AMBIENT WATER QUALITY ADVISORY
XYLENE
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER REGULATIONS AND STANDARDS
CRITERIA AND STANDARDS DIVISION
WASHINGTON, D.C.

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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

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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

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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

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ACKNOWLEDGMENTS
AQUATIC LIFE
Mary D. Balcer, author
University of Wisconsin-Superior, Superior, WI
iv

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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

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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

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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

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(>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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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.

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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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

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