PI HAL 3RAF7
£ CAD-01?! -^
April, 1987
&EPA Research and
Development
HEALTH AND ENVIRONMENTAL EFFECTS PROFILE
FOR DIRECT LI6HTFAST BLUE'
Prepared for
OFFICE OF SOLID WASTE AND
EMERGENCY RESPONSE
Prepared by
Environmental Criteria and Assessment Office
Office of Health and Environmental Assessment
U.S. Environmental Protection Agency
Cincinnati, OH 45268
DRAFT: DO NOT CITE OR.QUOTE
NOTICE
This document Is a preliminary draft. It has not been formally released
by the U.S. Environmental Protection Aqency and should not at this stage be
construed to represent Agency policy. It is being circulated for coilments
on its technical accuracy and policy implications.
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DISCLAIMER
Thi? report 's an external draft for review purposes only and does not
constitute Agency policy. Mention of trade names or commercial products
does not cons'tHute endorsement or recommendation for use.
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PREFACE
Health and Environmental Effects Profiles (HEEPs) are prepared for the
Office of Solid Waste and Emergency Response by the Office of Health and
Environmental Assessment. The HEEPs are intended to support listings of
hazardous- constituents o.f a wide range of waste streams under Section 3001
of the Resource Conservation and Recovery Act (RCRA), as well as to provide
health-related limits for emergency actions under Section 101 of the Compre-
hensive Environmental Response, Compensation and Liability Act (CERCLA).
Both published literature and information obtained from Agency program
office .files are evaluated as they pertain to potential human health,
aquatic life and 'environmental effects of hazardous waste constituents. The
literature searched and the dates of the searches are included in -the
section titled "Appendix: Literature Searched." The literature search
material is current through November, 1985.
Quantitative estimates are presented provided. • sufficient data are
available. For systemic toxicants, these include Reference doses (RfDs) for
chronic exposures. An RfD is defined as the amount of a chemical to which
humans can be exposed on a daily basis over an extended period of time
(usually 'a lifetime) without suffering a deleterious effect. In the .case of
suspected carcinogens, RfDs are not estimated in this document series.
Instead, a carcinogenic potency factor of q-]* is provided. These potency
estimates are derived for both oraTand inhalation exposures where possible.
In addition, unit risk estimates for air and drinking water are presented
based on inhalation and oral data, respectively.
Repprtable quantities (RQs).based on both chronic toxicity and carcino-
genicity. are derived., The RQ is used to determine the quantity of a hazard-
pus substance for which notification is required in the event of a release
as specified under CERCLA. These two 'RQs (chronic tox-icity and carclnoge'n-
IcKy) represent two of six scores developed (the remaining four reflect
ignltabil.Hy,. reactivity, aquatic toxicity and acute mammalian tox'lclty).
The first draft of this . document was prepared by Syracuse Research
Corporation under EPA Contract No. 68-03-3228. The document was subse-
quently revised after, reviews by staff within the Office of Health and
Environmental Assessment: Carcinogen Assessment Group, Reproductive Effects
Assessment Group, Exposure Assessment Group, and the Environmental Criteria
and Assessment Office in Cincinnati.
The HEEPs will become part of the EPA RCRA and CERCLA dockets.
iii
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EXECUTIVE SUMMARY
Direct Lightfast Blue is a common name for the commercial .azo dye Direct
Blue 71, which is produced by the diazotlzation of 3-amino-l,5-naphthalene-
dlsulfonic acid with lrnaphthylamine and subsequent coupling reactions with
l-naphthylamine-7-sulfonic acid and 2-am1no-5-naphthol-7-sulfonic acid
(Society of Dyers and Colourlsts. 1971a). It is soluble in water but
insoluble in most nonpolar organic solvents. It can be used to dye, stain
or print cellulose, silk, leather, paper, casein-formaldehyde plastics,
cellophane, cotton, wool or nylon and to color soap (Society of Dyers and
Colourists, 1971a). In 1973, four U.S. manufacturers produced 0.131 million
pounds of Direct Lightfast Blue (USITC, 1975),. but only one U.S. manufac-
turer' reported production in 1984 (USITC, .1985). Three U.S. companies cur-
rently market Direct Lightfast Blue under various tradenames (AATCC, 1985).
The only available data specific to the environmental fate of Direct
LVghtfa,s.t Blue is a study by'which Wuhrmann et al. (1980) found that it can
be reduced microbially by a strain of Baci1lus cereus Isolated from soil.
If released to water, Direct Lightfast Blue may be susceptible to signifi-
cant adsorption because dyestuffs by their substantive nature (ability to be
exhaustively deposited to fibers from aqueous baths) are likely to be
.adsorbed onto both sewage works sludge and silts and sediment of rivers and
lakes (Brown and Laboureur, 1983). Removal of adsorbed Direct Lightfast
Blue may occur by anaerobic biodegradat ion since a number of azo dyes have
been found to be substantially biodegraded under anaerobic conditions (Brown
and Laboureur, 1983). In general, direct dyes are expected to be relatively
stable to direct photolysis in natural waters (Porter, 1973), but humic
materials in natural water have .been found to strongly accelerate the
indirect photodecompositlon of some azo dyes (Haag and Mill, 1985).
iv
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riyurolysis, volatilization jna oiocsncantration are not expected to be
significant; Indirect photolysis, mlcroblal degradation and adsorption are
the. important fate processes in water. If r?leas'ed to the atmosphere,
Direct Llghtfast Blue will probably.be associated with participate matter
and dusts that are suoject -.0 wet ' and cry deposition. Some of it may be
removed by reaction with atmospheric HO radical. If released to soil,
Direct Llqhtfast Blue may not leach siqnlficantly, since dyestuffs are
susceptible to significant adsorption. Mlcroblal degradation may occur 1n
soil. Photodegradatlon on soil surfaces Is possible, but is expected to be
'.fislg.Vif'.cant • beyond the'surface layer.
Occupational .exposure to Direct Llghtfast Blue occurs during Its produc-
tion ana it's use 1n dyeing. Hastewater effluents are probably the major
source of release to the environment. Ambient monitoring data could not be
located In the available literature as cited 1n the Appendix.
Pertinent data regarding aquatic toxldty, pharmacoklnetlcs, carcl'no-
genldty, mutagenlclty, developmental and reproductive, effects, chronic,
subchronlc or acute toxldty and biochemical effects of Direct Llghtfast
Blue could not be located In the .avanabls "literature as cited 1n the
Appendix. While confirming studies on animal test systems 1s not available,
a hypothesis that the azo component of tne dye may be reducible to a- or
B-naphthalamine or benz'dene provide a rsasbn for concern about the possible
carcinogenic potential.
The lack of data on the health effects of Direct Llghtfast Blue
precludes derivation of an RfO, q * RQ and F factor either Directly or by
analogy. In terms of the available evidence for carclnogenldty, Direct
Llghtfast Blue was classified as a EPA Group D chemical (U.S. EPA, 1986b);
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that Is, data for carcinogenicity are Inadequate for public health
purposes. A cautionary approach to exposure would be prudent in view of the
hypothesis that biochemical reduction in humans may produce products that
have known human carcinogenic potential.
vl
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••,8LE JF ;::ITEHTS
1. INTRODUCTION 1
1.1. STRUCTURE AND CAS NUMBER 1
1.2. PHYSICAL AND CHEMICAL PROPERTIES 1
1.3. PRODUCTION DATA 2
i.4. USE OATA ' i
1.5. SUMMARY . . . 4
2. ENVIRONMENTAL FATE AND TRANSPORT'PROCESSES. .....' 5
2.1. WATER . . . . 5
2.1.1 . Hydrolysis 5
2.1.2. Oxidation/Reduction 5
2.1,.3. Photolysis 5
2.1.4. ' M1crob1al Degradation 5
2.1.5. Volatilization 6
2.1.6. Adsorption. . 6
2.1.7. 31oconcer.t:at1bn . . . 7
2.2. AIR . : 7
2.3. SOIL 7
2.4. SUMMARY 8
3. EXPOSURE 9
3.1. WATER. ' .......... 9
3.2. FOOD : 9
. 3.3. INHALATION • •. . . 10
3.4. DERMAL 10
3.5. SUMMARY 10
4. PHARMACOKINETCS 11
5. EFFECTS ...:.. 12
6. AQUATIC TOXICITY. 13
7. EXISTING GUIDELINES AND STANDARDS 14
7.1. HUMAN 14
7.2. AQUATIC. 14
8. RISK ASSESSMENT 15
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7A5LS; ir JCNTEHTS iesr
9. REPORTABLE QUANTITIES
9.1. REPORTABLE QUANTITY (RQ) RANKING BASED ON CHRONIC
TOXICITY ......................... 16
9.2. WEIGHT OF. EVIDENCE AND POTENCY FACTOR (F«1/ED10)
FOR CARCINOGENICITY. . ....... ........... 16
10. REFERENCES. . ..... ..•...' ..... ........... . 17
APPENDIX: LITERATURE SEARCHED ..................... • 20
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LIST OF ABBREVIATIONS
AOI Acceptable dally Intake
CAS Chemical Abstract Service
Kow Octanol/water partition coefficient
oom Parts per million
RQ Reportable quantity
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1. INTRODUCTION
1.1. STRUCTURE AND CAS NUMBER
Direct Llghtfast Blue Is .commonly referred to as Direct Blue 71. The
Colour Index reference number 1s C.I. 34140 (Society of Dyers and Colour-
1sts, 1971a). The current CAS designation for Direct Ughtfast Blue 1s
1,5-naphthalenedlsulfonlc add, . 3-[{4-((4-( (6-am1no-l-hydroxy-3-sulfo-2-
napht.haleny 1 }azo)-6-sulfo-l-naphthalenyl)a:o)-l-naphthenyl)azo], tetrasodium
salt. Direct Blue 71 1s currently marketed 1n the United States under the
tradenames, Am1d1ne Fast Blue FFB (John Campbell & Co.), IntralHe Blue FFC
Cone., FFC Ex. Cone. (Crampton i Knowles Corp.) and OrcolHefast Blue. FFC
(Organic Chem. Corp.) (AATCC, 1985). The structure, empirical . formula and
CAS Registry number for Direct Llghtfast Blue are as follows:
NaO,S
oio
— N..N—
NH,
Molecular weight: 1024
Empirical formula: C40H27N7013$4Na4
CAS Registry number: 4399-55-7
1.2. PHYSICAL AND CHEMICAL PROPERTIES
Direct Llghtfast Blue Is soluble 1n water (forming a bright blue
solution), slightly soluble In ethylene glycol monoethyl ether, very
slightly soluble 1n ethanol and Insoluble In most other organic solvents
(Society of Dyers and ColouMsts, 1971a). All direct dyes are water soluble
and form anlons by dissociation (Kuehnl et al., 1979). In aqueous solution,
the molecules of direct dyestuffs are linked by hydrogen bonds forming
085Up
OS/20/36
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larger agglomerates or coioioai so tutions, . wnicn recuces '.neir iuiuoiiity
and promotes deposition on cellulosic fibers. The structure of .these
agglomerates allows firm linkage to the cellulose molecule by multiple
hydrogen bonds (Kuehni et al., 1979).
Physical properties sucn as meiung poini, boiling ooini, .vaoor pres-
sure, density and log K could not be located in the available lltera-
ow
ture. Lack of appropriate fragment values precluded the comouter calcula-
tion of log K (U.S. EPA, 1986a). The air conversion factor for Direct
Lightfast Blue is 1 ppm = 43.0 mg/m3.
The ^lanuf^ctars and testing of. Direct Lightfast Blue probably does not
conform to rigid chemical specifications, and Its composition may vary in
order to meet the ihau'e and intensify requirement j.
1.3. PRODUCTION DATA
Direct Lightfast Blue (C.I. 34140) is produced by coupling 3-am1no-l,5-
naphthalenedlsulfonic acid to 1-naphthylamine followed by coupling to
l-naphthylam1ne-7-sulfon1c add. which is finally coupled to 2-amino-5-naph-
thol-7-sulfon1c add under alkaline conditions (Society of Dyers and Colour-
. Ists. 1971a). . '
In 1973, four U.S. companies produced 0.131 million pounds of Direct
L'.ghtfjsl Blue (USITC, 1975/, che mcsz recent proauccion ngure available.
In 1984, Cr.3ir.pton i-Knowles Corp. uos reportedly the only U.S. producer of
Direct Lightfast Blue (USITC, 1985). U.S. companies that currently market
the dye are listed in Section 1.1. The production and import data available
from the oublic portion of the TSCA oroduction file for 1977 are listed in
Table 1-1.
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T.'8LE ^-!
"Irect Mnhtfast 31i:e "reduction Oata enr 1977*
Producer/Location
Manfacturer
or !mDorter
Production Range
Fabr Icolor Inc.
Paterson, NJ
Ugine Kuhlmann of America
Paramus, NJ
L & R Dyestuffs Corp.
Clifton, NJ
Allied Chemical
Morrlstown, NJ
Atlantic Chemical Corp.
Nutley, NJ
on USA
New York, NY
manufacturer
Importer
Importer
Importer
Importer
impor T.er
none
confidential
none
none
confidential
none
cs: j.2. EPA. 19/7
0850D
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Import of Direct Liqhtfast Blue through principal U.S. customs districts
1n recent years has been reported as follows (USITC, 1981, 1982, 1983, 1984):
Import Volume
Year (pounds)
1983 2480
1982 2313
1981 1000
1980 4253
1.4. USE DATA
Direct Ughtfast Blue Is a dye that can be used to dye cellulose, silk,
leather, paper, casein-formaldehyde plastics and cellophane; stain silk,
cotton, wood and nylon; print cellulose; and color soap (Society of Dyers
and Colourlsts, 1971b).
1.5. SUMMARY
Direct Llghtfast Blue 1s a common name for the commercial azo dye Direct
Blue 71, which Is produced by the dlazotlzation of 3-amino-l,5-naphthalene-
dlsulfonlc add with l-naphthylam1ne and subsequent coupling reactions with
1 -naphthylam1ne-7-sulfon1c add and 2-am1no-5-naphtho1-7-sulfonic acid
[Sodely of Dyers and ColouMstG, 1971a). It. 's soluble in ' water but.
insoluble in most nonpolar organic solvents. It can'be -used to dye, sta.in.
or print cellulose, silk, leather, paper, casein-formaldehyde plastics,
cellophane, cotton, wool or nylon and to color soap (Society of Dyers and
Colourlsts, 1971a). In 1973, four U.S. manufacturers produced. 0.131 million
pounds of Direct Llghtfast Blue (USITC, 1975), but only one U.S. manufac-
turer reported production in 1984 (USITC, 1985). Three U.S. companies cur-
rently market Direct Llghtfast Blue under various tradenames (AATCC, 1985).
0850p -4- 09/20/86
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i. cNVIRONMENTAL r'ATE AND TRANSPORT PROCESSES
2.1. WATER
2.1.1. Hydrolysis. Experimental hydrolysis data could not be located in
the available literature; however, since Direct Llghtfast Blue does not
contain functional groups that are readily susceptible .to environmental
hydrolysis, hydrolysis is not expected to be environmentally significant.
2.1.2. Oxidation/Reduction. Specific experimental oxidation and reduc-
tion data could not be located in the available literature. Takemura et al.
(1965) reported that bubbling of H S through a pure azo-dye solution
yields aromatic amines and suggested ' that .a.zo dyes in wastewater may be.
reduced at the azo linkage .(by H S or SO. In the water) to form inter-
mediates, such as benzldlne or naphthylamlne, from which the dye was
produced. A water system receiving dyes, however, would have to be very
polluted and the environment has to be reducing for. this reduction reaction
to proceed.
2.1.3. Photolysis. Porter (1973) examined the photodegradatlon rate In
aqueous solution of 8 direct dyes and 12 other azo dyes In artificial light
and one direct dye and one acid dye 1n natural sunlight. flawed on the
experimental results, the author concluded- that direct dyes are relatively
stable to direct photolysis in natural waters. Although Direct Lightfast
Blue was not one of the dyes studied, its structure 1s similar to several
dyes that were tested.
Haag and Mill (1985) examined the aqueous photodegradation rate of 15
azo dyes by simulated or natural sunlight. Potentially significant direct
photolysis was observed for some dyes; however, humlc materials in natural
water were found to strongly accelerate the photodecomposition rate of all
the dyes. Therefore, indirect photolysis may be an important removal
mechanism for azo dyes in water.
1850p -5- . 09/20/36
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2.1.4. H1crob1al Degradation. Wuhrmann et al. (1980) founa mat a strain
of Bad 1 lus cereus Isolated from soil was. able, to reduce Direct Llghtfast
31ue and other azo dyes under anoxlc conditions. Other mlcroblal 'data
specifVc to Direct Llghtfast Blue were not found 1n the available literature.
Brown and Laboureur (1983) reported that a number of azo dyes were
substantially blodegraded under anaerobic test conditions and suggested that
the breakdown of dyestuffs 1n the environment may be Initiated under
anaerobic conditions.
2.1.5. Volatilization. Experimental volatilization data could not be
located in the available literature. Direct Llghtfast Slue is soluble in
water (Society of Dyers and Colourists, 1971a) and Is expected- to have a
relatively low vapor pressure, based on Its chemical structure, whlcn would
predict a relatively small Henry's Law constant. Therefore, volatilization
from water Is not expected to occur in the environment.
2.1.6. Adsorption. Experimental adsorption data specific to Direct
Lightfast Slue could not be located in the available literature. Dyestuffs
by their substantive nature (ability to be exhaustively deposited to fibers
from aqueous baths!, however, a-e likely to be adsorbed onto both sewage
works sludge and silts and sediments of rivers and lakes (Brown and
Laboureur, 1983). In conventional biological waste treatment systems,
soluble dyes are known to be adsorbed onto sludge (Porter, 1973).
2.1.7. B1oconcentrat1on. Experimental bioconcentratlon data could not be
located 1n the available literature.
The presence of Direct Llghtfast Blue 1n the atmosphere is most likely
to be associated with partlculate matter and dusts, especially from atmo-
spheric effluents resulting from production and use. These particulate
matter and dusts are subject to wet and dry deposition. Since aromatic
amines readily react with HO radical in the atmosphere (Atkinson, 1985).
J85Gp -o- T-/28/a7
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cMs jye may os removeo significantly from cne atmospnere oy riO raaical
reaction.
2.3. SOIL
Pertinent experimental data regarding the fate of Direct Lightfast Blue
!n soil could not be located in che available literature as cited in the
Appendix. Chemical degradation may not significantly occur in soil since
dyes, in general, are resistant, to oxidative degradation (Porter, 1973) and
hydrolysis Is not expected to be environmentally significant. If signifi-
cant chemical transformation of Direct Lightfast Blue 1s to occur 1n soil,
m1crob1al degradation may be the environmental fate process Involved.
Huhrmann et al. (1980) found that a strain of Bacillus cereus Isolated from
soil was able to reduce Direct Lightfast Blue and other azo dyes under
anoxic conditions. Additionally, a number of azo dyes have been shown to be
susceptible to anaerobic biodegradation (Brown and Laboureur, 1983).
Photodegradatlon on soil surfaces may be possible.
Since Direct Lightfast Blue is water soluble (Society of Dyers and
Colourists, 1971a), leaching 1n soil might be expected; however, the
substantive nature of dyestuffs (Brown and Laboureur, 1983), Including the
direct dyes (Kuehni et al., 1979), Indicates that significant adsorption to
soil may occur. Therefore, significant leaching in soil may not occur.
2.4. SUMMARY
The only available data regarding the environmental fate of Direct
Lightfast Blue was a study that found that It can be reduced microbially by
a strain of Bacillus cereus isolated from soil (Wuhrmann et al.. 1980). If
released to water, Direct Lightfast Blue may be susceptible to significant
adsorption because dyestuffs by their substantive nature (ability to be
exhaustively deposited to fibers from aqueous baths) are likely to be
adsorbed onto both sewage works sludge and silts and sediment of rivers and
OflSOo -?- ••4.;2<3/37
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lakes (Brown and Laboureur, 1983). Removal of adsorbed Direct Ughtfast
Blue may occur by anaerobic b.1odegradat1on since a number of azo dyes have
been found to be substantially blodegraded under anaerobic conditions (Brown
and Laboureur, 1983). In general, direct dyes are expected to be relatively
stable to direct photolysis In natural waters (Porter, 1973), but humic
materials In natural water have been found to strongly accelerate the
Indirect photodecomposltlon of some azo dyes (Haag and H111, 1985).
'Hydrolysis and volatll1zat1on 'are not expected to be significant; Indirect
photolysis, microblal degradation and adsorption are the Important fate
processes 1n water. If released to the atmosphere, Direct Lightfast Blue
will probably be associated with particulate matter and dusts that are
subject to wet and dry deposition. Some of 1t may be removed by reaction
with atmospheric HO radical! If released to soil, Direct Lightfast Blue may
not leach significantly, since dyestuffs are susceptible to • significant.
adsorption. Microblal degradation may occur in. soil. Photodegradatlon on
soil surfaces Is possible, but Is expected to be 'insignificant beyond the
surface layer.
JBSOp -3-
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3. EXPOSURE
Direct Lightfast 'Blue has not been reported to occur in nature; there-
fore, exposure from natural sources 1s not expected to.occur. Occupational
exposure to Direct ,Lightfast Blue occurs during Its production and Its use
for the dyeing of various products. Likely routes of exposure are Inhala-
tion of particulates and dermal exposure.
3.1. WATER
Pertinent monitoring data for Direct Lightfast B.lue could not be located
In the available literature as cited In the Appendix. For the organic dye
Industry, 1,n general, 1t has been estimated that -90% of the dye during use
ends up on the fabric, while 10% 1s lost to wastewater effluents (Porter.
1973; Brown et al., 1981). Losses of dyes to wastewater effluents during
manufacture were estimated to be 1-2*/. (Brown et al., 1981). Waste streams
from dye -manufacture contain dissolved'inorganic salts and small amounts of
dye and dy.e Intermediate (Steadman et al., 1977). Wastewater effluents are-
therefore the major source of release to water. The efficiency of waste-
water treatment operations will deterge '.he amount jf dye '.hat -eaches
natural waters..
Release of dye from textile fabrics may occur from commercial or
consumer washing; however, dyes in most finished products are considered to
be essentially "fast" (they do not migrate or wash out) (Jones, 1979).-
Various after-treatments are commonly applied to fabrics dyed with direct
dyes to Improve the wetfastness quality (Kuehni et al., 1979).
3.2. FOOD
Pertinent data regarding exposure to Direct Lightfast Blue through food
could not be located In the available literature as cited In the Appendix.
0850p -9- 09/20/86
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3.3. INHALATION
No ambient or occupational air monitoring data specific to Direct Light-
Fast Slue were located In the available literature as cited In the Appendix.
Ambient atmospheric emissions may occur from ventilation effluents at
production and use sites. In addition, air effluents from production
operations, .such as spray drying, may be sources of release. Partlculate
emissions from these sources are usually filtered at the plant site, which
should reduce significantly the amount of participate matter actually
reaching the ambient atmosphere.
3.4. DERMAL
Pertinent monitoring data could not be located .in the available litera-
ture as cited in the Appendix. The general .public is exposed mainly to
finished dyes after they have been applied to the product; however, there 1s
little chance of dyes coming off In perspiration, saliva or washings 1,f
label instructions are followed (Jones, 1979).
3.5. SUMMARY
Occupational exposure to. Direct Lightfast Blue occurs during its produc-
tion and Its use in dyeing. Hastewater effluents are probably the major
source of release to the environment. No ambient monitoring data were found
in the available literature as cited in the Appendix.
0850p -10- . 09/20/36
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4. PHARMACOKINETICS
Pertinent data regarding the absorption, distribution, metabol ism • and
excretion of Direct lightfast Blue could not be located in the available
literature as cited in the Appendix.
0850p -II- 09/20/86
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3. cr rti. i i
Pertinent . data regarding the carclnogenicHy, mutagenicVty, develop-
mental and reproductive effects, chronic, subchronlc or acute toxicity and
biochemical effects of Direct Lightfast Blue could not be located in the
available literature as cited In the Appendix.
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6. AQUATIC TOXICITV
Pertinent data regarding toxicity of Direct lightfast Blue to aquatic
organisms could not be located in the available literature as cited in the
Appendix.
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;. EXISTING GUIDELINES AND STANDARDS
7.1. HUMAN
Pertinent guidelines and standards, including EPA ambient water and air
quality criteria, drinking water • standards, FAO/WHO ADIs, EPA or FDA toler-
ances for raw agricultural commodities or foods, and ACGIH, NIOSH or OSHA
occupational exposure limits- could not be located in the available litera-
ture as cited in the Appendix.
7.2. AQUATIC
Guidelines and standards for the protection of aquatic biota from the
effects of Direct Lightfast Blue could not 'be located in the available
literature as cited in the Appendl.x.
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8. RISK ASSESSMENT
The total lack of data on the health effects of Direct Ug'htfast Blue
precludes derivation • of an RfD or q * either directly or by analogy.
However, the possibility exists that the azo component of the dye has the
potential to be degraded 1n a reducing environment (the gut) to substances
that are clearly shown to have a carcinogenic potential of Group C, 8_ and
A (a- and B-naphthalam1ne benzldene). Since this degradation, has/not been
conflmed 1n annual test systems, the possibility can only be hypothesized.
A cautionary public health approach to limit exposure would be prudent In
view of the hypothesis.
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4. IMPORTABLE QUANTITIES
9.1. REPORTABLE QUANTITY (RQ) BASED ON CHRONIC TOXICITY
Data are not sufficient for deriving an RQ.
9.2. WEIGHT OF EVIDENCE AND POTENCY FACTOR (F=1/ED,Q) FOR CARC.INOGENICITY
Data are not sufficient for aeMving an F factor. Oirect' Lightrast 31ue
is best classified as- an EPA Group D chemical (U.S. EPA, 1986b), since no
"confirming" data regarding the carclnoqenldty of this chemical were
available. However, the chemical makeup of the dye and the potential for
biochemical'reduction In the human gut suggests a hypothesis whereby the azo
component of the dye would yield a- .or S-naphthalarnines/benz'.dene. These
degradation products have shown possibly probable/definite. human
carcinogenic potential, e.g., EFA ' group B~ ana A, respectively. A
confirmation of the hypothesis would be required before a higher weight of
evidence classification would be warranted. For public health purposes
however, a cautionary approach would- be prudent 1n view of the degradation
hypothesis.
1H5G;
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1 , c
10. REFERENCES
AATCC (American Association of Textile Chemists and Colorlsts)! 1985.
AATCC Buyers' Guide. Text. Chem. Color. 17: 80.
Atkinson, R. 1985. Kinetics and mechanisms of the gas phase reactions of
the hylroxyl .rBdlcal wUh orqanlc ccmoounds under atmosohsr^c tond'' Ions.
Chem. Rev. 85: 69-201.
Brown. D. and P. Laboureur. ~i983. 'The degradation of dyestuffs. Part I.
Primary blodegradatlon under anaerobic conditions. Chemosphere. 12:
397-404.
Brown, 0., H.R. Hltz and L. Schaefer. 1981. The assessment of the possible
Inhibitory effect of dyestuffs on aerobic wastewater bacteria. Experience
with a screening test. Chemosphere. 10(3): 245-261. .
Haaq, 't!.S.' and T. Nil!. 1585. Tlrect and ^ndlr^ct -jhotolysls of • azodyes.
Summary Report, EPA Contract 68-02-3968, Versar, Inc., Springfield. VA.
Subcpntraci 367-1 .
Jones, T.C. 1979. Preliminary Risk Assessment. Phase 1. 8enz1d1ne, Us
Congeners and Their Derivative Dyes and Pigments. U.S. EPA, Office of
Pesticides and Toxic Substances. EPA 560/11-80-019.
J9/20/36
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Kuehnl. R.G., J.C. King. R.E. Phillips, et al. 1979. Dyes, application and
evaluation, in: Slrk-Othmer Encyclopedia of Chemical Technology, 3rd ed.,
Vol. 8, H. Grayson and D. Eckroth.' Ed. John Wiley and Sons, Inc., New York.
p. 302-305.
Porter, J.J. 1973. Stability of add, basic and direct dyes to light and
water. Text. Res. 3. 43(12): 735-^44
Society of Dyers and Colourlsts.. 197.1a. Colour Index, 3rd ed.. Vol. 4.
Lund Humphries, Bradford, UK. p. 4318.
Society of Dyers and Colourlsts. 1971b.. Colour Index, 3rd ed., Vol. 2.
Lund Humphries, Bradford, UK. p. 2246.
Steadnwn, T.R.. E.W. Helper, T. Parsons, G.E. Wllklns and N.P. Phillips.
1977. Industrial Process Profiles for Environmental Use: Chapter 7.
Organic Dyes and Pigments Industry. EPA 600/2-77-023g. NTIS P8281479.
p. 69.
Takemura, N., T. Aklyama and C. Nakahama. 1965. A survey of the pollution
of the Sumlda River, especially on the aromatic amines 1n the water
(Interv.) J. Air Pollut. 9(10): 665-670.
U.S. EPA. 1977. Computer print-out of non-confidential production data
fronrTSCA Inventory. OPTS. CID. U.S. EPA. Washington. DC.
U.S. EPA. 1986a. Graphical Exposure Modeling System (GEMS). Octanol Water
Partition Coefficient (CLOGP) Data Base. Washington, DC.
065up -id- 'U/30/36
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J.j. EPA. i386b. dtiiaeilnes ror Carcinogen AISK Assessment. federal
Register. 51(185): 33992-34003.
USITC (U.S. International . Trade Commission). 1975. Synthetic Organic
Chemicals. U.S. Production and Saies, 1973. , USITC Publ. 728, Washington,
DC. p. 57.
USITC (U.S. International Trade Commission). 1981. Imports of Benzenold
Chemicals and Products. 1980. USITC Publ. 1163, Washington, OC. p. 57.
USITC (U.S. International Trade Commission). 1982. Imports of Benzenold
Chemicals and. Products. 1981. USITC Publ. 1272, Washington, OC. p. 52.
USITC (U.S. International Trade Commission). 1983. Imports of Benzenold
Chemicals and Products. 1982. USITC Publ. 1401, Washington, DC. p. 50.
USITC (U.S. International Trade Commission). 1984. Imports of Benzenold
Chemicals and Products. 1983. USITC Publ. 1548. Washington, OC. p. 51.
USITC (U.S. International Trade Commission). 1985. Synthetic Organic
Chemicals. U.S. Production and Sales, 1984. USITC Publ. 1745, Washington,
00. p. 66.
Wuhrmann, K., K. Mechsner and T. Kappeler. 1980. Investigation of rate-
determining factors In the mlcroblal reduction of azo dyes. Eur. J. Appl.
Hlcroblol. Blotechnol. 9(4): 325-38. [CA 95(5) :38494p]
0850D -T?- Ti/:G/8f,
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,PPE;IOIX .
LITERATURE SEARCHED
This profile is based on data identified by computerized literature
searches of the foil owing:
GLOBAL
TSCATS
CASR online (U.3. EPA Chemical Activities Status Report)
CAS online STN International
TOXLIME
TOXBACK 76
TOXBACK 65
RTECS
OHM TADS
STORET
SRC Environmental Fate Data Bases
SANSS
AQUIRE
TSCAPP
NTIS
Federal Register
These searches were conducted in April, 1986.' In- addition, hand searches
were made of Chemical Abstracts (Collective Indices 6 and 7), and the
following secondary sources were reviewed:
ACGIH (American Conference of Governmental Industrial Hyglenists).
1986. Documentation of the Threshold Limit Values and Biological
Exposure Indices, 5th ed. Cincinnati, OH.
ACGIH (American Conference of Governmental Industrial Hygienists).
1985-1986. TLVs: Threshold Limit Values for Chemical Substances
and Physical Agents In the Workroom Environment with Intended
Changes for 1985-1986. Cincinnati, OH. 114 p.
Clayton, G.O. and F.E. Clayton, Ed. 1981. Patty's Industrial
Hygiene and Toxicology, 3rd rev. ed.. Vol. 2A. John Wiley and
Sons. NY. 2878 p.
Clayton, G.D. and F.E. Clayton, Ed. 1981. Patty's Industrial
Hygiene and Toxicology, 3rd rev. ed., Vol. 28. John Wiley and
Sons, NY. p. 2879-3816.
0850p
-20-
09/20/86
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j.J. ;no -.;'. ^iy-ton, :d. .982. :ai:v; I
Hygiene and Toxicology, 3rd rev. ed.. Vol. 2C. John Wiley and
Sons, NY. p. 3817-5112.
Grayson, H. and D. Eckroth, Ed. 1978-1983. Klrk-Othmer Encyclo- .
pedia of Chemical Technology, 3rd ed. John Wiley and ions, NY. 23
Volumes.
Hamilton, A. :nd H.L. Hardy. 1974. Industrial Toxicology, 3rd ed.
Dijbl ishlng Sciences Grouo. Inc., Littleton, MA. 575 p.
IARC (International Agency for Research on Cancer). IARC Mono-
graphs on the Evaluation of Carcinogenic Risk of Chemicals to
Humans. riHO, IARC, Lyons, France.
ITII (International Technical Information Institute). 1982. Toxic
and Hazardous Industrial Chemicals Safety Manual for Handling and
Disposal wHh ToxIcHy ar.d Hazard Data. ITII, Tokyo, Japan. 700 p.
Jaber, H.M.. W.R. Mabey, S.T. Liu, T.W. Chow and H.L. Johnson.
1.984. Data aqu1s1t1on for environmental transport and fate screen-
Ing for compounds of Interest In the Office of Solid Waste. EPA
600/6-84-010. NTIS PB84-2439G6. SRI International, Menlo Park. .CA.
NTP (National Toxicology Program). 1986. Toxicology Research and
Testing Program. Chemicals on Standard Protocol. Management
Status.
Ouellette, R.P. and J.A. King. 1977. Chemical Week Pesticide
Register. McGraw-Hill Book Co., NY.
Sax, N.I. 1979. Dangerous Properties of Industrial Materials, 5th
ed. Van Nostrand Relnhold Co., NY.
SRI (Stanford Research Institute). 1934. Directory- -if Chemical
Producers. Menlo Park, CA.
U.S. EPA. 1985. Status Report on Rebuttable Presumption Against
Registration (SPAR) or Special Review Process. Registration Stan-
dards and the Data Call In Programs. Office of Pesticide Programs,
Washington, DC.
U.S. EPA. 1985. CS8 Existing Chemical Assessment Tracking System.
Name and CAS Number Ordered Indexes. Office of Toxic Substances,
Washington, DC.
USITC (U.S. International Trade Commission). 1985. Synthetic
Organic Chemicals. U.S. Production and Sales, 1984, USITC Publ.
1745, Washington, DC.
Verschueren, K. 1983. Handbook of Environmental Data on Organic
Chemicals, 2nd ed. Van Nostrand Relnhold Co., NY.
0850p -21- 09/20/86
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I'inchoiz. •!.. -.••-. .9b2. "he :ercx ..".ae.x. jth -'J. !erc::c ilia ,j..
inc ., *anway, i^J.
Worthing. C.R. and S.B. Walker. Ed. 1983. The Pesticide Manual.
British Crop Protection Council. 695 p.
In addition, approximately 30 compendia of aquatic toxicity data were
reviewed, including the following:
Batieile's Columous Laporatories. 1971. Water Quality Cr'tarla
Data Book. . Volume 3. Effects of Chemicals, on -Aquatic Life.
Selected Data from the Literature through 1968. Prepared for the
U.S. EPA under Contract No.. 68-01-0007. Washington. DC.
Johnson, .W.W. and M.T. Flnley. 1980. Handbook of Acute Toxicity
of Chemicals to Fish ana Aquatic Invertebrates. Summaries or
Toxicity Tests Conducted at Columbia .National Fisheries Research
Laboratory. 1965-1978. U.S. .Oept. Interior, Fish ana Wildlife
Serv. Res. Publ. 137, Washington, DC.
McKee, J.E. and H.W. Wolf. .1963. Water Qua!ity .CMterla, 2nd ed.
Prepared for the Resources Agency of California, State Water
Quality Control Board. . Publ. No. 3-A.
Plmental, 0. 1971. Ecological 'Effects of Pesticides on Non-Target
Species. Prepared for the U.S. EPA, Washington, DC. PB-269605.
Schneider, B.A. 1979. Toxicology Handbook. Mammalian and Aquatic
Data. Book 1: Toxicology Data. Office of Pesticide Programs, U.S.
EPA, Washington, DC. EPA 540/9-79-003. NTIS PB 80-196876.
0850p -22- 09/20/86
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