlife Service, Washington, DC. Kauss, P.B. and T.C. Hutchinson. 1975. The effects of water- soluble petroleum components on the growth of Chlorella vulgaris Beiierinck. Environ. Pollut. 9:157-174. Kauss, P.B., T.C. Hutchinson and M. Griffiths. 1972. Field and laboratory studies of the effects of crude oil spills on phytoplankton. In: Proceedings 18th annual technical meeting on environmental progress in science and education. Institute of Environmental Sciences, Mt. Prospect, IL. pp. 22-26. Kauss, P., T.C. Hutchinson, C. Soto, J. Hellebust and M. Griffiths. 1973. The toxicity of crude oil and its components to freshwater algae. In: Proceedings of joint conference on prevention and control of oil spills. American Petroleum Institute, Washington, DC. pp. 703-714. IV-3 ------- Konemann, W.H. 1979. Quantitative structure-activity relationships in fish toxicity studies. Part 1: A relationship for 50 industrial pollutants. In: Quantitative structure- activity relationships for kinetics and toxicity of aquatic pollutants and their mixtures in fish. Konemann, W.H. (Ed.). University of Utrecht, Utrecht, The Netherlands, pp. 33-45. Konemann, H. 1981. Quantitative structure-activity relationships in fish toxicity studies. Part 1: Relationships for 50 industrial pollutants. Toxicology 19:209-221. Legore, R.S. 1974. The effect of Alaskan crude oil and selected hydrocarbon compounds on embryonic development of the Pacific oyster, Crassostrea qiqas. Ph.D. thesis, University of Washington, Seattle, WA. Available from: University Microfilms, Ann Arbor, MI. Order No. 74-29,447. Mattson, V.R., J.W. Arthur and C.T. Walbridge. 1976. Acute toxicity of selected organic compounds to fathead minnows. EPA- 600/3-76-097. National Technical Information Service, Springfield, VA. Mayer, F.L., Jr. and M.R. Ellersieck. 1986. Manual of acute toxicity: Interpretation and data base for 410 chemicals and 66 species of freshwater animals. Resource Publ. No. 160. U.S. Fish and Wildlife Service, Washington, DC. Maynard, D.J. and D.D. Weber. 1981. Avoidance reactions of juvenile coho salmon (Onchorhynchus kisutch) to monocyclic aromatics. Can. J. Fish. Aquat. Sci. 38:772-778. Morrow, J.E., R.L. Gritz and M.P. Kirton. 1975. Effects of some components of crude oil on young coho salmon. Copeia 2:326-331. Pickering, Q.H. and C. Henderson. 1966. Acute toxicity of some important petrochemicals to fish. J. Water Pollut. Control Fed. 38:1419-1429. Rogerson, A., W.Y. Shiu, G.L. Huang, D. Mackay and J. Berger. 1983. Determination and interpretation of hydrocarbon toxicity to ciliate protozoa. Aquat. Toxicol. 3:215-228. Slooff, W. 1979. Detection limits of a biological monitoring system based on fish respiration. Bull. Environ. Contam. Toxicol. 23:517-523. Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. 1985. Guidelines for deriving numerical national water quality criteria for the protection of aquatic organisms and their uses. PB85-227049. National Technical Information Service, Springfield, VA. IV-4 ------- Stephan, C.E., G.A. Chapman, D.J. Hansen and T.W. Purcell. 1986. Guidelines for deriving ambient aquatic life advisory concentrations. December 2 draft. U.S. Environmental Protection Agency, Environmental Research Laboratory, Duluth, MN. Tatem, H.E., B.A. Cox and J.W. Anderson. 1978. The toxicity of oils and petroleum hydrocarbons to estuarine crustaceans. Estuarine Coastal Mar. Sci. 6:365-373. Walsh, D.F., J.G. Armstrong, T.R. Bartley, H.A. Salman and P.A. Frank. 1977. Residues of emulsified xylene in aquatic weed control and their impact on rainbow trout Salmo qairdneri. PB267270 or REC-ERC-76-11. National Technical Information Service, Springfield,.VA. Winters, K., C. Van Baalen and J.A.C. Nicol. 1977. Water soluble extractives from petroleum oils: Chemical characterization and effects on microalgae and marine animals. Rapp. P.V. Reun. Cons. Int. Explor. Mer. 171:166-174. IV-5 ------- SECTION V. EPA CONTACTS AQUATIC LIFE ADVISORIES For further information regarding the aquatic life and fish and water exposure advisories contact: FTS 382-7144 (202)382-7144 FTS 475-7315 (202)475-7315 V-l ------- |