-8Z2-R-$7-100
Draft
9/25/87
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
2. 4. 5-TRICHLOROPHENOL
U.S. ENVIRONMENTAL PROTECTION AGENCY
OriflCE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH. MINNESOTA
NARRAGANSETT. RHODE ISLAND
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NOTICES
This document has been
the Criteria and
Mention of trade names or commercial products does not constitute *nitn
or recommendation for use. constitute endorsement
This document is available to the public through the National
Informanon Service (NTIS). 5285 Port Royal Rofd. Sprin«neti.
i. •
22?6t
11
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NOTICES
This document has been revi»w»H K^
of *ater Re.ul ations^s^ JarSl.
approved for publication.
Dlvisi°- Office
Protection Agency, and
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Draft
9/25/87
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
2.4,5-TRICHLOROPHENOL
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH. MINNESOTA
NARRAGANSETT. RHODE ISLAND
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FOREWORD
accurately reflect th. latest JclStifiS k»~l.^ "^ ^ "iteria that
.11 Identifiable effects on h.alth and "elfar* th.t°mi± t"* ""* '^'" °l
presence of pollutants in any body of water %,1rJ, ^ ! «xPe<=tei1 fr
document proposes water quality criteria ° th" "ld' this
Th-. criteria do not involve
After
issue th. criteria in final
previously published EPA
at
... EPA win
..i /
pollutant concentrations that can b4 nsld to Lri^! J"1™"" ««eptabl«
for discharges to such waters. * enforceable permit limits
under section 304 to reflec r
incorporation into water qua UtJ«S£
assist States in the modification ofseSon
development of water quality standards Ui
part of State water qualit/standard,*^'^
criteria
Before
aiable fr°B EpA to
*"* i
Martha G. Prothro
Director
Office of Water Regulations and Standards
iii
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ACKNOWLEDGMENTS
Daniel J. Call
(freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
Jeffrey L. Hyland
Richard K. Peddicord
(saltwater authors)
Battelle Ocean Sciences
Duzbury, Massachusetts
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David .'. Hans en
(saltwater coordinator)
Environmental Research Laboratory
Narrajansett, Rhode Island
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CONTENTS
Page
Notices
11
Foreword
ill
Acknowledgments
iv
Tables
' v i
Introduction
Acute Toxicity to Aquatic Animals 2
Chronic Toxicity to Aquatic Animals 4
Toxicity to Aquatic Plants »
Bioaccumulation a
o
Other Data
Unused Data 0
o
Summary
8
National Criteria
Implementation
References
*'*'•***•• 40
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TABLES
Pii
1. Acute Tozicity of 2.4,5-Trichlorophenol to Aquatic Animals :
2. Chronic Toricity of 2.4.5-Trtchlorophenol to Aquatic Animals
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios
4. Toxicity of 2,4,5-Trichlorophenol to Aquatic Plants ..
5. Bioaccumulation of 2.4.5-Trichlorophenol by Aquatic Organisms 22
6. Other Data on Effects of 2.4.5-Trichlorophenol on Aquatic Organi
18
21
sms
23
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I ntroduction
2,4,5-Trichlorophenol (2,4,5-TCP) is a crystalline solid at room
temperature. It is soluble in water up to 2.000 mg/L. has an ionization
constant (pKa) of 7.0 to 7.4 (Ahlborg and Thunberg 1980; Doedens 1964- U S
EPA 1980), and a log n-octanol/water partition coefficient of 3.70 (Hansch
and Leo 1979). 2.4.5-TCP is used as an algicide. fungicide, and bactericide
and as an antimildew and preservation agent in cooling towers, pulp mills.
. and in hide and leather processing (Ahlborg and Thunberg 1980; U.S. EPA
1980). It is also used in the production of the pesticides erbon.
fenchiorphos, fenoprop (2,4.5-TP). hexachlorophene. and 2,4.5-trichloro-
phenoxyacetic acid (2.4.5-T) (Ahlborg and Thunberg 1980; Buikema et al. 1979;
Doedens 1964; Kozak et al. 1979; Stolzenburg and Sullivan 1984).
Contamination of waters with 2.4.5-TCP and other chlorophenols has
resulted from the use of chlorophenoryacetic acid herbicides containing
chlorophenolic impurities, from the chlorination of waste treatment plant
effluents, and from pulp bleaching (Ahlborg and Thunberg 1980; Buikema et al.
1979; Jolley et al. 1978; Rockwell and Larsen 1978). Residues have been
detected in fish and other organises collected downstream fro» pulp am,
(Paasivirta et al. 1985). Considerable concern has been expressed that
2.3.7.8-tetrachlorodib«ni<>-p-diosin (TCOD) can be an impurity in 2.4.5-TCP
(Anonymous 1978; Firtstono et al. 1972).
At rerj lew concentrations, some phenolic compounds impair the odor and/
or taste of wattr and fish. 2.4.5-TCP has a taste threshold concentra-
tion in water of 1 m/L arid an odor threshold concentration of 200 Mg/L
(Dietz and Traud 1978). However. Shumway and Palensky (1973) did not observe
flavor impairment in rainbow trout exposed to 320 m/L for 48 hr.
An understanding of the "Guidelines for Deriving Numerical National water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses
1
-------
ues
(Stephtn et al. 1985). hereinafter referred to as the Guidelines, and the
response to public comment (U.S. EPA 1985a) ,, necessarj in order to
understand the following text, tables, and calculations. Results of such
. intermediate calculations as recalculated LCSOs and Species Mean Acute Val
are given to four significant figures to prevent round off error in
subsequent calculations, not to reflect the precision of the value. The
criteria presented herein supersede the aquatic life information in a
previous criteria document (U.S. EPA 1980) because these criteria are baaed
on additional information. The latest literature search for information for
this document was conducted in July. 1988; some more recent information was
included. Data that are in the files of the U.S. EPA's Office of Pesticide
Programs concerninf the effects of 2,4.5-TCP on aquatic life and its uses
have not been evaluated for possible use in the derivation of aquatic life
criteria.
Acute Toxicitv to Aquatic Anim.lj
Data that can be used. accordinf to the Guidelines, in the derivation of
Final Acute Values for 2.4.5-TCP are presented in Table I. The rainbow
trout. iiil2 Hird.ne.ri. »*« the «o»t sensitive freshwater species with a
96-hr LC50 of 280 ftg/l. Thw cladoceran. fliaHnH. lltai. was the »ost
resistant species, with a 48 hr ECSO of 2.660 M|/L. The range of acute
values for fish was fro* 260 Mf/L in the trout to 3.060 M|/L in the
«uppjr, poecUlj rtm.lltl. A si.ilar ranfe for invertebrates extended from
338 ni/L in.the aaphipod, Gaaaarm oseudol iana.e.u.j to 2.880 M|/L in
Paohnia.
The effect of pH on the acute toxicity of 2.4.5-TCP w», examined with the
«upp7. Pmilli rctjculiti (Saarilcoski and Viluksela 1981.1982; Salkinoj*-
Salonen et al. 1981). The 98-hr LCSOs at pH = 6. 7. and 8 were 990. 1.240.
2
-------
and 3.060 MK/L. r«3p«ctive17. The freshwater criterion was not made
pH-dependent because data are available for onlf one species.
Freshwater Species Mean Acute Values (Table 1) were determined from the
available acute values. Genus Mean Acute Values (Table 3) were the same as
the:Species Mean Acute Values. Of the ten freshwater genera for which mean
acute values are available, the most sensitive genus, Sal mo. is about 10
times more sensitive than the most resistant, Daohnia. The freshwater Final
Acute Value for 2.4,5-TCP was calculated to be 199.2 »g/L using the
procedure described in the Guidelines and the Genus Mean Acute Values in
Table 3. The Final Acute Value is lower than the lowest available Species
Mean Acute Value.
The stock of 2,4.5-TCP that was used in freshwater acute tests reported
b7 Sabourin et al. (1986) and Spehar (1986) w«, found to contain U.2 ng/g of
the contaminant, 2.3.7,8-tetrachlorodibenzo-p-dioxin (TCDD) (Durhan 1988).
This resulted in estimated 2.3.7,8-TCDD concentrations in the exposure water
as high as 115 pg/L (Table 1). it is not known if 2.3.7.8-TCDD
concentrations of 115 pf/L or less had an effect upon the observed toxicity.
Concentration, of 2.3.7.8-TCDD were not determined in the other freshwater
acute tests.
Tests of the tout* twicity of 2.4.5-TCP to resident North American
saltwater ammals hav, been performed with six species of invertebrates and
five species of fish (T.kle I). The range of acute values for invertebrates
extends fro. 492 MC/L for the amphipod. Rhepoxvnim tbron.ua (Battelle
Ocean Sciences 1987) to 3.830 Mg/L for adult mjaids. Mrsidonsi, hahji
(U.S. EPA 1978). The range of acute values for saltwater fish is narrower,
from 588 m/L for both juvenile English sole. Paroohvs vetulua. and adult
P»cific sand lance. Afliadj.tC-1 h«tDterus (Battelle Ocean Sciences 1987) to
-------
1.680 pc/L for both juvenile sheepshead minnows. Crprinod^ varier-.lt
(Heitrauller et al. 198 , and juvenile inland silversides, Mgnid^ .rynina
(Hughes and Pruell 1987).
The 24- and 98-hr LCSOs differed little with both mysids and sheepshead
minnows (Heitmuller et al. 1981; U.S. EPA 1978). In contrast, mortalities
continued throu«hout acute tests with polychaete worm,, urchiannelids. and
inland silversides (.Battelle Ocean Sciences 1987). Rao et al. (1981) found
that 2,4,5-TCP was about twice as toric to molting jrass shrimp as it was to
intermolt shrimp. The effect of environmental factors such as salinity and
temper ure on the acute toricity of 2.4,5-TCP to saltwater animals is not
known.
Of the ten fenera for which saltwater Genus Mean Acute Values are
available (Table 3). the most sensitive (enus, Rhea0Tvn,hlf is about 7 a
times sore sensitive than the most resistant, Mvsidomi. The six most
sensitive jenera are within a factor of 1.8 and include four invertebrates
and two fishes. The saltwater Final Acute Value for 2,4,5-TCP *., calculated
to be 472.9 »g/L. which is lower than the mean acute value for the most
sensitive tested saltwater species.
Chronic TotieitT ta A^q^tie ini..|g
Th« available data that are uieable accordinj to tht Guidelines con-
cerninc tht chronic toxicitf of 2.4,5-TCP are presented in Table 2. In a
seven-d»7 lif«-cjcl« tt»t with Ceriodaphni* dj^j^ tn 0rCtnis«s died at a
concentration of 1.480 Mf/L (Speh.r 1986). A concentration of 748 M|/L
did not cause •ortalitj. but sijnificantlj reduced production of 7ounc. A
concentration of 375 M€/L affected neither survival nor reproduction. The
resultinf chronic value was 528.9 /^/L and eh« acute-chronic ratio was
3.294 (Table 2).
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in a 90-day ear!7 nfe-3tage test with rainbow trout (Spehar 1986). a
concentration of 441 Mg/L caused im mortalit7 of 3wim_up ^^ ^
concentration of 208 Mg/L did not affect hatchability or swim-up larvae
but Signmcantly (P < 0.05) decreased surviva, of juveniles.
effects .ere observed at 108 Mg/L or below. The chronic vaiue and
acute-chronic ratio were 149.9 Mg/L and 1.734, respectively (Table 2).
Fathead minnow,, P^*^ prone I a,. eKposed to IQQ
adversely affected in an early life-,tafe test (Spehar 1986). Reduced growth
and approximately 50% mortality occurred at 342 M«/L. Complete mortality
was observed at 673 and 1.322 n/L. The chronic value wa, 233.9
and the acute-chronic ratio was 5.421 (Table 2)
The stock 2.4.5-TCP that wa, used in the freshwater chronic test,
reported by Spehar (1986) contained up to 14.2 Bf/f of 2.3.7. 8-TCDD (Durhan
1986). This resulted in estimated maximu. 3.3.7.8-TCDD concentration, in the
exposure water of 40.9 Pf/L |B th. ^^^ t-it§
trout test, and 18.8 Pf/L in the fathead minnow test. It i, not known at
present if 2.3.7.8-TCDD at these concentration, had any effect upon the
observed toxicitj.
The chronic toxicitj of 2,4.5-TCP ha, been «a,ured in salt water with
Che ini.nd silver.id.. M^d^ j^UJni (Hughe, and PrueU 1987). ,„ thl,
earl7 life-,t.f. t..t. M% of the e.br7o, expo.ed to 104 n/L died before
h*cchinf. SurTir.1 of both e.bryo, and fry „., reduced at 59.8 MI/L. but
no effect, „„ dtt.cted at 25.1 MC/L. The resultinj chronic value wa,
38.88 MC/L, tnd the acute-chronic ratio was 42.92 (Table 2).
The available Specie, M,ean Acute-Chronic Ratio, are 3.294. 5.421. and
1.734 in fresh water and 42.92 in s.U water (Table 3). The freshwater F.nal
Acute-Chronic Ratio of 3.140 wa, calculated a, the Ceo.etric mean of the
-------
three ratios. whereas 42.92 was used a, the saltwater Final Acute-Chronic
Ratio. Division of the freshwater and saltwater Final Acute Values by the
respective Final Acute-Chronic Ratios results in freshwater and saltwater
Final Chronic Values of 63.4* and 11.02 Mf/L, respectively. These Final
Chronic Values are lower than the lowest available respective chronic values
in fresh and salt water.
Toxicitv to Aquatic Planta
Two toxicity tests with exposure periods of four or more days have been
conducted on 2.4,5-TCP with aquatic plants (Table 4). An EC50, based on
reduction of chlorophyll a,, was 1.200 ng/L for the freshwater «reen alga.
?tUnmry(B glgMwnWllH (U.S. EPA 1978). The ECSO, based on reduction in
chlorophyll A. was 890 Mf/L for the saltwater diatoa, SJceletone»a
c.9?my.B. "berets the EC50 based on cell counts was 960 M|A (U.S. EPA
1978). These concentrations are abore the Final Acute Values for 2.4.5-TCP.
A Final Plant Value, a, defined in the Guidelines, cannot be obtained because
no test in which the concentrations of 2.4.5-TCP were .easured and the
endpoint wa, bioloficallj important has been conducted with an i-portant
aquatic plant species.
14
Bioaccuaulatjflfl
In a bio«w»centration test with the fathead .Innow, equilibrium of
C-labeitd f,4.5-TCP between water and fish occurred within 24 to 48 hr at
exposure concentrations of 4.8 and 49.3 Mf/L (Call et at. 1980). At the
hifher concentration, 78.8% of the radiolabel was associated with 2.4.5-TCP
at the end of the 28-day uptake phase. The BCF was 1.410 and the half-life
12 hr (Table 5).
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Inland silversides, Menidia beryl 1ina. that survived a 28-day early life-
stage toxicity test accumulated 2,4,5-TCP to concentrations between 47.2 and
71.3 times the concentration measured in test solutions (Table 5). Biocon-
centration factors for grass shrimp, Palaemonetea pugjo. exposed for one hour
to 14C-trichlorophenol were 13 for intermolt and 32 for new molt stages
(Table 6). Concentrations after 12 hours of exposure of intermolts were
highest in the digestive tract and hepatopancreas and lowest in the cephalo-
thorax and abdomen. Shrimp depurated 98% of accumulated 2,4.5-TCP in 24 hr
(Rao et al. 1981).
; No U.S. FDA action level or other maximum acceptable concentration in
tissue, as defined in the Guidelines, is available for 2,4,5-TCP. Therefore,
a Final Residue Value cannot be calculated.
Other Datt
Additional data on the lethal and sublethal effects of 2,4.5-TCP on
aquatic species are presented in Table 8. Exposures of an alga. Chlorella
Pmn9Jd.9?l. to 2,4.5-TCP for 3 days at concentrations from 1.000 to
10,000 Mg/L reduced chlorophyll by 12 to 1007. (Huang and Gloyna 1967.
1988). The 24-hr EC50 for the protozoan, Tetrahragn. prriformia. was
680 MI/L (Yoshiok* et al. 1985). A 24-hr exposure to 1.912 ng/L caused
100% aortalitj of ly»natid snails (Batte and Swanson 1952). A 24-hr EC50 of
2.080 fig/L was obtained with the cladoceran. Daphnit mtrn« (Devillers and
Chambon 1986). A 48-hr exposure of rainbow trout to 2.4,5-TCP at
1.000 MI/L resulted in 100% mortality (Shuaway and Palensky 1973). LC50s
of 900. 533. and 1.700 Mf/L were obtained at 24 hr with the brown trout.
guppy. and goldfish, respectively.
-------
Ribo and Kaiser (1983) reported a 30-min EC50 of 1.300 ng/L, based on
reduction in light production by the photoluminescent bacterium,
Phocabacterium phosphor-en^ (Table 6). Rao et al. (1981) found that exposure
to 500 and 750 Mg/L for 9 days inhibited limb regeneration by the grass
shrimp. Palaemonetea pugio. Limb regeneration was not affected in
100
Unused Data
Some data on the effects of 2.4,5-TCP on aquatic organisms were not used
because the tests were conducted with species that are not resident in North
America (e.g.. Hattori et al. 1984; Hosaka et al. 1984; Nagabhushanam and
Vaidya 1981). Kaiser et al. (1984), LeBlanc (1984). and Persson (1984)
compiled data froa other sources. Bringaann and Kuhn (1982) cultured
organisms in one water and conducted tests in another. Dojlido (1979) did
not specify which trichlorophenol was used. Blackaan et al. (1955a.b)
conducted tests at pH below 8.5.
Results were not used when th« test procedures were not adequately
described (Knie et al. 1983). Studies 07 Kobayashi et al. (1984) on the
sulfate conjugating enxjM systta and McKia et al. (1985) on the efficiency
of cheaical uptakt bj fish gills did not provide data pertinent to water
quality crittria.
Summary
The acute toxicitj of 2,4,5-trichlorophenol to freshwater aniaals ranged
froa 260 ^g/L for the rainbow trout to 2.660 Mg/L for Danhnia aatna.
The acu:e toxicitj of 2.4.5-TCP to the gupp/ increased as the pH of the water
decreased. Chronic toxicitf values for three freshwater species ranged from
-------
150 to 529 m/L, and the three acute-chronic ratios ranged from 1.734 to
5.421. A freshwater alga was affected at a concentration of 1.220 Mg/L.
A BCF of 1,410 was obtained with the fathead minnow.
Acute values for 2. 4.5-trichlorophenol are available for eleven saltwater
animal species in ten genera and range from 492 Mg/L for the amphipod.
Rhep°^niu3 *fr""iM?. to 3.830 Mg/L for the mysid, M^idon.,, bahia. The
six most sensitive species include three crustaceans, two fishes, and a
polychaete worm and their acute values are all within a factor of 1.8. The
only saltwater species with which a chronic test has been conducted is the
inland silverside, MgJlilU ber7}|ina. The chronic value is 38.68 Mf/L.
and the acute-chronic ratio is 42.92. The saltwater ditto..
- was «ffected by 890 ,,,/L. BCFs determined with the inland
silverside ranced from 47 to 71.
National
The procedures described in the "Guidelines for Deri*inC Numerical
National W.ter Quality Criteria for the Protection of Aquatic Organisms and
Their Use," indicate that, except possibly where t locally important specie,
is very sensitive, freshwater tquttic orftnis.s and their uses should not be
affected untccepttbiy if tht four-dty arerije concentrttion of 2.4.5-tri-
chlorophenol dots not tzcttd 63 Mf/L .ore Chtn once erery three yetrs on
the trertft and if tht ont-hour evertfe concentrttion does not exceed
100 ng/L mort thtn onet every three yetrs on the trertfe. Because
sensitive freshwater tni.tls appear to have a narrow ranfe of acute
susceptibilities to 2. 4. 5-tr ichlorophenol . this criterion will probably be as
protective as intended only when the mafnttudet and/or durations of
excursions are appropriately small.
-------
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important 3pecies
is very sensitive, saltwater aquatic organisms and their uses should not be
affected unacceptably if the four-day average concentration of
3.4.5-trichlorophenol does not exceed 11 Mg/L more than once every three
years on the average and if the one-hour average concentration does not
exceed 240 ng/L more than once every three years-on the average. Because
sensitive saltwater animals appear to have a narrow range of acute
susceptibilities to 2.4.5-trichlorophenol. this criterion will probably be as
protective as intended only when the magnitudes and/or durations of
excursions are appropriately small.
tmplementati op
As discussed in the Water Quality Standards Regulation (U.S. EPA I983a)
and the Foreword to this docuaent. a water quality criterion for aquatic life
has regulatory impact only after it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the
U.S. EPA, states designate one or .ore uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
I983b,1887). In each standard a state aay adopt the national criterion, if
one exists, or, if adequately justified, a site-specific criterion.
Site-specific criteria aay include not only site-specific criterion
concentrations (U.S. EPA 1983b). but also site-specific, and possibly
pollutant-specific, durations of averaging period, and frequencies of allowed
excursion, (U.S. EPA I985b). The averaging per.od, of "one hour" and four
10
-------
days" were selected by the U.S. EPA on the basis of data concerning how
rapidly some aquatic species react to increases in the concentrations of some
aquatic pollutants, and "three years" is the Agency's best scientific
judgment of the average amount of time aquatic ecosystems should be provided
between excursions (Stephan et al. 1985; U.S. EPA I985b). However, various
species and ecosystems react and recover at greatly differing rates.
Therefore, if adequate justification is provided, site-specific and/or
pollutant-specific concentrations, durations, and frequencies may be higher
or lower than those given in national water quality criteria for aquatic
life.
Use of criteria, which have been adopted in state water quality
standards, for developing water quality-based permit limits and for designing
waste treatment facilities requires selection of an appropriate wasteload
allocation model. Although dynamic model, are preferred for the application
of these criteria (U.S. EPA I985b). limited data or other consideration,
might require the use of a steady-state model (U.S. EPA 1986). Guidance on
mixing zone, and the design of monitorinc pro|ra., i, also available (U.S.
EPA 1985b,1987).
11
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