£% ["j'liJl United States
Environmental Protection
^J^lniiil M % Agency
EPA/690/R-12/001F
Final
10-01-2012
Provisional Peer-Reviewed Toxicity Values for
Acetone Cyanohydrin
(CASRN 75-86-5)
Superfund Health Risk Technical Support Center
National Center for Environmental Assessment
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati, OH 45268

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AUTHORS, CONTRIBUTORS, AND REVIEWERS
CHEMICAL MANAGER
Scott C. Wesselkamper, PhD
National Center for Environmental Assessment, Cincinnati, OH
DRAFT DOCUMENT PREPARED BY
ICF International
9300 Lee Highway
Fairfax, VA 22031
PRIMARY INTERNAL REVIEWERS
Zheng (Jenny) Li, PhD, DABT
National Center for Environmental Assessment, Washington, DC
Anuradha Mudipalli, MSc, PhD
National Center for Environmental Assessment, Research Triangle Park, NC
This document was externally peer reviewed under contract to
Eastern Research Group, Inc.
110 Hartwell Avenue
Lexington, MA 02421-3136
Questions regarding the contents of this document may be directed to the U.S. EPA Office of
Research and Development's National Center for Environmental Assessment, Superfund Health
Risk Technical Support Center (513-569-7300).
li
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TABLE OF CONTENTS
COMMONLY USED ABBREVIATIONS	iv
BACKGROUND	1
DISCLAIMERS	1
QUESTIONS REGARDING PPRTVs	1
INTRODUCTION	2
REVIEW OF POTENTIALLY RELEVANT DATA (CANCER AND NONCANCER)	4
HUMAN STUDIES	8
Oral Exposures	8
Inhalation Exposures	8
ANIMAL STUDIES	8
Oral Exposures	8
Inhalation Exposures	12
OTHER DATA (SHORT-TERM TESTS, OTHER EXAMINATIONS)	20
Tests Evaluating Carcinogenicity, Genotoxicity, and/or Mutagenicity	23
Other Toxicity Studies (Exposures Other Than Oral or Inhalation)	23
Metabolism/Toxicokinetic Studies	23
Short-Term Studies	23
Mode of Action/Mechanistic Studies	23
Immunotoxicity	23
Neurotoxicity	23
DERIVATION 01 PROVISIONAL VALUES	24
DERIVATION OF ORAL REFERENCE DOSES	25
Derivation of Subchronic Provisional RfD (Subchronic p-RfD)	25
Derivation of Chronic Provisional RfD (Chronic p-RfD)	26
DERIVATION OF INHALATION REFERENCE CONCENTRATIONS	26
Derivation of Subchronic Provisional RfC (Subchronic p-RfC)	26
Derivation of Chronic Provisional RfC (Chronic p-RfC)	26
CANCER WEIGHT-OF-EVIDENCE DESCRIPTOR	27
MODE 01 ACTION (Y10A) DISCI SSION	27
DERIVATION OF PROVISIONAL CANCER POTENCY VALUES	27
Derivation of Provisional Oral Slope Factor (p-OSF)	27
Derivation of Provisional Inhalation Unit Risk (p-IUR)	27
APPENDIX A. PROVISIONAL SCREENING VALUES	28
APPENDIX B. DATA TABLES	31
APPENDIX C. BMD OUTPUTS	37
APPENDIX D. REFERENCES	38
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COMMONLY USED ABBREVIATIONS
BMC
benchmark concentration
BMCL
benchmark concentration lower bound 95% confidence interval
BMD
benchmark dose
BMDL
benchmark dose lower bound 95% confidence interval
HEC
human equivalent concentration
HED
human equivalent dose
IUR
inhalation unit risk
LOAEL
lowest-observed-adverse-effect level
LOAELadj
LOAEL adjusted to continuous exposure duration
LOAELhec
LOAEL adjusted for dosimetric differences across species to a human
NOAEL
no-ob served-adverse-effect level
NOAELadj
NOAEL adjusted to continuous exposure duration
NOAELhec
NOAEL adjusted for dosimetric differences across species to a human
NOEL
no-ob served-effect level
OSF
oral slope factor
p-IUR
provisional inhalation unit risk
POD
point of departure
p-OSF
provisional oral slope factor
p-RfC
provisional reference concentration (inhalation)
p-RfD
provisional reference dose (oral)
RfC
reference concentration (inhalation)
RfD
reference dose (oral)
UF
uncertainty factor
UFa
animal-to-human uncertainty factor
UFC
composite uncertainty factor
UFd
incomplete-to-complete database uncertainty factor
UFh
interhuman uncertainty factor
UFl
LOAEL-to-NOAEL uncertainty factor
UFS
subchronic-to-chronic uncertainty factor
WOE
weight of evidence
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PROVISIONAL PEER-REVIEWED TOXICITY VALUES FOR
ACETONE CYANOHYDRIN (CASRN 75-86-5)
BACKGROUND
A Provisional Peer-Reviewed Toxicity Value (PPRTV) is defined as a toxicity value
derived for use in the Superfund Program. PPRTVs are derived after a review of the relevant
scientific literature using established Agency guidance on human health toxicity value
derivations. All PPRTV assessments receive internal review by a standing panel of National
Center for Environment Assessment (NCEA) scientists and an independent external peer review
by three scientific experts.
The purpose of this document is to provide support for the hazard and dose-response
assessment pertaining to chronic and subchronic exposures to substances of concern, to present
the major conclusions reached in the hazard identification and derivation of the PPRTVs, and to
characterize the overall confidence in these conclusions and toxicity values. It is not intended to
be a comprehensive treatise on the chemical or toxicological nature of this substance.
The PPRTV review process provides needed toxicity values in a quick turnaround
timeframe while maintaining scientific quality. PPRTV assessments are updated approximately
on a 5-year cycle for new data or methodologies that might impact the toxicity values or
characterization of potential for adverse human health effects and are revised as appropriate. It is
important to utilize the PPRTV database (http://hhpprtv.ornl.gov) to obtain the current
information available. When a final Integrated Risk Information System (IRIS) assessment is
made publicly available on the Internet (www.epa. gov/iris). the respective PPRTVs are removed
from the database.
DISCLAIMERS
The PPRTV document provides toxicity values and information about the adverse effects
of the chemical and the evidence on which the value is based, including the strengths and
limitations of the data. All users are advised to review the information provided in this
document to ensure that the PPRTV used is appropriate for the types of exposures and
circumstances at the site in question and the risk management decision that would be supported
by the risk assessment.
Other U.S. Environmental Protection Agency (EPA) programs or external parties who
may choose to use PPRTVs are advised that Superfund resources will not generally be used to
respond to challenges, if any, of PPRTVs used in a context outside of the Superfund program.
QUESTIONS REGARDING PPRTVs
Questions regarding the contents and appropriate use of this PPRTV assessment should
be directed to the EPA Office of Research and Development's National Center for
Environmental Assessment, Superfund Health Risk Technical Support Center (513-569-7300).
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INTRODUCTION
Acetone cyanohydrin (C4H7NO; see Figure 1), CAS No. 75-86-5, is a colorless liquid
with an odor of bitter almonds. It is used in the manufacturing of insecticides, as an intermediate
for pharmaceuticals, and as a chemical intermediate for production of methyl methacrylate,
methacrylic acid, and higher methacrylate esters (HSDB, 2011). A table of physicochemical
properties is provided below (see Table 1).
Table 1. Physicochemical Properties of Acetone Cyanohydrin (CASRN 75-86-5)a
Property (Unit)
Value
Boiling point (°C)
95
Melting point (°C)
-19
Density (g/cm3)
0.93
Vapor pressure (kPa at 20°C)
3.0
pH (unitless)
No data
Solubility in water (g/100 mL at 25°C)
Soluble in water (dissociates to form hydrogen cyanide and acetone)
Relative vapor density (air =1)
2.93
Molecular weight (g/mol)
85.1
aWHO (2004).
OH
HjC •*—* — N
ch3
Figure 1. Acetone Cyanohydrin Structure
No Reference Dose (RfD), Reference Concentration (RfC), or cancer assessment for
acetone cyanohydrin is included in the United States Environmental Protection Agency
(U.S. EPA) Integrated Risk Information System (IRIS; U.S. EPA, 2010b) or on the Drinking
Water Standards and Health Advisories List (U.S. EPA, 2009). No RfD or RfC values are
reported in the Health Effects Assessment Summary Tables (HEAST; U.S. EPA 2010a).
Provisional subchronic and chronic oral RfDs have been derived by U.S. EPA as a part of the
Provisional Peer-Reviewed Toxicity Value program (PPRTV) (U.S. EPA, 2004). The RfDs are
based on a subchronic gavage study in Sprague-Dawley rats (Ogrowsky, 1988—laboratory was
Hazelton Laboratories America, Inc.) with a No-Observed-Adverse-Effect Level (NOAEL) of
8.75 mg/kg-day based on death at the Lowest-Ob served-Adverse-Effect Level (LOAEL)
15 mg/kg-day, which is also considered a frank effect level (FEL). The subchronic p-RfD was
3x10" mg/kg-day. This value included a composite uncertainty factor (UFc) of 300 (10 each
for intraspecies variability, interspecies extrapolation, and 3 for a deficient database lacking a
supporting chronic or subchronic study, a developmental toxicity study in a second species, and a
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"3
multi-generation reproduction study). The chronic p-RfD was 3 x 10" mg/kg-day with a UFc of
3000 (10 each for intraspecies variability, interspecies extrapolation, extrapolation from a
subchronic to chronic data, and 3 for a deficient database lacking a supporting chronic or
subchronic study, a developmental toxicity study in a second species, and a multi-generation
reproduction study) (U.S. EPA, 2004). A reevaluation of the Ogrowsky (1988) study for the
current acetone cyanohydrin PPRTV identified 2.5 mg/kg-day as a FEL based on mortality in
both male (2/20) and female rats (2/20).
The Chemical Assessments and Related Activities (CARA; U.S. EPA, 1994) list included
a Health and Environmental Effects Profile (HEEP) for acetone cyanohydrin (U.S. EPA, 1985);
however, the document is unavailable for review. The toxicity of acetone cyanohydrin has not
been reviewed by the Agency for Toxic Substances and Disease Registry (ATSDR, 2010). The
World Health Organization (WHO, 2004) listed an occupational exposure limit (OEL) of
4.7 ppm or 5 mg/m for acetone cyanohydrin as hydrogen cyanide (HCN) along with a skin
notation based on a threshold limit value (TLV) derived by the American Conference of
Governmental Industrial Hygienists (ACGIH, 2008). The National Institute of Occupational
Safety and Health (NIOSH, 2010) listed 4 mg/m3 (15-minute exposure) as a recommended
exposure limit (REL) for acetone cyanohydrin. No OEL was adopted by the Occupational
Safety and Health Administration (OSHA, 2006). The California Environmental Protection
Agency (CalEPA, 2008, 2009) has not derived toxicity values for exposure to acetone
cyanohydrin.
The HEAST (U.S. EPA, 2010a) does not report a cancer weight-of-evidence (WOE)
classification, an oral slope factor, or an inhalation unit risk for acetone cyanohydrin. The
International Agency for Research on Cancer (IARC, 2010) has not reviewed the carcinogenic
potential of acetone cyanohydrin. Acetone cyanohydrin is not included in the 12th Report on
Carcinogens (NTP, 2011). CalEPA (2009) has not derived a quantitative estimate of
carcinogenic potential for acetone cyanohydrin.
Literature searches were conducted on sources published from 1900 through
September 13, 2011 for studies relevant to the derivation of provisional toxicity values for
acetone cyanohydrin, CAS No. 75-86-5. Searches were conducted using U.S. EPA's Health and
Environmental Research Online (HERO) database of scientific literature. HERO searches the
following databases: AGRICOLA; American Chemical Society; BioOne; Cochrane Library;
DOE: Energy Information Administration, Information Bridge, and Energy Citations Database;
EBSCO: Academic Search Complete; GeoRef Preview; GPO: Government Printing Office;
Informaworld; IngentaConnect; J-STAGE: Japan Science & Technology; JSTOR: Mathematics
& Statistics and Life Sciences; NSCEP/NEPIS (EPA publications available through the National
Service Center for Environmental Publications [NSCEP] and National Environmental
Publications Internet Site [NEPIS] database); PubMed: MEDLINE and CANCERLIT databases;
SAGE; Science Direct; Scirus; Scitopia; SpringerLink; TOXNET (Toxicology Data Network):
ANEUPL, CCRIS, ChemlDplus, CIS, CRISP, DART, EMIC, EPIDEM, ETICBACK, FEDRIP,
GENE-TOX, HAPAB, HEEP, HMTC, HSDB, IRIS, ITER, LactMed, Multi-Database Search,
NIOSH, NTIS, PESTAB, PPBIB, RISKLINE, TRI; and TSCATS; Virtual Health Library; Web
of Science (searches Current Content database among others); World Health Organization; and
Worldwide Science. The following databases outside of HERO were searched for health-related
information: ACGIH, ATSDR, CalEPA, U.S. EPA IRIS, U.S. EPA HEAST, U.S. EPA HEEP,
U.S. EPA OW, U.S. EPA TSCATS/TSCATS2, NIOSH, NTP, OSHA, and RTECS.
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REVIEW OF POTENTIALLY RELEVANT DATA
(CANCER AND NONCANCER)
Table 2 provides an overview of the toxicity database for acetone cyanohydrin and
includes all potentially relevant repeated short-term-, subchronic-, and chronic-duration studies.
Principal studies are identified in bold and are labeled PS. The phrase "statistical significance"
used throughout the document indicates ap-walue of <0.05.
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Table 2. Summary of Potentially Relevant Data for Acetone Cyanohydrin (CASRN 75-86-5)
Category
Number of Male/Female,
Strain, Species, Study
Type, Study Duration
Dosimetry"
Critical Effects
NOAEL"
BMDL/
BMCLa
LOAEL'
Reference
(Comments)
Notesb
Human
1. Oral (mg/kg-d)a
Subchronic
ND
NA
Chronic
ND
NA
Developmental
ND
NA
Reproductive
ND
NA
Carcinogenicity
ND
NA
2. Inhalation (mg/m3)a
Subchronic
ND
NA
Chronic
ND
NA
Developmental
ND
NA
Reproductive
ND
NA
Carcinogenicity
ND
NA
Animal
1. Oral (mg/kg-d)a
Subchronic
20/20, Sprague-Dawley,
Rat, gavage, 13 wk
0,2.5, 8.75, 15
Mortality (>10%) in males and
females at all doses; increased
absolute and relative liver weight in
males
NA
NDr
2.5 (FEL)
Ogrowsky
(1988)
NPR
Chronic
50 Albino Rat,
Unspecified strain, sex,
and route of
administration; up to 8 mo
5 mg°
Effects not clearly reported
NDr
NDr
NDr
Motoc et al.
(1971)
PR
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Table 2. Summary of Potentially Relevant Data for Acetone Cyanohydrin (CASRN 75-86-5)
Category
Number of Male/Female,
Strain, Species, Study
Type, Study Duration
Dosimetry"
Critical Effects
NOAEL"
BMDL/
BMCLa
LOAEL'
Reference
(Comments)
Notesb
Chronic
44 Albino Rat, 16 Rabbit,
Unspecified strain, sex,
dosing schedule, and route
of administration; 6 mo
0.00005, 0.0005,
0.005, 1.33
Effects not clearly reported
NDr
NDr
NDr
Shkodich
(1966, as
reported in
U.S. EPA,
1985)
NPR
Developmental
0/25, CD, Rat, gavage,
GDs 6-15
0, 1,3, 10
No treatment-related fetal
malformations or developmental
variations observed in any group
10 (maternal
and
developmental)
NDr
NA
International
Research and
Development
Corporation
(1986)
NPR
Reproductive
ND
NA
Carcinogenicity
ND
NA
2. Inhalation (mg/m3)a
Subchronic
10/10, Sprague-Dawley,
Rat, 6 hr/d, 5 d/wk, 28 d
0, 5.7,18.6,37.0
(extrarespiratory
effects)
Breathing difficulties in males
and females
5.7
NDr
18.6
Monsanto
(1986b)
PS
NPR
15/15, Sprague-Dawley,
Rat, 6 hr/d, 5 d/wk, 14 wk
0,6.3, 17.8,35.9
(extrarespiratory
effects)
No significant effects reported
35.9
NDr
NA
Monsanto
(1986a)
NPR
Chronic
50 Albino Rat,
Unspecified sex, strain; up
to 8 mo
1 mL/84 L air0
Effects not clearly reported
NDr
NDr
NDr
Motoc et al.
(1971)
PR
Developmental
ND
NA
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Table 2. Summary of Potentially Relevant Data for Acetone Cyanohydrin (CASRN 75-86-5)
Category
Number of Male/Female,
Strain, Species, Study
Type, Study Duration
Dosimetry"
Critical Effects
NOAEL"
BMDL/
BMCLa
LOAEL'
Reference
(Comments)
Notesb
Reproductive
0/24, Sprague-Dawley,
Rat, inhalation, 6 hr/d,
7 d/wk, 21 d
0, 9.3,26.5,51.0
(extrarespiratory
effects)
No significant effects reported
51.0
NDr
NA
Monsanto
(1986c)
NPR
15/0, Sprague-Dawley,
Rat, inhalation, 6 hr/d,
5 d/wk, 10 wk
0,6.2, 17.7,35.6
(extrarespiratory
effects)
No significant effects reported
35.6
NDr
NA
Monsanto
(1986d)
NPR
Carcinogenicity
ND
NA
""Dosimetry: All exposure values of long-term exposure (4 weeks and longer) are converted from a discontinuous to a continuous (weekly) exposure. Values for inhalation
(cancer and noncancer), and oral (cancer only) are further converted to an HEC/HED. Values from animal developmental studies are not adjusted to a continuous
exposure.
HECexresp = (ppm x MW ^ 24.45) x (hours per day exposed ^ 24) x (days per week exposed ^ 7) x blood:gas partition coefficient.
NA = not applicable, ND = No data, NDr = Not determined, hr = hour, d = day, wk = week.
bNotes: PS = principal study, PR = peer reviewed, NPR = not peer reviewed.
°Due to lack of clearly stated dosing methods and illegible data tables in the study report, an adjusted daily dose (oral) or HEC (inhalation) is not calculated for this study.
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HUMAN STUDIES
Oral Exposures
The database of literature on the effects of oral exposure of humans to acetone
cyanohydrin is limited to acute accidental exposures, coexposures with other chemicals, or
combined exposure pathways (oral, dermal, and inhalation) (i.e., Sunderman and Kincaid, 1953;
Krefft, 1955; Lang and Stintzy, 1960; Thiess and Hey, 1969; Winter et al., 1989; Sinitsyna,
1993). Because the specific duration and route of exposure are unclear, these studies are
considered inappropriate for deriving a provisional oral reference dose.
Inhalation Exposures
Similarly, the literature database on effects of inhalation exposure of humans to acetone
cyanohydrin are limited to acute accidental and multiple exposure pathways (i.e., Sunderman and
Kincaid, 1953; Krefft, 1955; Lang and Stintzy, 1960; Thiess and Hey, 1969; Winter et al., 1989;
Sinitsyna, 1993). These studies in humans are not considered appropriate for deriving a
provisional inhalation reference concentration because details on the inhalation exposure to
acetone cyanohydrin were not well reported, and the literature describes acute exposures.
ANIMAL STUDIES
Oral Exposures
The effects of oral exposure of animals to acetone cyanohydrin have been evaluated in
one subchronic-duration study (i.e., Ogrowsky, 1988), one chronic-duration study (i.e.,
Motoc et al., 1971), and one developmental study (i.e., International Research and Development
Corporation, 1986). No reproductive or carcinogenicity studies were identified in the literature.
Short-Term Studies
No information is available.
Subchronic-Duration Study
Ogrowsky (1988)
Ogrowsky (1988), from Hazelton Laboratories of America, Inc., conducted an
unpublished, GLP-compliant subchronic oral toxicity study in Sprague-Dawley rats. Male and
female rats (20/sex/dose; Charles River Breeding Laboratories, Inc., Raleigh, North Carolina)
received 0, 2.5, 8.75, or 15 mg/kg-day acetone cyanohydrin in 0.01 N sulfuric acid via gavage
for 13 weeks. The control group received vehicle only. The test material was stated to be
>98% pure, and the stock and dosing solutions were stored in light-restrictive containers during
the study. Animals were 43 days old at study initiation. Males weighed 174.9-231.7 g and
females weighed 130.2-182.3 g at study initiation. The rats were provided Purina Certified
Rodent Chow® and tap water ad libitum and were maintained on a 12-hour light/dark cycle.
The rats were observed for overt signs of toxicity 1 hour after daily dosing and were
checked for mortality or moribundity twice daily. The rats were physically examined weekly
beginning at the initiation of the study. Body weight and food consumption were also recorded
weekly. Ophthalmological examinations were performed prior to study initiation and during the
final week of dosing. Five untreated rats per sex were examined for clinical pathology prior to
study initiation. On Weeks 4 and 13, the first 10 survivors/sex/dose group were also examined
for clinical pathology. Blood samples were collected via the orbital sinus while rats were under
carbon dioxide anesthesia. Clinical pathology included hematological and serum chemistry
examinations. Hematological parameters examined included the following: leukocyte count
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(total and differential), erythrocyte count, hemoglobin, hematocrit, platelet count, reticulocyte
count, and cell morphology. Serum chemistry parameters examined included: sodium,
potassium, chloride, total protein, albumin, calcium, phosphorous, total bilirubin, urea nitrogen,
creatinine, glucose, aspartate aminotransferase (AST), alanine aminotransferase (ALT), globulin,
alkaline phosphatase (ALP), cholesterol, albumin:globulin ratio, and lactate dehydrogenase. All
surviving rats at Week 13 and all rats that died during the study were necropsied. The external
surface, cranial cavity, carcass, external surface of the brain, thoracic, abdominal, and pelvic
cavities and their viscera, tissues and organs of the neck region, and all orifices, were examined.
The following organs were weighed: liver, kidneys, spleen, heart, adrenal glands, the brain with
stem, and testes with epididymides or ovaries. The following tissues were excised and examined
microscopically for histopathology in all rats: gross lesions, lungs, liver, and kidneys. For all
control and high-dose rats and for all rats not surviving until study termination, the following
organs were also examined: all gross lesions, brain with brainstem (medulla/pons, cerebellar
cortex, and cerebral cortex), pituitary, thyroid with parathyroids, thymus, lungs, trachea, heart,
mandibular salivary glands, liver, sternum with bone marrow, mammary gland, thigh
musculature, eyes, skin, epididymides, prostate, seminal vesicles, kidneys, adrenals, pancreas,
testes or ovaries, spleen, aorta, esophagus, stomach (forestomach and glandular), duodenum,
jejunum, ileum, colon, cecum, rectum, urinary bladder, mesenteric lymph node, sciatic nerve,
femur including articular surface, cervical spinal cord, mid-thoracic spinal cord, lumbar spinal
cord, and exorbital lacrimal glands.
Cumulative survival data were analyzed using Life Table Analysis in the National Cancer
Institute Package using Fisher's Exact Test to compare groups. Total body-weight gain, food
consumption, clinical pathology, and organ-weight data were compared between treated and
control rats of the same sex. Food consumption was assessed for Weeks 1-5, 5-9, and 9-13.
These data were first analyzed using Levene's test for homogeneity of variance. Heterogeneous
data were then transformed and retested for homogeneity of variance using the following
transformations, in order, until the transformed data were homogeneous or until none of the
transformations resulted in homogeneous data: log 10, square, square root, reciprocal, angular
(arcsine), or rank transformation. Homogeneous and/or transformed data were then analyzed
using ANOVA. Where statistically significant results were indicated, Dunnett's t-test was used
to assess difference between treated rats and controls, by sex.
The study author reported a statistically significant positive trend in mortality in males.
Ten percent mortality (2/20) was observed in males receiving 2.5 and 8.75 mg/kg-day acetone
cyanohydrin, and 25% mortality (5/20) was observed in males receiving 15 mg/kg-day acetone
cyanohydrin. While there was no statistically significant positive trend in mortality observed in
females, 10% mortality (2/20) was observed in all treated female groups. Importantly, no deaths
were observed in the control group for either males or females. The study authors reported a
statistically significant increase in absolute liver weight (19% increase compared to control) in
males of the 15 mg/kg-day dose group (see Table B. 1). The study author also observed a
statistically significant increase in relative liver weight in males of the 8.75 and 15 mg/kg-day
dose groups; however, these data are illegible and cannot be reported. No other treatment-related
absolute or relative organ weight effects were observed. There were no significant differences in
clinical observations, body-weight gain, food consumption, or the results of ophthalmological
examinations between treated and control rats. For the clinical pathology parameters examined,
the study author did not observe any treatment-related effects. Gross pathology and
histopathology did not reveal any treatment-related effects. Due to frank effects
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(>10% mortality) observed in both male and females at all doses tested, identification of a
NOAEL or LOAEL is precluded for this study.
Chronic-Duration Study
Motoc et al. (1971)
Motoc et al. (1971) conducted a peer-reviewed toxicity study originally published in
French and translated to English. Both oral and inhalation exposures were investigated in this
study. The study authors administered 5 mg acetone cyanohydrin (vehicle and purity not
reported) to 6 groups of 50 albino rats of unspecified strain and sex via "digestive route" twice
per week for 3, 5, or 8 months. The corresponding adjusted daily dose cannot be determined
because the experimental design for the compound administration is not clearly reported. The
study report provided data on the total amount of substance administered per kg/body weight;
however, these data are illegible. Details regarding animal husbandry were not reported. The
study authors did not report whether the study adhered to GLP standards. Based on information
in the study data tables, rats were sacrificed at 3, 5, and 8 months, although this is not explicitly
stated in the experimental methods. At necropsy, blood, stomach, liver, and kidneys were
removed. Biochemical analysis of the blood serum was carried out to determine enzyme activity
of leucine aminopeptidase (LAP), transaminases (ALT and AST), aldolase (Aid), glucose-
6-phosphate dehydrogenase (G6P-D), total proteins, electrophoretic fractions, and glucoproteins.
The study authors also used H&E and VG stains and a lipid histogram made on silica gel to
detect proteins, lipids, mucopolysaccharides, nucleic acids, ATPase, G6P-D, p-glucuronidase,
nonspecific esterase, and dehydrogenases (lactate, succinic, and malate).
The biochemical results were reported in graphs not included in the study document.
Several of these results were mentioned in the discussion, including decreased albumin/globulin
ratio and albumin; changes AST and ALT (direction of change not specified); and increased
y-globulins, serum glucoproteins, P-glucuronidase, LAP, G6P-D, and Aid activity compared to
control; however, the study authors do not clearly specify whether these effects occurred as a
result of oral or inhalation exposure. Furthermore, the timepoint at which the biochemical
parameters were measured is not specified. The study authors concluded that rats in the exposed
group exhibited varying degenerative lesions in the stomach as well as reversible and irreversible
degenerative lesions in the liver and kidney. The study authors did not delineate the meaning of
reversible versus irreversible lesions. Stomach lesions were reported to increase in severity over
the study period whereas liver lesions decreased in reversibility in the last two stages of the
study. Lesions in the kidney were reported to be less severe and irreversible in the last study
stage. The study authors did not specify the number of rats in the treatment groups displaying
any of the noted effects or at which exposure duration the effects occurred. No other effects
were reported. Due to lack of dosing information and poor reporting of methods and results,
identification of a NOAEL or LOAEL is precluded for this study.
Shkodich (1966, as reported in U.S. EPA, 1985)
In an oral toxicity study originally published in Russian, Shkodich (1966) studied the
chronic toxicity of acetone cyanohydrin in 44 albino rats and 16 rabbits given 0.00005, 0.0005,
0.005, and 1.33 mg/kg-day for 6 months (as reported in U.S. EPA, 1985). Details on the sex and
strain of the rats and rabbits used, as well as the route of dose administration and dosing schedule
were not provided. The U.S. EPA (1985) report states that in rats, there were increases in
erythrocytes, reticulocytes and hemoglobin, as well as increased liver and adrenal vitamin C at
1.33 mg/kg-day. Decreased brain sulfhydryl content and decreased serum catalase and
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cholinesterase were also observed at 1.33 mg/kg-day. Changes in serum catalase and
cholinesterase were also reported at 0.0005 mg/kg-day, but the directionality is unknown.
Nervous system effects qualitatively described as "attenuation of the processes of internal
inhibition and certain intensification of the excitatory process" were reported at 0.0005 and
1.33 mg/kg-day. It was not clear if the changes observed at 0.0005 and 1.33 mg/kg-day were
also observed at 0.005 mg/kg-day. In rabbits, a reduced rate of galactose utilization and
decreased serum sulfhydryl concentration was observed at 1.33 mg/kg-day. The study author did
not specify the number of rats or rabbits in the treatment groups displaying any of the noted
effects. Due to lack of dosing information and poor reporting of methods and results,
identification of a NOAEL or LOAEL is precluded for this study.
Developmental Study
International Research and Development Corporation (1986)
In an unpublished, non-peer-reviewed developmental study, International Research and
Development Corporation (1986) investigated the potential teratogenic effects of acetone
cyanohydrin in rats. Seventy-five pregnant Charles River COBS CD rats (25/dose) were
administered single daily gavage doses of 1, 3, or 10 mg/kg-day (5.0 mL/kg volume) of acetone
cyanohydrin (purity not reported) in deionized water vehicle on gestation days (GDs) 6-15.
Doses were calculated using body-weight measurements taken on GDs 6, 9, and 12. A control
group of 25 female rats received deionized water over the same test conditions and period. Rat
body weights were recorded on GDs 0, 6, 9, 12, 16, and 20. Prior to treatment, rats were
observed for mortality and changes in appearance and behavior twice daily and once daily for
clinical signs on GDs 6-20. On GD 20, surviving females were sacrificed, and fetuses were
removed via Cesarean section for teratologic evaluation. Maternal tissues were preserved for
examination of gross findings. The study was reported to adhere to GLP guidelines.
Rats were provided with Purina Certified Rodent Chow #5002 and tap water ad libitum
throughout the study period. Animal rooms were environmentally controlled at approximately
21-23°C and 25-78% humidity. Prior to mating, 131 virgin female Charles River COBS CD
rats were acclimated and observed for changes in appearance and behavior for 29 days. During
acclimation, rats were housed in individual hanging wire-mesh cages. After the acclimation
period, rats were weighed and physically examined for suitability to mate. One male and one
female rat of the same strain and source were housed together for mating. Successfully mated
females were returned to individual cages and assigned to control or treated groups using a block
design.
Mated females were sacrificed on GD 20 to determine the number and location of viable
and nonviable fetuses, early and late resorptions, and total number of implantations and corpora
lutea. Gross necropsies on females included examinations of abdominal and thoracic cavities,
organs, and morphological changes. One hundred litters were weighed, sexed, and examined for
malformations and developmental variations including the palate and eyes. Fetuses were
examined externally, viscerally, and skeletally using the Wilson razor-blade sectioning technique
and Dawson method.
All comparisons of the treatment groups to the control groups were performed at
significance levels ofp < 0.05 andp < 0.01. The study authors used % tests with Yates's
correction and Fisher's exact tests for identifying statistically significant differences in male to
female fetal sex ratios and proportions of litter malformations. Mann-Whitney U-test was used
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to compare the proportion of resorbed and dead fetuses and postimplantation losses. Bartlett's
test was used to determine homogeneity of variances. T-tests were used to calculate equal or
unequal variances.
The study authors reported no maternal deaths in treated and control groups. Differences
in antemortem and necropsy observations were found to be statistically nonsignificant between
dams in the control and treated groups. Clinical observations included hair loss, soft stool, and
scabbing on the nose. Instances of red, swollen hindlimbs were reported in the 1 mg/kg-day dose
group, and lower lip nodules were reported in the 10 mg/kg-day dose group. Control-group
necropsy observations include single instances of hydronephrosis, intestinal worms, and
subcutaneous abdominal mass. Gross lesions were not identified in the treated animals. The
study authors concluded that the decrease in body-weight gain during treatment and GDs 12-16
and 16-20 in the 3 and 10 mg/kg-day dose groups were not treatment related. Body-weight
changes observed in the 1 mg/kg-day dose group during treatment Days 6-15 (GDs 0-20) were
not considered treatment related.
The study authors reported no differences in Cesarean section observations between the
control group and the 1 or 3 mg/kg-day dose groups. Similarly, the number of viable fetuses per
dam, mean postimplantation losses per dam, fetal body weights, and fetal sex distribution were
comparable between the control group and dosed groups. The study authors reported
significantly fewer corpora lutea (p < 0.05) and total implantations (p < 0.01) per dam in the
10 mg/kg-day dose group compared to the control group; however, the study authors did not
consider this effect related to treatment because the values were established prior to compound
administration. Table B.2 shows the mean maternal and fetal observations at Cesarean section.
The study authors reported no significant differences between the control and treated
groups for incidence of fetal malformations and developmental variations. Two to three
incidences of microphthalmia were reported within the control and all three treated groups. The
study authors concluded that the following malformations were not "biologically relevant:"
transposition of great vessels with right-sided aortic arch, interventricular septal defect,
malpositioned heart, malformed lungs, diaphragmatic hernia, vestigial uterine horn, and bent
ribs.
The study authors concluded that orally administered acetone cyanohydrin at dose levels
up to 10 mg/kg-day did not produce a teratogenic response in Charles River COBS CD rats.
Thus, a NOAEL of 10 mg/kg-day (the highest dose tested) is identified from the study.
Reproductive Studies
No information is available.
Carcinogenicity Studies
No information is available.
Inhalation Exposures
The effects of inhalation exposure of animals to acetone cyanohydrin have been
evaluated in two sub chronic-duration studies (i.e., Monsanto 1986a,b), one chronic-duration
study (i.e., Motoc et al., 1971), and two reproductive toxicity studies examining the effect of
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acetone cyanohydrin on fertility (i.e., Monsanto, 1986c,d). No carcinogenicity studies were
identified in the literature.
Short-Term Study
Sunder man and Kinkaid (1953)
Sunderman and Kinkaid (1953) conducted a published acute-duration toxicity study. The
study authors exposed 125 Wistar albino rats of unspecified sex and origin to 250 mL
(-95% purity) of acetone cyanohydrin by placing the material in a saturator comprised of a glass
vessel with a glass disperser immersed to a depth of 13 cm. Air was passed through a calcium
chloride drying tower, through the saturator, and, finally, through a dessicator (total void 8 L) at
23°C. The corresponding adjusted daily dose cannot be determined since the study does not
involve a standard exposure duration or number of days, and the study authors do not report the
total exposure time. Details regarding animal husbandry and handling were not reported. The
study compliance with GLP standards was not reported. The study authors reported animal
collapse after 4 minutes and death after 11 minutes following exposure to air saturated with
acetone cyanohydrin. At approximately 10 minutes, 50% mortality occurred.
Of the 125 animals used in the study, only 15 were deemed to be employed under
sufficiently controlled conditions. These 15 were included in the determination of the average
exposure time required for death by the study authors. No other results were reported.
Identification of a NOAEL or LOAEL is precluded for this study.
Subchronic Studies
Monsanto (1986b)
The study by Monsanto (1986b) is selected as the principal study for derivation of
both the screening subchronic and chronic provisional RfC. In an unpublished, subchronic
inhalation toxicity study conducted by Monsanto (1986b), the study authors exposed groups of
10 male and 10 female Sprague-Dawley rats (Crl:CD®[S-D]BR) to mean analytical
concentrations of 0, 9.2, 29.9, or 59.6 ppm acetone cyanohydrin vapor (purity 99.21%) via
whole-body inhalation exposure for 6 hours/day, 5 days/week, for 28 days. The corresponding
concentrations adjusted for continuous exposure over 24 hours/day, 7 days/week are 5.7, 18.6,
and 37.0 mg/m , respectively. The study authors did not state whether the experiment adhered to
GLP standards. Animals were obtained from the Charles River Breeding Laboratories (Portage,
MI). After a quarantine period (8 days), animals were randomly assigned on the basis of body
weight to each of the four exposure concentrations and housed individually in suspended
stainless steel wire mesh cages in rooms routinely maintained at 70-74°F, 30-65%) relative
humidity, with a 12-hour light/dark cycle. Ralston-Purina Certified Rodent Chow® and tap water
were available ad libitum except during the exposure period. During exposure, the rats were
individually housed in suspended wire mesh cages within Rochester-type stainless steel and glass
-3
exposure chambers (10 m volume).
Animals were examined for gross signs of toxicity prior to and following each exposure.
During exposure, animals were observed between the second and fifth hours to estimate the
percentage of subjects exhibiting signs of toxicity (hypoactivity, hyperactivity, tremors and/or
convulsions, irritation of the eyes and/or nose, and breathing difficulties). Animals were
weighed and examined weekly for gross signs of toxicity. Mortality was checked and recorded
on nonexposure days. Five animals per sex per group (with the exception of high-dose males in
which mortality occurred prior to sacrifice) were randomly selected for each of the two
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scheduled necropsy days. Urine was collected overnight from each animal prior to sacrifice. At
necropsy, blood samples were taken for hematology assays (red blood cell count [RBC], white
blood cell count [WBC], hemoglobin [HGB], hematocrit [HCT], mean corpuscular volume
[MCV], mean corpuscular hemoglobin [MCH], mean corpuscular hemoglobin concentration
[MCHC]) and serum chemistry analysis (alkaline phosphatase [ALP], alanine aminotransferase
[ALT], blood urea nitrogen [BUN], glucose, total protein, lactic dehydrogenase [LDH], LDH
isoenzymes, bilirubin, thiocyanate, T3, T4). Serum proteins were analyzed by electrophoresis.
Urine samples were analyzed for thiocyanate. The study authors conducted gross pathology on
the following tissues: abdominal aorta, adrenals, bone and bone marrow from the femur, brain,
esophagus, eyes with optic nerve, ovaries, testes with epididymides, heart, kidneys, liver, lung
(with mainstem bronchi), lymph nodes, mammary gland (if present), nasal turbinates, pancreas,
pituitary, prostate, salivary gland, sciatic nerve, skeletal muscle, skin, spleen, stomach, thymus,
trachea, thyroid/parathyroid, urinary bladder, uterus, and any gross lesions. Additionally, the
following organs were weighed: adrenals, brain, testes (with epididymides), heart, kidneys, liver,
pituitary, and spleen. The following select tissues from the control and high level exposure
animals were examined microscopically: adrenals, bone and bone marrow, brain, eyes with optic
nerves, intestine (duodenum), liver, lung, trachea, stomach, spleen, kidneys, heart, testes, skeletal
muscle, thyroid, and nasal turbinates. The study authors analyzed differences in body weight,
absolute organ weight, and clinical chemistry data using Dunnett's two-tailed test. Significant
differences in organ-to-body-weight ratios were analyzed using the Mann-Whitney test with
Bonferroni's inequality. Frequency of lesions was compared using Fisher's exact test with
Bonferroni's inequality.
During exposure, irritation of the eyes and/or nose and breathing difficulties were noted
in all animals in the mid- and high-exposure groups, and hypoactivity was observed in all
animals in the high-exposure group. Respiratory distress (4/10), tremors and/or convulsions
(3/10), foaming at the mouth (2/10), and prostrate posture (4/10) were observed in high-exposure
males after the first exposure. Signs of acute toxicity were followed by death in
3/10 high-exposure males. Chromorhinorrhea (5/10 mid-exposure males, 1/10 mid-exposure
females, 8/10 high-exposure males, 1/10 high-exposure females) and irritation around the ear (all
males and females in mid and high-exposure groups) were noted during exposure, as well as
during weekly weigh periods. Mean body weights of high-dose males were lower than controls;
however, these changes were not significant and were within 10% of control values. RBC,
HGB, and MCHC were significantly decreased in high-exposure females (see Table B.3). Urine
thiocyanate levels were statistically significantly elevated in all animals in the mid and
high-exposure groups. Serum thiocyanate levels were also statistically significantly elevated in
all animals in the low- and mid-exposure groups. These markers serve as indicators that acetone
cyanohydrin was absorbed in the animals. The study authors reported that total serum protein
was statistically significantly decreased in the mid- and high-exposure males, and
nonsignificantly decreased at the lowest concentration. Serum T3 levels were elevated, and LDH
levels were decreased significantly in the mid-exposure males. BUN levels were significantly
elevated in the high exposure females. No biologically significant changes were reported in the
serum protein fraction or LDH isoenzyme levels. No gross or microscopic exposure-related
lesions were observed. No significant changes in absolute organ weights or terminal body
weights were observed. The mean liver-to-terminal-body-weight ratio was significantly
increased in mid-exposure males (6% increase compared to control), although this change is
<10% and not considered to be biologically significant (see Table B.4). Based on increased
incidence of clinical signs of breathing difficulties observed in mid-dose males and females, the
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3	3
study authors identified a NOAEL of 5.7 mg/m (5.7 mg/m HEC for extrarespiratory effects).
The corresponding LOAEL is 18.6 mg/m3 (18.6 mg/m3 HEC for extrarespiratory effects) (see
Table B. 3).
Monsanto (1986a)
Monsanto (1986a) conducted an unpublished, 14-week subchronic toxicity study. The
study authors exposed groups of 15 male and 15 female Sprague-Dawley rats (Crl:CD®[S-D]BR)
to mean analytical concentrations of 0, 10.1, 28.6, or 57.7 ppm acetone cyanohydrin (purity
97.79-98.13 %), 6 hours/day, 5 days/week, for 14 weeks, with a minimum of 69 exposure days.
The corresponding concentrations adjusted for continuous exposure over 24 hours/day,
7 days/week are 0, 6.3, 17.8, and 35.9 mg/m3, respectively. The study authors did not state
whether the experiment adhered to GLP standards. Animals were obtained from the Charles
River Breeding Laboratories (Portage, MI). After a quarantine period (10 days), animals were
randomly assigned on the basis of body weight to each of the four exposure groups and housed
individually in suspended stainless steel wire mesh cages in rooms routinely maintained at
70-74°F, 35-60% relative humidity, with a 12-hour light/dark cycle. Purina Laboratory
Certified Rodent Chow® and tap water were available ad libitum except during the exposure
period.
Animals were examined for gross signs of toxicity prior to and following each exposure.
During exposure, animals were observed between the second and fifth hours to estimate the
percentage of subjects exhibiting signs of toxicity (hypoactivity, hyperactivity, tremors and/or
convulsions, irritation of the eyes and/or nose, and breathing difficulties). Animals were
weighed and examined weekly for gross signs of toxicity. Five animals per sex per group were
randomly selected for each of the three scheduled necropsy days. Urine was collected overnight
from each animal prior to sacrifice. At necropsy, blood samples were taken for hematology
(RBC, WBC [total and differential], HGB, HCT, MCV, MCH, MCHC, platelets, reticulocyte
count) and serum chemistry analysis (ALP, AST, ALT, BUN, glucose, total protein, globulin,
albumin, LDH, total bilirubin, thiocyanate, T3, T4, and serum protein electrophoresis). Urine and
serum samples were also analyzed for thiocyanate. The study authors also examined the
following tissues microscopically: abdominal aorta, adrenals, bone and bone marrow from the
femur, brain, esophagus, eyes with optic nerve, ovaries, testes with epididymides, heart, colon,
ileum, kidneys, liver, lung (with mainstem bronchi), lymph nodes, mammary gland (if present),
nasal turbinates, pancreas, pituitary, prostate, salivary gland, sciatic nerve, skeletal muscle, skin,
spinal cord, spleen, stomach, thymus, trachea, thyroid/parathyroid, urinary bladder, uterus
(including cervix). Additionally, the following organs were weighed: adrenals, testes (with
epididymides), heart, kidneys, liver, and spleen. Body weight, absolute organ weight, and
clinical chemistry were analyzed using Dunnett's test. Organ-to-body-weight ratios were
compared to controls using the Mann-Whitney U test with Bonferroni's correction, and
incidence of lesions were compared between treated groups and the control with Fisher's exact
test with Bonferroni's inequality procedure.
The study authors reported no signs of toxicity during the exposure period. Pre and
postexposure observations of swaying movement, ocular and integument conditions, salivation,
and discharges about the nose were not considered exposure related by the study authors. With
the exception of the highest exposure group of males on exposure Day 7, no significant decreases
in mean body weight were observed throughout the study. No animals died during the course of
exposure. Statistically significant changes in hematological parameters (MCHC and MCH for
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males; RBC, HCT, MCV, MCH, MCHC for females) were observed in low- and mid-exposure
animals; however, the study authors did not consider these values to be biologically significant
because the values remained within the normal variation for rats, and no dose-response was
observed. In the mid- and high-exposure groups of females, a dose-related decrease in glucose
levels was observed as well as a significant decrease of globulin and total protein (p = 0.01) in
the low- and mid-exposure females; however, the study authors did not consider these changes to
be biologically significant because the values remained within the normal variation for rats.
There were no significant differences in urinary output. There were no changes in serum protein
fractions or in serum T3 and T4 levels. Urine thiocyanate levels were elevated significantly in the
mid- and high-exposure animals (p = 0.01). Serum thiocyanate levels were increased
significantly in the low- and mid-exposure females (p = 0.01). The presence of thiocyanate
indicated that animals absorbed the test substance. No exposure-related lesions or microscopic
lesions were observed. No changes in mean body weights, fasted body weights, absolute organ
weights, or organ-to-body-weight ratios were observed in any exposure group. Based on the lack
of toxic effects observed at the exposure concentrations tested, the study authors identified a
NOAEL of 35.9 mg/m3 (35.9 mg/m3 HEC for extrarespiratory effects). This NOAEL represents
the highest exposure concentration tested. A LOAEL is not identified from the study.
Chronic-Duration Studies
Motoc et al. (1971)
Motoc et al. (1971) conducted a chronic toxicity study originally published in French and
translated to English. The study authors exposed groups of 50 albino rats of unspecified sex to
acetone cyanohydrin (1 mL/84 L air) via inhalation twice per week (exposure length not
specified) for the duration of the study (up to 8 months). The corresponding human equivalent
concentrations (HECs) cannot be determined because the study does not specify the number of
exposure hours per day and does not clearly indicate the study duration. Details regarding
animal husbandry, animal handling, and the exposure chamber were not reported. Study authors
did not report whether the experiment adhered to GLP standards. Based on information in a
study table, the study authors appear to have sacrificed animals at 3, 5, and 8 months, although
this is not explicitly stated in the experimental methods section. At sacrifice, blood, lungs, liver,
and kidneys were removed. Biochemical analysis was carried out to determine enzyme activity
of leucine aminopeptidase (LAP), transaminases (ALT and AST), aldolase (Aid),
glucose-6-phosphate dehydrogenase (G6P-D), total proteins, electrophoretic fractions, and
glucoproteins. The study authors also used H&E and V.G. stains and a lipid histogram made on
silica gel to detect proteins, lipids, mucopolysaccharides, nucleic acids, ATPase, G6P-D,
P-glucuronidase, nonspecific esterase, and dehydrogenases (lactate, succinic, and malate).
The biochemical results were reported in graphs not included in the study document.
Several of these results are mentioned in the discussion, including decreased albumin/globulin
ratio and albumin; changes AST and ALT (direction of change not specified); and increased
y-globulins, serum glucoproteins, P-glucuronidase, LAP, G6P-D, and Aid activity compared to
control; however it is unclear at which exposure duration, substance, or route of administration
pertains to these results. The study authors concluded that rats in the exposed group exhibited
degenerative lesions in the lung with desquamation of the bronchial epithelium, irreversible
degenerative lesions in the liver, and irreversible lesions in the kidney. The study authors did not
elaborate on the type of pathology that they considered to be irreversible. The study authors did
not specify the number of animals in the exposed group displaying any of the noted effects or at
which exposure lengths the effects occurred. No other effects were reported. Due to lack of
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dosing information and poor reporting of methods and results, a NOAEL or LOAEL are not
determined from this study.
Developmental Studies
No information is available.
Reproductive Studies
Monsanto (1986c)
Monsanto (1986c) conducted an unpublished study that investigated the effects of inhaled
acetone cyanohydrin to female fertility. The study authors exposed groups of 24 female
Sprague-Dawley rats (Crl:CD®[S-D]BR) to mean analytical concentrations of 0, 10.7, 30.4, or
58.6 ppm acetone cyanohydrin vapor (purity 97.79-98.5%) via whole-body inhalation for
6 hours/day, 7 days/week, for 21 days (constant airflow of 1699 L/min in chamber). The
corresponding concentrations adjusted for continuous exposure over 24 hours/day, 7 days/week
-3
are 0, 9.3, 26.5, or 51.0 mg/m . The study's compliance with GLP standards was not reported.
Animals were obtained from the Charles River Breeding Laboratories (Portage, MI). After a
quarantine period (7 days), animals were randomly assigned on the basis of body weight to each
of the four groups, and housed individually in suspended stainless steel wire mesh cages in
rooms routinely maintained at ~72°F, 40-60% relative humidity, with a 12-hour light/dark cycle.
Tap water treated with ion exchange water softener was available ad libitum. Purina Certified
Rodent Chow® No. 5002 was also available ad libitum except during the exposure periods.
Female animals were treated for 21 exposure days and mated to untreated males.
Exposure was then continued until copulation was confirmed or for a maximum of five nights
cohoused with a male without signs of copulation. Females were given a thorough physical
examination and weighed once per week and on GDs 0 and 13. Vaginal smears were performed
on females without confirmed copulation on five consecutive days to evaluate the estrus cycle.
Males were weighed prior to assignment in the study and the week prior to mating. Females
were observed for clinical signs before and after exposures, and all animals were checked twice
daily for gross abnormalities and mortality. Successfully mated females were sacrificed at
GD 13; females without confirmed copulation were sacrificed in the second week after the last
day of cohousing. Gross necropsies on females included examination of the external surface,
tissues and organs of the thoracic and abdominal cavities for lesions, and pregnancy status.
Nidations were classified and counted, and numbers of corpora lutea were recorded for pregnant
females. The ovaries and uteri (including corpus and cervix) were preserved. No necropsies
were performed on males. Body weights were analyzed using Dunnett's test, and counted and
proportional data were evaluated with the Mann-Whitney U-test and Fisher's exact test,
respectively, using Bonferroni's correctional inequality.
No mortalities were reported. The study authors did not report any treatment-related
effects on body weight during exposure or during gestation for pregnant females. Red nasal
discharge or encrustation was observed postexposure and appeared to be concentration-related in
the third week of exposure. No significant clinical signs or treatment-related effects were
reported during the weekly physical examinations or preexposure. No clinical signs of toxicity
were observed during exposure. No significant difference was observed for terminal body
weights, and no treatment-related lesions were reported. No treatment-related fertility effects
were observed at any of the exposure concentrations. Efficiency in mating and pregnancy rates
were similar in all exposure groups and in the control group. No significant differences were
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observed in the pre or postimplantation loss for any of the exposure groups compared to controls.
Five females did not exhibit confirmed copulation. Four of these five females exhibited signs of
estrus during the five-day observation period, while the final female did not exhibit signs of
estrus and was subsequently determined to be pregnant. No other significant effects were
reported. Based on lack of treatment-related effects observed at any exposure concentration, the
study authors identified a NOAEL of 51.0 mg/m3 (51.0 mg/m3 HEC for extrarespiratory effects).
This NOAEL represents the highest exposure concentration tested in the study.
Monsanto (1986d)
Monsanto (1986d) conducted an unpublished study that investigated the effects of
inhaled acetone cyanohydrin to fertility in male rats. The study authors exposed groups of
15 male Sprague-Dawley rats (Crl:CD®[S-D]BR) to mean analytical concentrations of 0, 10,
28.5, or 57.2 ppm acetone cyanohydrin vapor (purity 97.79-98.5%), 6 hours/day, 5 days/week
for 10 weeks. The corresponding HECs are 0, 6.2, 17.7, and 35.6 mg/m for extra-respiratory
effects. The study compliance with GLP standards was not reported. Animals were obtained
from the Charles River Breeding Laboratories (Portage, MI). After a quarantine period
(7-10 days), animals were randomly assigned on the basis of body weight to each of the
4 groups, and housed individually in suspended stainless steel wire mesh cages in rooms
routinely maintained at ~72°F, 40-60% relative humidity, with a 12-hour light/dark cycle. Tap
water treated with ion exchange water softener was available ad libitum. Purina Certified
Rodent Chow® No. 5002 was also available ad libitum except during the exposure periods.
Male animals were treated for 48 days and then mated to untreated virgin females.
Exposure was then continued for an additional 10 days. Males were weighed and given a
thorough physical examination once per week. Females were weighed the week prior to mating
and on GDs 0 and 13. Males were observed for clinical signs before, during, and after
exposures, and all animals were checked twice each day for gross abnormalities and mortality.
Mated females were sacrificed on GD 13 to determine pregnancy status, number of
implantations, and pre and postimplantation loss. At necropsy for females, gross examination of
the external surface and tissues and organs of the thoracic and abdominal cavities was
performed. Total nidations, numbers of resorptions, live implantations, and corpora lutea were
recorded for pregnant females. Males were also sacrificed three weeks after treatment, and gross
necropsies were performed to determine if treatment-related lesions were present. The following
tissues and organs were examined: thoracic, abdominal, and scrotal cavities; testes,
epididymides, prostate glands, and seminal vesicles. The study authors used Dunnett's test, the
Mann-Whitney U test, and Fisher's exact test to analyze body weights, counted data, and
proportional data, respectively. Bonferroni's correction was used to compare multiple groups to
the control where appropriate.
No treatment-related effects were reported for any of the male exposure groups. No
mortality was reported prior to sacrifice. No treatment-related clinical effects were reported for
any of the exposure groups. At necropsy, no significant differences in mean body weight were
reported. No treatment-related lesions were reported in any of the exposure group males. There
was no evidence of treatment-related effects on fertility in any exposure group. Efficiency in
mating and effecting pregnancy in treated groups was not significantly different from controls.
The numbers of live implantations and pre or postimplantation loss were not significantly
different in females mated to exposed males compared to females mated to control males. Based
"3
on the lack of observed toxic effects, the study authors identified a NOAEL of 35.6 mg/m
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(35.6 mg/m HEC for extrarespiratory effects). This NOAEL represents the highest exposure
concentration tested in the study.
Carcinogenicity Studies
No carcinogenicity studies on exposure of animals to acetone cyanohydrin via the
inhalation route were identified in the literature.
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OTHER DATA (SHORT-TERM TESTS, OTHER EXAMINATIONS)
There are some in vitro and in vivo genotoxicity studies for acetone cyanohydrin available. The results of these studies are negative
for mutagenicity (see Table 3 A).
Table 3A. Summary of Acetone Cyanohydrin Genotoxicity
Endpoint
Test System
Dose/Concentration"
Resultsb
Comments
References
Without
Activation
With
Activation
Genotoxicity studies in prokaryotic organisms
Reverse mutation
Salmonella typhimurium strains TA1535,
TA1537, TA1538, TA100, TA98 with or
without S9 activation
6.1, 18.3, 55.0, 165,
495 ng/plate


Not mutagenic to Salmonella
typhimurium
Hazleton
Laboratories
(1986)
SOS repair
induction
ND
Genotoxicity studies in nonmammalian eukaryotic organisms
Mutation
ND
Recombination
induction
ND
Chromosomal
aberration
ND
Chromosomal
malsegregation
ND
Mitotic arrest
ND
Genotoxicity studies in mammalian cells—in vitro
Mutation
Chinese Hamster Ovarian (CHO-K1-BH4)
cells
100, 500, 700, 850,
950 iig/mL


No significant occurrence of
mutants compared to control
Pharmakon
Research
International
(1986)
Chromosomal
aberrations
ND
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Table 3A. Summary of Acetone Cyanohydrin Genotoxicity
Endpoint
Test System
Dose/Concentration"
Resultsb
Comments
References
Without
Activation
With
Activation
Sister chromatid
exchange (SCE)
ND
DNA damage
ND
DNA adducts
ND
Genotoxicity studies in mammals—in vivo
Chromosomal
aberrations
S-D rats, gavage, sacrifice at 6, 12, 24, and
48 hr
0, 1.5, 5,
15 mg/kg-bw


Not clastogenic at the tested
concentrations. No significant
increase in chromosome
aberration frequency or mean
mitotic indices.
Center for
Human
Development
(1986)
Sister chromatid
exchange (SCE)
ND
DNA damage
ND
DNA adducts
ND
Mouse
biochemical or
visible specific
locus test
ND
Dominant lethal
ND
Genotoxicity studies in subcellular systems
DNA binding
ND
aLowest effective dose for positive results, highest dose tested for negative results.
b+ = positive, ± = equivocal or weakly positive, - = negative, ND = no data.
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Table 3B. Other Studies
Test
Materials and Methods
Results
Conclusions
References
Carcinogenicity other
than oral/inhalation
ND
Other toxicity studies
(exposures other than
oral or inhalation)
Male and female (2/2 per dose) New Zealand
white rabbits; percutaneous application of 6,
25, or 40 mg/kg; no control; LD50 values
calculated as 1/2 logio (LD84/LDi6)
Slight or moderate redness, slight
swelling, slight necrosis, lethargy,
labored breathing, convulsions, death.
Acute percutaneous
absorption LD50 was
16 mg/kg (8-28 mg/kg,
95% confidence
interval)
Dow Chemical Company
(1981)
Male (9-10 per group) CD-I mice; i.p.
injection of 0-12 mg/kg
Dyspnea, gasping, ataxia, corneal
opacity, hypothermia, convulsions,
death
Acute i.p. LD50 was
8.7 mg/kg (8-9 mg/kg,
95% confidence
interval)
Willhite and Smith (1981)
Metabolism/toxicokinetic
Male (5) CD-I mice; i.p. injection of 9
mg/kg; sacrificed 5 min after injection
Detectable liver and brain cyanide
levels
Acetone cyanohydrin
distribution displayed
the same characteristics
as its molar equivalent
of free cyanide
Willhite and Smith (1981)
Short-term studies
ND
Mode of action/
mechanistic
ND
Immunotoxicity
ND
Neurotoxicity
ND
ND = no data.
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Tests Evaluating Carcinogenicity, Genotoxicity, and/or Mutagenicity
Acetone cyanohydrin has been evaluated in several in vitro and in vivo genotoxicity (e.g.,
clastogenicity, mutagenicity) tests (see Table 3 A). Results indicated that acetone cyanohydrin
was not mutagenic to S. typhimurium and did not induce mutations in CHO cells in vitro.
Additionally, acetone cyanohydrin did not induce significant increases in chromosome aberration
frequency compared to that of control in a rat in vivo bioassay.
Other Toxicity Studies (Exposures Other Than Oral or Inhalation)
An acute dermal toxicity test on New Zealand white rabbits indicated that acetone
cyanohydrin induced slight swelling at the application site and also induced clinical signs
including labored breathing and lethargy (see Table 3B). A dermal LD50 of 16 mg/kg was
determined by the study authors (Dow Chemical Company, 1981). An acute i.p. injection study
in CD-I mice indicated that acetone cyanohydrin induced clinical signs including labored
breathing, ataxia, corneal opacity, hypothermia, and convulsions. A i.p. LD50 of 8.7 mg/kg was
determined by the study authors (Willhite and Smith, 1981).
Metabolism/Toxicokinetic Studies
Cyanide distribution in the liver and brain were reported by Willhite and Smith (1981)
following i.p. injection of 9 mg/kg acetone cyanohydrin in CD-I mice. Acetone cyanohydrin
distribution displayed the same characteristics as its molar equivalent of free cyanide.
Short-Term Studies
No information is available.
Mode of Action/Mechanistic Studies
No information is available.
Immunotoxicity
No information is available.
Neurotoxicity
No information is available.
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DERIVATION OF PROVISIONAL VALUES
Tables 4 and 5 present a summary of noncancer reference and cancer values, respectively. IRIS data are indicated in the table, if
available.
Table 4. Summary of Noncancer Reference Values for Acetone Cyanohydrin (CASRN 75-86-5)
Toxicity Type (Units)
Species/Sex
Critical Effect
p-Reference
Value
POD
Method
POD
UFC
Principal Study
Subchronic p-RfD (mg/kg-d)
NA
NA
NDr
NA
NDr
NDr
NA
Chronic p-RfD(mg/kg-d)
NA
NA
NDr
NA
NDr
NDr
NA
Screening Subchronic p-RfC
(mg/m3)
Rat/M+F
Increased incidence of
clinical signs of breathing
difficulties
(extrarespiratory effect)
2 x 10"2
NOAEL
5.7
300
Monsanto (1986b)
Screening Chronic p-RfC
(mg/m3)
Rat/M+F
Increased incidence of
clinical signs of breathing
difficulties
(extrarespiratory effect)
2 x 10"3
NOAEL
5.7
3000
Monsanto (1986b)
NA = Not applicable, NDr = Not determinable, M = male, F = female.
Table 5. Summary of Cancer Values for Acetone Cyanohydrin (CASRN 75-86-5)
Toxicity Type
Species/Sex
Tumor Type
Cancer Value
Principal Study
p-OSF
NDr
NDr
NDr
NDr
p-IUR
NDr
NDr
NDr
NDr
NDr = Not determined
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DERIVATION OF ORAL REFERENCE DOSES
Derivation of Subchronic Provisional RfD (Subchronic p-RfD)
No available studies investigating the effects of oral exposure to acetone cyanohydrin in
humans are considered appropriate for derivation of a subchronic p-RfD. The available studies
on oral exposure to acetone cyanohydrin in animals include one unpublished sub chronic-duration
study (i.e., Ogrowsky, 1988), one chronic-duration study (i.e., Motoc et al., 1971), and one
unpublished developmental study (i.e., International Research and Development Corporation,
1986). The only published study on the oral exposure of acetone cyanohydrin to animals is a
chronic-duration oral study by Motoc et al. (1971) that also included evaluation of toxicity
following subchronic-duration (3 months). This study was originally written in French and
translated to English. The information on experimental design and methods of dosing were not
clearly documented. It is unclear what type of oral exposure method was used to treat the
animals (e.g., gavage, drinking water). Additionally, it is not clear whether the biochemical
results section refers to the oral exposure portion of the study or the inhalation exposure, and at
what timepoint these changes occurred. Due to lack of clarity in reporting methods and results,
this study is not selected as the principal study.
The remaining two studies are nonpeer-reviewed and, therefore, are candidates only for
possible development of a screening subchronic p-RfD. In an unpublished study, Ogrowsky
(1988) administered acetone cyanohydrin in 0.01 N sulfuric acid vehicle via daily gavage to
Sprague-Dawley rats (20/sex/dose) at dose levels of 0 (vehicle), 2.5, 8.75, or 15 mg/kg-day for
13 weeks. The study authors evaluated mortality, clinical signs, body weights, food
consumption, ophthalmologic examinations, hematology, clinical chemistry, organ weights,
organ-to-body-weight ratios, gross pathology, and histopathology. In this study, frank effects
(>10% mortality) were reported at all doses tested in both male and female rats. The study
authors determined a probable cause of death/moribundity for only 2 of 15 animals in the
treatment groups that were found dead or were prematurely sacrificed. One male in the
high-dose group likely died due to gavage error, and one male in the low-dose group died of a
rare liver neoplasm. No animals in either the male or female control group died. Although the
histopathology report states that "there were no histopathologic changes in the tissues examined
that could be attributed to the test material" (p. 26), the study authors do not list an alternate
cause of death. The pathology report also states that "most of the animals that died during study
had gross observations of failure of the lung to collapse, red mottling of lung lobes, and/or
frothy, clear fluid in the trachea" (p. 27). Because the study authors do not give an alternate
cause of death for animals in the treatment groups, it is possible that the deaths may be related to
compound administration and, thus, cannot be discounted. Additionally, the first deaths occurred
during Week 4 of treatment, thus indicating that an acute effect of cyanide was not likely to be
the cause of death. Because the LOAEL identified in Ogrowsky (1988) is also a FEL
(2.5 mg/kg-day), this study is not appropriate for deriving a screening subchronic p-RfD.
However, it is notable that the previous PPRTV document prepared in 2004 derived subchronic
and chronic p-RfDs based on this study. In the previous PPRTV assessment, only male mortality
in the high-dose group was considered to be treatment related. There was no explanation as to
why mortality in the low-dose group (2/20 females, 2/20 males) was not considered related to
treatment even though 10% mortality was observed.
The remaining unpublished developmental study, conducted by International Research
and Development Corporation (1986), identified a NOAEL of 10 mg/kg-day, the highest dose
tested in this experiment. Because the NOAEL from this study is not protective of the frank
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effects observed at the lowest dose (2.5 mg/kg-day) in Ogrowsky (1988), a screening subchronic
p-RfD is not derived from this study. Thus, due to lack of appropriate studies, derivation of a
subchronic p-RfD or screening subchronic p-RfD is precluded.
Derivation of Chronic Provisional RfD (Chronic p-RfD)
For reasons stated above, no appropriate studies are available to derive a chronic p-RfD
or screening chronic p-RfD.
DERIVATION OF INHALATION REFERENCE CONCENTRATIONS
Derivation of Subchronic Provisional RfC (Subchronic p-RfC)
No studies investigating the effects of inhalation exposure to acetone cyanohydrin in
humans are considered appropriate for derivation of a subchronic provisional RfC. These studies
are limited by poor exposure characterization, coexposures with other chemicals, or multiple
routes of exposure. The database of inhalation studies on acetone cyanohydrin in animals
includes two unpublished sub chronic-duration studies (i.e., Monsanto 1986a,b), one published
chronic-duration study (i.e., Motoc et al., 1971), and two unpublished reproductive studies (i.e.,
Monsanto 1986c,d). Although the chronic-duration study by Motoc et al. (1971) included
subchronic-duration exposure regimens, the study report is not considered appropriate for
deriving a subchronic p-RfC due to inadequate reporting of methods and results. No
treatment-related effects were noted in the remaining subchronic-duration and reproductive
studies (i.e., Monsanto 1986a,c,d). The most appropriate study for derivation of a subchronic
p-RfC is an unpublished 28-day study in rats conducted by Monsanto (1986b) that identified
increased incidence of clinical signs of breathing difficulties in male and female rats. Because
the data are unpublished, the value is relegated to a screening subchronic p-RfC and is discussed
further in Appendix A.
It is important to note that the laboratory that conducted the 28-day study in rats
(Monsanto, 1986b) also performed three additional studies utilizing similar experimental
conditions (e.g., same strain and species of rat, exposure regimen, exposure chamber, and test
substance purities [ranging from 97.79% to 99.21%]) in which the study authors stated that no
signs of toxicity was observed in exposed rats. These studies included a 14-week exposure of
males and females (Monsanto, 1986a), a female reproductive toxicity study (21-day duration;
Monsanto, 1986c), and a male reproductive toxicity study (10-week duration; Monsanto, 1986d).
3	3
NOAELs identified from these studies ranged from 35.6 to 51.0 mg/m compared to 5.7 mg/m
from the Monsanto (1986b) study based on increased incidence of clinical signs of breathing
difficulties in male and female rats. The study authors do not state any potential reasons for the
observed discrepancies in toxicity between the four studies (e.g., errors in quantifying acetone
cyanohydrin concentrations, compromised animal health, etc.). Therefore, in the absence of any
cogent evidence to discount the 28-day Monsanto (1986b) study, the screening subchronic p-RfC
is derived based on effects observed in this study (see Appendix A).
Derivation of Chronic Provisional RfC (Chronic p-RfC)
Similar to the discussion above, the available published inhalation studies are considered
insufficient for deriving a chronic provisional RfC. The most appropriate study for derivation of
a chronic p-RfC is an unpublished subchronic-duration inhalation study in rats conducted by
Monsanto (1986b). Therefore, the value is relegated to screening, and further discussion of the
screening chronic p-RfC is provided in Appendix A.
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CANCER WEIGHT-OF-EVIDENCE DESCRIPTOR
Table 6 identifies the cancer weight-of-evidence (WOE) descriptor for acetone
cyanohydrin.
Table 6. Cancer WOE Descriptor for Acetone Cyanohydrin
Possible WOE
Descriptor
Designation
Route of entry
(Oral, Inhalation,
or Both)
Comments
"Carcinogenic to
Humans "
NS
NA
NA
"Likely to Be
Carcinogenic to
Humans "
NS
NA
NA
"Suggestive Evidence of
Carcinogenic Potential"
NS
NA
NA
"Inadequate
Information to Assess
Carcinogenic
Potential"
Selected
Both
No studies on the carcinogenic potential of
acetone cyanohydrin in animals or humans via
the oral or inhalation route are available.
"Not Likely to Be
Carcinogenic to
Humans "
NS
NA
NA
NS = Not selected; NA = Not applicable.
MODE OF ACTION (MOA) DISCUSSION
In the case of acetone cyanohydrin, there are insufficient data to determine the mode of
action.
DERIVATION OF PROVISIONAL CANCER POTENCY VALUES
Derivation of Provisional Oral Slope Factor (p-OSF)
No studies on the carcinogenic potential of acetone cyanohydrin to animals or humans
via the oral route are available in the literature; therefore, derivation of a provisional oral slope
factor is precluded.
Derivation of Provisional Inhalation Unit Risk (p-IUR)
No studies on the carcinogenic potential of acetone cyanohydrin to animals or humans
via the inhalation route are available in the literature; therefore, derivation of a provisional
inhalation unit risk is precluded.
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APPENDIX A. PROVISIONAL SCREENING VALUES
For reasons noted in the main document, it is inappropriate to derive provisional
subchronic or chronic p-RfCs for acetone cyanohydrin. However, information is available for
this chemical which, although insufficient to support derivation of a provisional toxicity value,
under current guidelines, may be of limited use to risk assessors. In such cases, the Superfund
Health Risk Technical Support Center summarizes available information in an Appendix and
develops a "screening value." Appendices receive the same level of internal and external
scientific peer review as the PPRTV documents to ensure their appropriateness within the
limitations detailed in the document. Users of screening toxicity values in an appendix to a
PPRTV assessment should understand that there is considerably more uncertainty associated
with the derivation of an appendix screening toxicity value than for a value presented in the body
of the assessment. Questions or concerns about the appropriate use of screening values should
be directed to the Superfund Health Risk Technical Support Center.
DERIVATION OF SCREENING PROVISIONAL INHALATION REFERENCE
CONCENTRATIONS
Derivation of Screening Subchronic Provisional RfC (Subchronic p-RfC)
The study by Monsanto (1986b) is selected as the principal study for derivation of a
screening subchronic p-RfC. The critical endpoint is increased incidence of clinical signs of
breathing difficulties in both male and female Sprague-Dawley rats (see Table B.3). The critical
effect is considered extrarespiratory because breathing difficulties may result from the effect of
cyanide inhibition of cellular respiration and histotoxic anoxia (HSDB, 2011). Acetone
cyanohydrin is thought to release free cyanide during metabolism (HSDB, 2011). Additionally,
the study authors did not observe any gross pathology or histopathological lesions in the airway
or lungs of the animals. Although the study by Monsanto (1986b) is unpublished and not stated
to be conducted under GLP guidelines, it meets the standards of study design and performance,
with numbers of animals, examination of potential toxicity endpoints, and presentation of
information. Details are provided in the "Review of Potentially Relevant Data" section. Among
the available, acceptable studies, this study represents the lowest point of departure (POD) for
developing a screening subchronic p-RfC.
"3
A POD of 5.7 mg/m is determined by the NOAEL/LOAEL approach and is adjusted for
continuous exposure as follows. The high and intermediate doses showed 100% response; the
data are not amenable to BMD analysis.
NOAELadj = NOAELMonsanto, 1986b x (Molecular Weight ^ 24.45) x (Hours per Day ^
24) x (Days Dosed ^ Total Days)
= 9.2 ppm x (85.1 g/mole - 24.45) x (6 - 24) x (5 - 7)
= 5.7 mg/m3
Dosimetric adjustment to a Human Equivalent Concentration (HEC) is calculated for
extrarespiratory effects. In the absence of blood gas partition coefficient information
[H(b/g)a ^ H(b/g)h] for acetone cyanohydrin (a Class 3 gas), a value of 1 is used. Therefore, the
NOAELHec,exresp is calculated as follows:
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NOAELhec,exresp - NOAELadj x [H(b/g)a H(b/g)h]
= 5.7 mg/m3 x 1
= 5.7 mg/m3
The screening subchronic p-RfC is calculated as follows:
Screening Subchronic p-RfC = NOAELhec,exresp ^ UFc
= 5.7 mg/m3 300
= 2 x 1 () 2 mg/m3
The UFC for the screening subchronic p-RfC for acetone cyanohydrin is 300, as explained
in Table A.l.
Table A.l. Uncertainty Factors for Screening Subchronic p-RfC
of Acetone Cyanohydrin
UF
Value
Justification
UFa
3
A UFa of 3 is applied for animal-to-human extrapolation to account for the toxicodynamic
portion of the UFA because the toxicokinetic portion (100 5) is addressed in dosimetric
conversions.
ufd
10
A UFd of 10 is applied because there are no acceptable two-generation reproductive toxicity
studies or developmental toxicity studies via the inhalation route.
UFh
10
A UFh of 10 is applied for intraspecies differences to account for potentially susceptible
individuals in the absence of information on the variability of response to humans.
ufl
1
A UFl of 1 is applied because the POD is developed using a NOAEL.
UFS
1
A UFS of 1 is applied because a subchronic-duration study is used to derive the screening
subchronic provisional value.
UFC
<3000
300
Composite uncertainty factor
Derivation of Screening Chronic Provisional RfC (Chronic p-RfC)
The only available chronic-duration inhalation study by Motoc et al. (1971) is considered
inappropriate for derivation of a screening chronic p-RfC due to inadequate reporting of methods
and results. Therefore, the subchronic-duration inhalation study by Monsanto (1986b) is selected
as the principal study for derivation of a screening chronic p-RfC. The critical endpoints and
POD are the same as the screening subchronic p-RfC. Among the available, acceptable studies,
this study represents the lowest POD for developing a screening chronic p-RfC.
Screening Chronic p-RfC = NOAELHec,exresp UFc
= 5.7 mg/m3 ^3000
= 2 x 10 3 mg/m3
The UFc for the screening chronic p-RfC for acetone cyanohydrin is 3000, as explained
in Table A.2.
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Table A.2. Uncertainty Factors for Screening Chronic p-RfC of Acetone Cyanohydrin
UF
Value
Justification
ufa
3
A UFa of 3 is applied for animal-to-human extrapolation to account for the toxicodynamic
portion of the UFA because the toxicokinetic portion (100 5) is addressed in dosimetric
conversions.
ufd
10
A UFd of 10 is applied because there are no acceptable two-generation reproductive toxicity
studies or developmental toxicity studies via the inhalation route.
UFh
10
A UFh of 10 is applied for intraspecies differences to account for potentially susceptible
individuals in the absence of information on the variability of response to humans.
ufl
1
A UFl of 1 is applied because the POD is developed using a NOAEL.
UFS
10
A UFS of 10 is applied for using data from a subchronic-duration study to assess potential
effects from chronic exposure because data for evaluating response from chronic exposure are
insufficient.
UFC
<3000
3000
Composite uncertainty factor
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APPENDIX B. DATA TABLES
Table B.l. Summary of Liver Weights of Male and Female Sprague-Dawley Rats After
Daily Oral Gavage with Acetone Cyanohydrin for 13 Weeks3
Parameter
Dose Group, mg/kg-d
Male
0
2.5
8.75
15
Original sample size
20
20
20
20
Terminal sample size
20
18
18
15
Necropsy body weight (g)b
554.9 ±55.2
ID
ID
547.4 ±59.8 (99)
Absolute liver weight (g)b
14.03 ± 1.38
13.56 ±2.12 (97)
15.38 ±2.50 (110)
16.64 ± 3.55° (119)
Relative liver weight (%)b
ID
ID
ID0
ID0
Female
0
2.5
8.75
15
Original sample size
20
20
20
20
Terminal sample size
20
18
18
18
Necropsy body weight (g)b
283.7 ±21.8
277.4 ± 25.3 (98)
287.7 ±28.9 (101)
ID
Absolute liver weight (g)b
7.36 ±0.83
7.25 ± 0.73 (99)
7.50 ± 1.26 (102)
7.87 ± 1.12 (107)
Relative liver weight (%)b
2.596 ±0.243
2.620 ±0.217 (101)
ID
2.704 ±0.205 (104)
aOgrowsky (1988).
bValues expressed as mean ± SD (% of control); % is calculated.
Significantly different from control (p < 0.05); Dunnett's test.
ID - Illegible data.
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Table B.2. Summary of Group Mean Maternal and Fetal Observations at Cesarean Section
of COBS CD Rats after Oral Administration of Acetone Cyanohydrin on GDs 6-15a
Parameter
Dose Group, mg/kg-d
0
1
3
10
Maternal sample size
25
25
25
25
No. of gravid animals
25
25
25
25
No. of dams with viable fetuses
25
25
25
25
Viable fetuses per damb
14.1 ±2.24
14.2 ±2.64
13.4 ±2.08
13.6 ± 1.47
Postimplantation loss per damb
1.4 ± 1.41
1 ± 1.17
1.0 ±0.93
0.9 ± 1.01
Total implantations per damb
15.5 ± 1.42
15.1 ±2.07
14.4 ±2.33
14.4 ± 1.33e
Corpora lutea per damb
16.9 ± 1.62
16.8 ±2.18
16.3 ±2.82
15.9 ± 1.54f
Group mean preimplantation loss (%)°
8.3
9.8
11.5
9.1
Group mean postimplantation loss (%)d
8.8
6.3
7.2
6.1
Mean fetal body weightb (g)
3.2 ±0.36
3.3 ±0.24
3.2 ±0.20
3.2 ±0.24
Fetal sex
distribution (%)
Male
52.4
49.2
46.9
52.2
Female
47.6
50.8
53.1
43.8
international Research and Development Corporation (1986).
bValues expressed as mean ± SD.
^reimplantation loss = [(Total No. Corpora Lutea - Total No. Implantations) Total No. Corpora Lutea] x 100.
dPostimplantation loss = [(Total No. Implantations - Total No. Viable Fetuses) Total No. Implantations] x 100.
"Significantly different from control group (p < 0.01); test was not reported.
Significantly different from control group (p < 0.05); test was not reported.
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Table B.3. Serum Chemistry, Urinalysis, and Respiratory Clinical Signs of
Male and Female Sprague-Dawley Rats After Inhalation Exposure to
Acetone Cyanohydrin for 28 Days"
Parameter
Exposure Concentration, ppm
(Human Equivalent Concentration, mg/m3)b
Male
0
9.2 (5.7)
29.9 (18.6)
59.6 (37.0)
Sample size
10
10
10
7
Hematology
(units not
reported)0
RBC
6.43 ± 0.24
6.22 ± 0.57 (97)
6.40 ±0.55 (100)
6.21 ±0.32 (97)
HGB
14.4 ±0.5
13.9 ± 1.6 (97)
14.3 ± 1.3 (99)
13.7 ±0.9 (95)
MCHC
39.8 ±0.5
40.0 ±0.6 (101)
40.3 ±0.5 (101)
39.9 ±0.4 (100)
Thiocyanate0
Serum (mg/dL)
9.6 ±1.1
13.5 ± 1.4° (141)
13.1 ± 1.8e (136)
11.3 ±2.8 (118)
Urine (mg/dL)
31.9 ± 12.2
127.3 ± 38.8 (399)
273.2 ±70.1° (856)
571.6 ±207.4°
(1792)
Incidence of clinical signs of
breathing difficulties
0/10
0/10
10/10
10/10
Female
0
9.2 (5.7)
29.9 (18.6)
59.6 (37.0)
Sample size
10
10
10
10
Hematology
(units not
reported)0
RBC
6.37 ±0.5
6.21 ±0.34 (97)
6.49 ±0.5 (102)
5.78 ± 0.55 d (91)
HGB
13.9 ± 1.2
13.7 ±0.8 (99)
14.2 ± 1.0 (102)
12.5 ± 1.1 d (90)
MCHC
39.6 ±0.7
39.5 ±0.4 (100)
39.9 ±0.8 (101)
38.8 ± 0.4 d (98)
Thiocyanate0
Serum (mg/dL)
12.6 ±4.0
22.7 ± 11.3° (180)
21.1 ±5.4d (167)
17.5 ±4.4 (139)
Urine (mg/dL)
42.4 ± 13.1
125.0 ±27.2 (295)
396.6 ± 177.8°
(935)
555.9 ± 180.4°
(1311)
Incidence of clinical signs of
breathing difficulties
0/10
0/10
10/10
10/10
aMonsanto (1986b).
bDoses are converted from ppm to HEC assuming 25°C and 1 atmosphere using conversion factor MW = 85.1 and
the following equation: HECexresp = (Dose x MW ^ 24.45) x (Hours Exposed per Day ^ 24) x (Days Exposed per
Week 7) x Blood:Gas Partition Coefficient.
°Values expressed as mean ± SD (% of control); % is calculated.
Significantly different from control (p < 0.05); two tailed Dunnett's Test.
"Significantly different from control (p < 0.01); two tailed Dunnett's Test.
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Table B.4. Mean Body Weight of Male and Female Sprague-Dawley Rats After
Inhalation Exposure to Acetone Cyanohydrin for 28 Days3
Parameter
Exposure Concentration, ppm
(Human Equivalent Concentration, mg/m3)b
Male
0
9.2 (5.7)
29.9 (18.6)
59.6 (37.0)
Initial sample size
10
10
10
10
Mean initial body weight0 (g)
243.7 ±7.8
243.0 ±7.60
(100)
243.2 ±7.96
(100)
244.7 ± 13.41
(100)
Final sample size
10
10
10
7
Mean final body weight0 (g)
416.3 ±29.92
420.1 ±25.15
(101)
420.5 ±25.37
(101)
396.6 ±35.75
(95)
Mean liver weight relative to
terminal body weight (%)°
3.045 ±0.045
3.144 ±0.115
(103)
3.249 ±0.057d
(107)
3.263 ±0.159
(107)
Female
0
9.2 (5.7)
29.9 (18.6)
59.6 (37.0)
Sample size
10
10
10
10
Mean body
weight0 (g)
Initial
180.5 ±4.55
179.8 ±4.61
(100)
180.2 ±4.21
(100)
179.0 ±8.88 (99)
Final
236.9 ± 14.87
243.5 ± 16.76
(103)
234.6 ± 12.25
(99)
234.9 ± 14.57
(99)
Mean liver weight relative to
terminal body weight (%)°
2.944 ±0.071
3.092 ±0.065
(105)
3.065 ±0.126
(104)
3.060 ±0.087
(104)
aMonsanto (1986b).
bDoses are converted from ppm to HEC assuming 25°C and 1 atmosphere using conversion factor
MW = 85.1 and the following equation: HECEXresp = (Dose x MW ^ 24.45) x (Hours Exposed per Day ^
24) x (Days Exposed per Week 7) x Blood: Gas Partition Coefficient.
°Values expressed as mean ± SD (% of control); % is calculated.
dSignificantly different from control (p < 0.05); Mann-Whitney U-test with Bonferroni inequality.
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Table B.5. Serum Chemistry and Urinalysis of Male and Female Sprague-Dawley Rats
After Inhalation Exposure to Acetone Cyanohydrin for 14 Weeks"
Parameter
Exposure Group, ppm (Human Equivalent Concentration, mg/m3)b
Male
0
10.1 (6.3)
28.6 (17.8)
57.7 (35.9)
Sample size
15
15
14
15
Serum
chemistry0
Glucose
(mg/dL)
174 ±29.3
174 ±25.8 (100)
178 ±51.1 (102)
192 ±26.9 (110)
Total
Protein
(g/dL)
6.5 ±.031
6.4 ± 0.27 (98)
6.5 ±0.26 (100)
6.7 ±.036 (103)
Thiocyanate
(mg/dL)
0.56 ±0.26
0.83 ± 0.29 (148)d
0.70 ±0.22 (125)
0.58 ±0.34 (103)
Globulin
(g/dL)
3.0 ±0.27
3.0 ±0.18 (100)
3.1 ±0.28 (103)
3.1 ±0.27 (104)
Sample size
15
15
15
15
Urinalysis0
Thiocyanate
(mg/dL)
0.29 ±0.45
3.14 ±2.10 (108)
9.40 ± 5.53 (3241)°
18.27 ±7.94
(6300)°
Female
0
10.1 (6.3)
28.6 (17.8)
57.7 (35.9)
Sample size
15
15
15
15
Serum
chemistry0
Glucose
(mg/dL)
171 ±27.8
162 ±30.8 (95)
144 ± 27.3 (84)d
139± 27.1 (81)°
Total
protein
(g/dL)
7.3 ±0.46
6.9± 0.28 (95)e
6.8 ±0.44 (93)°
7.1 ±0.24 (97)
Thiocyanate
(mg/dL)
0.43 ±0.21
0.86 ±0.18(200)°
0.84 ±0.38 (195)°
0.48 ±0.26 (112)
Globulin
(g/dL)
3.3 ±0.20
3.0 ±0.18(91)°
2.9 ±0.21(88)°
3.1 ±0.16 (94)
Sample size
15
14
15
15
Urinalysis0
Thiocyanate
(mg/dL)
0.01 ±0.05
2.40 ± 1.98 (24,000)
5.60 ±3.88 (56,000)°
11.49 ±6.69
(114,900)°
aMonsanto (1986a).
bDoses are converted from ppm to HEC assuming 25°C and 1 atmosphere using conversion factor MW = 85.1 and
the following equation: HECexresp = (Dose x MW ^ 24.45) x (Hours Exposed per Day ^ 24) x (Days Exposed per
Week 7) x Blood:Gas Partition Coefficient.
°Values expressed as mean ± SD (% control); % is calculated.
Significantly different from control (p < 0.05); two tailed Dunnett's Test.
Significantly different from control (p < 0.01); two tailed Dunnett's Test.
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Table B.6. Incidence of Fertility Effects in Female Sprague-Dawley Rats After
Inhalation Exposure to Acetone Cyanohydrin for 6 Hours/Day for 21 Days"
Parameter0
Exposure Concentration, ppm (Human Equivalent Concentration, mg/m3)b
0.0 (0.0)
10.7 (9.3)
30.4 (26.5)
58.6 (51.0)
Sample Size
22
22
22
23
No. of live implants
14.0 ±0.7
14.6 ±0.5 (104)
14.0 ±0.8 (100)
15.5 ±0.4d (111)
No. of resorptions
0.5 ±0.2
0.5 ±0.2 (100)
1.0 ±0.4 (200)
0.7 ±0.2 (140)
No. of nidations
14.6 ±0.7
15.1 ±0.5 (103)
15.1± 0.7 (103)
16.2 ±0.4d (111)
No. of corpora lutea
15.8 ±0.5
16.1 ±0.5 (102)
16.9 ±0.4 (107)
16.8 ±0.5 (106)
aMonsanto (1986c).
bDoses are converted from ppm to HEC assuming 25°C and 1 atmosphere using conversion factor MW = 85.1 and
the following equation: HECEXresp = (Dose x MW ^ 24.45) x (Hours Exposed per Day ^ 24) x (Days Exposed per
Week 7) x Blood:Gas Partition Coefficient.
°Values expressed as mean number observed in each group ± SE (% of control).
Significantly different from pooled control (p = 0.05) using the Mann-Whitney U test; no significant difference
from control (p = 0.05) using Bonferroni inequality.
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APPENDIX C. BMD OUTPUTS
BMD analysis is not performed for this assessment.
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