vvEPA
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA 440/5-84-028
January 1985
Water
Ambient
Water Quality
for
Cyanide -1984
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
CYANIDE
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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DISCLAIMER
This report has been reviewed by che Criceria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication. Mention of trade names or commercial
oroducts does not constitute endorsement or recommendation for use.
\VAILABILITY NOTICE
This document is available to che public through the National Technical
Information Service (NTIS) , 5285 Port Royal Road, Springfield, VA 22161.
UT1S fc^ce&s iGKj Melees- T8SS"- £27
1 L
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FOREWORD
Section 304(a)(l) of the Clean Water Ace of 1977 (P.L. 95-217) requires
che Administrator of the Environmental Protection Agency to publish criteria
for water quality accurately reflecting the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare which
may be expected from the presence of pollutants in any body of water,
including ground water. This document is a revision of proposed criteria
based upon a consideration of comments received from other Federal agencies,
State agencies, special interest groups, and individual scientists. The
criteria contained in this document replace any previously published EPA
aquatic life criteria.
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(l) and section 303(c)(2). The term has a different
program impact in each section. In section 304, the term represents a
non-regulatory, scientific assessment of ecological effects. The criteria
presented in this publication are such scientific assessments. Such water
quality criteria associated with specific stream uses when adopted as State
water quality standards under section 303 become enforceable maximum
acceptable levels of a pollutant in ambient waters. The water quality
criteria adopted in the State water quality standards could have the same
numerical limits as the criteria developed under section 304. However, in
many situations States may want to adjust water quality criteria developed
under section 304 to reflect local environmental conditions and human
exposure patterns before incorporation into water quality standards. It is
not until their adoption as part of the State water quality standards that
the criteria become regulatory.
Guidelines to assist the States in the modification of criteria
presented in this document, in the development of water quality standards,
and in other water-related programs of this Agency, have been developed by
EPA.
Edwin L. Johnson
Director
Office of Water Regulations and Standards
111
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ACKNOWLEDGMENTS
Sceven J. Broderius
(freshwacer author)
Environmental Research Laboratory
Duluth, Minnesota
John H. Gencile
(saltwater author)
Environmental Research Laboratory
Narragansett, Rhode Island
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluch, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support: Terry L. Highland
IV
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CONTENTS
Page
Foreword iii
Acknowledgmencs iv
Tables vi
Incroduccion 1
Acuce Toxicicy co Aquacic Animals ^
Chronic Toxicicy co Aquacic Animals . 6
Toxicicy co Aquacic Planes 7
Bioaccumulacion 7
Ocher Daca 8
Unused Daca 8
Summary 9
Nacional Criteria 10
References 40
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TABLES
Page
1. Acuce Toxicicy of Cyanide co Aquatic Animals 12
2. Chronic Toxicicy of Cyanide E.O Aquacic Animals 21
3. Ranked Genus Mean Acuce Values wich Species Mean Acuce-Chronic
Racios 23
4. Toxicicy of Cyanide co Aquacic Planes 26
5. Ocher Data on Effects of Cyanide on Aquacic Organisms 28
VI
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Incroduccion*
Compounds concaining che cyanide group (CN) are used and readily formed
in many industrial processes and can be found in a variecy of effluencs, such
as chose from che sceel, pecroleura, plascics, synchecic fibers, mecal
placing, mining, and chemical induscries. Cyanide occurs in water as hydro-
cyanic acid (HCN), che cyanide ion (CN~), simple cyanides, raecallocyanide
complexes, and as simple chain and complex ring organic compounds (Callahan,
ec al. 1979). "Free cyanide" is defined as che sura of che cyanide presenc as
HCN and as CN~, and che relacive concencracions of chese cwo forms depend
mainly on pH and ceraperacure. When pH is below 8 and ceraperacure is below 25
C, ac lease 94 percenc of che free cyanide exiscs as HCN. When pH or
cemperacure or boch are higher, a greacer percencage of free cyanide exiscs
as CN~. For example, when pH is 9 and cemperacure is 30 C, abouc 55
percenc of che free cyanide exiscs as HCN.
Alchough simple cyanides such as sodium cyanide and pocassium cyanide
readily dissociate and hydrolyze co form CN~ and HCN, che mecallocyanide
complex anions have a wide range of scabilicies. Zinc and cadmium cyanide
complexes dissociate rapidly and nearly completely in dilute solutions,
whereas che scabilicy of che copper and nickel raecallocyanide anions are
pH-dependenc. Cyanide complexes of iron dissociate very liccle, buc they are
subject to photolysis by natural light. Release of cyanide ion by phoco-
decomposicion might be important in relatively clear receiving waters.
*An understanding of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
(Stephan, et al. 1985), hereafter referred to as the Guidelines, is necessary
in order to understand che following text, cables, and calculations.
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The apparent coxicicy co aquacic organisms of raosc simple cyanides and
mecallocyanide complexes is due mainly co the presence of HCN derived from
dissociation, photodecoraposition, and hydrolysis (Doudoroff, ec al. 1966;
Smith, ec al. 1979), although CN~ is apparencly also toxic (Broderius, ec
al. 1977). Most mecallocyanide complexes are noc very toxic. The available
literature on the coxicicy of cyanides and related compounds to fish was
critically reviewed by Doudoroff (1976, 1980). Additional reviews on the
environmental effeccs of cyanides have been prepared by Leduc (1984), Leduc,
ec al. (1982), and Towill, ec al. (1978).
Because (a) both HCN and CN~ are coxic co aquacic life, (b) the vase
majoricy of free cyanide usually exiscs as che more coxic HCN, and (c) CN~
can be readily converced co HCN ac pK values chat commonly exisc in surface
wacers, cyanide criceria will be scaced in cerms of free cyanide expressed as
CN. Free cyanide is a much more reliable index of coxicicy co aquacic life
chan cocal cyanide because cocal cyanide can include nicriles (organic
cyanides) and relacively scable mecallocyanide complexes. In highly alkaline
wacers a criterion chat takes into accounc che relative coxicicies of HCN and
CN~ may be appropriace due co che dependence of che form of free cyanide on
pH.
If performed ofcen enough over a wide enough geographical area, measure-
ment of free cyanide (ASTM, 1984; Broderius, 1981) should be adequace for
monitoring cyanide in a body of water. However, because dissociacion of
several mecallocyanide complexes is very dependent on pH in the range chac
commonly occurs in many wacer bodies, a measuremenc such as (a) free cyanide
ac che lowesc pH occurring in che receiving wacer or (b) cyanide amenable co
chlorinacion or cocal cyanide (U.S. EPA, 1983a) is probably more appropriace
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if only a few measurements are made on a water body and whenever measurements
are made on an effluent. Dilution of an effluent with receiving water before
measuring cyanide should demonstrate whether the receiving water can decrease
the cyanide of concern because of sorption or complexation. Some
measurements of total cyanide in the receiving water or effluent or both are
desirable because if total cyanide is much higher than free cyanide or
cyanide amenable to chlorination, the importance of release of cyanide from
metallocyanide complexes by photolysis should receive consideration.
All cyanide concentrations reported herein are in terms of free cyanide
expressed as CN. Thus, data reported in the original literature in terras of
free cyanide expressed as CN did not have to be adjusted. However, when free
cyanide was expressed as HCN, KCN, etc., the results were adjusted using the
molecular weights of the compound and CN. When data were reported in the
original literature in terms of HCN, rather than in terms of free cyanide,
the data were converted from molecular HCN to free cyanide as CN as follows:
(ug of free cyanide as CN/L) =• Og of HCN/L) (1 * iQ^'P^CN ™>1. wc • <*
m O I . Wt .
where pKHCN - 1.3440 + T"T~TTTTb (Izacc, et al . 1962)
and T * degrees Celsius. The criteria presented herein supersede previous
aquatic life water quality criteria for cyanide (U.S. EPA, 1976, 1980)
because these new criteria were derived using improved procedures and
additional information. Whenever adequately justified, a national criterion
may be replaced by a site-specific criterion (U.S. EPA, 1983b), which may
include not only site-specific criterion concentrations (U.S. EPA, 1983c) ,
but also site-specific durations of averaging periods and site-specific
frequencies of allowed exceedences (U.S. EPA, 1985). The latest literature
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search for informacion for chis documenc was conducced in May, 1984; some
newer informacion was also used.
Acuce Toxicicy to Aquatic Animals
Mosc of che invercebrace species cesced were considerably more resiscanc
chan fishes, buc Daphnia sp. and Gammarus pseudolimnaeus were comparable co
fishes in sensicivicy. On che ocher hand, abouc half of che cescs wich
invercebrace species were scacic and che cesc concencracions were noc
measured, whereas many of che cescs wich fish were flow-chrough cescs in
which free cyanide concencracions were measured (Table 1).
Cercain life scages and species of fish appear co be more sensicive co
cyanide chan ochers. Embryos, sac fry, and warrawacer species cended co be
che most resiscanc. Free cyanide concencracions from abouc 50 co 200 ug/L
evencually were facal co juveniles of mosc of che more sensicive fish
species, wich concencracions much above 200 Jg/L being rapidly facal co mosc
juvenile fish. Thus, chere is a relacively narrow range of species
sensicivicy for fish. A comparison of acute coxicicy values for fishes
(Table 1) supporcs che conclusion (Doudoroff, 1976) chac resulcs of scacic
coxicicy cescs cend co be somewhac higher chan resulcs of renewal or
flowchrough cescs of equal, fairly prolonged duracion.
The coxicicy of cyanide increases wich reduccion in dissolved oxygen
below che sacuracion level (Doudoroff, 1976; Sraich, ec al. 1978) and che
resiscances of fishes co cyanide solucions chac are rapidly lechal decreases
wich an increase in cemperacure. Long-cera lechalicy cescs, however, have
de^ionscraced chac juvenile fishes are more sensicive co cyanide wich a
reduccion in ceraperacure (Doudoroff, 1980; Leduc, ec ai. 1982; Smich, ec al.
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1978). No pronounced relacionship has been observed between che acute toxic-
icy of cyanide to fishes and alkalinity, hardness, or pH below about 8.3.
Genus Mean Acute Values (Table 3) were calculated as the geometric -neans
of the available Species Mean Acuce Values (Table 1). Dara are available for
more than one species in cwo genera and che Species Mean Acute Values in. each
are within a factor of 2, Of che 15 genera che most sensitive, S a liao, is 39
times more sensitive than the most resistant, Tanycarsus (Table 3). A
freshwater Final Acute Value of 62.68 yg/L was calculated from the Genus Mean
Acute Values using the calculation procedure described in che Guidelines.
However, che Species Mean Acuce Value for the important rainbow trout is
44.73 Jg/L. Because this value is based on the results of flow-through tests
in which the concencrations were measured, it replaces the calculated
freshwater Final Acute Value (Table 3). At low temperatures acute effects on
rainbow trout have been observed (Kovacs, 1979; Kovacs and Leduc, 1982b) at
concentrations below the Final Acute Value (Table 1).
Data are available on the acute coxicicy of cyanide to saltwater species
in three fish genera and five invertebrate genera (Tables 1 and 3). Species
Mean Acuce Values for invertebrates ranged from 4.893 Jg/L for larvae of che
rock crab, Cancer irroracus, to over 10,000 Jg/L for larvae of che common
Atlantic slippershell, Crepidula fornicaca. £. irroracus is six times more
sensitive to cyanide than che nexc most sensitive species, the calanoid
copepod, Acartia consa. Acuce values for fishes only ranged from 59 jJg/L to
372 'Jg/L. Only the genus Mysidopsis contained more than one species and che
Species Mean Acuce Values were within a faccor of 1.1. The salcwacer Final
Acute Value calculated from che Genus Mean Acute Values in Table 3 is 2.030
Mg/L, which is approximately one-half che Species Mean Acuce Value of the
most sensitive of che nine species for which acute values are available.
5
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Chronic Toxicicy co Aquaeic Animals
The long-term survival and growth of various freshwater fish species
were observed co be substantially reduced at free cyanide concentrations of
about 20 to 50 Jg/L (Tables 2 and 5). Based on reduced long-term survival in
an early life-stage test with the bluegill, and reduced reproduction by the
brook trout and fathead minnow in a partial life-cycle and life-cycle test,
the chronic values were 13.57, 7.849, and 16.39 ^g/L, respectively. Life-
cycle tests (Table 2) have been conducted with two freshwater invertebrates.
The chronic values were 34.06 ;jg/L for the isopod, Asellus communis, and
18.33 kJg/L for the amphipod, Gatmnarus pseudolimnaeus.
Four of the freshwater acute-chronic ratios are between 7 and 11,
whereas the one for the resistant isopod is 68.29 (Tables 2 and 3). It seems
reasonable to use the geometric mean of the four as the freshwater Final
Acute-Chronic Ratio. Division of the Final Acute Value by the Final Acute-
Chronic Ratio results in a freshwater Final Chronic Value of 5.221 ,Jg/L
(Table 3).
Data are available on the chronic toxicity of cyanide to the saltwater
fish, Cyprinodon variegatus, and the raysid, Mysidopsis bahia (Table 2). The
early life-stage test with the sheepshead minnow, C_. variegatus, showed chat
growth was not significantly reduced at a cyanide concentration of 462 Jg/L.
Survival, however, was significantly reduced at cyanide concentrations >45
iJg/L but not at
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The cwo acute-chronic racios available from cescs wich salcwacer species
are 8.306 and 1.621 (Table 3), hue both of these species are relatively
resistant co cyanide and the acute values in those ratios were obtained with
juveniles of the fish and raysid. On the other hand, the acute value for the
sensitive rock crab was obtained using larvae of that species. Thus, this
acute value for the rock crab is probably a better indication of the chronic
sensitivity of this species than would be obtained by dividing this acute
value by an acute-chronic ratio. Therefore, it seems reasonable to set the
saltwater Final Chronic Value equal to the Criterion Maximum Concentration of
1.015 ug/L (Table 3). Division of the geometric mean of the two saltwater
acute-chronic ratios into the Species Mean Acute Values of all saltwater
species except the rock crab results in values that are at least 1.6 times
greater than this Final Chronic Value.
Toxicity to Aquatic Plants
Data on the toxicity of free cyanide to freshwater and saltwater plant
species are presented in Table 4. Both freshwater and saltwater plants show
a wide range of sensitivities to cyanide, and the saltwater red macroalga,
Champia parvula, is extremely sensitive to cyanide poisoning with growth and
reproductive effects occurring at 11 to 25 ug/L. Adverse effects of cyanide
on plants are unlikely, however, at concentrations which do not cause chronic
effects on most freshwater and saltwater animal species.
Bioaccumulation
No studies have been reported showing a biomagnification of cyanide in
the food chain (Towill, et al. 1978). Pennington, et al. (1982) found no
detectable levels of cyanide in four species of fish from a Mississippi lake.
7
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Murachi, et al. (1978) and Holden and Marsden (1964) measured che
concencracion of cyanide in various cissues of fish exposed co very rapidly
lechal cyanide levels. It is obvious from such experiraencs chat cyanide does
penecrace aquatic organisms buc bioaccumulacion cannot be demonstrated
because it is readily metabolized.
Other Data
Embryos of the fathead minnow are possibly slightly less sensitive to
cyanide than fry and juveniles, whereas embryos of yellow perch are about as
sensitive as fry, but less sensitive than juveniles (Tables 1 and 5)
(Broderius, et al. 1977; Smith, et al. 1978). Several authors (Broderius,
1970; Dixon and Leduc, 1981; Kovacs, 1979; Kovacs and Leduc, 1982a; Leduc,
1977, 1978; Leduc and Chan, 1975; Lesniak, 1977; McCracken and Leduc, 1980;
Neil, 1957; Oseid and Siith, 1979; Ruby, et al. 1979) reported adverse
effects due to cyanide concentrations as low as 10 Jg/L. In another study,
Kimball, et al. (1978) reported that no reproduction occurred among adult
bluegills when exposed for 289 days to the lowest concentration tested (5.2
'jg of HCN/L » 5.4 'jg of free cyanide as CN/L). During this period, however,
only a total of 13 spawnings occurred in two controls and no concentration-
effect relationship was observed. Because of reservations regarding the
spawning data, the chronic value for the bluegill was based on long-term fry
survival. On the other hand, the most sensitive adverse effect of cyanide on
both the fathead minnow and brook trout was reduced reproduction.
Unused Data
Some data on the effects of cyanide on aquatic organisms were not used
because the studies were conducted with species that are not resident in
8
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North America (Abram, 1964; Brockway, 1963; Costa, 1966; Lorate and Jadhav,
1982; Woker and Wuhrmann, 1950). Daca were noc used if cyanide was a
componenc of a complex cyanide (Doudoroff, 1976) or an effluent (Lloyd and
Jordan, 1964; Shelford, 1917).
Some data were noc used because che results were only presented
graphically (Downing, 1954; Renn, 1955; Smith and Heath, 1979). Studies
conducted using inadequate dilution water (Jones, 1941) or without controls
(Bridges, 1958; Costa, 1965a,b,c) were also not used. Bringraann and Kuhn
(1982) cultured Daphnia magna in one water but conducted tests in another
water. Data in some papers were not used because either the test conditions
were not clearly stated (Burdick and Lipschuecz, 1950; Ishio, 1965; Lewis and
Tarrant, 1960; Whittingham, 1952) or che cest procedures were considered
inadequate (Lund, 1918; Moore and Kin, 1968; Suimnerfelt and Lewis, 1967;
Washburn, 1948). The 96-hr values reported by Buikema, et al. (1977) were
subject to error because of possible reproductive interactions.
Summary
Data on the acuce toxicity of free cyanide (the sum of cyanide present
as HCN and CN~, expressed as CN) are available for a wide variety of
freshwater species that are involved in diverse community functions. The
acute sensitivities ranged from 44.73 ug/L to 2,490 ug/L, but all of the
species with acute sensitivities above 400 [Jg/L were invertebraces. A
long-terra survival, and a partial and life-cycle test with fish gave chronic
values of 13.57, 7.849, and 16.39 Jg/L, respectively. Chronic values for two
freshwater invertebrate species were 18.33 and 34.06 ug/L. Freshwater plants
were affected at cyanide concentrations ranging from 30 ug/L to 26,000
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The acuce coxicicy of free cyanide to salcwacer species ranged from
4.893 ug/L co >10,000 ug/L and invertebrates were both the raosc and lease
sensitive species. Long-term survival in an early life-stage cesc wich the
sheepshead minnow gave a chronic value of 36.12 yg/L. Long-term survival in
a raysid life-cycle test resulted in a chronic value of 69.71 ^g/L. Tests
with the red raacroalga, Champia parvula, showed cyanide toxicity at 11 to 25
Jg/L, but other species were affected at concentrations up to 3,000 ;jg/L.
National Criteria
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 oossibly where a locally important species
is very sensitive, freshwater aquatic organisms and their uses should not be
affected unacceptably if the four-day average concentration of cyanide does
not exceed 5.2 Jg/L more than once every three years on the average and if
the one-hour average concentration does not exceed 22 jg/L more chan once
every three years on the average.
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 species
is very sensitive, saltwater aquatic organisms and their uses should not be
affected unacceptably if the one-hoar average concentration of cyanide does
not exceed 1.0 ^Jg/L more than once every three years on the average.
EPA believes that a measurement such as free cyanide would provide a
more scientifically correct basis upon which to establish criteria for
cyanide. The criteria were developed on this basis. However, at this time,
no EPA approved methods for such a measurement are available to implement the
10
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criteria through che regulatory programs of the Agency and che States. The
Agency is considering development and approval of methods for a measurement
such as free cyanide. Until available, however, EPA recommends applying che
criteria using the total cyanide method. These criteria may be overly
protective when based on the total cyanide method.
The recommended exceedence frequency of three years is the Agency's best
scientific judgment of the average amount of time it will take an unstressed
system to recover from a pollution event in which exposure to cyanide exceeds
che criterion. Stressed systems, for example, one in which several outfalls
occur in a limited area, would be expected to require more time for recovery.
The resilience of ecosysceras and their ability to recover differ greatly,
however, and site-specific criteria may be established if adequate
justification is provided.
The use of criteria in designing wasce treatment facilities requires che
selection of an appropriate wasteload allocation model. Dynamic models are
preferred for che application of these criteria. Limited data or ocher
factors may make their use impractical, in which case one should rely on a
sceady-state model. The Agency recommends che interim use of 1Q5 or 1QIO for
Criterion Maximum Concentration (CMC) design flow and 7Q5 or 7Q10 for che
Cricerion Concinuous Concentration (CCC) design flow in sceady-scace models
for unstressed and stressed systems respectively. These matters are
discussed in more detail in the Technical Support Document for Wacer
Quality-Based Toxics Control (U.S. EPA, 1985).
11
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Table 1. Acute Toxic Ity of Cyanide to Aquatic Anl««ls
Species
Method*
LC50 Species Mean
or EC5O Acute Value
" (»ig/L)-*
FRESHWATER SPECIES
Sna 1 1 ,
Physa heterostropna
Cladoceran,
Oaphnla magna
Cladoceran,
Oaphnla magna
Cladoceran,
Daphnla put ex
Cladoceran,
Daphnla pulex
1 sopod ,
Aselfus common 1 s
Amph 1 pod ,
Garwuarus pseudol Imnaeos
Stonetly,
Pteronarcys dorsata
Midqe,
Tanytarsus dlsslmllis
Rainbow trout ( try).
Sal no qalrdner 1
Rainbow trout (juvenile).
Sal mo qalrdnerl
Rainbow trout (juvenile).
Sal mo qalrdnerl
Rainbow trout (juvenile),
Salmo go Ir drier 1
Rainbow trout (juvenile).
S, U
s, u
s. u
s, u
S, M
FT, M
FT, M
FT, M
S. M
s, u
S. U
S, U
S, U
S, II
432 432
< 1.800
160 160
83
110 95.55
2,326 2,326
167 167
426 426
2,490 2,490
90
97
46.3
Vt.l
S a I cno qalrdner I
Reference
Cairns 4 Scheler, 1958;
Patrick, et at . 1968
Anderson, 1946
Dowden & Bennett,
1965
Lee, 1976
Cairns, et al . 1978
Oseld & Smith, 1979
Osetd & Smith, 1979
Cal 1 & Brooke, 1962
Cal 1, et al. 1983
Bll Is. et al. 1977
Sklbbd, 198)
Marking, et al . 1984
Marking, et al . 1984
Marking, et al . 1984
12
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Table I. (Continued)
Species Method*
Rainbow trout (juvenile), S. U
Sat mo gal rdner I
Rainbow trout (juvenile), S, U
SaliBo gal rdner I
Rainbow trout (juvenile). fT, M
Sat mo ga I rdner I
Rainbow trout (juvenile), FT, M
Saiino go i rdner i
Rainbow trout ( juvenile), FT, M
Sal mo gal rdner I
Rainbow trout (juvenile). FT, M
Sal mo gal rdner I
Atlantic salmon (Juvenile), R, M
Salmo sal or
Brook trout (sac fry), FT, M
Sat veil ntis fontlnalls
Brook trout (sac fry), FT, M
Snivel Inns fontlnalls
Brook trout (sac fry), FT. M
Snlvellnus fontlnalls
Brook trout (sac fry), FT, M
Salvel Inus fontlnalls
Brook trout (swim-up fry), FT. M
Salvel Inus fontlnalls
Brook trout (swim-up fry), FT, M
Salvel Inus fontlnalls
Brook trout (swim-up fry), FT, M
Salvel Inus fontlnalls
LC50
or EC50
Species Mean
Acute Value
(M9/l)*«
62.1
74.8
57
27
40
65
90
105""
342»*»
507 »*»
84
54.4
86.5
44.73
90
Reference
Marking, et al. 1984
Marking, et al . 1984
Smith, et al. 1978;
Broderlus & Smith, 1979
Kovacs, 1979; Kovacs &
Leduc. iS82b
Kovacs, 1979; Kovacs &
Leduc, I982b
Kovacs, 1979; Kovacs 4
Leduc. 19826
Try I and and Grande,
1983
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
13
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Table I. (Continued)
LC50
or EC50
Species Method* (tig/D"
Brook trout (swim-up fry), FT, M 104
Salvellnus fontlnalls
Brook trout (swim-up fry), FT, M 90.3
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 73.5
Salvellnus fontlnalls
Brook trout (Juvenile), FT, M 83
Salvellnus fontlnalls
Brook trout (Juvenile), FT, M 75
Salvellnus fontlnalls
Brook trout (Juvenile), FT, M 86.4
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 91.9
Salvellnus fontlnalls
Brook trout (Juvenile), FT, M 99
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 96.7
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 112
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 52
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 60.2
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 66.8
Salvellnus fontlnalls
Brook trout (juvenile), FT, M 71.4
Salvellnus fontlnalls
Species Mean
Acute Value
Reference
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
14
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Table 1. (Continued)
Species
Brook trout (juvenile),
Salvellnus fontlnalls
Brook trout ( J uven He),
Salvellnus fontlnalls
Brook trout (adult) ,
Salvellnus fontlnalls
Goldfish (juvenile) .
Car ass 1 us auratus
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow (fry),
Plmephales promelas
Fathead minnow (fry),
Plmephales promelas
Fathead minnow (fry),
Plmephales promelas
Fathead minnow (fry),
Plmephales promelas
Fathead minnow (fry),
Plmaphales promelas
Fathead minnow (juvenile),
P 1 mepha 1 es promelas
Fathead minnow (juvenile).
Method*
FT.
fT.
FT,
FT,
s.
s.
s.
FT,
FT,
FT,
FT,
FT,
FT,
FT,
M
M
M
M
U
M
M
M
M
M
M
M
M
M
LC50
or EC50
(trg/L)**
97
143
136
518
230
350
230
120
98.7
81.8
no
116
119
126
Species Mean
Acute Value
lug/I)** Reference
Smith, et
Smith, et
83.80 Car dwell,
1976
318 Cardwell,
1976
Doudoroff,
Henderson,
1961
Henderson,
»96I
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
et
et
et
et
et
et
et
at. 1978
al. 1978
et al.
et al .
1956
et
et
al.
al.
at.
al .
al .
al.
al.
al.
al.
1978
1978
1978
1978
1978
1978
1978
Plmephales promelas
15
-------
Table 1. (Continued)
Species
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
P 1 mepha 1 es prome 1 as
Fathead minnow (juvenile),
PI mepha les promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile).
Method*
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT.
H
H
H
H
M
M
H
M
M
H
M
M
M
M
LC50 Specie* Mean
or EC5O Acute Value
163
169
120
Reference
Smith,
et
Smith, et
Broder lus
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
Smith,
et
et
et
et
et
et
et
et
et
et
et
Broder lus.
al.
1978
al. 1978;
& Smith, 1979
al.
af .
al.
al.
al.
al.
al.
al.
al.
al.
al.
et
1978
1978
1978
1978
1978
1978
1978
1978
1978
1978
1978
al.
P1mephales promelas
1977
16
-------
Table I. (Continued)
Species
Fathead minnow (juvenile).
Plmephales promelas
Fathead minnow (juv,. >le).
Plmephales promelas
Fathead minnow (Juvenile),
Plmephales promelas
Guppy (adult) ,
Poecllla retlculata
Blueqlll (juvenile),
Lepomls macrochlrus
Blueqlll,
Lepomls macrochlrus
Blueqlll,
Lepomls macrochlrus
Blueqlll,
Lepomts macrochlrus
Blueqlll (juvenile),
Lepomls macrochlrus
Blueqlll (juvenile).
Lepomls macrochlrus
Blueqlll (fry).
Lepomls macrochlrus
Blueqlll (fry),
Lepomls macrochlrus
Blueqlll (fry),
Lepomls macrochlrus
Blueqlll (fry).
LC50 Species Mean
or EC50 Acute Value
Method* (nq/L)** (wg/L)**
FT,
FT,
FT,
FT,
s.
s,
s,
s,
s.
s,
FT.
FT.
FT,
FT.
H
H
M
M
U
M
M
M
M
M
M
M
H
M
113
128
128 125.1
147 147
180
220
180
230
150
160
364"«
232««»
279«»»
27i»*«
Reference
Broderlus. et al .
1977
Broderlus, et al .
1977
Broderlus, et al .
1977
Anderson & Weber,
1975
Cairns S, Scheler, 1958,
1968; Patrick, et al.
1968
Cairns & Scheler,
1959
Cairns & Scheler,
1959
Cairns & Scheler,
1959
Henderson, et al .
1961
Cairns 4 Scheler,
1963
Smith, et al . 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
Lepomls macrochlrus
17
-------
Table I. (Continued)
Method"
Blueqlll (juvenile), FT, M
Lapomls macrochlrus
Blueqlll (Juvenile), FT. M
Lopomls macrochjrus
Blueqlll (juvenile), FT, M
Lepomls macrochlrus
Blueqlll (juvenile), FT, M
Lepomls macrochlrus
Blueqlll (juvenile), FT, M
Lapomls macrochlrus
Blueglll (juvenile), FT, M
Lepomls macrochlrus
Blueqlll (juvenile), FT, M
Lepomls macrochlrus
Blueqlll (juvenile), FT, M
Lepomls macrochlrus
Blueqlll (juvenile) , FT, M
Lepomls macrochlrus
Larqeroouth bass FT, M
(juvenile),
Mtcropterus sal moIdes
Black crapple, FT, M
Pomoxls nlqromaculatus
Yellow perch (embryo), FT, M
Perca fjavescans
Yellow parch (fry), FT, M
Perca flavescens
Yellow oerch (try), FT, M
Perca flavescens
LC50
or EC50
(pg/L)**
85.7
74
100
107
99
113
121
126
102
102
Sp«cl«s Mean
Acute Valu*
(Mg/L)«*
99.28
102
102
530««"
Smith, at al. 1978
Smith, et at. 1976
Smith, et al. 1978
Smith, et al. 1978
Smith, et al. 1978
Smith, et al . 1978
Smith, et al. 197B
Smith, et a». 1978
Smith, et al. 1978
Smith, at al. 1979
Smith, et al. 1979
Smith, et al. 1978
Smith, et al. 1978
Smith, et at . 1978
18
-------
Table 1. (Continued)
Species
Yellow perch (juvenile),
Perca flavescens
Yellow perch (juvenile),
Perca flavescens
Yellow perch (juvenile),
Perca flavescens
Yellow perch (juvenile),
Perca flavescens
Yellow perch (juvenile),
Perca flavescens
Yellow perch (juvenile),
Perca flavescens
Common Atlantic
si Ippershel 1 ,
Crepldula fornlcata
Copepod ,
Acartla clausl
Mysld,
Mysldopsls bah la
Mysld,
Mysldopsls bah la
Mysld,
Mysldopsls blgelowl
Amphlpod,
Ampellsca abdlta
Amphl pod,
Ampel Isca abdlta
Method*
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
S, U
S, U
S, U
FT, M
S, U
S. U
S, U
LC50 Species Mean
or EC50 Acute Value
(ng/L)" (Mq/L>"»
88.9
93
74.7
94.7
101
107 92.64
SALTWATER SPECIES
>10,000 >10,000
30 30
93
113 113
124 124
1,220
1,150
Reference
Smith, et al . 1978
Smith, et al . 1978
Smith, et al . 1978
Smith, et al . 1978
Smith, et al . 1978
Smith, et al . 1978
Gardner & Nelson,
1981
Gentile, 1980
Gentile, 1980
Lussler, et al .
Manuscript
Gentile, 1980
Scott, et al .
Manuscript
Scott, et al .
Manuscript
19
-------
Table t. (Continued)
LC50
or EC50
Species Method* ( wq/L ) " "
Amphlpod, S, U 704
Ampel Isca abdlta
Rock crab (larva), FT, M 4.2
Cancer Irroratus
Rock crab (larva), FT, M 5.7
Cancer Irroratus
Sheepshead minnow, FT, M 300
Cyprlnodon varleqatus
Atlantic sllverslde, FT, M 59
Menldla menldla
Winter flounder, S, U 372
Pseudop 1 euronectes
amerlcanus
Species Mean
Acute Value
(ii
-------
Table 2. Chronic Toxlclty of Cyan Ida to Aquatic Animals
Species
Isopod,
Asellus common Is
AmphI pod,
Gammarus pseudolImnaeus
Brook trout,
SaIva11nus font Ina11s
Fathead minnow,
Plmephales promelas
BIueqIII,
Lepomls macrochlrus
Test*
LC
LC
LC
LC 13.3-20.2
ELS 9.3-19.8
Limits Chronic Value
(>ig/L)** Reference
34.06 Oseld A Smith, 1979
18.33 Oseld & Smith, 1979
7.849 Koenst, et al . 1977
16.39 Llnd, et al . 1977
13.57 Klmball, et al . 1978
FRESHWATER SPECIES
29-40
16-21
5.6-11.0
Mysld,
Hysldopsls bah Ia
Sheepshead minnow,
Cyprlnodon varlegatus
SALTWATER SPECIES
LC 43-113
ELS 29-45
69.71 Lussler, et al.
Manuscript
36.12 Schlmmel, et al. 1981
* LC = 11fe cycle or partial life cycle; ELS = early life staqe.
"Results are expressed as free cyanide as CM.
Acute-Chronic Ratio
Species
Isopod,
Asellus communls
Amph I pod,
Gammarus pseudolImnaeus
Acute Value
(Mg/L)
2,326
167
Chronic Value
(»g/L) Ratio
34.06
18.33
68.29
9.111
21
-------
Table 2. (Continued)
Acute-Chronic Ratio
Acute Value Chronic Value
Species (ng/l) (»g/l) Ratio
Brook trout,
Salvel Inus fontlnalls
Fathead minnow,
Plmephales prometas
B 1 ueq 1 1 1 ,
Lepomls macrochlrus
Mysld,
Mysldopsls bah la
Sheepshead minnow,
Cypr Inodon var legatus
83.14"* 7.849
125.l""» 16.39
99 28 ***•• 1357
113 69.71
300 36.12
10.59
7.633
7.316
1.621
8.306
»»• Geometric mean of 19 values from Smith, et al. (1978) In
Table t.
••»* Geometric mean of 24 values from Smith, et al. (1978) and
Broderlus, et al. (1977) In Table 1.
»••"» Geometric mean of 9 values from Smith, et al. (1978) In
Table 1.
22
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
tank*
15
14
13
12
11
10
9
8
7
6
5
4
Genus Mean
Acute Value
(pg/L)
2.490
2,526
432
426
318
167
147
125.1
123.6
102
102
99.28
Species Mean Species Mean
Acute Value Acute-Chronic
Species (ug/L) Ratio
FRESHWATER SPECIES
Midge,
Tanytarsus dlsslmllls
Isopod,
Asellus communls
Sna 1 1 ,
Physa heterostropha
Stonef ly,
Pteronarcys dorsata
Goldfish,
Carasslus auratus
Amph 1 pod ,
Gammarus pseudol Imnaeus
Guppy,
Poecl lla reticulata
Fathead minnow,
Pltnephales promelas
Cladoceran,
Daphnla roaqna
Cladoceran,
Daphnla pulex
Larqemouth bass,
Mlcropterus sal mo Ides
Black crapple,
Pomoxls nlgromaculatus
Blueqll 1,
2.490
2,326 68.29
432
426
318
167 9.111
147
125.1 7.633
160
95.55
102
102
99.28 7.316
Lepoinl s macrochlrus
23
-------
Tabl* 3. (ContlniMd)
Rank*
3
2
1
8
7
6
5
4
3
2
1
Genus Mean
Acute Value
(pq/D Species
92.64 Ye 1 low perch,
Perca flavescens
85.80 Brook trout,
Salve) Inus fontlnalis
63.45 Rainbow trout,
Sal mo galrdnerl
Atlantic salmon,
Sal mo salar
SALTWATER SPECIES
>IO,OOO Common Atlantic
si Ippershe) 1 ,
Crap 1 dula fornlcata
995.9 Anphlpod,
Ampelfsca abdlta
372 Winter flounder,
Pseudpp 1 euronectas
amer Icanus
300 Sheepshead minnow,
Cyprlnodon varlegatus
118.4 Mysld,
Mysldopsls bah la
Mysld,
Mysldopsls blgelowl
59 Atlantic sllverslde,
Menldla menldla
50 Cope pod,
Acartla clausi
4.89J Rock crab.
Species Mean
Acute Value
92.64
85.80
44.73
90.00
>10,000
995.9
372
300
113
124
59
30
4.893
Species Mean
Acute-Chronic
Ratio
10.59
8.306
1.621
Cancer Irroratus
24
-------
Table 3. (Continued)
* Ranked fron most resistant to most sensitive based on Genus Mean Acute Value.
Fresh water
Final Acute Value = 62.68 vq/L (calculated fron Genus Maan Acute Values)
Final Acute Value = 44.73 pg/L (lowered to protect rainbow trout - see text)
Criterion Maximum Concentration = (44.73 uq/L) /2 = 22.36 ng/L
Final Acute-Chronic Ratio' 8.568 (see text)
Final Chronic Value = (44.73 Mq/L) / 8.568 = 5.221 Mg/L
Salt water
Final Acute Value * 2.030 uq/L
Criterion Maximum Concentration = (2.030 ng/L) 12 = 1.015 n9/L
Final Chronic Value = 1.015 Pg/L (see text)
25
-------
Table 4. Toxic Ity of Cyanide to Aquatic Plants
Species
Blue-green alqa,
Hlcrocystls aeruglnosa
Blue alqa,
M 1 crocyst 1 s aerug 1 nosa
Green alga,
Scenedesmus quadrlcauda
Diatom,
Navlcula semi nu turn
Volvocales,
Chlamydomones sp.
Duckweed,
Lemna glbba G3
Eurasian waterml 1 fol 1 ,
Hyrlophyl turn sp lea turn
Green alga,
Prototheca zoptl
Green alga,
Chloral la sp.
Red alga,
Champ la parvula
Red alqa,
Champ la parvula
Red alqa.
Champ la parvula
Effect
FRESHWATER SPECIES
90« KIM
Incipient
Inhibition
Incipient
Inhibition
50K reduction In
dlvl slon
No effect on mean
or maximum growth
rate
Decreased
potassium uptake
32-day EC50
(root weight)
SALTWATER SPECIES
Resplrat Ion
Inhibition
Enzyme Inhibition
Reduced tetrasporo-
phyte growth
Reduced tetraspor-
anqla production
Reduced female
growth
Result
li»g A)*
8,000
75
30
277-491
10-100
26,000
22,400
3,000
30,000
16
25
n
Refer MIC*
Fitzgerald, et al .
1952
Brlngmann, 1975;
Brlngmann 1 Kuhn,
1976, I978a,b
Brlngmann & Kuhn,
I977a, 1978a,b,
1979, I980b
Academy of Natura 1
Sciences, I960
Cairns, et al. 1978
Kondo & Tsudzukl ,
1980
Stanley, 1974
Webster & Hackett,
1965
Nelson & Tolbert,
1970
Steel e & Thursby,
1983
Steele & Thursby,
1983
Steele & Thursby,
1983
26
-------
Table 4. (Continued)
Result
Species Effect (ng/U* Reference
Red alga. Stopped sexual II Steele & Thursby,
Champ I a parvula reproduction 1983
* Results are expressed as free cyanide as CN.
27
-------
Table 5. Other Data on Effects of Cyanide on Aquatic Organises
Species
Result
(iig/L)* Reference
Green alga,
Scenedesmus quadrlcauda
Bacteria,
Escherlchla col 1
Bacteria,
Pseudomonas putlda
Protozoan,
Entoslphon sulcatum
Protozoan,
Mlcroregma heterostoma
Protozoan,
Ch 1 1 omonas paramec 1 urn
Protozoan,
Uronama parduazl
Rotifer,
Phllodlna acutlcornls
Worm,
A eo 1 osoma head 1 ey 1
Snail,
Gon 1 obas Is II vescens
Snail,
Nltocrls sp.
FRESHWATER SPECIES
96 hr Incipient
Inhibition
Incipient
Inhibition
16 hrs Incipient
Inhibition
72 hrs Incipient
Inhibition
28 hrs Incipient
Inhibition
48 hrs Incipient
Inhibition
20 hrs Incipient
Inhibition
48 hrs LC50
48 hrs LC50 ( 5 C)
(10 C)
(15 C)
(20 C)
(25 C)
48 hrs LC50
48 hrs LC50 ( 5 C)
(10 C)
(15 C)
(20 C)
(25 C)
160"
400-800
1
1,800
40
1,200
270
20 ,000-
145,000
10,000
9,000
120,000
160,000
160,000
760 ,000
13,600
12,800
10,000
8,000
7,000
Br Ingmann & Kuhn,
I959a,b
Br Ingmann & Kuhn ,
1959a
Br Ingmann & Kuhn, 1976,
I977a, 1979, I980b
Br Ingmann, 1978;
Br Ingmann & Kuhn, 1979,
19806, 1981
Br Ingmann & Kuhn, 1959b
Br Ingmann, et al . 1980,
1981
Br Ingmann 1 Kuhn, |980a,
1981
Cairns, et al . 1978
Cairns, et al. 1978
Cairns, et al . 1976
Cairns, et al . 1978
28
-------
Table 5. (Continued)
Species
Snail,
Lymnaea emarglnata
Snail (embryo).
Lymnaea sp.
Snail,
Physa heterostropha
Snail ,
Physa Inteqra
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla luaqna
Cladoceran,
Oaphnla pulex
Amphlpod,
Gammarus pseudol Imnaeus
Mayfly,
Stertonen»a rubrum
Caddlsf ly ( larva) ,
Hydropsyche sp.
Mldqe,
Tanytarsus dlsslmllls
Coho salmon.
Oncorhynchus klsutch
Duration
46 hrs
96 hrs
96 hrs
48 hrs
48 hrs
24 hrs
48 hrs
98 days
48 hrs
48 hrs
48 hrs
2 hrs
Effect
LC50
LC50
LC50 (periodic
low 0.0.)
LC50
EC50
LC50
LC50 < 5 C)
(10 C)
(15 C)
(25 C)
Competition with
Asel lus affects
HCN toxlclty
LC50
LC50
EC50
Swlmmlnq speed
reduced
Result
(ng/t)«
3,300
52,000
190
1,350
800"
530
330
330
180
1
9
500
2,000
<880
10
Reference
Cairns, et al . 1976
Dowden & Bennett,
1965
Cairns & Scholar. 1958
Cairns, et al . 1976
Brlnqmann & Kuhn,
1959a,b
Brlnqmann 4 Kuhn, I977b
Cairns, et al . 1978
Osatd i Smith, 1979
Roback, 1965
Roback, 1965
Cal 1, et al . 1979
Broderlus, 1970
Coho salmon (juvenile),
Oncorhynchus klsutch
36 days Reduction In
growth
77 Leduc, 1966
29
-------
Tab!* 5. (Continued)
Species Duration
Chinook salmon (juvenile), 64 days
Oncorhynchus tshawytscha
Rainbow trout (Juvenile), 250 mln
Sal mo galrdnerl
Rainbow trout (adult), 2 mln
Salmo galrdnerl
Rainbow trout (adult), 8 mln
Salmo galrdnerl
Rainbow trout (adult), 12 mln
Salmo qalrdnerl
Rainbow trout (adult), 12 mln
Salmo galrdnerl
Rainbow trout (adult), 24 mln
Salmo galrdnerl
Rainbow trout (adult), 72 mln
Salmo galrdnerl
Rainbow trout (adult), 90 min
Salmo galrdnerl
Rainbow trout (adult), 2,525 mln
Salmo qalrdnerl
Rainbow trout (adult), 1,617 mln
Salmo galrdnerl
Rainbow trout (adult), 3,600 mln
Salmo galrdnerl
Rainbow trout (adult), 4,441 mln
Salmo galrdnerl
Rainbow trout, 46 hrs
Result
Effect <««gA)*
27| reduction In 20
bl amass
Approximate median 200
survival time
Mean survival time 2,000
Mean survival time 500
Mean survival time 250
Mean survival time 200
Mean survival time 180
Mean survival time 160
Mean survival time 140
Mean survival time 100
Mean survival time 90
Mean survival time 80
Mean survival time 70
LC50 68
Reference
Neqllskl, 1973
Oep. Scl . Ind. Res.,
1956
Herbert & Her kens,
1952
Herbert & Merkens,
1952
Herbert & Merkens,
1952
Herbert & Merkens,
1952
Herbert & Merkens,
1952
Herbert & Merkens,
1952
Herbert 4 Merkens,
1952
Herbert & Merkens,
1952
Herbert 4 Merkens,
1952
Herbert & Merkens,
1952
Herbert & Merkens,
1952
Brown, 1968
Salmo qalrdnerl
30
-------
Table 5. (Continued)
Species Duration
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (Juvenile)
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (Juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (yearling),
Salmo galrdnerl
Rainbow trout (yearling),
Salmo galrdnerl
Rainbow trout (yearling),
Salmo galrdner)
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (yearling),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerI
Rainbow trout (juvenile), 18 days
Salmo galrdnerl
Rainbow trout (yearling), 7 days
Salmo galrdnerI
Effect
18 days
4 days
18 days
18 days
18 days
21 days
21 days
21 days
28 days
20 days
18 days
Weight gain reduced
Increased respira-
tion rate
Liver damage
(necroblosl s)
Reduction In fat
content
Higher relative
body water content
654 reduction In
weight gain
75$ reduction In
swimming ability
Higher relative
body water content
Altered blood chloride
and osmolarlty
Abnormal oocyte
development
Production of dividing
Result
(»g/D* Reference
9.6 Dlxon & Leduc, 1981
9.6 Dlxon & Leduc, 1981
9.6 Dlxon & Leduc, 1961
19 Olxon 4 Leduc, 1981
9.6 Olxon & Leduc, 1981
19 Speyer, 1975
spermatoqonla
reduced by I J<
Production of dividing
spermatoqonia
reduced by 50f
Serum calcium reduced;
hepatosomatIc Indices
dec) Ined
19
Speyer, 1975
19 Speyer, 1975
9.6 Leduc & Chan, 1975
9.6 Lesnlak, 1977;
Lesnlak & Ruby, 1982
9.6 Ruby, et al. 1979
29 Ruby, et al. 1979
9.6 Costa & Ruby, 1984
19
31
-------
TabU 5. (Continued)
Species
Rainbow trout (juvenile),
Sal mo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (juvenile),
Salfrvo galrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Duration
24 hrs
21 days
21 days
144 hrs
20 days
20 days
20 days
20 days
Rainbow trout (Juvenile), 20 days
Salmo galrdnerl
Result
Effect tug/I)'
LC50 ( 5 C) 90
(12 C) 98
08 C) 92
No effect on dry 33
weight gain
Kidney damage 33
LC50 93
Reduction In 4.8-43
swimming ablIIty
(6-18 C)
Threshold concen-
tration (6-18 C) for
reduction of
relative:
wet weight gain 9.6-29
dry weight gain <4.8-29
fat gain <4.8-24
Increase In 4.8-43
relative water
content (6-18 C>
No effect on wet 9.6
or dry weight rela-
tive growth rate or
fat weight change
for 8 g fish forced
to swim at 12 cm/sec
and 10 C
Increased food main- 13
tenance requirements,
decreased wet and
dry weight relative
growth rate and fat
weight change for IS
q fish forced to swim
at 12 cm/sec and 10 C
Cairns, et al . 1978
Dlxon & Spraque,
1981
Dlxon & Sprague,
1981
Dlxon & Sprague,
1981
Kovacs, 1979; Kovacs 4
Leduc. 1982a
Kovacs, 1979; Kovacs &
Leduc, I982a
Kovacs, 1979; Kovacs
Leduc, 1982a
McCracken & Leduc.
1980
McCracken & Leduc,
1980
32
-------
Table 5. (Continued)
Result
Species Duration
Rainbow trout (Juvenile), 20 days
Sal mo go 1 r drier 1
Atlantic salmon (larva), 58 days
Salmo sal or
Atlantic salmon (smolt), 24 hrs
Salmo salar
Brown trout (fry), 8.2 mln
Salmo trutta
Brown trout (try), 8.9 mln
Salmo trutta
Brown trout (fry), 8.2 mln
Salmo trutta
Brown trout (fry), 140 mln
Salmo trutta
Brown trout (juvenile), 6.58 mln
Salmo trutta
Brown trout (juvenile), 15 mln
Salmo trutta
Brown trout (juvenile), 50.1 mln
Salmo trutta
Brown trout (juvenile), 5 hrs
Salmo trutta
Brook trout (fry), 15.2 mln
Salvellnus fontlnalls
Brook trout (fry), 10.8 mln
Salvellnus fontlnalls
Brook trout (fry), 11.7 mln
Effect (wg/D* Reference
Decreased wet weight 9.6 McCracken 1 Leduc,
gain for 27 q fish \960
forced to swim at 12
cm/sec and 10 C
Abnormal embryo and 9.6 Leduc, 1978
larval development
LC50 (10 mq D.O./L) 70 Alabaster, et al .
(1.5 mg D.O./L) 25 1983
Death 8,030 Karsten, 1934
Death 4,140 Karsten, 1934
Death 2,070 Karsten, 1934
Death 217 Karsten, 1934
Geometric mean 1,006 Bur dick, et al . 1958
time to death
Geometric mean 510 Burdlck, et al . 1958
time to death
Geometric mean 320 Burdlck, et al . 1958
tlrno to death
Oxyqen uptake 25 Carter, 1962
Inhibited
Death 8,640 Karsten, 1934
Death 4,290 Karsten, 1934
Death 2,130 Karsten, 1934
Salvellnus fontlnrtlls
33
-------
Table 5, (Coat!nu«d)
Spec I •<
Brook trout ( fry) ,
Salvellnus fontinalls
Brook trout ( fry) ,
Salvellnus fontlnalls
Brook trout ( fry),
Salvellnus fontinalls
Brook trout { fry) ,
Salvellnus fontlnalls
Brook trout ( fry) ,
Salvellnus fontlnalls
Brook trout (juvenile),
Salvellnus fontlnalls
Brook trout (Juvenile),
Salvellnus fontlnalls
Brook trout (juvenile),
Salvellnus fontlnalls
Brook trout (juvenile),
Salvellnus tontlnalls
Goldfish (juvenile) ,
Car ass i us auratus
Goldfish (juvenile) ,
Carasslus auratus
Golden shiner (juvenile),
Notemlgonus crysoleucas
Fathead minnow,
P Itnephales promelas
Fathead minnow (juvenile),
P Itnephales promelas
Duration
26 mln
58 mln
210 mln
J30 hrs
27 days
3.6 days
40 days
25.5 mln
90 days
336 hrs
24 hrs
24 hrs
48 hrs
5 days
Eft«et
Death
Death
Death
Death
100* survival
Death
No death
75t reduction In
swimming endurance
Reduced growth
LC50
LC50 ( 5 C)
(15 C)
(30 C)
LC50 ( 5 C)
(15 C)
(30 C)
LC50
LC50
Result
853
392
217
50
20
80
50
10
33
261
3,250
440
280
540
310
300
240
120
Reference
Karsten, !934
Karsten, 1934
Karsten, !934
Karsten, 1934
Karsten, 1934
Nell . 1957
Nell, 1957
Nell, 1957
Koenst, et al . 1977
Cardwel 1 , et al . 1976
Cairns, et al . 1978
Cairns, et al . 1978
Black, et al . 1957
Cardwel 1 , et al .
1976
34
-------
Table 5. (Continued)
Species
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (embryo),
PI map hates promelas
Fathead minnow (embryo),
Plmephales promelas
Fathead minnow (embryo),
Plmephales promelas
Fathead minnow (embryo),
Plmephates promelas
Fathead minnow (embryo),
Plmephales promelas
Fathead minnow (embryo),
P 1 mep ha 1 es pr ome 1 a s
Fathead minnow (embryo),
Plmephales promelas
Blacknose dace,
Rhlnlchthys atratulus
Channel catfish (juvenile),
Ictalurus punctatus
Channel catfish (juvenile),
Ictalurus punctatus
Flagf Ish,
Jordanelia florldae
Duration
10 days
28 days
56 days
96 hrs
96 hrs
96 hrs
96 hrs
% hrs
% hrs
96 hrs
24 hrs
26 hrs
24 hrs
10 days
exposure
Result
Effect (nq/L)»
LC50
Reduced Increase In
length
Reduced Increase In
length and weight
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50 ( 5 C)
(15 C)
(30 C)
Reduced fecundity
and hatching
114
35
62
347
272
201
123
186
200
206
220
161
200
310
230
63
Reference
Cardwel 1 , et
1976
Llnd, et al.
Llnd, et al .
Smith, et al .
Smith, et al .
Smith, et al.
Smith, et al .
Smith, et al .
Smith, et al .
Smith, et al .
Llpschuetz &
1955
Cardwel 1 , et
1976
Cairns, et al
Cheng A Ruby,
al.
1977
1977
1978
1978
1978
1978
1978
1978
1978
Cooper ,
al.
. 1978
1981
35
-------
Table 5. (Continued)
Species
Mosqultof Ish,
Gambusla atflnls
Guppy (juvenile) ,
Poecllla ret leu lot a
Threesplne stickleback,
Gasterosteus aculeatus
Threesplne stickleback
(adult),
Gasterosteus aculeatus
Threesplne stickleback
(adult),
Gasterosteus aculeatus
Threesplne stickleback
(adult),
Gasterosteus aculeatus
Blueql II (juvenile),
L epom 1 s macroch 1 ru s
Bluegl 1 1 (juvenile) ,
L epom Is macroch Irus
BluaglH (juvenile),
L epom Is macroch Irus
Blueql 1 1 ( juvenl le) ,
L epom Is macroch Irus
Bluegl 1 1 (juvenile) ,
L epom Is macroch Irus
Bluegl II (juvenile),
Lepomls macroch Irus
Blueql 1 1 (juvenile) .
Lepomls macroch Irus
Duration Effect
96 hrs LC50 (hlqh
turbidity)
120 hrs Threshold
concentration
90 min Depressed respira-
tion rate to 32*
of normal
824 min Median survival
time
642 min Median survival
time
412 min Median survival
time
202 min Median survival
time
260 min Median survival
time
351 min Median survival
time
258 min Median survival
time
352 min Median survival
time
655 min Median survival
time
48 hrs LC50
Result
(tig/D* Reference
640 Wai len. et al . 1957
236 Chen & Sel leek, 1969
1,040 Jones, 1947
134 Broderlus, 1973
170 Broderlus, 1973
237 Broderlus, 1973
198 Broderlus, 1973
194 Broderlus, 1973
165 Broderlus, 1973
165 Broderlus, 1973
144 Broderlus, 1973
127 Broderlus, 1973
134 Cardwel 1, et al .
1976
36
-------
Table 5. (Continued)
Species
Blueqlll (juvenile),
Lepomls macrochlrus
Blueqlll (Juvenile),
Lepomls macrochlrus
Blueglll (juvenile),
Lepomls macrochlrus
Blueqlll (Juvenile),
Lepomis macrochlrus
Blueglll (Juvenile),
Lepomls macrochlrus
Blueqlll (juvenile),
Lepomls macrochlrus
Blueglll (juvenile),
Lepomls macrochlrus
Blueqlll (juvenile),
Lepomls macrochlrus
Blueglll (adult),
Lepomls macrochlrus
Blueglll (adult),
Lepomls macrochlrus
Blueglll (adult),
Lepomls macrochlrus
Smal 1 mouth bass
( juvenl le),
Mlcropterus dolomleul
Smal Imouth bass
( juven lie).
Duration
48 hrs
50 mln
91 mln
129 mln
700 mln
72 hrs
24 hrs
96 hrs
48 hrs
289 days
289 days
7.8 mln
12.4 mln
Effect
LC50
Median resistance
time
Median resistance
time
Median resistance
time
Median resistance
time
LC50
LC50 ( 5 C)
(15 C)
(30 C)
LC50 (periodic
low D.O.)
LC50
Survival reduced
No reproduction
Geometric mean
time to death
Geometric mean
time to death
Result
(jig/t)*
280
960
720
540
170
154
240
160
190
48
160
67.8
5.4
1,900
1,430
Reference
Turnbul 1 , et al .
1954
Doudorof f, et al .
1966
Ooudorott, et al .
1966
Doudorof t, et al .
1966
Ooudorott, et al .
1966
Doudorof f, et al .
1966
Cairns, et al . 1978
Cairns 4 Scholar,
1958
Cairns, et al . 1965
Klmbat 1, et al . 1978
Klmball, et al . 1978
Burdlck, et al . 1958
Burdlck, et al . 1958
Mlcropterus dolomieul
37
-------
Table 5. (Continued)
Species Duration
Small mouth bass 15.4 mln
(juvenl10),
Mlcropterus dolomleul
SfflalImouth bass 30.6 mln
(juvenlle),
Mlcropterus dolomleul
SmaIImouth bass 42.8 mln
(juvenlle),
Mlcropterus dolomleul
SmaIImouth bass 80.5 mln
(juvenlle),
Mlcropterus dolomleul
SmalImouth bass 122 mln
(juvenlle),
Hlcropterus dolomleul
Sma I Imouth bass 290 mln
(juvenlle),
Mlcropterus dolomleul
Largemouth bass 2 days
(juvenlle),
Mlcropterus salmoIdes
Largemouth bass (juvenile), 24 hrs
Mlcropterus salmoIdes
Result
Effect
Geometric mean
time to death
Geometric mean
time to death
Geometric mean
time to death
Geometric mean
time to death
Geometric mean
time to death
Geometric mean
time to death
Slgnl f leant
Increases In
opercular rate
Affected opercular
rhythm
Reference
978 Burdlck, et al . 1958
755 Burdlck, et al . 1958
478 Burdlck, et al. 1958
338 Burdlck, et al. 1958
243 Burdlck, et al . 1958
175 Burdlck, et al. 1958
40 Morgan & Kuhn, 1974
10 Morgan, 1979
Oyster,
Crassostrea sp.
Oyster,
Crassostrea sp.
SALTWATER SPECIES
10 mln Suppressed
cl I lary activity
3 hrs Inhibited
cl I lary activity
150 Usukl, 1956
30,000 Usukl, 1956
38
-------
Table 5. (Continued)
Result
Species
Atlantic salmon.
Sal mo salar
Plnflsh,
Laqodon r horn bo Ides
Duration Effect
24 hrs LC50
24 hrs LC50
(ng/D* Reference
20-75 Alabaster, et al .
1983
69 Oauqherty & Garrett,
1951
* Results are expressed as free cyanide as CN.
""In river Mater.
39
-------
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