Document ID: EPA-HQ-OW-2002-0033-0154
Agency: epa
Document Type: Supporting & Related Material
Title: 
Posted Date: 2003-04-14T04:00Z

United
States
Environmental
Protection
Agency
Office
of
Emergency
and
Remedial
Response
Washington,
DC
20460
Publication
9345.1­
21
EPA/
540/
R­
96/
028
PB96­
963509
June
1996
Superfund
Superfund
Chemical
Data
Matrix
Publication
9345.1­
21
EPA/
540/
R­
96/
028
PB96­
963509
June
1996
Superfund
Chemical
Data
Matrix
Office
of
Emergency
and
Remedial
Response
U.
S.
Environmental
Protection
Agency
Washington,
DC
20460
Additional
copies
of
this
document
may
be
obtained
from:

National
Technical
Information
Service
(
NTIS)
U.
S.
Department
of
Commerce
5285
Port
Royal
Rd.
Springfield,
VA
22161
(
703)
487­
4600
ii
Superfund
Chemical
Data
Matrix
Table
of
Contents
TABLE
OF
CONTENTS
Section
Page
List
of
Figures
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v
1
INTRODUCTION
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1
1.1
Definitions
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1
2
SUPERFUND
CHEMICAL
DATA
MATRIX
DATA
SELECTION
METHODOLOGY
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3
2.1
Hazardous
Substance
Identities
and
SCDM
Protocols
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3
2.2
Toxicity
Information
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5
2.2.1
Reference
Dose
(
RfD)
 
Oral,
Inhalation
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2.2.2
LD
50
 
Oral,
Dermal
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6
2.2.3
LC
50
 
Inhalation
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7
2.3
Carcinogenicity
Information
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8
2.3.1
Cancer
Slope
Factor
(
SF)
and
Weight
of
Evidence
 
Oral,
Inhalation
8
2.3.2
ED
10
and
Weight
of
Evidence
 
Oral,
Inhalation
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9
2.4
Mobility
Information
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2.4.1
Vapor
Pressure
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10
2.4.2
Henry's
Law
Constant
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11
2.4.3
Water
Solubility
 
Nonmetallic
Compounds
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2.4.4
Water
Solubility
 
Metals
and
Metalloids
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13
2.4.5
Soil/
Water
Distribution
Coefficient
(
K
d)
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14
2.5
Persistence
Information
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15
2.5.1
Hydrolysis,
Biodegradation,
and
Photolysis
Half­
Lives
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15
2.5.2
Radioactive
Half­
Life
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15
2.6
Bioaccumulation
Potential
Information
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16
2.6.1
Bioconcentration
Factor
 
Freshwater,
Saltwater
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16
2.6.2
Octanol/
Water
Partition
Coefficient
(
Log
K
ow)
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17
2.7
Ecotoxicity
Parameters
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18
2.7.1
Acute
and
Chronic
Freshwater
and
Saltwater
Criteria
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18
2.7.2
LC
50
 
Freshwater,
Saltwater
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18
2.8
Regulatory
Benchmarks
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18
2.8.1
National
Ambient
Air
Quality
Standards
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19
2.8.2
National
Emissions
Standards
for
Hazardous
Air
Pollutants
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19
iii
Superfund
Chemical
Data
Matrix
Table
of
Contents
TABLE
OF
CONTENTS
(
Continued)

Section
Page
2.8.3
Maximum
Contaminant
Levels
and
Maximum
Contaminant
Level
Goals
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19
2.8.4
FDA
Action
Level
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19
2.8.5
Uranium
Mill
Tailings
Radiation
Control
Act
Standards
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20
2.8.6
Ecological
Based
Benchmarks
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20
2.9
Other
Chemical
Data
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20
2.9.1
Physical
Properties
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20
2.9.2
Logical
Fields
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21
2.9.3
Substitution
Classes
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21
3
CALCULATIONS
IN
SUPERFUND
CHEMICAL
DATA
MATRIX
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23
3.1
Volatilization
Half­
Life
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23
3.1.1
Volatilization
Half­
Life
for
Rivers,
Oceans,
Coastal
Tidal
Waters,
and
the
Great
Lakes
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25
3.1.2
Volatilization
Half­
Life
for
Lakes
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26
3.2
Soil/
Water
Distribution
Coefficients
(
K
d)
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26
3.3
Screening
Concentration
Benchmarks
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27
3.3.1
Screening
Concentrations
for
Drinking
Water
Pathways
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28
3.3.2
Screening
Concentrations
for
the
Surface
Water
Food
Chain
Pathway
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30
3.3.3
Screening
Concentrations
for
Soil
Ingestion
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32
3.3.4
Screening
Concentrations
for
the
Air
Pathway
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34
4
CHEMICAL
DATA,
FACTOR
VALUES,
AND
BENCHMARKS
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36
5
REFERENCES
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41
Appendixes
A
Chemical
Data,
Factor
Values,
and
Benchmarks
for
Chemical
Substances
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.
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A­
1
B­
1
Tables
for
Non­
Radioactive
Hazardous
Substances
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B­
1
B­
2
Tables
for
Radionuclides
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B­
77
C
Synonym
List
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C­
1
iv
Superfund
Chemical
Data
Matrix
List
of
Figures
LIST
OF
FIGURES
Number
Page
1
Page
Heading
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36
2
Toxicity
Section
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36
3
Persistence
Section
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37
4
Physical
Characteristics
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37
5
Mobility
Section
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37
6
Bioaccumulation
Section
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38
7
Other
Data
Section
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38
8
Class
Information
Section
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38
9
Assigned
Factor
Values
Section
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39
10
Benchmarks
Section
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40
v
Superfund
Chemical
Data
Matrix
Introduction
SECTION
1
INTRODUCTION
The
Superfund
Chemical
Data
Matrix
(
SCDM)
is
a
source
for
factor
values
and
benchmark
values
applied
when
evaluating
potential
National
Priorities
List
(
NPL)
sites
using
the
Hazard
Ranking
System
(
HRS;
40
CFR
Part
300,
55
FR
51583).
The
HRS
assigns
factor
values
for
toxicity,
gas
migration
potential,
gas
and
ground
water
mobility,
surface
water
persistence,
and
bioaccumulation
potential
based
on
the
physical,
chemical,
and
radiological
properties
of
Comprehensive
Environmental
Response,
Compensation,
and
Liability
Act
(
CERCLA)
hazardous
substances
present
at
a
site.
Hazardous
substances,
as
defined
for
HRS
purposes,
are
CERCLA
hazardous
substances
plus
CERCLA
pollutants
and
contaminants.
The
HRS
also
assigns
extra
weight
to
targets
with
exposure
levels
to
hazardous
substances
that
are
at
or
above
benchmarks.
These
benchmarks
include
both
risk­
based
screening
concentrations
and
concentrations
specified
in
regulatory
limits
for
the
hazardous
substances
present
at
a
site
for
a
particular
migration
pathway.

SCDM
contains
HRS
factor
values
and
benchmarks
for
hazardous
substances
that
are
frequently
found
at
sites
evaluated
using
the
HRS,
as
well
as
the
physical,
chemical,
and
radiological
data
used
to
calculate
those
values.
The
raw
data
in
SCDM
are
taken
directly
from
literature
sources
or
other
databases
or
are
calculated.
HRS
rules
are
then
applied
to
the
raw
data
to
determine
a
factor
value
or
benchmark.

Section
2
of
this
document
explains
how
data
are
selected
for
inclusion
in
SCDM.
Section
3
describes
how
some
types
of
data
(
i.
e.,
volatilization
half­
lives,
distribution
coefficients,
and
screening
concentrations)
are
internally
calculated
using
data
in
SCDM
and
methodologies
from
published
literature
or
regulatory
guidance
documents.
Section
4
describes
how
SCDM
data,
HRS
factor
values,
and
benchmark
values
are
presented.
The
factor
values
and
benchmark
values
are
listed,
substance
by
substance,
in
Appendix
A.
Appendix
B­
1
contains
the
HRS
factor
values
and
benchmark
tables
(
organized
by
pathway)
for
nonradiological
hazardous
substances.
Appendix
B­
2
contains
similar
tables
for
radionuclides,
and
Appendix
C
contains
a
cross­
reference
index
of
substance
name
synonyms.

1.1
DEFINITIONS
In
addition
to
the
definitions
found
in
Section
1.1
of
the
HRS
(
55
FR
51585­
51587),
the
following
definitions
are
used
in
this
document:

°
Cancer
Risk
Screening
Concentrations:
Substance­
specific
intake
concentrations
that
are
based
on
a
cancer
slope
factor
and
on
estimates
of
a
daily
exposure
level
of
a
1
Superfund
Chemical
Data
Matrix
Introduction
substance.
They
are
used
in
the
HRS
as
benchmarks
in
evaluating
target
populations
actually
exposed
to
carcinogenic
substances
(
see
also
the
definitions
of
"
Slope
Factor"
and
"
Screening
Concentration"
in
Section
1.1
of
the
HRS).

°
Reference
Dose
Screening
Concentrations:
Substance­
specific
intake
concentrations
that
are
based
on
a
noncancer
reference
dose
(
RfD)
and
estimates
of
a
daily
exposure
level
of
a
substance.
They
are
used
in
the
HRS
as
benchmarks
in
evaluating
target
populations
actually
exposed
to
noncarcinogenic
substances
(
see
also
the
definitions
of
"
Reference
Dose"
and
"
Screening
Concentration"
in
Section
1.1
of
the
HRS).

2
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
SECTION
2
SUPERFUND
CHEMICAL
DATA
MATRIX
DATA
SELECTION
METHODOLOGY
This
section
describes
how
the
data
available
in
specified
literature
sources
and
regulatory
guidance
documents
are
selected
for
inclusion
in
SCDM.
Section
2.1
describes
how
to
resolve
ambiguities
that
arise
in
determining
whether
particular
values
apply
to
particular
hazardous
substances.
Sections
2.2
through
2.9
specify
the
references
used
to
obtain
the
data
for
SCDM
and
the
methodologies
used
to
extract
the
data.
The
criteria
described
in
these
sections
were
developed
based
on
the
type
and
quality
of
data
available
in
the
current
SCDM
references;
they
are
not
intended
to
apply
to
all
data
in
general.
As
different
compilations
of
data
become
available,
different
criteria
may
be
considered.

2.1
HAZARDOUS
SUBSTANCE
IDENTITIES
AND
SCDM
PROTOCOLS
Compiling
data
for
SCDM
requires
determining
which
data
reasonably
apply
to
a
hazardous
substance.
Data
in
the
references
cited
in
Sections
2.2
through
2.9
are
sometimes
available
for
classes
and
mixtures
of
hazardous
substances,
but
not
for
the
individual
substances
that
make
up
that
mixture.
Thus,
there
may
be
questions
concerning
whether
the
hazardous
substance
identities
in
the
references
match
the
hazardous
substance
identities
in
SCDM.
This
section
describes
how
ambiguities
in
assigning
particular
values
to
members
of
classes
of
hazardous
substances
in
SCDM
have
been
resolved.

SCDM
contains
generic
values
for
the
following
classes
of
compounds
(
for
chromium
and
chlordane,
these
generic
values
are
used
only
when
the
specific
oxidation
state
or
isomer
concentration
is
not
adequately
known):

°
chromium
(
III
and
VI
oxidation
states)
°
arsenic
(
III
and
V
oxidation
states)
°
mercury
(
elemental
and
inorganic
compounds)
°
polychlorinated
biphenyls
(
PCBs)
(
various
congeners
and
Arochlors)
°
endosulfans
(
I
and
II)
°
chlordane
(
a
and
g
)
.

In
general,
if
any
member
of
these
classes
is
present
at
a
hazardous
substance
site,
it
is
assumed
that
the
most
toxic,
most
persistent,
or
most
bioaccumulative
member
of
the
class
is
present.
In
other
words,
from
among
the
data
given
in
the
specified
references
for
members
of
these
classes,

3
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
SCDM
contains
those
data
resulting
in
the
greatest
HRS
factor
values
(
e.
g.,
lowest
LD
50,
longest
half­
life,
greatest
bioaccumulation
factor).

For
chromium,
if
the
oxidation
state
is
known,
the
generic
values
are
not
used.
For
arsenic,
SCDM
contains
data
for
the
more
mobile
and
toxic
arsenic
III
species.
For
mercury,
SCDM
contains
data
for
elemental
and
inorganic
species.
The
oral
RfD
is
for
mercuric
chloride
and
the
inhalation
RfD
is
for
elemental
mercury
vapor.
Vapor
pressure
and
Henry's
law
constant
are
for
the
elemental
form,
while
the
distribution
coefficient
is
for
the
(+
2)
species.

PCBs
are
represented
solely
as
a
class
of
compounds
in
SCDM,
with
a
single
value
used
regardless
of
the
mixture
of
compounds
identified
at
a
site.
For
PCBs,
chemical
properties
in
SCDM
are
based
on
Arochlor
1254,
which
results
in
the
most
conservative
bioaccumulation/
human
food
chain­
based
factor
values
for
this
group
of
compounds.
Although
the
endosulfans
I
and
II
can
be
distinguished
analytically,
no
data
for
either
isomer
by
itself
are
available
in
the
designated
sources.
All
data
in
SCDM
represent
a
mixture
of
endosulfan
isomers.
SCDM
contains
some
data
for
the
a
and
g
isomers
of
chlordane,
but,
for
the
most
part,
values
represent
a
mixture
of
the
isomers.

For
the
following
classes
of
compounds,
SCDM
contains
values
for
individual
substances:

°
dichlorobenzenes
°
dinitrotoluenes
°
hexachlorocyclohexanes
°
xylenes.

If
no
data
can
be
found
in
the
specified
references
for
an
individual
substance
in
the
class
but
data
are
available
for
the
generic
class,
SCDM
assigns
the
generic
value
to
that
substance.
These
classes
are
all
relatively
small
sets
of
isomers,
which
are
likely
to
occur
as
mixtures.
Furthermore,
these
classes
are
well
defined
in
the
sense
that
the
generic
class
(
e.
g.,
xylenes)
almost
always
refers
to
a
mixture
of
all
members
of
the
class
(
o­,
m­,
and
p­
xylene).
The
expected
similarity
in
chemical
behavior
for
members
of
each
class,
as
well
as
the
likelihood
that
they
will
occur
as
mixtures,
makes
using
data
from
mixtures
reasonable.

SCDM
also
defines
another
class
of
compounds
containing
the
following
polychlorinated
dibenzo­
p­
dioxins
and
polychlorinated
dibenzofurans:

°
2,3,7,8­
tetrachlorodibenzo­
p­
dioxin
(
TCDD)
°
1,2,3,7,8­
pentachlorodibenzo­
p­
dioxin
°
1,2,3,4,7,8­
hexachlorodibenzo­
p­
dioxin
°
1,2,3,6,7,8­
hexachlorodibenzo­
p­
dioxin
°
1,2,3,7,8,9­
hexachlorodibenzo­
p­
dioxin
4
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
°
1,2,3,4,6,7,8­
heptachlorodibenzo­
p­
dioxin
°
2,3,7,8­
tetrachlorodibenzofuran
°
1,2,3,7,8­
pentachlorodibenzofuran
°
2,3,4,7,8­
pentachlorodibenzofuran
°
1,2,3,4,7,8­
hexachlorodibenzofuran
°
1,2,3,6,7,8­
hexachlorodibenzofuran
°
1,2,3,7,8,9­
hexachlorodibenzofuran
°
2,3,4,6,7,8­
hexachlorodibenzofuran
°
1,2,3,4,6,7,8­
heptachlorodibenzofuran
°
1,2,3,4,6,7,9­
heptachlorodibenzofuran.

SCDM
contains
the
cancer
slope
factor
for
2,3,7,8­
tetrachlorodibenzo­
p­
dioxin
(
TCDD)
from
the
Health
Effects
Assessment
Summary
Tables
(
HEAST)
(
EPA,
1995d).
For
all
other
dioxins
and
dibenzofurans,
the
cancer
slope
for
TCDD
is
multiplied
by
the
toxicity
equivalence
factor
(
TEF)
for
each
substance
to
give
an
estimated
slope
factor
that
is
entered
into
SCDM
for
that
substance.
TEF
values
are
obtained
from
Section
3,
Table
2
of
EPA's
Interim
Procedures
for
Estimating
Risks
Associated
with
Mixtures
of
Chlorinated
Dibenzo­
p­
Dioxins
and
Dibenzofurans
(
CDDs
and
CDFs)
and
1989
Update,
(
1989a,
p.
12).
All
members
of
this
class
are
assigned
the
weight
of
evidence
for
TCDD
(
B2).

For
cadmium,
the
Integrated
Risk
Information
System
(
IRIS)
contains
two
RfD
values:
one
for
drinking
water
and
one
for
dietary
exposure.
Since
SCDM
calculates
RfD­
based
screening
concentrations
for
both
drinking
water
and
dietary
exposure,
and
only
one
RfD
per
substance
can
be
entered
into
SCDM,
SCDM
uses
the
more
conservative
drinking
water
RfD
for
cadmium.

The
HRS
specifies
that
a
human
toxicity
factor
of
10,000
be
assigned
to
asbestos
and
lead
compounds.
SCDM
does
this
automatically
within
the
data
manager's
computer
code.

2.2
TOXICITY
INFORMATION
2.2.1
Reference
Dose
(
RfD)
 
Oral,
Inhalation
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
oral
and
inhalation
RfD:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1996a.
Integrated
Risk
Information
System
(
IRIS).
Office
of
Research
and
Development,
Cincinnati,
OH.

5
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
2.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995d.
Health
Effects
Assessment
Summary
Tables
(
HEAST).
EPA
5401R­
95­
036.
Office
of
Research
and
Development,
Washington,
DC.
NTIS
PB95­
921199.

SCDM
prefers
IRIS
data
over
HEAST
data.
Inhalation
data
in
IRIS
are
given
as
reference
concentrations
(
RfCs)
equivalent
to
dose
rather
than
RfDs.
RfCs
are
converted
to
RfDs
by
the
following
equation:

where:
(
1)
RfD
inhal
RfC
×
IR
×
AR
BW
×
100
RfC
=
Reference
concentration
in
air
(
mg/
m3)
IR
=
Inhalation
rate
(
20
m3/
day)
AR
=
Absorption
rate
(%)
BW
=
Adult
body
weight
(
70
kg).

Using
the
default
exposure
assumptions
listed
above,
Equation
(
1)
may
be
simplified
as:

Equation
(
2)
is
used
to
convert
RfCs
to
RfDs
for
use
in
SCDM.
If
IRIS
or
HEAST
does
not
(
2)
RfD
inhal
mg/
kg
day
RfC
inhal
×
AR
×
2.857
×
10
3
.

provide
an
absorption
rate,
it
is
assumed
to
be
100
percent;
this
is
consistent
with
the
convention
described
in
HEAST.

SCDM
also
contains
interim
or
provisional
reference
dose
values
for
certain
hazardous
substances
for
use
in
the
Superfund
site
assessment
program
for
compounds
that
do
not
have
values
in
IRIS
or
HEAST.
These
values
are
identified
by
their
datafile
source,
LIVECHEM,
with
data
sources
described
in
the
LIVECHEM
datafile
comment
field
(
not
displayed
on
screen).
Sources
of
human
toxicity
data
in
LIVECHEM
are
also
given
in:

Research
Triangle
Institute
(
RTI).
1996.
Chemical
Properties
for
SCDM
Development.
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response.
Washington,
DC.

2.2.2
LD
50
 
Oral,
Dermal
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
oral
and
dermal
LD
50:

6
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
1.
C­
E
Environmental,
Inc.
1990.
The
Identification
of
Health
Effects
Data
for
Chemicals
Contained
in
the
Clean
Air
Act
Amendments:
Final
Report
to
Dr.
John
Vanderburg.
U.
S.
Environmental
Protection
Agency,
Research
Triangle
Park,
NC.

2.
American
Conference
of
Governmental
Industrial
Hygienists
(
ACGIH).
1991.
Documentation
of
the
Threshold
Limit
Value
and
Biological
Exposure
Indices.
ACGIH,
Cincinnati,
OH.

3.
National
Institute
for
Occupational
Safety
and
Health
(
NIOSH).
1995.
Registry
of
Toxic
Effects
of
Chemical
Substances
(
RTECS).
NIOSH,
Cincinnati,
OH.

SCDM
contains
the
lowest
value
for
any
mammalian
species
by
the
specified
route
of
exposure
(
i.
e.,
oral
or
dermal)
in
controlled
dose
studies
in
laboratory
animals.
Human
lethality
data
(
i.
e.,
data
from
suicide
and
worker
poisonings)
are
not
used
due
to
the
associated
inaccuracy
of
the
dosage
estimates.
Data
from
former
Eastern
Bloc
countries
(
e.
g.,
former
Soviet
Union)
are
not
used
due
to
the
typically
poor
data
quality.
Only
data
for
exposure
durations
<
24
hours
are
used.
If
an
LD
50
value
is
not
given,
SCDM
uses
an
LD
LO
value:
(
1)
if
it
is
for
the
same
exposure
route,
(
2)
if
it
has
an
exposure
<
24
hours,
and
(
3)
if
it
is
reasonable
relative
to
the
other
values
(
e.
g.,
relative
to
chronic
values)
given
for
that
substance
and
exposure
route.

2.2.3
LC
50
 
Inhalation
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
inhalation
LC
50:

1.
American
Conference
of
Governmental
Industrial
Hygienists
(
ACGIH).
1991.
Documentation
of
the
Threshold
Limit
Value
and
Biological
Exposure
Indices.
ACGIH,
Cincinnati,
OH.

2.
National
Institute
for
Occupational
Safety
and
Health
(
NIOSH).
1995.
Registry
of
Toxic
Effects
of
Chemical
Substances
(
RTECS).
NIOSH,
Cincinnati,
OH.

SCDM
contains
the
lowest
value
for
any
mammalian
species
by
inhalation
in
controlled
dose
studies
in
laboratory
animals.
Human
lethality
data
(
i.
e.,
data
from
suicide
and
worker
poisonings)
are
not
used
due
to
the
associated
inaccuracy
of
the
dosage
estimates.
Data
from
former
Eastern
Bloc
countries
(
e.
g.,
former
Soviet
Union)
are
not
used
due
to
the
typically
poor
data
quality.
Only
data
for
exposure
durations
<
24
hours
are
used.
If
an
LC
50
value
is
not
given,
SCDM
uses
an
LC
LO
value:
(
1)
if
it
is
for
the
same
exposure
route,
(
2)
if
it
has
an
exposure
<
24
hours,
and
(
3)
if
it
is
reasonable
relative
to
the
other
values
(
e.
g.,
relative
to
chronic
values)
given
for
that
substance
and
exposure
route.

7
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
2.3
CARCINOGENICITY
INFORMATION
2.3.1
Cancer
Slope
Factor
(
SF)
and
Weight
of
Evidence
 
Oral,
Inhalation
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
oral
and
inhalation
cancer
slope
factors
and
the
associated
weights
of
evidence:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1996a.
Integrated
Risk
Information
System
(
IRIS).
Office
of
Research
and
Development,
Cincinnati,
OH.

2.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995d.
Health
Effects
Assessment
Summary
Tables
(
HEAST).
EPA­
540/
R­
95­
036.
Office
of
Research
and
Development,
Washington,
DC.
NTIS
PB95­
921199.

SCDM
prefers
IRIS
values
for
nonradioactive
hazardous
substances
over
HEAST
values.
For
radioactive
hazardous
substances,
SCDM
contains
values
from
HEAST.

Data
in
IRIS
for
inhalation
are
given
as
unit
risk
factors
(
URFs),
which
are
related
to
cancer
slope
factors
by
the
following
equation
(
used
for
nonradionuclides
only):

(
3)
SF
inhal
URF
×
BW
×
CF
×
100
IR
×
AR
where:

SF
=
Cancer
slope
factor
(
mg/
kg­
day)­
1
URF
=
Unit
risk
factor
(
µ
g/
m3)­
1
BW
=
Adult
body
weight
(
70
kg)
CF
=
Conversion
factor
(
1,000
µ
g/
mg)
IR
=
Inhalation
rate
(
20
m3/
day)
AR
=
Absorption
rate
(%).

Using
the
assumptions
listed
above
reduces
Equation
(
3)
to
the
following
equation:

(
4)
SF
inhal
(
mg/
kg
day)
1
URF
×
3.50
×
105
AR
.

8
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
Equation
(
4)
is
used
to
convert
unit
risk
to
cancer
slope
factors
for
use
in
SCDM.
If
IRIS
or
HEAST
does
not
provide
an
absorption
rate,
it
is
assumed
to
be
100
percent;
this
is
consistent
with
the
convention
described
in
HEAST.

SCDM
uses
the
weight
of
evidence
from
the
same
reference
that
provides
the
corresponding
slope
factor.
Typically,
IRIS
reports
a
single
weight
of
evidence;
this
value
is
recorded
separately
as
both
the
oral
weight
of
evidence
and
the
inhalation
weight
of
evidence.
In
HEAST,
there
are
usually
two
values
listed,
one
for
oral
and
one
for
inhalation.
Usually
these
values
are
identical;
SCDM
records
each
value
separately.

SCDM
also
contains
interim
or
provisional
cancer
slope
factors
for
certain
hazardous
substances
for
use
in
the
Superfund
site
assessment
program
for
compounds
that
do
not
have
values
in
IRIS
or
HEAST.
These
values
are
identified
by
their
datafile
source,
LIVECHEM,
with
data
sources
given
in
the
LIVECHEM
datafile
comment
field
(
not
displayed
on
screen).
Sources
of
human
toxicity
data
in
LIVECHEM
are
also
given
in:

Research
Triangle
Institute
(
RTI).
1996.
Chemical
Properties
for
SCDM
Development.
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.

2.3.2
ED
10
and
Weight
of
Evidence
 
Oral,
Inhalation
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
oral
and
inhalation
ED
10
and
the
associated
weights
of
evidence:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1988.
Methodology
for
Evaluating
Potential
Carcinogenicity
in
Support
of
Reportable
Quantity
Adjustments
Pursuant
to
CERCLA
Section
102
(
EPA_
ED10).
Office
of
Health
and
Environmental
Assessment,
Washington,
DC
(
EPA/
600/
8­
89/
053).

2.
U.
S.
Environmental
Protection
Agency
(
EPA).
1986.
Superfund
Public
Health
Evaluation
Manual
(
SPHEM).
Office
of
Emergency
and
Remedial
Response,
Washington,
DC
(
EPA/
540/
1­
86/
060).

A
single
potency
factor
(
1/
ED
10)
is
reported
for
oral
and
inhalation
exposure
routes
in
EPA
(
1988).
The
reported
value
is
the
reciprocal
of
ED
10.
Therefore,
the
oral
and
inhalation
ED
10
values
contained
in
SCDM
are
calculated
by
taking
the
reciprocal
of
the
potency
factor
(
i.
e.,
ED
10
=
1/
potency
factor).

9
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
2.4
MOBILITY
INFORMATION
2.4.1
Vapor
Pressure
SCDM
generally
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
vapor
pressure:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995c.
FATE
Database.
Office
of
Research
and
Development,
Athens,
GA.

2.
Syracuse
Research
Corporation
(
SRC).
1995.
CHEMFATE
Database.
SRC,
Syracuse,
NY.

3.
CHEMCALC
values,
calculated
according
to
procedures
in
Lyman
et
al.
(
1990),
as
described
in
Research
Triangle
Institute
(
RTI).
1996.
Chemical
Properties
for
SCDM
Development.
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.

4.
GSC
Corporation.
1990.
CHEMEST
Database.
Developed
for
U.
S.
EPA
Office
of
Pesticides
and
Toxic
Substances,
Washington,
DC.

SCDM
only
uses
measured
values
from
the
FATE
database.
If
an
estimated
or
calculated
value
is
presented
in
FATE,
that
value
is
not
used
in
SCDM.
Within
CHEMFATE,
the
recommended
value
is
preferred.
If
more
than
one
recommended
value
is
available,
SCDM
uses
the
highest
value.
If
a
recommended
value
is
not
available,
SCDM
uses
a
value
measured
at
25
°
C.
If
more
than
one
value
measured
at
25
°
C
is
available,
SCDM
uses
the
highest
one.
If
values
are
not
available
for
measurements
at
25
°
C,
values
determined
within
the
range
of
20
to
30
°
C
are
used.
If
there
is
more
than
one
value
measured
at
the
same
temperature
and
none
is
recommended,
SCDM
uses
the
highest
value.
If
no
temperature
is
specified
in
CHEMFATE
for
all
vapor
pressure
measurements
for
a
substance,
SCDM
uses
the
highest
value.

If
vapor
pressure
values
are
not
available
in
either
FATE
or
CHEMFATE,
the
procedures
described
in
Lyman
et
al.
(
1990)
are
used
to
calculate
vapor
pressure,
which
is
entered
in
the
CHEMCALC
datafile.
RTI
(
1996)
describes
the
use
of
these
procedures
for
specific
hazardous
substances
found
in
SCDM.
If
these
procedures
are
not
applicable,
a
CHEMEST
estimated
value
is
used.

The
above
heirarchy
is
superseded
by
values
in
the
LIVECHEM
datafile
when
a
value
selected
by
the
heirarchy
is
suspect
or
a
measured
value
is
not
available
in
the
SCDM
data
sources.
For
a
particular
chemical,
suspect
values
are
identified
by
comparison
with
other
vapor
pressure
values
in
SCDM
data
sources
or
other
sources
of
chemical
property
data.
The
10
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
LIVECHEM
datafile
includes
a
comment
field
(
not
displayed
onscreen
by
SCDM­
DM)
listing
the
source
of
each
LIVECHEM
value.
RTI
(
1996)
describes
the
selection
of
LIVECHEM
values
and
documents
their
sources.

For
nonmetallic
substances,
if
vapor
pressure
is
not
available,
a
normal
boiling
point
is
obtained
from
the
Handbook
of
Chemistry
and
Physics
(
Lide,
1994)
and
entered
into
BASEDATA.
If
a
boiling
point
is
not
available
from
the
handbook,
a
value
from
the
Merck
Index
(
Merck,
1989)
is
used.
If
the
boiling
point
at
1
atmosphere
(
atm)
is
<
25
°
C,
a
default
vapor
pressure
of
760
Torr
is
entered
into
LIVECHEM
(
i.
e.,
the
compound
is
assumed
to
be
a
gas
at
25
°
C).

If
no
vapor
pressure
is
available
for
a
substance
and
the
normal
boiling
point
is
³
25
°
C,
SCDM
assumes
that
the
substance
is
in
a
particulate
rather
than
a
gaseous
form,
and
no
default
vapor
pressure
value
is
assigned.
This
assumption
is
made
because
the
absence
of
a
vapor
pressure
value
often
reflects
an
extremely
low
and
difficult­
to­
measure
(
under
standard
conditions)
value
for
nongaseous
substances.

2.4.2
Henry's
Law
Constant
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
Henry's
law
constant
(
HLC):

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995c.
FATE
Database.
Office
of
Research
and
Development,
Athens,
GA.

2.
Syracuse
Research
Corporation
(
SRC).
1995.
CHEMFATE
Database.
SRC,
Syracuse,
NY.

3.
CHEMCALC
values,
calculated
according
to
procedures
in
Lyman
et
al.
(
1990)
(
no
values
available
for
June
1996
version).

4.
GSC
Corporation.
1990.
CHEMEST
Database.
Developed
for
U.
S.
EPA
Office
of
Pesticides
and
Toxic
Substances,
Washington,
DC.

SCDM
uses
only
measured
values
from
the
FATE
database.
If
an
estimated
or
calculated
value
is
presented
in
FATE,
that
value
is
not
used
in
SCDM.
Within
CHEMFATE,
the
recommended
value
is
preferred.
If
more
than
one
recommended
value
is
available,
SCDM
uses
the
highest
value.
If
a
recommended
value
is
not
available,
SCDM
uses
a
value
measured
at
25
°
C.
If
more
than
one
value
measured
at
25
°
C
is
available,
SCDM
uses
the
highest
one.
If
values
are
not
available
for
measurements
at
25
°
C,
values
determined
within
the
range
of
20
to
30
°
C
are
used.
If
more
than
one
value
measured
at
the
same
temperature
is
available
and
none
11
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
is
recommended,
SCDM
uses
the
highest
value.
If
temperature
is
specified
in
CHEMFATE
for
all
HLC
measurements
for
a
substance,
SCDM
uses
the
highest
value.

If
HLC
values
are
not
available
in
either
FATE
or
CHEMFATE,
the
procedures
described
in
Lyman
et
al.
(
1990)
are
used
to
calculate
an
HLC.
If
these
procedures
do
not
apply,
a
CHEMEST
estimated
value
is
used.

The
above
heirarchy
is
superseded
by
values
in
the
LIVECHEM
datafile
when
a
value
selected
by
the
heirarchy
is
suspect
or
a
measured
value
is
not
available
in
the
SCDM
data
sources.
For
a
particular
chemical,
suspect
values
are
identified
by
comparison
with
other
Henry's
law
values
in
SCDM
data
sources
or
other
sources
of
chemical
property
data.
The
LIVECHEM
datafile
includes
a
comment
field
(
not
displayed
on
screen
by
SCDM­
DM)
listing
the
source
of
each
LIVECHEM
value.
RTI
(
1996)
describes
the
selection
of
LIVECHEM
values
and
documents
their
sources.

2.4.3
Water
Solubility
 
Nonmetallic
Compounds
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
water
solubility
for
nonmetallic
compounds:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995c.
FATE
Database.
Office
of
Research
and
Development,
Athens,
GA.

2.
Syracuse
Research
Corporation
(
SRC).
1995.
CHEMFATE
Database.
SRC,
Syracuse,
NY.

3.
CHEMCALC
values,
calculated
according
to
procedures
in
Lyman
et
al.
(
1990),
as
described
in
Research
Triangle
Institute
(
RTI).
1996.
Chemical
Properties
for
SCDM
Development.
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.

4.
GSC
Corporation.
1990.
CHEMEST
Database.
Developed
for
U.
S.
EPA
Office
of
Pesticides
and
Toxic
Substances,
Washington,
DC.

SCDM
uses
only
measured
values
from
the
FATE
database.
If
an
estimated
or
calculated
value
is
presented
in
FATE,
that
value
is
not
used
in
SCDM.
Within
CHEMFATE,
the
recommended
value
is
preferred.
If
more
than
one
recommended
value
is
available,
SCDM
uses
the
highest
value.
If
a
recommended
value
is
not
available,
SCDM
uses
a
value
measured
at
25
°
C.
If
more
than
one
value
measured
at
25
°
C
is
available,
SCDM
uses
the
highest
one.
If
values
are
not
available
for
measurements
at
25
°
C,
values
determined
within
the
range
of
20
to
30
°
C
are
used.
If
more
than
one
value
measured
at
the
same
temperature
is
available
and
none
12
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
is
recommended,
SCDM
uses
the
highest
value.
If
no
temperature
is
specified
in
CHEMFATE
for
all
water
solubility
measurements
for
a
substance,
SCDM
uses
the
highest
value.

If
water
solubility
values
are
not
available
in
either
FATE
or
CHEMFATE,
the
procedures
described
in
Lyman
et
al.
(
1990)
are
used
to
calculate
water
solubility.
RTI
(
1996)
describes
the
use
of
these
procedures
for
specific
hazardous
substances
found
in
SCDM.
If
these
procedures
do
not
apply,
a
CHEMEST
estimated
value
is
used.

The
above
heirarchy
is
superseded
by
values
in
the
LIVECHEM
datafile
when
a
value
selected
by
the
heirarchy
is
suspect
or
a
measured
value
is
not
available
in
the
SCDM
data
sources.
For
a
particular
chemical,
suspect
values
are
identified
by
comparison
with
other
water
solubility
values
in
SCDM
data
sources
or
other
sources
of
chemical
property
data.
The
LIVECHEM
datafile
includes
a
comment
field
(
not
displayed
onscreen
by
SCDM­
DM)
listing
the
source
of
each
LIVECHEM
value.
RTI
(
1996)
describes
the
selection
of
LIVECHEM
values
and
documents
their
sources.

2.4.4
Water
Solubility
 
Metals
and
Metalloids
SCDM
uses
data
from
the
following
references
(
in
order
of
preference)
for
water
solubility
of
metals
and
metalloid
compounds:

1.
Weast,
R.
C.
1981.
Handbook
of
Chemistry
and
Physics.
62nd
ed.
CRC
Press,
Cleveland,
OH.
pp.
B­
73
 
B­
166.

2.
Dean,
J.
A.
(
Ed.).
1985.
Lange's
Handbook
of
Chemistry,
13th
ed.
McGraw­
Hill,
New
York.
pp.
5­
7
 
5­
12.

SCDM
contains
geometric
mean
water
solubility
values
that
are
defined
in
the
HRS
as
the
geometric
mean
of
the
highest
and
the
lowest
water
solubility
values
available
for
any
inorganic
compound
containing
the
metal
or
metalloid.
Highest
and
lowest
compound
solubility
values
were
taken
directly
from
Weast
(
1981),
except
for
the
following
low­
solubility
compounds:

°
copper
(
II)
sulfide
°
thallium
(
III)
hydroxide
°
lead
(
II)
sulfide
°
thorium
(
IV)
hydroxide
°
mercury
(
II)
sulfide
°
uranyl
hydroxide
°
nickel
(
II)
sulfide
°
zinc
(
II)
sulfide.
°
silver
(
I)
sulfide
Solubility
values
for
these
compounds
were
calculated
using
the
standard
expression
for
the
solubility
product
(
K
sp)
for
each
compound
and
the
K
sp
value
taken
from
Dean
(
1985).

13
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
2.4.5
Soil/
Water
Distribution
Coefficient
(
K
d)

SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
soil/
water
distribution
coefficients
(
K
d)
values
for
metals:

1.
U.
S.
Envrionmental
Protection
Agency
(
EPA).
1996b.
Soil
Screening
Guidance:
Technical
Background
Document.
EPA/
540/
R95/
128.
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.
NTIS
PB96­
963502.

2.
Baes
III,
C.
F.,
R.
D.
Sharp,
A.
L.
Sjoreen,
and
R.
W.
Shor.
1984.
A
Review
and
Analysis
of
Parameters
for
Assessing
Transport
of
Environmentally
Released
Radionuclides
through
Agriculture.
Oak
Ridge
National
Laboratory,
Oak
Ridge,
TN.
ORNL­
5786.

For
metals,
SCDM
uses
K
d
values
contained
in
EPA
(
1996b)
that
were
estimated
for
the
Soil
Screening
Guidance
using
the
MINTEQ
aqueous
speciation
geochemical
model
or,
when
the
required
thermodynamic
data
are
not
available
in
the
MINTEQ
databases,
using
empirical
pHdependent
relationships
developed
by
EPA's
Office
of
Research
and
Development
Laboratory
in
Athens,
Georgia.
Values
corresponding
to
a
typical
subsurface
pH
(
6.8)
are
used
in
SCDM.
The
derivation
of
these
metal
K
d
values
is
described
in
EPA
(
1996b).

For
organic
hazardous
substances,
SCDM
uses
K
d
values
calculated
using
the
following
relationship
between
K
d
and
K
oc:

K
d
=
K
oc
×
f
oc
(
5)

where:

K
oc
=
Soil
organic
carbon/
water
partition
coefficient
(
mL/
g)
f
oc
=
Fraction
of
organic
carbon
in
soil
(
g
carbon/
g
soil).

The
f
oc
is
assumed
to
be
0.002
g/
g,
which
is
typical
of
subsurface
soils.
This
f
oc
and
the
K
oc
values
used
in
SCDM
are
consistent
with
those
used
for
the
Soil
Screening
Guidance.
SCDM
datafiles
(
SSG_
KD
and
RTI_
ION)
contain
K
d
values
calculated
from
Soil
Screening
Guidance
K
oc
values
for
volatile
organic
compounds,
certain
chlorinated
pesticides,
and
ionizing
organic
compounds.
K
oc
values
for
organic
hazardous
substances
that
ionize
under
subsurface
pH
conditions
(
i.
e.,
pH
=
4.9
to
8.0)
are
derived
by
applying
a
theoretical
relationship
that
accounts
for
both
the
neutral
and
the
ionized
fractions
of
the
compound.
Values
corresponding
to
a
typical
subsurface
pH
(
pH
=
6.8)
are
used
in
SCDM.
The
methodology
used
to
develop
these
K
oc
values
is
described
in
Soil
Screening
Guidance:
Technical
Background
Document.
K
d
values
for
other
organic
compounds
are
calculated
directly
from
Log
K
ow
values
in
SCDM,
as
described
in
14
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
Section
3.2.
RTI
(
1996)
provides
additional
detail
on
the
selection
of
soil/
water
distribution
coefficients
for
organic
compounds
in
SCDM.

2.5
PERSISTENCE
INFORMATION
2.5.1
Hydrolysis,
Biodegradation,
and
Photolysis
Half­
Lives
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
hydrolysis,
biodegradation,
and
photolysis
half­
lives:

1.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995c.
FATE
Database.
Office
of
Research
and
Development,
Athens,
GA.

2.
Howard,
P.
H.,
W.
F.
Jarvis,
W.
M.
Meylan,
and
E.
M.
Michalenko.
1991.
Handbook
of
Environmental
Degradation
Rates
(
FATERATE).
Lewis
Publishers/
CRC
Press,
Boca
Raton,
FL.

3.
Syracuse
Research
Corporation
(
SRC).
1995.
CHEMFATE
Database.
SRC,
Syracuse,
NY.

SCDM
only
uses
measured
values
from
the
FATE
Database.
If
estimated
or
calculated
values
are
presented
in
FATE,
those
values
are
not
used
in
SCDM.
SCDM
only
uses
values
listed
as
"
first­
order"
in
Howard
et
al.
(
1991).
If
high
and
low
values
are
given,
the
highest
values
are
used.
Within
CHEMFATE,
the
recommended
values
are
preferred.
If
more
than
one
recommended
value
is
available,
the
highest
is
selected.
If
a
recommended
value
is
not
available,
SCDM
uses
a
value
measured
at
25
°
C.
If
more
than
one
value
measured
at
25
°
C
is
available,
the
highest
is
selected.
If
values
are
not
available
for
measurements
at
25
°
C,
values
determined
within
the
range
of
20
to
30
°
C
are
used.
If
there
is
more
than
one
value
measured
at
the
same
temperature
and
none
is
recommended,
SCDM
uses
the
highest
value.
If
no
half­
life
value
is
provided
in
CHEMFATE,
the
half­
life
used
in
SCDM
is
calculated
based
on
the
percent
change
over
time
by
assuming
a
first­
order
rate
law.

2.5.2
Radioactive
Half­
Life
SCDM
uses
data
from
the
following
reference
for
radioactive
half­
life:

International
Commission
on
Radiological
Protection
(
ICRP).
1983.
Radionuclide
Transformations
Energy
and
Intensity
of
Emissions.
ICRP
Publication
No.
38.
Pergamon
Press,
New
York.

15
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
If
more
than
one
value
is
given
for
a
single
decay
mode,
SCDM
uses
the
highest
value.
If
values
are
given
for
more
than
one
decay
mode,
the
half­
life
of
the
isotope
is
computed
from
the
values
for
all
decay
modes
according
to
the
following
formula:

t
1/
2
=
1/(
1/
t
1
+
1/
t
2
.
.
.
+
1/
t
n)
(
6)

where:

t
1/
2
=
Half­
life
of
the
isotope
t
1
=
Value
given
for
the
first
decay
mode
t
2
=
Value
given
for
the
second
decay
mode
t
n
=
Value
given
for
the
n­
th
decay
mode.

2.6
BIOACCUMULATION
POTENTIAL
INFORMATION
2.6.1
Bioconcentration
Factor
 
Freshwater,
Saltwater
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
freshwater
and
saltwater
bioconcentration
factors
(
BCFs):

1.
Versar,
Inc.
1990.
Issue
Paper:
Bioaccumulation
Potential
Based
on
Ambient
Water
Quality
Criteria
Documents
(
VER_
BCF).
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.
Contract
No.
68­
W8­
0098.

2.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995a.
Aquatic
Information
Retrieval
(
AQUIRE)
Database.
Environmental
Research
Laboratory,
Duluth,
MN.

SCDM
contains
the
highest
measured
value
from
the
Versar
(
1990)
document
in
preference
to
an
estimated
value
from
the
same
document.
If
no
value
is
reported
in
Versar
(
1990),
the
highest
value
from
AQUIRE
is
used.
All
values
where
no
environment
(
i.
e.,
saltwater
or
freshwater)
is
given
but
that
list
NaCl
as
a
control
are
considered
as
freshwater
values.

SCDM
uses
the
highest
value
from
the
following
aquatic
organisms
to
establish
human
food
chain
threat
BCF
values
(
this
list
includes
only
aquatic
human
food
chain
organisms
in
the
cited
references
and
is
not
meant
to
be
a
complete
list
of
aquatic
human
food
chain
organisms):

°
American
or
Virginia
oyster
°
Atlantic
silverside
°
Asiatic
clam
°
black
crappie
°
Atlantic
salmon
°
black
bullhead
16
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
°
black
mussel
°
mussel
°
blue
crab
°
northern
pike
°
bluegill
°
northern
anchovy
°
brook
trout
°
pilchard
sardine
°
brown
trout
°
pinfish
°
channel
catfish
°
pink
salmon
°
clam
°
rainbow
trout
°
common
bay
mussel
°
red
swamp
crayfish
°
common
mirror
colored
carp
°
rock
bass
°
common
shrimp
°
sauger
°
crayfish
°
shore
crab
°
dungeness
or
edible
crab
°
spot
°
giant
gourami
°
striped
bass
°
gulf
toadfish
°
striped
mullet
°
kiyi
°
swan
mussel
°
lake
trout
(
siscowet)
°
tong
sole
°
lake
whitefish
°
topmouth
gudgeon
(
golden
shiner)
°
mangrove
snapper
°
white
mullet
°
Manila
littleneck
clam
°
white
sand
mussel
Nonhuman
food
chain
aquatic
organisms
are
not
used
for
the
food
chain
BCF.
The
highest
value
from
any
aquatic
organism
mentioned
in
each
reference
is
used
to
establish
environmental
threat
BCF
values,
using
the
same
order
of
preference
described
above.

2.6.2
Octanol/
Water
Partition
Coefficient
(
Log
K
ow)

For
n­
octanol/
water
partition
coefficient
(
K
ow),
SCDM
uses
Log
K
ow
(
also
referred
to
as
Log
P)
data
from
the
following
references
(
listed
in
order
of
preference):

1.
Research
Triangle
Institute
(
RTI).
1996.
Chemical
Properties
for
SCDM
Development.
Prepared
for
U.
S.
EPA
Office
of
Emergency
and
Remedial
Response,
Washington,
DC.

2.
U.
S.
Environmental
Protection
Agency
(
EPA).
1995c.
FATE
Database.
Office
of
Research
and
Development,
Athens,
GA.

3.
Syracuse
Research
Corporation
(
SRC).
1995.
CHEMFATE
Database.
SRC,
Syracuse,
NY.

4.
GSC
Corporation.
1990.
CHEMEST
Database.
Developed
for
U.
S.
EPA
Office
of
Pesticides
and
Toxic
Substances,
Washington,
DC.

17
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
Most
of
the
chemicals
in
SCDM
are
addressed
in
RTI
(
1996).
Many
of
these
values
were
selected
by
EPA's
Office
of
Research
and
Development
in
Athens,
Georgia
(
ORD­
Athens),
from
an
extensive
list
of
measured
values
compiled
by
RTI
and
values
calculated
by
ORD­
Athens
using
the
SPARC
and
CLOGP
computer
programs.
Values
not
selected
by
ORD­
Athens
were
selected
by
RTI
from
a
compilation
of
measured
values.
Compilation
and
selection
procedures
are
described
in
RTI
(
1996).
SCDM
only
uses
measured
values
from
the
FATE
database.
If
estimated
or
calculated
values
are
presented
in
FATE,
those
values
are
not
used
in
SCDM.
SCDM
uses
only
recommended
values
from
the
CHEMFATE
Database.
CHEMEST
estimated
Log
K
ow
values
are
used
if
values
are
not
available
from
the
other
data
sources.

2.7
ECOTOXICITY
PARAMETERS
2.7.1
Acute
and
Chronic
Freshwater
and
Saltwater
Criteria
SCDM
uses
data
from
the
following
reference
for
acute
and
chronic
freshwater
and
saltwater
criteria:

U.
S.
Environmental
Protection
Agency
(
EPA).
1995e.
Water
Quality
Criteria­
Draft
(
the
Silver
Book).
Office
of
Water,
Washington,
DC.

SCDM
uses
only
values
that
are
specifically
stated
as
criteria.
At
this
time,
no
Ambient
Aquatic
Life
Advisory
Concentrations
(
AALACs)
have
been
specified.

2.7.2
LC
50
 
Freshwater,
Saltwater
SCDM
uses
data
from
the
following
reference
for
freshwater
and
saltwater
LC
50
values:

U.
S.
Environmental
Protection
Agency
(
EPA).
1995a.
Aquatic
Information
Retrieval
(
AQUIRE)
Database.
Environmental
Research
Laboratory,
Duluth,
MN.

SCDM
uses
the
lowest,
acute
LC
50
value
found
for
any
aquatic
organism
in
the
specified
environment
with
an
acute
exposure
duration
of
>
1
day
and
£
4
days.
All
LC
50
values
where
no
environment
is
given
but
that
use
NaCl
as
a
control
are
considered
as
freshwater
LC
50
values.
When
no
durations
or
environments
are
given,
LC
50
values
are
not
entered
into
SCDM.

2.8
REGULATORY
BENCHMARKS
The
HRS
assigns
extra
weight
to
targets
with
exposure
levels
to
hazardous
substances
that
are
at
or
above
benchmark
values.
This
section
describes
the
sources
for
certain
regulatory
limits
that
the
HRS
uses
as
health­
based
or
ecological­
based
benchmarks.

18
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
2.8.1
National
Ambient
Air
Quality
Standards
SCDM
uses
data
from
the
following
reference
for
National
Ambient
Air
Quality
Standards
(
NAAQS):

40
CFR
Part
50.
1994.
National
Ambient
Air
Quality
Standards.

2.8.2
National
Emissions
Standards
for
Hazardous
Air
Pollutants
SCDM
uses
the
following
reference
for
National
Emission
Standards
for
Hazardous
Air
Pollutants
(
NESHAP):

40
CFR
Part
61.
1994.
National
Emission
Standards
for
Hazardous
Air
Pollutants.

SCDM
uses
only
values
that
are
reported
in
ambient
concentration
units
(
µ
g/
m3).

2.8.3
Maximum
Contaminant
Levels
and
Maximum
Contaminant
Level
Goals
SCDM
uses
the
following
reference
for
Maximum
Contaminant
Levels
(
MCLs)
and
Maximum
Contaminant
Level
Goals
(
MCLGs):

U.
S.
Environmental
Protection
Agency
(
EPA).
1995b.
Drinking
Water
Regulations
and
Health
Advisories.
Office
of
Water,
Washington,
DC.

SCDM
uses
only
MCLs
that
are
reported
in
units
of
concentration
(
mg/
L
or
µ
g/
L).
SCDM
does
not
contain
MCLs
for
total
trihalomethanes
(
bromoform
+
bromodichloromethane
+
chloroform
+
dibromochloromethane),
asbestos,
radium
isotopes,
gross
a
­
particle
activity,
or
b
­
particle
plus
photon
radioactivity.

SCDM
uses
only
nonzero
MCLGs
that
are
reported
in
units
of
concentration
(
mg/
L
or
µ
g/
L).
For
substances
where
multiple
values
are
listed
due
to
lack
of
consensus
on
appropriate
carcinogen
class,
SCDM
contains
the
lowest
number.
For
substances
where
both
MCLs
and
MCLGs
are
reported
but
are
different,
SCDM
selects
the
MCLG
as
the
lower
of
the
two
values
(
55
FR
51593).

2.8.4
FDA
Action
Level
SCDM
uses
the
following
references
(
listed
in
order
of
preference)
for
Food
and
Drug
Administration
(
FDA)
Action
Levels:

19
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
1.
U.
S.
Food
and
Drug
Administration.
1994.
Changes
in
Action
Levels,
Addendum
to
the
1992
Action
Levels
for
Poisonous
or
Deleterious
Substances
in
Human
and
Animal
Feed.
Center
for
Food
Safety
and
Applied
Nutrition,
Washington,
DC.

2.
U.
S.
Food
and
Drug
Administration.
1992.
Action
Levels
for
Poisonous
or
Deleterious
Substances
in
Human
and
Animal
Feed.
Center
for
Food
Safety
and
Applied
Nutrition,
Washington,
DC.

SCDM
contains
FDA
Action
Levels
for
fish
and
shellfish
only.

2.8.5
Uranium
Mill
Tailings
Radiation
Control
Act
Standards
SCDM
uses
the
following
reference
for
Uranium
Mill
Tailings
Radiation
Control
Act
(
UMTRCA)
standards:

40
CFR
Part
192.
1994.
Uranium
Mill
Tailings
Radiation
Control
Act
Standards.

2.8.6
Ecological
Based
Benchmarks
The
Ambient
Water
Quality
Criteria
and
the
Ambient
Aquatic
Life
Advisory
Concentrations
discussed
in
Section
2.7.1
are
also
used
to
assign
the
ecological­
based
benchmarks.

2.9
OTHER
CHEMICAL
DATA
SCDM
contains
other
chemical
data
and
information
that
are
not
contained
in
the
28
datafiles
previously
discussed.
This
information
is
contained
in
the
BASEDATA
file.

2.9.1
Physical
Properties
SCDM
uses
data
from
the
following
references
(
listed
in
order
of
preference)
for
chemical
formula,
molecular
weight,
density,
boiling
point,
and
melting
point:

1.
Lide,
D.
R.
(
Ed.).
1994.
CRC
Handbook
of
Chemistry
and
Physics.
75th
ed.
CRC
Press,
Boca
Raton,
FL.

2.
Merck.
1989.
The
Merck
Index.
11th
Edition.
S.
Budavari,
Ed.
Merck
&
Co.,
Inc.,
Rahway,
NJ.

Data
are
extracted
directly
from
Section
3.
Physical
Constants
of
Organic
Compounds
and
Section
4.
Properties
of
the
Elements
and
Inorganic
Compounds
in
the
CRC
Handbook.
If
data
are
unavailable
in
the
CRC
Handbook,
or
if
the
conditions
of
the
experiment
are
not
appropriate
20
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
to
standard
conditions
(
e.
g.,
temperature
is
not
in
the
range
of
20
to
30
°
C),
data
from
the
Merck
Index
are
used.

Density
values
are
extracted
(
preferably
in
g/
mL
or
g/
cc)
along
with
the
temperature
at
which
the
density
was
measured
(
preferably
Celsius,
or
°
C).
If
multiple
values
are
available
for
density,
the
value
measured
closest
to
25
°
C
is
selected.

Boiling
point
and
melting
point
are
extracted
(
preferably
in
°
C)
along
with
the
pressure
at
which
boiling
point
was
measured.
Note
that
tests
to
determine
the
melting
point
are
usually
performed
at
the
same
pressure
as
the
boiling
point
tests.
If
multiple
values
are
available,
the
value
measured
closest
to
1
atm
(
760
Torr
or
760
mm
Hg)
is
selected.

2.9.2
Logical
Fields
SCDM
uses
four
logical
(
or
boolean
yes/
no)
flags
to
classify
substances
that
are
entered
into
BASEDATA.

°
Organic
Substance
("
Organic")
 
"
Y"
indicates
that
the
substance
is
organic,
and
"
N"
indicates
an
inorganic
substance.
This
flag
is
used
to
determine
factor
values
for
ground
water
mobility
and
bioaccumulation
potential.

°
Metal­
Containing
Substance
("
Metal
Contain")
 
"
Y"
indicates
that
the
substance
is
a
metal
or
metalloid
or
an
inorganic
compound
that
contains
a
metal
or
metalloid.
"
N"
indicates
that
the
substance
is
not,
or
does
not
contain,
a
metal
or
metalloid.
This
flag
is
used
to
determine
factor
values
for
ground
water
mobility
and
surface
water
persistence.

°
Radioactive
Isotope
("
Radionuclide")
 
"
Y"
indicates
that
the
substance
is
a
radionuclide
or
radioactive
isotope,
and
"
N"
indicates
that
it
is
not.
A
substance
in
SCDM
cannot
be
both
a
radioactive
element
and
a
radioactive
isotope.
This
flag
is
used
to
determine
factor
values
for
human
toxicity,
ecosystem
toxicity,
and
surface
water
persistence.

°
Radioactive
Element
("
Rad.
Element")
 
"
Y"
indicates
that
the
substance
is
a
radioactive
element,
and
"
N"
indicates
that
it
is
not.
This
flag
determines
whether
or
not
the
HRS
factors
and
benchmarks
are
printed
in
Appendix
A.

2.9.3
Substitution
Classes
SCDM
contains
fields
for
three
substitution
classes:
toxicity,
ground
water
mobility,
and
other
data.
For
a
particular
chemical,
a
parent
CAS
number
can
be
entered
for
any
of
these
three
substitution
classes
and
SCDM
automatically
copies
the
relevant
data
from
the
parent
chemical
to
the
chemical
of
interest.
Toxicity
class
data
include
all
toxicity
and
benchmark
data
used
to
21
Superfund
Chemical
Data
Matrix
Data
Selection
Methodology
determine
human
or
ecotoxicity
factor
values.
Ground
water
mobility
class
data
include
water
solubility,
geometric
mean
water
solubility,
and
soil/
water
distribution
coefficient
(
K
d).
"
Other"
class
data
include
hydrolysis,
biodegredation,
photolysis,
and
volatilization
half­
lives,
as
well
as
BCF
and
Log
K
ow.

Currently
two
groups
of
substances
inherit
data
from
a
parent
substance:
metals
and
radioactive
substances.
Generally,
metal­
containing
substances
inherit
data
for
the
ground
water
mobility
class
with
the
elemental
metal
as
the
class
parent.
Radioactive
isotopes
may
inherit
data
from
their
primary
radioactive
element
for
the
ground
water
and
"
other"
classes.

22
Superfund
Chemical
Data
Matrix
Calculations
SECTION
3
CALCULATIONS
IN
SUPERFUND
CHEMICAL
DATA
MATRIX
3.1
VOLATILIZATION
HALF­
LIFE
SCDM
estimates
volatilization
half­
life
in
surface
water
for
organic
substances
using
Equation
15­
12
from
Thomas
(
1990).
In
this
method,
the
volatilization
half­
life
(
t
½
)
can
be
expressed
as
follows,

(
7)
t
1/
2
Z
×
ln
2
K
L
hr
where:

Z
=
Mean
water
body
depth
(
cm)
K
L
=
Overall
liquid­
phase
mass
transfer
coefficient.

The
following
expression
gives
the
overall
liquid­
phase
mass
transfer
coefficient:

(
8)
K
L
(
H/
RT)
k
g
×
k
1
(
H/
RT)
k
g
k
1
cm/
hr
where:

H
=
Henry's
law
constant
(
atm
·
m3/
mol)
R
=
Universal
gas
constant
(
8.2
×
10­
5
atm
·
m3/
mol
·
K)
T
=
Temperature
(
K
;
°
C
+
273)
k
g
=
Gas­
phase
exchange
coefficient
k
l
=
Liquid­
phase
exchange
coefficient.

The
gas­
phase
exchange
coefficient
expression
depends
on
the
molecular
weight
(
MW)
of
the
compound.
If
MW
is
<
65
g/
mol,
the
following
equation
is
used:

(
9)
k
g
3,000
×
(
18/
MW)
1/
2
cm/
hr
.

23
Superfund
Chemical
Data
Matrix
Calculations
If
MW
is
³
65
g/
mol,
the
following
equation
is
used:

(
10)
k
g
1,137.5
×
(
V
wind
V
curr)
×
(
18/
MW)
1/
2
cm/
hr
where:

V
wind
=
Wind
velocity
(
m/
sec)
V
curr
=
Current
velocity
(
m/
sec).

The
liquid­
phase
exchange
coefficient
expression
also
depends
on
the
molecular
weight
of
the
compound.
If
MW
is
<
65
g/
mol,
the
following
equation
is
used:

(
11)
k
1
20
×
(
44/
MW)
1/
2
cm/
hr
.

If
MW
is
³
65
g/
mol,
the
expression
also
depends
on
the
wind
and
current
velocities;
the
following
equation
is
used
when
V
wind
is
£
1.9
m/
sec
and
MW
is
³
65
g/
mol:

(
12)
k
1
23.51
×
(
V
0.969
curr
/
Z0.673)
×
(
32/
MW)
1/
2
cm/
hr
.

The
following
equation
is
used
when
V
wind
is
>
1.9
m/
sec
and
£
5
m/
sec,
and
MW
is
³
65
g/
mol:

(
13)
k
1
23.51
×
(
V
0.969
curr
/
Z0.673)
×
(
32/
MW)
1/
2
e
0.526(
V
wind
1.9)
cm/
hr
.

No
liquid­
phase
exchange
coefficient
equation
is
provided
in
Thomas
(
1990)
for
wind
velocities
>
5
m/
sec.

Combining
Equations
(
7),
(
8),
(
9),
and
(
11)
into
a
single
equation
for
estimating
volatilization
half­
life
(
t
1/
2)
for
compounds
with
MW
<
65
g/
mol
gives
the
following
equation:

(
14)
t
1/
2
Z
×
ln2
×
{
[(
1/
20)
×
(
MW/
44)
1/
2]
[(
RT/
H
×
3,000)
×
(
MW/
18)
1/
2]}
hr
.

The
following
equation,
combining
Equations
(
7),
(
8),
(
10),
and
(
12),
can
be
used
to
estimate
the
volatilization
half­
life
(
t
1/
2)
for
compounds
with
MW
³
65
g/
mol
if
the
wind
velocity
is
£
1.9
m/
sec:

24
Superfund
Chemical
Data
Matrix
Calculations
The
following
equation,
combining
Equations
(
7),
(
8),
(
10),
and
(
13),
can
be
used
to
estimate
(
15)
t
1/
2
Z
×
ln2
×
{
[(
Z
0.673/
23.51
×
V
0.969
curr
)
×
(
MW/
32)
1/
2]

[(
RT/
H
×
1,137.5)
×
(
V
wind
V
curr)
×
(
MW/
18)
1/
2]}
hr
.

the
volatilization
half­
life
(
t
1/
2)
for
compounds
with
MW
³
65
g/
mol
if
the
wind
velocity
is
>
1.9
m/
sec
and
£
5
m/
sec:

If
H
is
<
10­
7
atm
·
m3/
mol,
the
substance
is
less
volatile
than
water
and
its
concentration
will
(
16)
t
1/
2
Z
×
ln2
×
{
[(
Z
0.673/
23.51
×
V
0.969
curr
)
×
(
MW/
32)
1/
2]
e
0.526(
1.9
V
wind)

[(
RT/
H
×
1,137.5)
×
(
V
wind
V
curr)
×
(
MW/
18)
1/
2]}
hr
.

increase
as
the
water
evaporates.
The
substance
is
considered
essentially
nonvolatile
(
Thomas,
1990,
p.
15­
15)
and
no
volatilization
half­
life
is
estimated
for
rivers
or
lakes.

3.1.1
Volatilization
Half­
Life
for
Rivers,
Oceans,
Coastal
Tidal
Waters,
and
the
Great
Lakes
In
order
to
calculate
the
volatilization
half­
life
for
rivers,
oceans,
coastal
tidal
waters,
and
the
Great
Lakes,
the
mean
water
body
depth
is
taken
as
100
cm,
the
temperature
as
298
K,
the
wind
velocity
as
5
m/
sec,
and
the
current
velocity
as
1
m/
sec.
Using
these
values,
Equations
(
14)
and
(
16)
reduce
to
the
following:

°
MW
<
65
g/
mol
t
1/
2
=
2.89
×
{
[
0.05
×
(
MW/
44)
1/
2]
+
[(
8.1
×
10­
6/
H)
×
(
MW/
18)
1/
2]}
days
(
17)

°
MW
³
65
g/
mol
t
1/
2
=
2.89
×
{
[
0.185
×
(
MW/
32)
1/
2]
+
[(
3.6
×
10­
6/
H)
×
(
MW/
18)
1/
2]}
days
(
18)

where
H
=
Henry's
law
constant
(
atm
·
m3/
mol)
MW
=
Molecular
weight
(
g/
mol).

25
Superfund
Chemical
Data
Matrix
Calculations
3.1.2
Volatilization
Half­
Life
for
Lakes
In
order
to
calculate
the
volatilization
half­
life
for
lakes,
the
mean
water
body
depth
is
taken
as
100
cm,
the
temperature
as
298
K,
the
wind
velocity
as
0.5
m/
sec,
and
the
current
velocity
as
0.05
m/
sec.
Using
these
values,
Equations
(
14)
and
(
15)
reduce
to
the
following:

°
MW
<
65
g/
mol
t
1/
2
=
2.89
×
{
[
0.05
×
(
MW/
44)
1/
2]
+
[(
8.1
×
10­
6/
H)
×
(
MW/
18)
1/
2]}
days
(
19)

°
MW
³
65
g/
mol
t
1/
2
=
2.89
×
{
[
17.2
×
(
MW/
32)
1/
2]
+
[(
3.9
×
10­
6/
H)
×
(
MW/
18)
1/
2]}
days
(
20)

where
H
=
Henry's
law
constant
(
atm
·
m3/
mol)
MW
=
Molecular
weight
(
g/
mol).

3.2
SOIL/
WATER
DISTRIBUTION
COEFFICIENTS
(
K
d)

As
described
in
Section
2.4.5,
SCDM
soil/
water
distribution
coefficients
(
K
d,
mL/
g)
are
based
on
the
relationship
(
21)
K
d
K
oc
×
f
oc
where
K
oc
is
the
chemical's
soil
organic
carbon/
water
partition
coefficient
(
mL/
g)
and
f
oc
is
assumed
to
be
0.002
g
organic
carbon/
g
soil.
For
organic
chemicals
without
K
d
values
in
SCDM
datafiles
SSG_
KD
or
RTI_
ION
(
see
Section
2.4.5),
SCDM
calculates
a
K
d
value
based
on
this
relationship,
using
a
K
oc
value
calculated
from
a
compound's
SCDM
Log
octanol/
water
partition
coefficient
(
Log
K
ow
or
Log
P).
To
perform
this
calculation,
SCDM
uses
the
relationship
between
these
properties
determined
by
DiToro
(
1985)
for
semivolatile
organic
compounds:

(
22)
K
oc
0.00028
0.983
Log
K
ow
.

This
equation
is
also
used
in
the
Soil
Screening
Guidance
(
EPA,
1996b).

26
Superfund
Chemical
Data
Matrix
Calculations
Combining
Equations
(
21)
and
(
22)
yields
the
following
equation:

(
23)
K
d
f
oc
×
10(
0.00028
0.983Log
K
ow)
.

For
any
organic
hazardous
substance
for
which
no
K
d
value
is
available
in
SCDM
datafiles
SSG_
KD
or
RTI_
ION,
but
with
a
Log
K
ow
value
chosen
as
described
in
Section
2.6.2,
SCDM
calculates
K
d
using
Equation
(
23).

3.3
SCREENING
CONCENTRATION
BENCHMARKS
The
HRS
assigns
extra
weight
to
targets
with
exposure
levels
to
hazardous
substances
that
are
at
or
above
benchmark
values.
In
addition
to
the
regulatory
limits
discussed
in
Section
2.8,
the
HRS
uses
a
number
of
benchmarks
called
screening
concentrations.
Screening
concentrations
correspond
to
a
10­
6
individual
cancer
risk
or
a
noncancer
hazard
quotient
of
1
under
specified
exposure
assumptions.
These
assumptions,
discussed
below,
are
conservative
and
broadly
apply
to
sites
nationwide.
The
Agency
recognizes
that
modeling
human
activity
patterns
would
provide
a
more
realistic
determination
of
exposure
or
risk.
While
such
information
may
be
determined
on
a
site­
specific
basis
with
considerable
effort,
it
is
difficult
to
develop
assumptions
on
the
activity
patterns
of
target
populations
that
could
be
applied
to
sites
on
a
nationwide
basis
in
order
to
develop
exposure
scenarios
for
the
HRS.
For
this
reason,
the
HRS
exposure
assumptions
reflect
values
used
for
the
assessment
of
risk
throughout
different
programs
within
the
Agency.
EPA
recognizes
that
a
critical
evaluation
of
the
references
cited
below,
along
with
other
information,
could
lead
to
differing
exposure
assumptions.
Moreover,
the
Agency
is
still
refining
the
assumptions
used
in
this
area
of
risk
assessment.

EPA
also
considered
the
limited
number
of
samples
available
at
the
National
Priority
List
(
NPL)
listing
stage
when
it
selected
these
assumptions.
As
outlined
in
the
Field
Test
of
the
proposed
revised
HRS,
the
Agency
generally
expects
to
have
<
100
samples
for
all
pathways
to
support
the
HRS
analysis.
This
limited
sampling
may
miss
areas
of
maximum
contamination,
or
"
hot
spots,"
and
thus
the
sample
results
may
not
represent
the
maximum
level
of
contamination.
Although
using
conservative
exposure
assumptions
does
not
fully
compensate
for
the
limited
data
available
for
analysis,
using
less
conservative
assumptions
would
likely
lead
to
a
greater
incidence
of
false
negatives;
i.
e.,
the
Agency
may
not
identify
sites
that
should
be
investigated
further
under
the
remedial
program.

27
Superfund
Chemical
Data
Matrix
Calculations
3.3.1
Screening
Concentrations
for
Drinking
Water
Pathways
The
following
equation
(
EPA,
1989b,
p.
6­
35)
is
used
to
calculate
the
average
daily
intake
of
a
hazardous
substance
from
the
ingestion
of
contaminated
ground
water
or
surface
water:

where:
(
24)
Average
Daily
Intake
(
mg/
kg
day)
C
water
×
IR
×
EF
×
ED
BW
×
AT
C
water
=
Contaminant
concentration
in
water
(
mg/
L)
IR
=
Drinking
water
intake
(
ingestion)
rate
(
L/
day)
EF
=
Exposure
frequency
(
days/
year)
ED
=
Exposure
duration
(
years)
BW
=
Body
weight
(
kg)
AT
=
Averaging
time
(
days).

Under
the
assumptions
used
for
HRS
purposes,
the
adult
drinking
water
ingestion
rate
is
2
L/
day,
the
exposure
frequency
for
residents
is
daily
(
350
days/
year),
the
exposure
duration
is
30
years,
and
the
average
adult
body
weight
is
70
kg.
The
ingestion
rate
of
2
L/
day
is
routinely
used
by
the
Agency
as
the
default
value
for
drinking
water
ingestion
and
assumes
that
the
entire
2
L
are
from
the
contaminated
drinking
water
source.
Refinements
in
risk
assessments
sometime
assume
that
an
individual
will
be
away
for
vacations
or
that
some
water
will
be
consumed
at
the
workplace.

Cancer
Risk
Screening
Concentration.
The
cancer
risk
screening
concentration
is
estimated
by
solving
Equation
(
24)
for
the
contaminant
concentration
in
a
medium
of
concern
(
C
medium),
at
a
specified
target
risk
level
using
the
following
relationship:

(
25)
Target
Risk
Average
Daily
Intake
×
Cancer
Slope
Factor
(
SF)
.

When
Equation
(
25)
is
rearranged
to
solve
for
the
average
daily
intake
(
I),
Equations
(
24)
and
(
25)
can
be
combined
to
estimate
the
water
concentration
(
C
water)
that
corresponds
to
a
10­
6
target
risk
level.
Over
a
lifetime,
the
average
daily
intake
may
be
calculated
assuming
an
averaging
time
(
AT)
of
25,550
days
(
i.
e.,
70
years)
for
carcinogenic
effects.
Therefore,
the
drinking
water
screening
concentration
for
carcinogens
presumed
to
result
in
one
excess
case
of
cancer
per
million
people
exposed
(
SC
c)
is
given
by:

28
Superfund
Chemical
Data
Matrix
Calculations
(
26)
SC
c
10
6
×
BW
×
25,550
days
SF
oral
×
IR
×
EF
×
ED
.

With
the
exposure
assumptions
described
above
for
Equation
(
24),
Equation
(
26)
may
be
simplified
as:

(
27)
SC
c
(
mg/
L)
8.52
×
10
5
SF
oral
.

This
equation
is
used
to
calculate
SC
c
for
nonradioactive
carcinogenic
substances.
Because
cancer
slope
factors
for
radionuclides
are
in
units
of
pC
i
­
1,
body
weight
and
averaging
time
do
not
apply.
Thus,
the
following
equation
for
radionuclides
is
analogous
to
Equation
(
26)
for
chemical
carcinogens:

(
28)
SC
c
10
6
SF
oral
×
IR
×
EF
×
ED
.

When
the
exposure
assumptions
described
for
Equation
(
24)
are
used,
Equation
(
28)
may
be
rewritten
to
estimate
the
concentration
in
water
that
corresponds
to
a
target
risk
level
of
10­
6.
The
screening
concentration
for
radionuclides
ingested
in
drinking
water
(
SC
r)
is
given
by:

(
29)
SC
r
(
pC
i/
L)
4.76
×
10
11
SF
oral
.

Noncancer
Risk
Screening
Concentration.
The
RfD
is
based
on
the
assumption
that
thresholds
exist
for
certain
toxic
effects.
In
general,
the
RfD
is
an
estimate
(
with
uncertainty
spanning
perhaps
an
order
of
magnitude)
of
a
daily
exposure
to
the
human
population
(
including
sensitive
subgroups)
that
is
likely
to
be
without
an
appreciable
risk
of
deleterious
effects
during
a
lifetime.
When
the
acceptable
daily
intake
for
drinking
water
ingestion
is
set
equal
to
the
RfD
oral
(
i.
e.,
hazard
quotient
=
1),
Equation
(
24)
may
be
rearranged
to
solve
for
the
contaminant
concentration
in
water
that
corresponds
to
the
no
adverse
effects
level
described
above.
To
solve
for
the
drinking
water
screening
concentration
for
noncarcinogens
(
SC
n),
Equation
(
24)
becomes:

29
Superfund
Chemical
Data
Matrix
Calculations
(
30)
SC
n
RfD
oral
×
BW
×
AT
IR
×
EF
×
ED
.

For
noncarcinogenic
effects,
the
averaging
time
is
30
years,
or
10,950
days.
When
the
assumptions
described
for
Equation
(
24)
are
used,
Equation
(
30)
may
be
simplified
as:

(
31)
SC
n
(
mg/
L)
RfD
oral
×
36.5
.

3.3.2
Screening
Concentrations
for
the
Surface
Water
Food
Chain
Pathway
The
following
equation
(
EPA,
1989b,
p.
6­
45)
is
used
to
calculate
the
average
daily
intake
from
fish
and
shellfish
ingestion:

(
32)
Average
Daily
Intake
(
mg/
kg
day)
C
fish
×
IR
×
F
×
EF
×
ED
BW
×
AT
where:

C
fish
=
Contaminant
concentration
in
fish/
shellfish
(
mg/
kg)
IR
=
Fish/
shellfish
intake
(
ingestion)
rate
(
kg/
day)
F
=
Fraction
ingested
from
contaminated
source
(
unitless)
EF
=
Exposure
frequency
(
days/
year)
ED
=
Exposure
duration
(
years)
BW
=
Body
weight
(
kg)
AT
=
Averaging
time
(
days).

The
high
end
fish
ingestion
rate
for
recreational
fishers
is
0.054
kg/
day
(
USDA,
1982),
with
the
fraction
ingested
(
F)
set
equal
to
1
(
i.
e.,
all
fish
are
assumed
to
come
from
contaminated
waters).
The
exposure
frequency
is
assumed
to
be
350
days/
year,
the
exposure
duration
is
30
years,
and
the
average
adult
body
weight
is
70
kg.

Cancer
Risk
Screening
Concentration.
When
Equation
(
25)
is
rearranged
to
solve
for
the
average
daily
intake
(
I),
Equations
(
25)
and
(
32)
can
be
combined
to
estimate
the
fish/
shellfish
concentration
that
corresponds
to
a
10­
6
target
risk
level.
Over
a
lifetime,
the
average
daily
intake
may
be
calculated
assuming
an
averaging
time
(
AT)
of
25,550
days
(
i.
e.,
70
years)
for
30
Superfund
Chemical
Data
Matrix
Calculations
carcinogenic
effects.
Therefore,
the
fish/
shellfish
concentration
presumed
to
result
in
one
excess
case
of
cancer
per
million
people
exposed
(
SC
c)
is
given
by:

(
33)
SC
c
10
6
×
BW
×
25,550
days
SF
oral
×
IR
×
F
×
EF
×
ED
.

Using
the
exposure
assumptions
listed
for
Equation
(
31)
results
in
a
simplified
screening
concentration
equation
for
nonradioactive
carcinogenic
substances
in
fish/
shellfish:

(
34)
SC
c
(
mg/
kg)
3.15
×
10
3
SF
oral
.

If
the
same
exposure
assumptions,
excluding
body
weight
and
averaging
time,
are
used,
Equation
(
34)
may
be
rewritten
to
estimate
the
fish/
shellfish
concentration
that
corresponds
to
a
target
risk
level
of
10­
6
for
ingestion
of
radionuclides
in
fish
and
shellfish
(
SC
r):

(
35)
SC
r
(
pC
i/
kg)
1.76
×
10
9
SF
oral
.

Noncancer
Risk
Screening
Concentration.
Setting
the
intake
from
fish
and
shellfish
ingestion
equal
to
the
oral
reference
dose
(
RfD
oral)
and
solving
Equation
(
32)
for
concentration
gives
the
following
equation:

(
36)
SC
n
RfD
oral
×
BW
×
AT
IR
×
F
×
EF
×
ED
.

For
noncarcinogenic
effects,
the
averaging
time
is
30
years,
or
10,950
days.
If
the
other
assumptions
listed
for
Equation
(
32)
are
used,
Equation
(
36)
may
be
simplified
as
follows:

(
37)
SC
n
(
mg/
kg)
RfD
oral
×
1,352
.

31
Superfund
Chemical
Data
Matrix
Calculations
3.3.3
Screening
Concentrations
for
Soil
Ingestion
The
following
equation
(
EPA,
1991,
p.
3­
25)
is
used
to
calculate
the
average
daily
intake
from
soil
ingestion:

(
38)
Average
Daily
Intake
(
mg/
kg
day)
C
soil
×
CF
×
IF
×
EF
AT
where:

C
soil
=
Contaminant
concentration
in
soil
(
mg/
kg)
CF
=
Conversion
factor
(
10­
6
kg/
mg)
IF
=
Age­
adjusted
soil
ingestion
factor
(
mg­
yr/
kg­
day)
EF
=
Exposure
frequency
(
days/
year)
AT
=
Averaging
time
(
days)

and
IF
is
given
by:

(
39)
IF
soil/
adj
(
mg
yr/
kg
day)
IR
soil/
age1
6
×
ED
age1
6
BW
age1
6
IR
soil/
age7
13
×
ED
age7
31
BW
age7
31
where:

IR
soil/
age1­
6
=
Soil
intake
(
ingestion)
rate,
age
1
to
6
(
mg/
day)
ED
age1­
6
=
Exposure
duration
during
ages
1­
6
(
yr)
BW
age1­
6
=
Average
body
weight
from
ages
1­
6
(
kg)
IR
soil/
age7­
31
=
Soil
intake
(
ingestion)
rate,
ages
7
and
older
(
mg/
day)
ED
age7­
31
=
Exposure
duration
during
ages
7­
31
(
yr)
BW
age7­
31
=
Average
body
weight
from
ages
7­
31
(
kg).

The
soil
ingestion
rate
is
assumed
to
be
200
mg/
day
for
ages
6
and
younger,
and
100
mg/
day
for
ages
7
and
older;
the
exposure
durations
are
6
years
and
24
years
for
children
and
"
adults"
(
ages
7
to
31),
respectively;
and
the
average
body
weights
are
15
kg
for
children
and
70
kg
for
adults.
As
with
Equation
(
24),
the
exposure
frequency
is
assumed
to
be
350
days/
year.
With
these
assumptions,
the
age­
adjusted
soil
ingestion
factor
is
114
mg­
yr/
kg­
day.

32
Superfund
Chemical
Data
Matrix
Calculations
Cancer
Risk
Screening
Concentration.
When
Equation
(
25)
is
rearranged
to
solve
for
the
average
daily
intake
(
I),
Equations
(
25)
and
(
38)
can
be
combined
to
estimate
the
soil
concentration
that
corresponds
to
a
10­
6
target
risk
level.
Over
a
lifetime,
the
average
daily
intake
may
be
calculated
assuming
an
averaging
time
(
AT)
of
25,550
days
(
i.
e.,
70
years)
for
carcinogenic
effects.
Therefore,
the
screening
soil
concentration
presumed
to
result
in
one
excess
case
of
cancer
per
million
people
exposed
(
SC
c)
is
given
by:

(
40)
SC
c
10
6
×
25,500
days
SF
oral
×
IF
×
CF
×
EF
.

Using
the
assumptions
listed
for
Equations
(
38)
and
(
39)
results
in
a
simplified
screening
concentration
equation
for
nonradioactive
carcinogenic
substances
in
soil:

(
41)
SC
c
(
mg/
kg)
0.640
SF
oral
.

Since
cancer
slope
factors
for
radionuclides
are
provided
in
pCi­
1,
body
weight
and
averaging
time
do
not
apply.
As
a
result,
IF
is
calculated
without
body
weight
(
BW)
in
Equation
(
39)
and
is
equal
to
3,600
mg­
yr/
day.
If
the
other
exposure
assumptions
described
for
chemical
carcinogens
are
used,
Equation
(
41)
may
be
rewritten
to
estimate
the
soil
concentration
that
corresponds
to
a
target
risk
level
of
10­
6
for
ingestion
of
radionuclides
in
contaminated
soils
(
SC
r):

(
42)
SC
r
(
pC
i/
kg)
7.94
×
10
7
SF
oral
.

Noncancer
Risk
Screening
Concentration.
Setting
the
intake
from
soil
ingestion
equal
to
the
oral
reference
dose
(
RfD
oral)
and
solving
Equation
(
38)
for
concentration
gives
the
following
equation:

(
43)
SC
n
RfD
oral
×
BW
×
AT
IR
×
CF
×
EF
×
ED
.

33
Superfund
Chemical
Data
Matrix
Calculations
For
noncarcinogenic
effects,
the
averaging
time
(
AT)
is
a
function
of
the
exposure
duration
(
ED)
assumed
for
children
or
6
years
×
365
days/
year
=
2,190
days.
Assuming
daily
exposure
(
i.
e.,
EF
=
350
days/
year),
an
average
body
weight
of
15
kg,
and
an
ingestion
rate
(
IR)
for
children
of
200
mg
soil
per
day
results
in
the
following
simplified
equation:

(
44)
SC
n
(
mg/
kg)
RfD
oral
(
mg/
kg
day)
×
78,214
.

3.3.4
Screening
Concentrations
for
the
Air
Pathway
The
following
equation
(
EPA,
1989b,
p.
6­
44)
is
used
to
calculate
intake
from
inhalation
of
airborne
hazardous
substances:

where:
(
45)
Average
Daily
Intake
(
mg/
kg
day)
C
air
×
IR
×
EF
×
ED
BW
×
AT
C
air
=
Contaminant
concentration
in
air
(
mg/
m3)
IR
=
Air
intake
(
inhalation)
rate
(
m3/
day)
EF
=
Exposure
frequency
(
days/
year)
ED
=
Exposure
duration
(
years)
BW
=
Body
weight
(
kg)
AT
=
Averaging
time
(
days).

The
inhalation
rate
is
assumed
to
be
20
m3/
day,
the
exposure
frequency
is
350
days/
year,
the
exposure
duration
is
30
years,
and
the
average
adult
body
weight
is
70
kg.

Cancer
Risk
Screening
Concentration.
By
rearranging
Equation
(
25)
to
solve
for
the
average
(
46)
SC
c
10
6
×
BW
×
25,550
days
SF
inhal
×
IR
×
EF
×
ED
.
daily
intake
(
I),
Equations
(
25)
and
(
45)
can
be
combined
to
estimate
the
concentration
in
air
that
corresponds
to
a
10­
6
target
risk
level.
Over
a
lifetime,
the
average
daily
intake
may
be
calculated
assuming
an
averaging
time
(
AT)
of
25,550
days
(
i.
e.,
70
years)
for
carcinogenic
effects.
Therefore,
the
air
concentration
presumed
to
result
in
one
excess
case
of
cancer
per
million
people
exposed
(
SC
c)
is
given
by:

34
Superfund
Chemical
Data
Matrix
Calculations
Using
the
exposure
assumptions
listed
above
for
Equation
(
45)
results
in
the
following
equation
for
nonradioactive
carcinogenic
substances:

(
47)
SC
c
(
mg/
m
3)
8.52
×
10
6
SF
inhal
.

Using
the
same
exposure
assumptions
(
excluding
body
weight
and
averaging
time),
Equation
(
46)
may
be
rewritten
to
estimate
the
air
concentration
of
radionuclides
that
corresponds
to
a
target
risk
level
of
10­
6
for
inhalation
of
contaminated
air
(
SC
r):

(
48)
SC
r
(
pC
i/
m
3)
4.76
×
10
12
SF
inhal
.

Noncancer
Risk
Screening
Concentration.
Setting
the
average
daily
intake
equal
to
the
inhalation
reference
dose
(
RfD
inhal)
and
solving
Equation
(
45)
for
the
air
concentration
results
in
the
following
equation:

For
noncarcinogenic
effects,
the
averaging
time
(
AT)
is
30
years,
or
10,950
days.
The
(
49)
SC
n
RfD
inhal
×
BW
×
AT
IR
×
EF
×
ED
.

inhalation
rate
(
IR)
is
assumed
to
be
20
m3/
day,
the
exposure
frequency
(
EF)
is
350
days/
year,
the
exposure
duration
(
ED)
is
30
years,
and
the
average
adult
body
weight
(
BW)
is
70
kg.
When
these
assumptions
are
used,
Equation
(
49)
may
be
simplified
as:

(
50)
SC
n
(
mg/
m
3)
RfD
inhal
×
3.65
.

35
Chemical
Data,
Factor
Values,
Superfund
Chemical
Data
Matrix
and
Benchmarks
SECTION
4
CHEMICAL
DATA,
FACTOR
VALUES,
AND
BENCHMARKS
Appendix
A
contains
a
two­
page
listing
of
selected
data,
HRS
factor
values,
and
benchmarks
for
each
hazardous
substance
in
SCDM
(
the
"
SCDM
page
reports").
Data
selected
for
SCDM
for
each
substance
are
on
the
first
page;
factor
values
and
benchmarks
are
on
the
second
page.

Figure
1
presents
the
header
that
appears
on
both
sides
of
the
page
report.
The
header
contains
the
date
the
report
was
printed,
the
substance
name
and
synonym,
the
SCDM
version
(
month,
year),
and
the
Chemical
Abstract
Service
(
CAS)
number
for
the
substance.

The
first
page
contains
all
of
the
Figure
1.
Page
Heading
Date:
06/
15/
96
SUPERFUND
CHEMICAL
DATA
MATRIX
SCDM
Version:
JUN96
Chemical:
Acenaphthene
CAS
Number:
000083­
32­
9
Figure
2.
Toxicity
Section
TOXICITY
Parameter
Value
Unit
Source
Oral
RfD:
6.0E­
02
mg/
kg/
day
IRIS
Inhal
RfD:
mg/
kg/
day
Oral
Slope:
(
mg/
kg/
day)^­
1
Oral
Wt­
of­
Evid:
Inhal
Slope:
(
mg/
kg/
day)^­
1
Inhal
Wt­
of­
Evid:
Oral
ED10:
mg/
kg/
day
Oral
ED10
Wgt:
Inhal
ED10:
mg/
kg/
day
Inhal
ED10
Wgt:
Oral
LD50:
mg/
kg
Dermal
LD50:
mg/
kg
Gas
Inhal
LC50:
ppm
Dust
Inhal
LC50:
mg/
L
ACUTE
Fresh
AWQC:
m
g/
L
Salt
AWQC:
m
g/
L
Fresh
AALAC:
m
g/
L
Salt
AALAC:
m
g/
L
CHRONIC
Fresh
AWQC:
m
g/
L
Salt
AWQC:
m
g/
L
Fresh
AALAC:
m
g/
L
Salt
AALAC:
m
g/
L
Fresh
Ecol
LC50:
6.0E+
01
m
g/
L
AQUIRE
Salt
Ecol
LC50:
2.2E+
03
m
g/
L
AQUIRE
selected
chemical
data,
the
data
units,
and
an
acroynym
describing
the
source
of
the
information
in
SCDM.
The
chemical
data
are
divided
into
six
functional
groups:
toxicity,
persistence,
physical
characteristics,
mobility,
bioaccumulation,
and
other
data.

The
toxicity
section
(
Figure
2)
contains
the
acute,
chronic,
and
carcinogenicity
data
that
were
compiled
using
the
methodology
described
in
Sections
2.2,
2.3,
and
2.7
and
used
to
derive
toxicity
and
ecotoxicity
factor
values.
The
top
half
of
this
section
contains
the
data
used
to
determine
the
human
toxicity
factor
value:
reference
dose
(
oral
and
inhalation
cancer
slope
factor
(
oral
and
inhalation),
ED
10
(
oral
and
inhalation),

36
Chemical
Data,
Factor
Values,
Superfund
Chemical
Data
Matrix
and
Benchmarks
LD
50
(
oral
and
dermal),
and
LC
50
(
gas
and
dust
inhalation).
The
bottom
half
of
this
section
contains
the
data
used
to
determine
an
ecotoxicity
factor
value:
acute
and
chronic
ambient
water
quality
criteria
(
AWQC)
for
fresh
and
salt
water,
acute
and
chronic
aquatic
life
advisory
concentrations
(
AALACs)
for
fresh
and
salt
water
(
at
this
time
no
AALACs
have
been
promulgated),
and
fresh
and
salt
water
LC
50
values.
Blank
entries
indicate
that
no
value
was
found
using
the
procedures
and
references
specified
in
Section
2.

Figure
3.
Persistence
Section
PERSISTENCE
Parameter
Value
Unit
Source
LAKE
­
Halflives
Hydrolysis:
days
Volatility:
1.1E+
02
days
THOMAS
Photolysis:
2.5E+
00
days
FATERATE
Biodeg:
1.0E+
02
days
FATERATE
Radio:
days
RIVER
­
Halflives
Hydrolysis:
days
Volatility:
1.4E+
00
days
THOMAS
Photolysis:
2.5E+
00
days
FATERATE
Biodeg:
1.0E+
02
days
FATERATE
Radio:
days
Log
Kow:
3.9E+
00
RTI_
LOGP
The
persistence
section
(
Figure
3)
contains
the
surface
water
persistence
data
compiled
using
the
methodology
described
in
Sections
2.5,
2.6.2,
and
3.1.
Surface
water
persistence
factors
can
also
be
determined
using
the
logarithm
of
the
n­
octanol/
water
partition
coefficient
(
Log
K
ow
or
Log
P)
if,
as
specified
in
the
HRS,
this
gives
a
higher
factor
value
than
the
half­
lives
(
or
a
default,
if
applicable).

The
physical
characteristics
section
(
Figure
4)
contains
logical
"
yes/
no"
flags
that
classify
the
substance.
The
"
metal
contain"
flag
indicates
that
Figure
4.
Physical
Characteristics
PHYSICAL
CHARACTERISTICS
Parameter
Value
Metal
Contain:
No
Organic:
Yes
Inorganic:
No
Gas:
Yes
Particulate:
Yes
Radionuclide:
No
Rad.
Element:
No
Molecular
Weight:
1.5E+
02
Density:
1.0E+
00
g/
mL
@
99.00
°
C
the
hazardous
substance
is
a
metal
or
metalloid
and
is
used
to
determine
ground
water
mobility
and
surface
water
persistence
factors.
The
"
organic
and
"
inorganic"
flags
are
used
to
determine
ground
water
mobility
and
bioaccumulation.
The
"
radionuclide"
flag
is
used
to
determine
the
human
toxicity
factor,
the
ecosystem
toxicity
factor,
and
the
surface
water
persistence
factor.
The
radioactive
element
flag
("
rad.
element")
is
used
to
determine
whether
or
not
the
HRS
factors
and
benchmarks
(
second
page)
are
printed.
The
Figure
5.
Mobility
Section
MOBILITY
Parameter
Value
Unit
Source
Vapor
Press:
2.5E­
03
Torr
CHEMFATE
Henry's
Law:
1.6E­
04
atm­
m3/
mol
CHEMFATE
Water
Solub:
4.2E+
00
mg/
L
LIVECHEM
Distrib
Coef:
1.4E+
01
ml/
g
Geo.
Mean
Sol.:
gas
and
particulate
flags
are
used
to
determine
mobility
and
likelihood
of
release
for
the
air
pathway.
Molecular
weight
is
used
to
determine
volatilization
half­
life,
as
described
in
Section
3.1.

The
mobility
section
(
Figure
5)
contains
the
air
and
ground
water
mobility
data
compiled
using
the
methodology
described
in
Sections
2.4.3,
2.4.4,
2.4.5,
and
3.2.
Vapor
pressure
and
37
Chemical
Data,
Factor
Values,
Superfund
Chemical
Data
Matrix
and
Benchmarks
Henry's
law
constant
are
used
to
determine
gas
migration
potential
and
gas
mobility
factors.
Henry's
law
constant
is
also
used
to
calculate
the
volatilization
half­
life
as
described
in
Section
3.1.
Water
solubility
and
the
soil/
water
distribution
coefficient
are
used
to
determine
the
ground
water
mobility
factor.
Substance­
specific
water
solubility
is
used
for
nonmetal
and
nonmetalloid
substances,
whereas
for
metal­
containing
substances
the
solubility
value
is
the
geometric
mean
of
the
available
water
solubilities
for
inorganic
compounds
containing
the
hazardous
substance.

The
bioaccumulation
section
(
Figure
6)
con­

Figure
6.
Bioaccumulation
Section
BIOACCUMULATION
Parameter
Value
Unit
Source
FOOD
CHAIN
Fresh
BCF:
3.9E+
02
VER_
BCF
Salt
BCF:

ENVIRONMENTAL
Fresh
BCF:
3.9E+
02
VER_
BCF
Salt
BCF:

Log
Kow:
3.9E+
00
RTI_
LOGP
Water
Solub:
4.2E+
00
mg/
L
LIVECHEM
tains
the
human
food
chain
and
environmental
bioaccumulation
potential
factor
data
compiled
using
the
methodology
described
in
Section
2.6.
Bioconcentration
factors
(
BCFs)
are
collected
for
fresh
and
salt
water
for
the
human
food
chain
and
environmental
threats.
Log
K
ow
or
water
solubility
is
used
to
establish
bioaccumulation
potential
when
a
BCF
is
not
available.

The
section
labeled
"
other
data"
(
Figure
7)
contains
values
for
melting
points
and
boiling
points
(
°
C)
along
with
the
associated
vapor
pres­

Figure
7.
Other
Data
Section
OTHER
DATA
Melting
Point
:
93.40
°
C
Boiling
Point
:
279.00
°
C
Formula
:
C12H10
sure
(
Torr),
if
applicable.
Chemical
formula
is
also
listed
here.

The
class
information
section
(
Figure
8)
lists
parent
substances
for
three
data
substitution
classes:
toxicity,
ground
water
mobility,
and
other
data.
The
toxicity
class
includes
all
toxicity
and
Figure
8.
Class
Information
Section
CLASS
INFORMATION
Class
Parent
Substance
Toxicity:
NA
GW
Mob:
NA
Other:
NA
benchmark
data
used
to
determine
human
or
ecotoxicity
factor
values.
The
ground
water
mobility
class
includes
water
solubility,
soil/
water
distribution
coefficient,
and
geometric
mean
water
solubility.
The
"
other"
class
includes
hydrolysis,
biodegradation,
photolysis,
and
volatilization
halflives
as
well
as
BCFs
and
Log
K
ow.

Currently
only
two
groups
of
substances
inherit
data
from
a
parent
substance:
metals
and
radioactive
substances.
Generally,
metal­
containing
substances
inherit
data
for
the
ground
water
mobility
class
with
the
elemental
metal
as
the
class
parent.
Radioactive
isotopes
may
inherit
data
from
their
primary
radioactive
element
for
the
ground
water
mobility
and
"
other"
classes.

38
Chemical
Data,
Factor
Values,
Superfund
Chemical
Data
Matrix
and
Benchmarks
Figure
9.
Assigned
Factor
Values
Section
ASSIGNED
FACTOR
VALUES
AIR
PATHWAY
GROUND
WATER
PATHWAY
SOIL
EXPOSURE
PATHWAY
Parameter
Value
Parameter
Value
Parameter
Value
Toxicity:
10
Toxicity:
10
Toxicity:
10
Gas
Mobility:
0.2000
Water
Solub:
4.2E+
00
Gas
Migration:
11
Distrib:
1.4E+
01
SURFACE
WATER
PATHWAY
Drinking
Water
Human
Food
Chain
Environmental
Parameter
Value
Parameter
Value
Parameter
Value
Toxicity:
10
Toxicity:
10
Fresh
Tox:
10000
Salt
Tox:
100
Persistence
Persistence
Persistence
River:
0.4000
River:
0.4000
River:
0.4000
Lake:
0.4000
Lake:
0.4000
Lake:
0.4000
Bioaccumulation
Bioaccumulation
Fresh:
500.0
Fresh:
500.0
Salt:
500.0
Salt:
500.0
The
second
page
for
each
substance
is
divided
into
top
and
bottom
sections
that
contain
factor
values
(
Figure
9)
and
benchmarks
(
Figure
10)
required
by
the
HRS.
SCDM
determines
factor
values
using
HRS
methodologies,
from
selected
data
on
the
first
page
of
the
SCDM
page
report.
The
factor
values
are
presented
by
pathway:
air,
ground
water,
soil
exposure,
and
surface
water.
The
surface
water
pathway
is
further
subdivided
by
threat:
drinking
water,
human
food
chain,
and
environmental.
The
toxicity
factor
value
represents
human
toxicity
and
is
the
same
for
all
pathways.
The
air
pathway
gas
migration
factor
value
is
used
to
determine
likelihood
of
release.
The
surface
water
environmental
toxicity
factor
values
are
based
on
fresh
and
salt
water
ecosystem
toxicity
data,
and
the
surface
water
persistence
factor
values
are
based
on
BCFs
for
all
aquatic
species.
The
surface
water
human
food
chain
factor
values
are
based
on
human
toxicity
and
BCFs
for
only
those
aquatic
species
consumed
by
humans.
For
radioactive
substances,
human
toxicity,
ecosystem
toxicity,
and
surface
water
persistence
factor
values
are
determined
as
specified
in
Chapter
7
of
the
HRS.

The
benchmarks
(
Figure
10),
like
the
factor
values,
are
presented
by
pathway:
air,
ground
water,
soil
exposure,
and
surface
water.
The
surface
water
pathway
is
further
subdivided
by
threat:
drinking
water,
human
food
chain,
and
environmental.
For
HRS
scoring,
actual
sampled
contaminant
concentrations
for
a
particular
media
are
compared
to
these
benchmark
concentrations
to
determine
if
the
target
will
be
scored
as
subject
to
Level
I
or
Level
II
contamination.

39
Chemical
Data,
Factor
Values,
Superfund
Chemical
Data
Matrix
and
Benchmarks
Figure
10.
Benchmarks
Section
BENCHMARKS
AIR
PATHWAY
GROUND
WATER
PATHWAY
SOIL
EXPOSURE
PATHWAY
RADIONUCLIDE
Parameter
Value
Unit
Parameter
Value
Unit
Parameter
Value
Unit
Parameter
Value
Unit
NAAQS/
NESHAPS:
m
g/
m3
MCL/
MCLG:
mg/
L
Cancer
Risk:
mg/
kg
MCL:
pCi/
L
Cancer
Risk:
mg/
m3
Cancer
Risk:
mg/
L
Non
Cancer
Risk:
4.7E+
03
mg/
kg
UMTRCA:
pCi/
kg
Non
Cancer
Risk:
mg/
m3
Non
Cancer
Risk:
2.2E+
00
mg/
L
CANCER
RISK
Air:
pCi/
m3
DW:
pCi/
L
FC:
pCi/
kg
Soil
Ing:
pCi/
kg
Soil
Gam:
pCi/
kg
SURFACE
WATER
PATHWAY
Drinking
Water
Human
Food
Chain
Environmental
Parameter
Value
Unit
Parameter
Value
Unit
Parameter
Value
Unit
MCL/
MCLG:
mg/
L
FDAAL:
ppm
ACUTE
Cancer
Risk:
mg/
L
Cancer
Risk:
mg/
kg
Fresh
AWQC:
m
g/
L
Non
Cancer
Risk:
2.2E+
00
mg/
L
Non
Cancer
Risk:
8.1E+
01
mg/
kg
Salt
AWQC:
m
g/
L
Fresh
AALAC:
m
g/
L
Salt
AALAC:
m
g/
L
CHRONIC
Fresh
AWQC:
m
g/
L
Salt
AWQC:
m
g/
L
Fresh
AALAC:
m
g/
L
Salt
AALAC:
m
g/
L
Appendix
B­
1
contains
tables
for
nonradioactive
hazardous
substances.
The
first
table
in
Appendix
B­
1
lists
all
of
the
factor
values
by
pathway.
The
second
table
presents
the
benchmarks
for
the
air
and
ground
water
pathways,
the
third
table
presents
benchmarks
for
the
surface
water
pathway,
and
the
fourth
table
presents
benchmarks
for
the
soil
exposure
pathway.
Appendix
B­
2
contains
tables
for
radionuclides;
the
first
table
lists
all
of
the
factor
values
by
pathway,
and
the
second
table
presents
benchmarks
for
all
pathways.
Appendix
C
contains
a
cross­
reference
index
of
hazardous
substance
names,
synonyms,
and
CAS
numbers
for
substances
in
SCDM.

40
Superfund
Chemical
Data
Matrix
References
SECTION
5
REFERENCES
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R.
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