Document ID: EPA-HQ-RCRA-2002-0028-0027
Agency: epa
Document Type: Supporting & Related Material
Title: 
Posted Date: 2003-01-21T05:00Z

Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
This
page
intentionally
left
blank.
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
3
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
This
appendix
documents
the
inputs
used
in
the
groundwater
modeling.
In
addition,
Attachment
A.
1
provides
additional
methodological
details
for
IWEM.
Note
that
Attachment
A.
1
is
a
memo
with
its
own
attachments
A
and
B;
for
clarity,
those
attachments
are
labeled
as
"
Memo
Attachment
A"
and
"
Memo
Attachment
B."

A.
1
Scenarios
Table
A­
1
summarizes
the
source
scenarios
modeled.
For
nonaerated
units,
EPA
did
one
central­
tendency
run,
in
which
all
WATER9
inputs
were
set
to
central­
tendency
values,
and
four
high­
end
runs,
in
which
two
of
the
most
critical
inputs
were
set
to
high­
end
values.
All
other
inputs,
including
all
waste
parameters,
were
set
to
central­
tendency
values
for
all
runs.
The
most
sensitive
parameters
for
nonaerated
units
are
biomass,
flow,
capacity,
and
solids
removal
efficiency
(
fraction
of
diverted
flow
that
is
solids).

For
the
aerated
treatment
train,
biomass
was
not
varied
because
a
very
low
value
would
not
be
realistic,
because
such
treatment
trains
are
designed
to
support
the
growth
of
biomass.
Solids
parameters
are
not
an
input
to
the
aerated
treatment
train
units
in
WATER9.
Thus,
there
were
only
two
critical
parameters
for
the
aerated
treatment
train:
flow
and
residence
time.
EPA
did
one
central­
tendency
run
and
two
high­
end
runs,
with
one
of
these
two
critical
parameters
set
to
high
end
for
each
run.

Table
A­
1.
Summary
of
Source
Scenarios
Modeled
Component
Scenario
Nonaerated
Units
Aerated
Treatment
Train
1
2
3
4
5
7
8
9
Biomass
high
central
high
central
high
not
varied
not
varied
not
varied
Flow
central
central
high
high
central
central
high
central
Capacity/
residence
time
high
central
central
high
central
central
central
high
Solids
central
central
central
central
high
NA
NA
NA
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
4
A.
2
Source
Inputs
A.
2.1
Data
Sources
EPA
used
four
primary
sources
of
data:

#
BRS
database
 
waste
flows
#
SIS
survey
database
 
unit
characteristics
for
surface
impoundments
and
waste
characteristics
#
Tanks
database
(
U.
S.
EPA,
1987)
 
unit
characteristics
for
tanks
#
WATER9
default
values
 
parameters
not
available
from
the
other
sources.

The
BRS
data
are
the
data
reported
by
facilities
to
EPA
on
quantities
of
hazardous
wastes
managed.
EPA
pulled
BRS
data
on
waste
volumes
by
facility
and
by
waste
stream
of
the
F002
and
F005
waste
streams
being
considered
for
exemption.
For
the
risk
modeling,
EPA
used
the
facility­
level
data,
assuming
that
most
facilities
would
combine
these
small
waste
streams
for
treatment
or
storage.

The
SIS
survey
database
(
U.
S.
EPA,
2001)
is
the
most
comprehensive
available
data
set
on
Subtitle
D
(
nonhazardous)
surface
impoundments.
Although
the
universe
of
impoundments
in
the
database
was
sampled
specifically
for
SIS
in­
scope
impoundments,
the
database
has
undergone
extensive
quality
assurance
checks
and
is
being
used
in
other
Office
of
Solid
Waste
(
OSW)
work.
In
using
the
SIS
survey
data,
EPA
limited
the
universe
to
impoundments
that
manage
at
least
one
organic
chemical
(
not
necessarily
one
of
the
three
analyzed
in
this
assessment).
EPA
has
taken
this
approach
before
(
most
recently
to
assess
default
values
for
the
Industrial
Waste
Air
Model
(
IWAIR))
to
weed
out
impoundments
managing
only
inorganics,
which
tend
to
be
rather
different
than
those
that
manage
organics.
EPA
pulled
the
data
needed
and
calculated
weighted
medians
for
each
parameter,
using
the
survey
weights.
The
SIS
data
include
volume,
flow,
area,
depth,
and
most
of
the
needed
waste
characteristics.

The
Tanks
database
was
developed
for
the
Air
Characteristic
Study
and
also
used
for
the
Paints
listing
(
RTI,
2001).
The
database
is
based
on
EPA's
National
Survey
of
Hazardous
Waste
Treatment,
Storage,
Disposal,
and
Recycling
Facilities
(
TSDR)
survey
(
U.
S.
EPA,
1987)
and,
therefore,
reflects
hazardous
waste
units
rather
than
Subtitle
D
facilities.
However,
EPA
believes
these
are
the
only
data
currently
available
for
characterizing
tanks.
The
Tanks
database
does
not
have
associated
weights,
so
those
data
were
used
unweighted.
The
database
contains
data
on
the
volume
of
the
tank
and
the
quantity
of
hazardous
and
nonhazardous
waste
managed.
The
Tanks
database
does
not
contain
data
on
area
or
depth.
It
also
does
not
include
waste
characteristic
data;
therefore,
we
used
the
SIS
data
to
characterize
the
waste,
on
the
assumption
that
the
waste
streams
are
similar
regardless
of
whether
they
are
managed
in
a
tank
or
a
surface
impoundment.
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
5
The
WATER9
default
values
are
based
on
engineering
principles
and
were
used
in
this
analysis
only
for
parameters
to
which
the
model
is
not
highly
sensitive,
when
data
were
not
readily
available
from
other
sources.

A.
2.2
Unit
Characterization
A.
2.2.1
Nonaerated
units.
Many
of
the
parameters
used
in
WATER9
are
interrelated
and
cannot
be
set
independently
without
producing
an
inconsistent
data
set.
For
example,
a
very
large
waste
volume
would
not
be
likely
to
be
managed
in
a
very
small
unit.
Similarly,
volume
of
the
unit
and
dimensions,
such
as
area
and
depth,
are
related
but
not
to
the
degree
of
having
a
fixed
mathematical
relationship.
The
goal
was
to
choose,
for
each
scenario,
a
set
of
inputs
that
was
internally
consistent
and
plausible.

EPA
started
with
a
flow
equal
to
a
waste
quantity
corresponding
to
central­
tendency
and
high­
end
percentiles
from
the
BRS
survey
data
and
then
sized
the
units
accordingly,
using
data
from
the
other
data
sources.
This
approach
reflects
the
assumption
that
the
exempted
waste
is
the
only
waste
managed
in
the
modeled
unit;
if
other
wastes
were
co­
managed,
the
flow
through
the
unit
would
be
greater
than
the
waste
quantity
of
the
exempted
waste
stream,
and
the
unit
would
be
commensurately
larger.
The
flows
from
the
BRS
data,
even
at
the
high
end
of
the
distribution,
are
relatively
small
flows
from
the
perspective
of
wastewater
treatment.
Thus,
they
may
be
combined
with
other
wastes.
However,
for
nonaerated
units,
even
small
waste
streams
may
be
managed
separately.
Therefore,
EPA
assumed
that
the
potentially
exempted
waste
constitutes
all
of
the
flow
to
the
nonaerated
units
modeled.

Starting
with
flow,
EPA
characterized
the
units
using
the
following
steps:

1.
Flow.
EPA
chose
a
flow
based
on
the
facility­
level
waste
quantity
data
from
the
BRS,
using
the
median
for
a
central­
tendency
value
and
the
90th
percentile
for
a
high­
end
value.

2.
Volume.
Using
the
unweighted
SIS
data,
EPA
selected
a
subset
of
about
10
impoundments
with
flows
similar
to
the
flows
selected
in
Step
1
for
central
tendency
and
high
end.
Using
those
impoundments,
EPA
identified
a
range
of
volumes
associated
with
the
flow;
EPA
used
the
central
volume
when
setting
volume
to
a
central­
tendency
value
and
the
lowest
volume
when
setting
volume
to
a
high­
end
value.
EPA
took
the
same
approach
with
the
tanks
data
to
select
corresponding
volumes
for
tanks.

3.
Depth
and
Area.
EPA
performed
a
regression
to
relate
area
to
volume
for
the
SIS
data.
A
similar
regression
relating
depth
to
volume
had
already
been
done
with
the
tanks
data
for
the
Air
Characteristic
Study.
EPA
used
these
regressions
to
estimate
a
reasonable
depth
or
area
for
the
selected
volume.
EPA
calculated
the
remaining
parameter
(
area
or
depth)
by
dividing
volume
by
depth
or
area.

4.
Length,
Width,
or
Diameter.
For
impoundments,
EPA
calculated
length
and
width
from
area
by
assuming
the
unit
is
square.
For
tanks,
EPA
calculated
diameter
from
area
by
assuming
the
tank
is
circular.
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
6
To
set
values
for
the
solids
diversion
parameters
for
WATER9,
EPA
used
data
on
solids
removal
efficiencies
and
the
percentage
of
diverted
sludge
that
is
solids
from
the
SIS
survey
and
calculated
the
inputs
needed
for
WATER9
from
these.

A.
2.2.2
Aerated
treatment
train.
Like
the
nonaerated
units,
many
of
the
inputs
to
WATER9
for
the
aerated
treatment
train
are
interrelated.
In
the
case
of
the
aerated
treatment
train,
there
is
also
the
added
complexity
that
such
treatment
trains
are
rarely
sized
for
a
waste
stream
as
small
as
even
the
90th
percentile
F002/
F005
waste
stream
from
the
BRS
data.
The
presence
of
an
aerator
in
the
activated
sludge
unit,
for
example,
places
certain
limitations
on
the
volume
of
the
unit.
Similarly,
flows
and
residence
times
must
be
sufficient
to
maintain
the
biomass
in
the
activated
sludge
unit
 
there
must
be
enough
chemical
mass
as
food
to
feed
the
biomass
or
it
will
die
off.

The
aerated
treatment
train
units
were
sized
by
taking
the
50th
and
90th
percentile
flows
from
the
BRS
data
as
a
starting
point,
as
was
done
for
nonaerated
units.
Then,
using
typical
ranges
of
retention
time
for
activated
sludge
systems,
EPA
selected
a
central­
tendency
residence
time
and
a
high­
end
residence
time.
Using
the
flow
and
the
residence
time
for
a
particular
scenario,
the
capacities
of
the
three
units
(
primary
clarifier,
activated
sludge
unit,
and
secondary
clarifier)
were
estimated.
The
capacities
consider
the
influent
flow
(
from
the
BRS
data),
as
well
as
recycle
flow
from
the
secondary
clarifier
to
the
activated
sludge
unit.

In
sizing
the
units,
EPA
determined
that
the
central­
tendency
flow
from
the
BRS
data
resulted
in
unit
capacities
that
were
too
small
to
be
feasible
given
good
engineering
design
principles.
Therefore,
for
central­
tendency
flow,
EPA
used
the
smallest
flow
that
resulted
in
feasible
unit
capacities.
That
flow
is
about
the
75th
percentile
of
the
BRS
data.

It
should
be
noted
that
the
units
sized
for
both
75th
percentile
flow
and
90th
percentile
flow
are
still
extremely
small
and
are
not
likely
to
be
typical
of
actual
treatment
systems
of
this
type.
These
systems
are
small
enough
that
operating
such
a
system
would
require
feeding
the
biomass
because
there
would
be
insufficient
chemical
mass
to
maintain
optimal
biomass
levels
for
biodegradation.
Real
systems
are
likely
to
be
considerably
larger
and
combine
smaller
waste
streams
into
one
large
flow.
However,
WATER9
is
not
highly
sensitive
to
the
unit
capacity
and
flow
for
aerated
treatment
trains
designed
for
biodegradation
and
aeration­
assisted
volatilization.
These
loss
processes
are
much
more
dependent
on
residence
time.
Since
the
residence
times
used
reflect
typical
to
low­
end
values
(
low
residence
times
result
in
less
loss,
so
greater
effluent
and
sludge
concentration),
the
risk
results
should
be
similar
or
slightly
higher
than
what
would
be
seen
if
a
waste
stream
with
the
same
concentration
were
modeled
in
larger
units.
Dilution
of
these
wastes
with
other
larger
waste
streams
not
containing
these
chemicals
(
or
containing
them
at
lower
concentrations)
would
have
a
much
greater
impact
on
risk.

Attachment
A.
2
provides
all
the
WATER9
input
values
used
for
each
scenario
for
nonaerated
units
and
the
aerated
treatment
train.
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
7
A.
2.3
Waste
Characteristics
EPA
set
all
waste
characteristics
to
weighted
central­
tendency
values
from
the
SIS
survey
data.
The
median
active
biomass
value
from
the
SIS
survey
data
was
0,
which
is
a
reasonable
value
for
nonaerated
units.
Table
A­
2
presents
the
waste
properties
used.

Table
A­
2.
Waste
Properties
Used
in
WATER9
Modeling
Parameter
Units
Nonaerated
Aerated
Treatment
Train
Value
Source
Value
Source
Solids
ppmw
141
SIS
survey
(
median)
200
best
professional
judgment
Oil
ppmw
0
SIS
survey
(
median)
1
best
professional
judgment
Temperature
C
24.52
Hartford,
CT
30
best
professional
judgment
A.
2.4
Physical­
Chemical
Properties
Some
of
the
WATER9
chemical
property
default
values
were
updated
using
the
Superfund
Chemical
Data
Matrix
(
SCDM)
(
U.
S.
EPA,
1997).
Table
A­
3
presents
the
physicalchemical
property
values
used
and
their
source
(
SCDM
or
WATER9
database).

Table
A­
3.
Physical­
Chemical
Properties
Used
in
WATER9
Parameter
Units
Value
Source
Benzene
2­
Ethoxyethanol
1,1,2­
Trichloroethane
Density
g/
cm3
0.88
0.93
1.4
SCDM
Molecular
weight
g/
mol
78
90
133
SCDM
Diffusivity
in
water
cm2/
s
1E­
5
9.8E­
6
1E­
5
WATER9
Diffusivity
in
air
cm2/
s
0.0895
0.082
0.067
WATER9
Vapor
pressure
mmHg
95
5.3
23
SCDM
Henry's
law
constant
atm­
m3/
m
5.55E­
3
1.23E­
7
9.1E­
4
SCDM
Vapor
pressure
temperature
coefficient
A
unitless
6.9
7.9
7.2
WATER9
Vapor
pressure
temperature
coefficient
B
unitless
1,200
1,800
1,500
WATER9
Vapor
pressure
temperature
coefficient
C
unitless
220
230
230
WATER9
(
continued)
Table
A­
3.
(
continued)
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
Parameter
Units
Value
Source
Benzene
2­
Ethoxyethanol
1,1,2­
Trichloroethane
A­
8
First­
order
biorate
constant
l/
g­
hr
1.4
1
0.74
WATER9
Zero­
order
biorate
constant
mg/
g­
hr
19
20
3.5
WATER9
Log
octanol
water
coefficient
(
Kow)
unitless
2.13
­
0.1
2
SCDM
Solubility
mg/
L
1,750
1,000,000
4,400
SCDM
A.
4
Fate
and
Transport
Inputs
The
groundwater
DAFs
are
all
for
a
no­
liner
scenario.
They
vary
by
duration
and
percentile
from
the
distribution
of
DAFs.
The
50th
percentile
values
were
used
for
central
tendency
and
the
90th
percentile
DAFs
for
high
end.
The
duration
was
chosen
to
match
the
exposure
duration.
Table
A­
4
shows
the
DAFs
used
for
surface
impoundments,
and
Table
A­
5
shows
them
for
landfills.
Because
2­
ethoxyethanol
is
a
noncarcinogen,
calculations
for
2­
ethoxyethanol
are
not
affected
by
changes
in
exposure
duration.
Therefore,
only
the
9­
year
duration
is
shown
for
2­
ethoxyethanol.

Table
A­
4.
IWEM
Tier
I
DAFs
for
Surface
Impoundments
Percentile
Benzene
2­
Ethoxyethanol
1,1,2­
Trichloroethane
Duration
9­
year
30­
year
9­
year
9­
year
30­
year
50th
12.5
14.9
12.3
14
16.9
90th
1.4
1.6
1.4
1.4
1.6
Table
A­
5.
IWEM
Tier
I
DAFs
for
Landfills
Percentile
Benzene
2­
Ethoxyethanol
1,1,2­
Trichloroethane
Duration
9­
year
30­
year
9­
year
9­
year
30­
year
50th
93.5
93.5
95.5
127
127
90th
2.2
2.2
2.2
2.5
2.5
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
9
A.
5
Exposure
Factors
For
central­
tendency
exposure
scenarios,
exposure
duration
was
set
to
9
years.
For
highend
exposure
scenarios,
exposure
duration
was
set
to
30
years.
All
other
exposure
factors
are
the
defaults
used
in
IWEM.

A.
6
Toxicity
Attachment
A.
3
summarizes
how
health
benchmarks
were
set
for
IWEM.
Table
A­
6
summarizes
the
health
benchmarks
for
the
three
chemicals
considered
in
this
assessment.

Table
A­
6.
Health
Benchmarks
Used
in
Groundwater
Assessment
Chemical
Cancer
Noncancer
Ingestion
CSF
(
per
mg/
kg­
d)
Inhalation
CSF
(
per
mg/
kg­
d)
RfD
(
mg/
kg­
d)
RfC
(
mg/
m3)

Benzene
Central
tendency
3.5E­
2
5.0E­
6
not
used
not
used
High
end
5.5E­
2
7.8E­
6
not
used
not
used
2­
Ethoxyethanol
NA
NA
0.4
0.2
1,1,2­
Trichloroethane
5.7E­
2
5.6E­
2
not
used
not
used
A.
7
References
RTI.
2001.
Risk
Assessment
Technical
Background
Document
for
the
Paints
and
Coatings
Hazardous
Waste
Listing
Determination.
Submitted
to
EPA
Office
of
Solid
Waste,
Washington,
DC.
http://
www.
epa.
gov/
epaoswer/
hazwaste/
id/
paint/
(
section
1­
2.
pdf;
section
3­
4.
pdf;
section
5­
6.
pdf;
and
section
7­
10.
pdf).

U.
S.
EPA
(
Environmental
Protection
Agency).
1987.
1986
National
Survey
of
Hazardous
Waste,
Storage,
Disposal,
and
Recycling
Facilities
Database.

U.
S.
EPA
(
Environmental
Protection
Agency).
1996.
Superfund
Chemical
Data
Matrix
(
SCDM).
Office
of
Emergency
and
Remedial
Response.
Web
site
at
http://
www.
epa.
gov/
oerrpage/
superfund/
resources/
scdm/
index.
htm.
June.

U.
S.
EPA
(
Environmental
Protection
Agency).
2001.
Industrial
Surface
Impoundments
in
the
United
States.
Office
of
Solid
Waste,
Washington,
DC.
EPA530­
R­
01­
005.
March.
Appendix
A
Data
Inputs
for
Phase
II
Groundwater
Modeling
A­
10
This
page
intentionally
left
blank.
Attachment
A­
1
Description
of
HBN
Development
Methodology
Used
for
IWEM
This
page
intentionally
left
blank.
RESEARCH
TRIANGLE
INSTITUTE
MEMORANDUM
Date:
August
9,
2001
To:
Ann
Johnson,
EPA
From:
Susan
N.
Wolf,
Pam
Birak,
Jessica
Lin,
and
Robert
S.
Truesdale,
RTI
Subject:
Description
of
HBN
development
methodology
used
for
IWEM
Two
Toxicity
Reference
Levels
(
TRLs)
are
included
in
the
Industrial
Waste
Evaluation
Model
(
IWEM)
software:
Maximum
Contaminant
Levels
(
MCLs),
which
are
available
for
some
waste
constituents,
and
Health­
Based
Numbers
(
HBNs),
which
are
available
for
all
waste
constituents
(
including
waste
constituent
daughter
products).
This
memorandum
describes
the
methodology
used
to
develop
HBNs
for
constituents
that
cause
cancer
and
constituents
that
produce
noncancer
health
effects.

All
constituents
currently
included
in
the
IWEM
software
have
an
ingestion
HBN.
In
IWEM,
an
ingestion
HBN
is
the
maximum
concentration
of
the
constituent
in
groundwater
that
is
not
expected
to
cause
adverse
health
effects
in
most
individuals
who
drink
the
groundwater.
For
organic
constituents
and
mercury,
IWEM
also
uses
inhalation
HBNs,
which
are
the
maximum
concentrations
of
a
constituent
in
groundwater
that
are
not
expected
to
cause
adverse
health
effects
in
most
adults
who
inhale
the
constituent
while
showering.
To
calculate
HBNs,
we
only
consider
parameters
that
describe
a
constituent's
health
effects
and
an
individual's
(
receptor's)
exposure
to
the
constituent
from
drinking
or
showering.
In
contrast,
the
MCL
includes
consideration
of
additional
factors,
such
as
the
cost
of
treatment,
and
does
not
consider
the
inhalation
exposure
route.

The
sections
below
provide
our
methodology
for
calculating
the
cancer
and
noncancer
HBNs
for
ingestion
and
inhalation
of
the
contituents
in
IWEM.
The
target
risk
used
to
calculate
the
HBN
for
carcinogens
is
1
×
10­
6
(
unitless).
The
target
hazard
quotient
used
to
calculate
the
HBN
for
noncarcinogens
is
1.0
(
unitless).
These
targets
are
used
to
calculate
independent
HBNs
for
inhalation
and
ingestion.
IWEM
does
not
combine
exposure
from
showering
and
drinking,
but
considers
these
routes
of
exposure
separately
to
ensure
use
of
the
lowest,
or
most
protective,
HBN
for
a
particular
chemical.

1.0
Ingestion
HBNs
The
IWEM
ingestion
HBNs
are
calculated
using
equations
based
on
the
U.
S.
Environmental
Protection
Agency's
(
EPA's)
Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991).
These
equations
and
inputs
Page
2
of
13
differ
for
cancer­
causing
chemicals
and
chemicals
that
have
adverse
health
effects
other
than
cancer.
The
primary
differences
result
from
cancer
toxicity
criteria's
being
based
on
an
average
daily
dose
over
a
lifetime,
while
noncancer
health
benchmarks
use
less­
than­
lifetime
estimates
of
exposure.

1.1
Ingestion
HBNs
for
Constituents
That
Cause
Cancer
The
equation
for
calculating
ingestion
HBNs
for
carcinogens
uses
the
cancer
slope
factor
(
CSF)
exposure
variables
to
determine
the
highest
concentration
of
the
carcinogen
in
drinking
water
that
will
not
exceed
the
target
risk.
Because
the
CSF
is
based
on
an
average
day's
exposure
over
a
lifetime,
the
equation
also
requires
estimates
of
how
many
days
per
year
a
person
is
exposed
(
exposure
frequency),
how
many
years
this
exposure
continues
(
exposure
duration),
and
the
average
amount
of
water
a
person
drinks
every
day
(
intake
rate).
Duration
of
exposure
is
critical
because
the
CSF
is
based
on
the
lifetime
average
daily
dose.
Therefore,
we
average
the
total
dose
received
over
an
average
person's
lifetime,
where
the
average
person's
lifetime
is
the
averaging
time
for
the
exposure
calculation.

where
C_
INGEST_
HBN
=
carcinogenic
risk
HBN
for
water
due
to
ingestion
(
mg/
L)
TR
=
target
risk
for
carcinogens
=
1
x
10­
6
CSFo
=
oral
cancer
slope
factor
(
mg/
kg­
d)­
1
AT
=
averaging
time
(
yr)
=
70
yrs
EF
=
exposure
frequency
(
d/
yr)
=
350
d/
yr
CRw
=
intake
rate
of
water
(
L/
kg/
d)
ED
=
exposure
duration
(
yr)
365
=
conversion
factor
(
d/
yr).

The
sources
for
the
exposure
parameter
values
used
to
calculate
the
cancer
HBNs
are
summarized
in
Table
1­
1.
To
be
protective
of
exposures
to
carcinogens
in
a
residential
setting,
EPA
focuses
on
exposures
to
individuals
who
may
live
in
the
same
residence
for
a
long
period
of
time
(
i.
e.,
an
exposure
duration
of
30
years,
the
95th
percentile
for
population
mobility).
Page
3
of
13
Table
1­
1.
Exposure
Parameter
Values
for
Carcinogens
Exposure
Parameter
Value
Units
Source
Drinking
Water
Intake
Rate
25.2
mL/
kg/
d
The
value
is
a
time­
weighted
average
of
mean
drinking
water
intake
rates
for
adults
aged
0
to
29
years.

Table
3­
7
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997a)

Exposure
Frequency
350
d/
yr
The
exposure
frequency
is
the
number
of
days
per
year
that
an
individual
is
exposed.
A
value
of
350
days
per
year
considers
that
an
individual
is
away
from
home
for
2
weeks
per
year.

Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991)

Exposure
Duration
30
yr
The
exposure
duration
is
the
number
of
years
that
an
individual
is
exposed.
Thirty
years
is
the
95th
percentile
value
for
population
mobility
(
exposure
duration).

Table
15­
176
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997b)

Averaging
Time
70
yr
Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991)

1.2
Ingestion
HBNs
for
Constituents
that
Cause
Noncancer
Health
Effects
To
develop
ingestion
HBNs
for
constituents
that
cause
health
effects
other
than
cancer,
we
used
an
equation
that
determines
the
maximum
concentration
that
will
not
exceed
the
target
hazard
quotient.
The
equation
uses
the
reference
dose,
which
is
the
maximum
average
daily
dose
that
will
not
cause
adverse
health
effects,
and
requires
estimates
of
exposure
frequency
and
water
intake
rate.
Page
4
of
13
where
NC_
INGEST_
HBN
=
noncarcinogenic
risk
HBN
for
water
(
mg/
L)
THI
=
target
hazard
index
for
noncarcinogens
=
1
RfD
=
reference
dose
(
mg/
kg­
d)
EF
=
exposure
frequency
(
d/
yr)
=
350
d/
yr
CRw
=
intake
rate
of
water
for
a
child
aged
1
to
6
yrs
(
L/
kg/
d)
365
=
conversion
factor
(
d/
yr).

The
sources
for
the
exposure
parameter
values
used
to
calculate
the
noncancer
HBN
are
summarized
in
Table
1­
2.
Because
toxicity
criteria
for
noncarcinogens
are
based
on
less­
thanlifetime
exposures,
and
to
be
protective
of
toxic
effects
to
children,
the
equation
uses
a
drinking
water
intake
rate
that
is
appropriate
for
children
under
6
years
old.

Table
1­
2.
Exposure
Parameter
Values
for
Noncancer
Health
Effects
Exposure
Parameter
Value
Units
Source
Drinking
Water
Intake
Rate
42.6
mL/
kg/
d
The
value
is
a
time­
weighted
average
of
mean
drinking
water
intake
rates
for
children
aged
0
to
6
years.

Table
3­
7
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997a)

Exposure
Frequency
350
d/
yr
The
exposure
frequency
is
the
number
of
days
per
year
that
an
individual
is
exposed.
A
value
of
350
days
per
year
considers
that
an
individual
is
away
from
home
for
2
weeks
per
year.

Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991)

2.0
Inhalation
HBN
Methodology
In
IWEM,
the
inhalation
HBN
is
the
maximum
concentration
of
a
constituent
in
groundwater
that
is
not
expected
to
cause
adverse
health
effects
in
most
adults
who
inhale
the
constituent
as
a
result
of
activities
associated
with
showering
(
we
assume
that
children
take
baths;
consequently,
we
do
not
evaluate
children's
shower­
related
exposure).
The
inhalation
HBN
is
the
groundwater
concentration
that
results
in
a
target
risk
of
1
×
10­
6
for
carcinogens
or
a
Page
5
of
13
target
hazard
quotient
of
1
for
noncarcinogens.
We
only
calculated
inhalation
HBNs
for
constituents
that
(
1)
volatilize
(
e.
g.,
mercury
and
organic
constituents)
and
(
2)
have
an
inhalation
health
benchmark
available
(
e.
g.,
reference
concentrations
[
RfC],
inhalation
unit
risk
factors
[
URF],
and/
or
inhalation
cancer
slope
factors
[
CSFi]).
Inhalation
HBNs
were
not
calculated
for
airborne
metal
particles
because
we
do
not
expect
these
to
be
produced
by
a
shower.

We
developed
the
inhalation
HBNs
in
two
basic
steps.
First,
Section
2.1
describes
how
we
used
a
shower
model
to
calculate
the
average
concentration
of
a
waste
constituent
in
air
that
an
adult
will
be
exposed
to
both
during
showering
and
during
time
spent
in
the
shower
stall
and/
or
bathroom
after
showering.
(
The
HBNs
do
not
reflect
inhalation
exposure
to
groundwater
that
results
from
other
household
uses
of
water.)
Because
the
relationship
between
groundwater
concentration
and
risk
(
or
hazard
quotient)
is
linear,
we
used
a
single
unit
groundwater
concentration
(
e.
g.,
1
mg/
L)
that
was
within
the
solubility
limits
of
the
constituent
so
that
the
model
would
calculate
a
unit
average
shower
air
concentration.
To
reflect
average
daily
dose,
the
model
adjusted
this
unit
shower
air
concentration
and
outputs
a
unit
average
daily
indoor
air
concentration
for
the
second
step
of
the
analysis.

Second,
we
used
this
unit
average
indoor
air
concentration
in
air
to
calculate
the
HBN.
The
HBN
equations
first
calculate
the
risk
or
hazard
quotient
associated
with
the
unit
air
concentrations
from
the
shower
model,
and
then
use
ratios
to
determine
the
groundwater
concentration
(
or
HBN)
associated
with
the
target
risk
level
or
target
hazard
quotient.
Section
2.2
describes
the
application
of
the
HBN
equations
for
cancer­
causing
chemicals
and
for
chemicals
with
non­
cancer
health
effects.

2.1
Calculation
of
Exposure
Concentrations
from
Showering
Individuals
may
be
exposed
to
waste
constituents
through
inhalation
of
vapor­
phase
emissions
from
groundwater.
Such
exposure
may
occur
during
the
time
spent
in
the
shower
while
showering,
in
the
shower
stall
after
showering,
and
in
the
bathroom
after
showering.
To
evaluate
these
exposures,
EPA
used
a
shower
model
to
calculate
the
average
constituent
concentration
in
the
shower
stall
and
bathroom
air.
This
section
describes
this
model
and
assumptions
(
Section
2.1.1)
along
with
uncertainties
and
limitations
associated
with
its
use
(
Section
2.1.2).

A
primary
assumption
of
this
evaluation
is
that
the
gas­
phase
concentration
of
a
constituent
results
solely
from
showering
activity.
Previous
versions
of
the
shower
model
included
emissions
due
to
other
household
uses
of
water
and
risks
due
to
inhalation
for
time
spent
in
the
remainder
of
the
house.
However,
the
risk
from
inhalation
exposures
in
the
remainder
of
the
house
has
been
shown
to
be
several
orders
of
magnitude
lower
than
the
risk
from
inhalation
exposures
in
the
bathroom
and
during
showering
(
EPA,
1997d).
Given
the
low
risk
due
to
exposure
from
the
remainder
of
the
house
and
the
difficulty
in
collecting
the
input
data
needed
to
estimate
household
chemical
concentrations
from
other
sources,
the
current
version
of
the
shower
model
has
been
simplified
to
focus
on
the
greatest
sources
of
exposure
and
risk
due
to
use
of
contaminated
water.
Page
6
of
13
2.1.1
Shower
Model
The
shower
model
estimates
the
change
in
the
shower
constituent
air
concentrations
over
time
as
a
function
of
the
mass
of
constituent
transferred
from
the
shower
water
to
shower
vapors.
After
calculating
the
predicted
vapor­
phase
constituent
concentration
in
the
shower
stall
and
bathroom
during
showering,
the
model
calculates
an
average
daily
indoor
air
concentration
using
volumetric
air
exchange
rates
between
the
shower
stall,
bathroom,
and
house.
The
shower
model
is
based
on
differential
equations
presented
in
McKone
(
1987)
and
Little
(
1992).
Memo
Attachment
A
provides
details
on
these
equations
and
explains
how
we
implemented
them
in
the
model.
Tables
A­
1
to
A­
11
(
in
Memo
Attachment
A)
present
the
equations,
and
Table
A­
12
(
in
Memo
Attachment
A)
provides
the
model
parameters
for
exposure
(
e.
g.,
exposure
time,
shower
properties).

The
model's
calculations
of
mass
transfer
between
the
liquid
and
vapor
phases
of
the
constituent
in
the
shower,
and
subsequent
air
transfer
between
the
shower
stall
and
bathroom
depend
on
both
physical
parameters
(
shower
properties)
and
chemical­
specific
properties.
With
respect
to
chemical­
specific
properties,
a
constituent's
ability
to
transfer
mass
from
the
liquid
phase
to
gas
phase
is
characterized
by
its
diffusivity,
or
how
well
it
mixes
with
other
gases.
Diffusion
coefficients
in
air
and
water
quantify
diffusivity
for
each
constituent,
which
depends
on
the
constituent's
density
and
molecular
weight.
Transfer
from
the
shower
water
to
air
is
controlled
by
the
air
pressure
in
the
shower
stall.
We
used
Henry's
law
to
quantify
the
amount
of
constituent
dissolved
in
the
shower
water
(
equation
in
Table
A­
3
of
Memo
Attachment
A).
Henry's
law
states
that
the
amount
of
a
gas
dissolved
in
solution
is
directly
proportional
to
the
pressure
of
the
gas
above
the
solution.
Once
a
constituent's
diffusion
coefficients
in
air
and
water
and
its
Henry's
law
constant
coefficient
were
known,
an
overall
mass
transfer
coefficient
was
calculated
to
quantify
the
constituent's
ability
to
volatilize
from
the
shower
water
into
the
air
(
equation
in
Table
A­
5
of
Memo
Attachment
A).

The
physical
properties
of
the
shower
also
affect
constituent
air
concentrations.
There
are
macro­
level
parameters,
such
as
the
volume
of
the
shower
stall,
the
water
flow
rate,
and
the
height
of
the
nozzle,
which
limit
the
length
of
time
the
constituent
is
in
the
shower
stall
and
the
amount
of
it
that
may
accumulate
in
the
shower
air.
These
macro­
level
physical
parameters
were
set
to
standard
values,
based
on
available
literature
(
see
Table
2­
1).
These
shower
parameters
provide
a
cap
on
the
maximum
possible
constituent
concentration
that
may
accumulate
in
the
shower
stall,
and
they
are
required
to
calculate
equilibrium
constituent
concentrations
between
the
water
and
air
during
shower
time
(
equations
in
Table
A­
6
of
Memo
Attachment
A).

On
a
smaller
scale,
the
fraction
of
constituent
emitted
by
a
water
droplet
into
the
shower
air
depends
upon
the
level
of
gas­
phase
saturation
in
the
shower
stall
and
a
dimensionless
mass
transfer
coefficient
(
equation
in
Table
A­
7
of
Memo
Attachment
A).
Calculation
of
the
dimensionless
mass
transfer
coefficient
uses
micro­
level
droplet
properties,
such
as
droplet
diameter
and
velocity,
and
some
macro­
level
shower
properties
discussed
above
to
quantify
the
length
of
time
a
constituent
is
in
contact
with
the
surrounding
air
and
the
amount
that
may
volatilize
(
surface
area
of
the
droplet)
(
equation
in
Table
A­
4
of
Memo
Attachment
A).
The
droplet's
diameter
(
0.098
cm)
and
velocity
(
400
cm/
s)
were
set
to
constant
values
that
correlated
well
with
existing
data
(
Table
2­
1).
Page
7
of
13
Table
2­
1.
Shower
Model
Input
Parameters
Input
Parameter
Description
Value
Units
Reference
Comment
ShowerStallTime
Time
in
shower
stall
after
showering
5
min
U.
S.
EPA,
1997c
Table
15­
23.
50th
percentile
overall
T_
bathroom
Time
spent
in
bathroom,
not
in
shower
5
min
U.
S.
EPA,
1997c
Table
15­
32.
50th
percentile
overall
ShowerTime
Shower
time,
50th
percentile
15
min
U.
S.
EPA,
1997c
Table
15­
21.
50th
percentile
overall
Vb
Volume
of
the
bathroom
10
m3
McKone,
T.,
1987
Vs
Volume
of
shower
2
m3
McKone,
T.,
1987
NozHeight
Height
of
shower
head
1.8
m
Little,
J.,
1992
Selected
based
on
the
maximum
height
reported
in
Table
1,
a
summary
of
five
studies.

Qsb
Volumetric
exchange
rate
between
the
shower
and
the
bathroom
100
L/
min
RTI­
derived
value
Estimated
from
the
volume
and
flow
rate
in
McKone
(
1987)
such
that
the
exchange
rate
equals
the
volume
divided
by
the
residence
time
(
e.
g.,

2000L/
20
min).

ShowerRate
Rate
of
water
flow
from
shower
head
10
L/
min
RTI­
derived
value
Value
obtained
by
averaging
the
flow
rates
reported
in
five
studies
in
Table
1
of
Little
(
1992)
(
QL)
=

10.08
L/
min.

DropVel
Terminal
velocity
of
water
drop
400
cm/
s
RTI­
derived
value
Selected
value
by
correlating
to
existing
data.

DropDiam
Diameter
of
shower
water
drop
0.098
cm
RTI­
derived
value
Estimated
as
a
function
of
terminal
velocity<=
600cm/
sec
(
Coburn,
1996).

Qbh
Volumetric
exchange
rate
between
the
bathroom
and
the
house
300
L/
min
RTI­
derived
value
Estimated
from
the
volume
and
flow
rate
in
McKone
(
1987)
such
that
the
exchange
rate
equals
the
volume
divided
by
the
residence
time
(
e.
g.,

10,000L/
30
min).

Cin
Constituent
concentration
in
incoming
water
0.001
mg/
L
NA
Unit
concentration
selected.
Page
8
of
13
After
calculating
the
fraction
of
constituent
that
can
be
emitted
from
a
droplet,
the
shower
model
calculates
the
potential
amount
of
constituent
mass
that
may
be
emitted
into
the
air
during
0.2­
minute
time
steps
for
the
duration
of
the
showering
time.
The
mass
emitted
during
a
time
step
is
limited
by
the
fraction
that
can
be
emitted
and
the
existing
gas­
phase
constituent
concentration
in
the
shower
stall
at
the
beginning
of
the
time
step.
We
calculate
this
incremental
mass
using
the
physical
parameters
of
the
shower
in
conjunction
with
constituent­
specific
properties
to
estimate
how
much
constituent
may
accumulate
in
the
shower
air
(
equation
in
Table
A­
6
of
Memo
Attachment
A).

Because
of
air
flow
between
the
shower
stall
and
bathroom,
the
actual
gas­
phase
constituent
concentration
in
the
shower
is
less
than
the
potential
amount
calculated
above.
The
volumetric
exchange
rates
between
the
shower
stall
and
bathroom
and
the
bathroom
and
rest
of
the
house
were
assigned
constant
values
derived
from
McKone
(
1987)
(
Table
2­
1).
These
two
parameters
quantify
the
dilution
of
constituent
concentration
in
the
shower
air.
The
shower
model
uses
these
two
loss
components
to
calculate
the
actual
constituent
concentration
in
the
shower
stall
and
in
the
bathroom
at
the
end
of
each
time
step
(
equations
in
Tables
A­
9
and
A­
10
of
Memo
Attachment
A).

To
calculate
average
daily
indoor
air
concentrations,
values
for
exposure
time
were
taken
from
the
Exposure
Factors
Handbook
(
EPA,
1997a).
We
selected
the
50th
percentile
for
adults'
time
spent
taking
a
shower,
time
spent
in
the
shower
stall
after
showering,
and
time
spent
in
the
bathroom
after
showering
(
Table
2­
1).
The
shower
model
calculates
constituent
concentrations
in
the
shower
stall
and
bathroom
for
each
time
step
until
the
end
of
the
time
spent
in
the
shower
and
bathroom,
and
then
averages
constituent
concentrations
for
the
two
compartments.
The
model
then
calculates
the
daily
indoor
constituent
concentration
by
averaging
these
concentrations
over
the
length
of
an
entire
day
(
equation
in
Table
A­
11
of
Memo
Attachment
A),
assuming
that
there
is
no
additional
inhalation
exposure
to
the
constituent
during
the
day
(
i.
e.,
that
the
gas­
phase
constituent
concentration
in
the
house
is
negligible).

2.1.2
Shower
Model
Uncertainties
and
Limitations
A
primary
limitation
of
the
shower
model
is
that
the
gas­
phase
concentration
of
a
constituent
in
the
house
results
only
from
shower­
related
activities.
The
model
does
not
include
other
household
uses
of
water
(
e.
g.,
toilet
use)
in
calculating
average
indoor
concentrations.
However,
the
risk
of
inhalation
exposure
from
other
water
use
activities
has
been
demonstrated
to
be
several
magnitudes
lower
than
the
exposure
risk
from
showering
(
EPA,
1997d).
In
addition,
there
is
also
large
uncertainty
in
estimating
other
household­
activity
chemical
concentrations.
To
quantify
the
inhalation
exposure
risk
for
the
entire
house,
the
model
would
require
an
estimate
of
the
air
exchange
rate
between
the
house
and
outdoor
air,
exposure
time
in
the
house,
and
the
amount
of
nonshower
water
usage.
Given
the
uncertainties
in
these
input
parameters
and
the
low
risk
due
to
exposure
from
the
remainder
of
the
house,
the
shower
model
focuses
only
on
the
greatest
source
of
exposure
and
risk
due
to
use
of
contaminated
water.

The
input
parameter
values
are
another
source
of
uncertainty
for
the
shower
model.
In
selecting
values
for
the
shower
properties
(
shower
and
bathroom
volume,
nozzle
height,
and
Page
9
of
13
flow
rate),
we
used
in
most
cases
mid­
range
values
that
were
reported
in
the
literature.
Though
setting
the
shower
parameters
to
constants
does
not
capture
possible
variability
in
these
variables,
the
results
using
these
fixed
values
compare
favorably
to
experimental
data
for
numerous
organic
compounds
of
varying
volatility
(
Coburn,
1996).
The
droplet
properties
(
diameter
and
velocity)
are
also
constants,
but
their
values
were
selected
based
on
correlation
to
existing
data,
resulting
in
less
uncertainty.
The
largest
uncertainty
is
likely
in
the
volumetric
exchange
rates
used
between
the
shower
and
bathroom
and
the
bathroom
and
the
rest
of
house.
These
values,
300
L/
min
for
the
exchange
rate
between
the
bathroom
and
the
house,
and
100
L/
min
for
the
exchange
rate
between
the
shower
and
the
bathroom,
were
derived
from
McKone
(
1987).
The
range
of
values
reported
in
a
five­
study
summary
(
Little,
1992),
however,
was
35
to
460
L/
min
for
exchange
between
the
shower
and
the
bathroom
and
38
to
480
L/
min
for
exchange
between
the
bathroom
and
the
rest
of
the
house,
making
these
the
most
uncertain
variables
among
the
shower
model
inputs.

2.2
Calculating
Inhalation
HBNs
To
calculate
HBNs,
we
selected
a
unit
groundwater
concentration
(
usually
1
mg/
L)
within
the
solubility
limits
of
each
constituent
and
ran
the
shower
model
using
that
concentration
to
calculate
a
unit
average
daily
indoor
air
concentration.
We
used
this
unit
air
concentration
to
calculate
a
corresponding
unit
risk
(
for
cancer­
causing
chemicals)
or
unit
hazard
quotient
(
for
constituents
with
noncancer
health
effects).
Because
there
is
a
linear
relationship
between
groundwater
concentration
and
risk,
we
could
use
simple
ratios
to
adjust
the
unit
groundwater
concentrations
to
the
groundwater
concentration
corresponding
to
the
target
risk
or
target
hazard
quotient
(
i.
e.,
the
inhalation
HBN).
Section
2.2.1
describes
this
process
for
carcinogens
while
Section
2.2.2
discusses
the
approach
we
used
for
noncarcinogens.
As
a
final
step,
we
checked
every
inhalation
HBN
to
ensure
that
it
did
not
exceed
the
constituent's
solubility,
as
described
in
Section
2.2.3.

2.2.1
Inhalation
HBNs
for
Carcinogens
To
calculate
the
inhalation
HBN
for
carcinogens,
we
first
calculate
the
average
daily
dose
(
ADD)
from
inhalation
due
to
exposure
to
contaminated
groundwater
during
showering.
The
ADD
is
calculated
from
the
unit
air
concentration
output
by
the
shower
model,
as
follows:

where
ADD
=
average
daily
dose
(
mg/
kg­
d)
at
the
unit
groundwater
concentration
Cair_
indoor
=
average
air
concentration
over
a
day
(
mg/
m3)
(
calculated
from
the
unit
groundwater
concentration
using
the
shower
model)
IR
=
inhalation
rate
(
m3/
d)
Page
10
of
13
BW
=
body
weight
(
kg).

We
then
calculated
the
risk
at
the
modeled
unit
groundwater
concentration
from
the
ADD,
as
shown
below:

where
Risk_
modeled
=
risk
resulting
from
groundwater
concentration
modeled
ED
=
exposure
duration
(
yr)
=
30
yr
EF
=
exposure
frequency
(
d/
yr)
=
350
d/
yr
AT
=
averaging
time
(
yr)
=
70
yr
CSFi
=
inhalation
cancer
slope
factor
(
mg/
kg­
d)­
1
ADD
=
average
daily
dose
(
mg/
kg­
d)
at
the
unit
groundwater
concentration
365
=
conversion
factor
(
d/
yr).

We
then
derived
the
target
groundwater
concentration
(
i.
e.,
the
inhalation
HBN)
by
adjusting
the
modeled
unit
groundwater
concentration
using
the
simple
ratio
of
target
risk
to
the
modeled
risk:

where
HBN
=
concentration
in
groundwater
resulting
in
target
risk
(:
g/
L)
C_
GW_
modeled
=
unit
concentration
in
groundwater
used
in
shower
model
(:
g/
L)
Risk_
T
=
target
risk
for
carcinogens
=
1
x
10­
6
Risk_
modeled
=
risk
resulting
from
groundwater
concentration
modeled.

This
equation
assumes
that
the
relationship
between
groundwater
concentration
and
risk
is
linear,
which
we
confirmed
by
running
the
shower
model
using
the
target
groundwater
concentration
for
several
constituents
and
comparing
the
results
to
the
target
risk
level.

The
inhalation
HBNs
for
cancer­
causing
chemicals
were
based
on
adult
exposure
parameters.
The
sources
for
the
exposure
parameter
values
used
in
the
equations
above
are
summarized
in
Table
2­
2.
Page
11
of
13
Table
2­
2.
Exposure
Parameter
Values
Exposure
Parameter
Value
Units
Source
Inhalation
Rate
13.25
m3/
d
The
value
corresponds
to
the
mean
inhalation
rates
for
adults
aged
19
to
65+.
The
value
was
calculated
by
averaging
the
daily
mean
inhalation
rates
for
females
(
11.3
m3/
d)
and
males
(
15.2
m3/
d).

Table
5­
23
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997a)

Body
Weight
71.8
kg
The
value
corresponds
to
the
mean
body
weight
of
18­
to
75­
year­
old
men
and
women.

Tables
7­
2
and
7­
11
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997a)

Exposure
Frequency
350
d/
yr
The
exposure
frequency
is
the
number
of
days
per
year
that
an
individual
is
exposed.
A
value
of
350
days
per
year
considers
that
an
individual
is
away
from
home
for
2
weeks
per
year.

Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991)

Exposure
Duration
30
yr
The
exposure
duration
is
the
number
of
years
that
an
individual
is
exposed.
Thirty
years
is
the
95th
percentile
value
for
population
mobility
(
exposure
duration).

Table
15­
176
of
the
Exposure
Factors
Handbook
(
U.
S.
EPA,
1997b)

Averaging
Time
70
yr
Risk
Assessment
Guidance
for
Superfund:
Volume
1
 
Human
Health
Evaluation
Manual
(
U.
S.
EPA,
1991)

2.2.1
Inhalation
HBNs
for
Noncarcinogens
Calculating
inhalation
HBNs
for
noncarcinogens
is
simpler
than
calculating
them
for
carcinogens
because
the
toxicity
criterion
(
RfC)
is
expressed
as
a
concentration
in
air.
The
HBN
Page
12
of
13
is
calculated
by
first
determining
the
hazard
quotient
resulting
from
the
unit
air
concentration
output
by
the
shower
model:

where
HQ_
modeled
=
hazard
quotient
resulting
from
the
groundwater
concentration
modeled
Cair_
indoor
=
average
air
concentration
over
a
day
(
mg/
m3)
(
calculated
from
the
unit
groundwater
concentration
using
the
shower
model)
RfC
=
reference
concentration
(
mg/
m3).

We
then
derived
the
target
groundwater
concentration
(
i.
e.,
the
inhalation
HBN)
by
adjusting
the
modeled
unit
groundwater
concentration
using
the
simple
ratio
of
target
hazard
quotient
to
the
modeled
hazard
quotient:

where
HBN
=
concentration
in
groundwater
resulting
in
target
hazard
quotient
(:
g/
L)
C_
GW_
modeled
=
unit
concentration
in
groundwater
used
in
shower
model
(:
g/
L)
THQ
=
target
hazard
quotient
for
noncarcinogens
=
1
HQ_
modeled
=
hazard
quotient
resulting
from
groundwater
concentration
modeled.

2.2.3
Solubility
Check
After
calculation,
we
checked
each
HBN
to
ensure
that
it
did
not
exceed
the
solubility
of
the
chemical
in
water
(
see
Memo
Attachment
B
for
the
aqueous
solubilities
used
for
this
check).
This
check
was
necessary
because
above
the
solubility
limit,
the
water
is
saturated
with
the
chemical,
and
any
additional
chemical
is
present
in
a
free,
separate
phase
(
pure
liquid
or
solid).
Above
saturation,
Henry's
law
(
a
basic
principle
of
the
shower
volatilization
model)
does
not
apply,
and
the
emission
flux
from
water
to
air
reaches
a
plateau.
In
other
words,
volatile
emissions
will
not
increase
above
this
level
no
matter
how
much
chemical
is
added
to
the
water
(
U.
S.
EPA,
1996).
Because
of
this
fact,
a
calculated
HBN
above
solubility
indicates
that
a
constituent
does
not
pose
a
significant
inhalation
risk,
and
IWEM
does
not
include
an
inhalation
HBN
for
that
constituent.
In
these
cases,
IWEM
will
evaluate
the
constituent
based
on
its
ingestion
risk
alone.
Page
13
of
13
REFERENCES:

Coburn,
J.
1996.
Memo
to
Dana
Greenwood
on
Emission
Flux
Equations
for
Showering,
July
1.

Little,
John
C.
1992.
Applying
the
two
resistance
theory
to
contaminant
volatilization
in
showers.
Environmental
Science
and
Technology
26:
1341­
1349.

McKone,
Thomas
E.
1987.
Human
exposure
to
volatile
organic
compounds
in
household
tap
water:
The
indoor
inhalation
pathway.
Environmental
Science
and
Technology
21:
1194­
1201.

U.
S.
Environmental
Protection
Agency
(
EPA).
1991.
Risk
Assessment
Guidance
for
Superfund:
Volume
1
­
Human
Health
Evaluation
Manual
(
Part
B,
Development
of
Risk­
Based
Preliminary
Goals).
EPA/
540/
R­
92/
003.
Interim
Draft.
Office
of
Emergency
and
Remedial
Response,
U.
S.
EPA,
Washington,
DC.

U.
S.
Environmental
Protection
Agency
(
EPA).
1996.
Soil
Screening
Guidance:
Technical
Background
Document.
EPA/
540/
R95/
128.
Office
of
Solid
Waste
and
Emergency
Response.
May.

U.
S.
Environmental
Protection
Agency
(
EPA).
1997a.
Exposure
Factors
Handbook,
Volume
I,
General
Factors.
EPA/
600/
P­
95/
002Fa.
Office
of
Research
and
Development,
Washington,
DC.

U.
S.
Environmental
Protection
Agency
(
EPA).
1997b.
Exposure
Factors
Handbook,
Volume
II,
Food
Ingestion
Factors.
EPA/
600/
P­
95/
002Fb.
Office
of
Research
and
Development,
Washington,
DC.

U.
S.
Environmental
Protection
Agency
(
EPA).
1997c.
Exposure
Factors
Handbook,
Volume
III,
Activity
Factors.
EPA/
600/
P­
95/
002Fc.
Office
of
Research
and
Development,
Washington,
DC.

U.
S.
Environmental
Protection
Agency
(
EPA).
1997d.
Supplemental
Background
Document;
Nongroundwater
Pathway
Risk
Assessment;
Petroleum
Process
Waste
Listing
Determination.
Office
of
Solid
Waste,
Research
Triangle
Park,
NC.
This
page
intentionally
left
blank.
Memo
Attachment
A
Shower
Algorithms
This
page
intentionally
left
blank.
Memo
Attachment
A
Page
1
of
10
BSResTime
ShowerTime
ShowerStallTime
T_
bathroom
=
+
+

ShowerResTime
ShowerStallTime
ShowerTime
=
+
Table
A­
1.
Total
time
spent
in
shower
and
bathroom
Shower
Name
Description
Value
BSResTime
Total
time
spent
in
shower
and
bathroom
(
min)
Calculated
above
ShowerTime
Duration
of
shower
(
min)
Provided
in
Table
A­
12
ShowerStallTime
Time
in
shower
stall
after
showering
(
min)
Provided
in
Table
A­
12
T_
bathroom
Time
spent
in
bathroom,
not
in
shower
(
min)
Provided
in
Table
A­
12
This
equation
calculates
the
total
time
that
a
receptor
is
exposed
to
vapors.

Table
A­
2.
Total
time
spent
in
shower
stall
Shower
Name
Description
Value
ShowerResTime
Total
time
spent
in
shower
stall
(
min)
Calculated
above
ShowerStallTime
Time
in
shower
stall
after
showering
(
min)
Provided
in
Table
A­
12
ShowerTime
Duration
of
shower
(
min)
Provided
in
Table
A­
12
This
equation
calculates
the
total
time
that
a
receptor
is
exposed
to
vapors
in
the
shower
stall.
Memo
Attachment
A
Page
2
of
10
Hprime
HLCcoef
HLC
HLCcoef
R
Temp
=
×
=
×
1
Table
A­
3.
Dimensionless
Henry's
law
constant
Shower
Name
Description
Value
Hprime
Dimensionless
Henry's
law
constant
(
dimensionless)
Calculated
above
HLCcoef
Coefficient
to
Henry's
law
constant
(
dimensionless)
Calculated
above
HLC
Henry's
law
constant
(
atm­
m3/
mol)
Chemical­
specific
R
Ideal
Gas
constant
(
atm­
m3/
K­
Mol)
0.00008206
Temp
Temperature
(
K)
298
This
equation
calculates
the
dimensionless
form
of
Henry's
law
constant.
Memo
Attachment
A
Page
3
of
10
N
=
Kol
AVRatio
DropResTime
DropResTime
×
×
=

=
×
AVRatio
DropDiam
NozHeight
DropVel
6
100
Table
A­
4.
Dimensionless
overall
mass
transfer
coefficient
Shower
Name
Description
Value
N
Dimensionless
overall
mass
transfer
coefficient
(
dimensionless)
Calculated
above
AVRatio
Area­
to­
volume
ratio
for
a
sphere
(
cm2/
cm3)
Calculated
above
Kol
Overall
mass
transfer
coefficient
(
cm/
s)
Calculated
in
Table
A­
5
DropResTime
Residence
time
for
falling
drops
(
s)
Calculated
above
DropDiam
Drop
diameter
(
cm)
Provided
in
Table
A­
12
NozHeight
Nozzle
height
(
m)
Provided
in
Table
A­
12
DropVel
Drop
terminal
velocity
(
cm/
s)
Provided
in
Table
A­
12
100
Conversion
factor
(
cm/
m)
Conversion
factor
This
equation
calculates
the
dimensionless
overall
mass
transfer
coefficient.
The
above
equation
is
based
on
Little
(
1992a),
which
provides
the
equation
as
N
=
Kol
×
A/
Q1
where
A
is
surface
area
and
Q1
is
flow
in
volume
per
time.
Memo
Attachment
A
Page
4
of
10
Kol
D
D
Hprime
w
a
=
×
+
×
 
 
 
 
 
 
 
 
 

 
25
1
2
3
2
3
1
.
/
/
Table
A­
5.
Overall
mass
transfer
coefficient
Shower
Name
Description
Value
Kol
Overall
mass
transfer
coefficient
(
cm/
s)
Calculated
above
beta
Proportionality
constant
(
cm­
s^­
1/
3)
216
Dw
Diffusion
coefficient
in
water
(
cm2/
s)
Chemical­
specific
Da
Diffusion
coefficient
in
air
(
cm2/
s)
Chemical­
specific
Hprime
Dimensionless
Henry's
law
constant
(
dimensionless)
Calculated
in
Table
A­
3
This
equation
calculates
the
overall
mass
transfer
coefficient.
The
above
equation
corresponds
to
Equation
17
in
McKone
(
1987)
and
was
modified
to
use
the
dimensionless
Henry's
law
constant.
The
value
for
beta
was
derived
based
on
data
for
benzene
and
verified
for
chemicals
of
varying
volatility
(
Coburn,
1996).
Memo
Attachment
A
Page
5
of
10
Es
=
Emax
Es
Et
=

(
)
Et
Cin
ShowerRate
ts
fem
y
y
Vs
eq
s
t
=
×
×
×
=
 
×
×
Emax
1000
,
Table
A­
6.
Contaminant
mass
emitted
in
the
shower
for
a
given
time
step
Shower
For
Et
>
Emax,

For
Et
#
Emax,

Where,

Name
Description
Value
Es
Contaminant
mass
emitted
in
the
shower
for
a
given
time
step
(
mg)
Calculated
above
Emax
Maximum
possible
mass
of
constituent
emitted
from
shower
during
time
step
(
mg)
Calculated
above
Et
Potential
mass
of
constituent
emitted
from
shower
during
time
step
(
mg)
Calculated
above
yeq
Gas­
phase
constituent
concentration
in
equilibrium
between
water
and
air
(
mg/
L)
Hprime
x
Cin
ys,
t
Gas­
phase
constituent
concentration
in
the
shower
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
Vs
Volume
of
shower
(
m3)
Provided
in
Table
A­
12
Cin
Liquid­
phase
constituent
concentration
in
the
incoming
water
(
mg/
L)
Provided
in
Table
A­
12
ShowerRate
Rate
of
flow
from
showerhead
(
L/
min)
Provided
in
Table
A­
12
ts
Time
step
(
min)
0.2
fem
Fraction
of
constituent
emitted
from
a
droplet
(
dimensionless)
Calculated
in
Table
A­
7
Hprime
Dimensionless
Henry's
law
constant
(
dimensionless)
Calculated
in
Table
A­
3
1000
Conversion
factor
(
L/
m3)
Conversion
factor
The
above
equations
are
used
to
determine
the
mass
of
contaminant
emitted
for
a
given
time
step.
The
equilibrium
concentration
in
air
(
y_
eq)
is
calculated
from
Equation
1
in
Little
(
1992a).
If
the
mass
emitted
based
on
the
mass
transfer
coefficient
(
Et)
is
greater
than
the
amount
emitted
to
reach
equilibrium
(
Emax),
the
mass
is
set
to
the
amount
that
results
in
the
air
concentration
at
equilibrium.
Memo
Attachment
A
Page
6
of
10
(
)
(
)
fem
Fsat
e
N
=
 
×
 
 

1
1
Fsat
y
y
s
t
eq
=
,
Table
A­
7.
Fraction
of
constituent
emitted
from
a
droplet
Shower
Name
Description
Value
fem
Fraction
of
constituent
emitted
from
a
droplet
(
dimensionless)
Calculated
above
Fsat
Fraction
of
gas­
phase
saturation
(
dimensionless)
Calculated
in
Table
A­
8
N
Dimensionless
overall
mass
transfer
coefficient
(
dimensionless)
Calculated
in
Table
A­
4
This
equation
is
used
to
calculate
the
fraction
of
a
given
chemical
emitted
from
a
droplet
of
water
in
the
shower.
The
equation
is
based
on
Equation
5
in
Little
(
1992a).
The
above
equation
is
obtained
by
rearranging
the
equation
in
Little
given
that
ys_
max/
m
=
Cin
and
f_
sat
=
ys/
ys_
max
=
ys/(
m
×
Cin).

Table
A­
8.
Fraction
of
gas­
phase
saturation
in
shower
Shower
Name
Description
Value
Fsat
Fraction
of
gas­
phase
saturation
in
shower
(
dimensionless)
Calculated
above
yeq
Gas­
phase
contaminant
concentration
in
equilibrium
between
water
and
air
(
mg/
L)
Hprime
x
Cin
ys,
t
Current
gas­
phase
contaminant
concentration
in
air
(
mg/
L)
Calculated
in
Table
A­
9
(
as
ys,
t+
ts
for
previous
time
step)

Hprime
Dimensionless
Henry's
law
constant
(
dimensionless)
Calculated
in
Table
A­
3
Cin
Constituent
concentration
in
incoming
water
(
mg/
L)
Provided
in
Table
A­
12
This
equation
is
used
to
calculate
the
fraction
of
gas
phase
saturation
in
shower
for
each
time
step.
The
equilibrium
concentration
in
air
(
y_
eq)
is
calculated
from
Equation
1
in
Little
(
1992a).
Memo
Attachment
A
Page
7
of
10
(
)
(
)
[
]
y
y
E
Q
y
y
ts
V
s
t
ts
s
t
s
sb
st
bt
s
,
,
,
,
+
=
+
 
×
 
×
×
1000
Table
A­
9.
Gas­
phase
constituent
concentration
in
the
shower
at
end
of
time
step
Shower
Name
Description
Value
ys,
t+
ts
Gas­
phase
constituent
concentration
in
the
shower
at
end
of
time
step
(
mg/
L)
Calculated
above
ys,
t
Gas­
phase
constituent
concentration
in
the
shower
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
yb,
t
Gas­
phase
constituent
concentration
in
the
bathroom
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
Es
Mass
emitted
in
the
shower
for
a
given
time
step
(
mg)
Calculated
in
Table
A­
6
Qsb
Volumetric
exchange
rate
between
the
shower
and
the
bathroom
(
L/
min)
Provided
in
Table
A­
12
Vs
Volume
of
shower
(
m3)
Provided
in
Table
A­
12
ts
Time
step
(
min)
0.2
1000
Conversion
factor
(
L/
m3)
Conversion
factor
This
equation
is
used
to
calculate
the
gas­
phase
constituent
concentration
in
the
shower
at
end
of
time
step.
The
equation
is
derived
from
Equation
9
in
Little
(
1992a).
Es
is
set
to
0
when
the
shower
is
turned
off
(
i.
e.,
at
the
end
of
showering)
to
estimate
the
reduction
in
shower
stall
air
concentrations
after
emissions
cease.
Memo
Attachment
A
Page
8
of
10
(
)
(
)
(
)
[
]
y
y
Q
y
y
Q
y
y
V
ts
b
t
ts
b
t
sb
s
t
ts
b
t
bh
b
t
h
t
b
,
,
,
,
,
,
+
+
=
+
×
 
 
×
 

×
×
1000
Table
A­
10.
Gas­
phase
constituent
concentration
in
the
bathroom
at
end
of
time
step
Shower
Name
Description
Value
yb,
t+
ts
Gas­
phase
constituent
concentration
in
the
bathroom
at
end
of
time
step
(
mg/
L)
Calculated
above
yb,
t
Gas­
phase
constituent
concentration
in
the
bathroom
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
ys,
t+
ts
Gas­
phase
constituent
concentration
in
the
shower
at
the
end
of
time
step
(
mg/
L)
Calculated
in
Table
A­
9
yh,
t
Gas­
phase
constituent
concentration
in
the
house
at
the
beginning
of
time
step
(
mg/
L)
Assumed
deminimus,
zero
Qsb
Volumetric
exchange
rate
between
the
shower
and
the
bathroom
(
L/
min)
Provided
in
Table
A­
12
Qbh
Volumetric
exchange
rate
between
the
bathroom
and
the
house
(
L/
min)
Provided
in
Table
A­
12
Vb
Volume
of
bathroom
(
m3)
Provided
in
Table
A­
12
ts
Time
step
(
min)
0.2
1000
Conversion
factor
(
L/
m3)
Conversion
factor
This
equation
is
used
to
calculate
the
gas­
phase
constituent
concentration
in
the
bathroom
at
end
of
time
step.
The
equation
is
derived
from
Equation
10
in
Little
(
1992a).
Memo
Attachment
A
Page
9
of
10
(
)(
)

(
)
[
]

(
)
[
]
C
C
ShowerResTime
C
T
bathroom
C
y
y
n
C
y
y
air
indoor
air
shower
air
bathroom
air
shower
s
t
ts
s
t
s
air
bathroom
b
t
ts
b
t
_
_
_

_
,

_
,
,
_

,
/

/
=
×
+
×
=
+
×
=
+
×
+

+
 

 
1440
1000
1000
nb
2
2
Table
A­
11.
Average
daily
concentration
in
indoor
air
Shower
Name
Description
Value
Cair_
indoor
Average
daily
concentration
in
indoor
air
(
mg/
m3)
Calculated
above
Cair_
shower
Average
concentration
in
shower
(
mg/
m3)
Calculated
above
Cair_
bathroom
Average
concentration
in
bathroom
(
mg/
m3)
Calculated
above
ShowerResTime
Total
time
spent
in
shower
stall
(
min)
Calculated
in
Table
A­
2
T_
bathroom
Time
spent
in
bathroom,
not
in
shower
(
min)
Provided
in
Table
A­
12
ys,
t
Gas­
phase
constituent
concentration
in
the
shower
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
ys,
t+
ts
Gas­
phase
constituent
concentration
in
the
shower
at
the
end
of
time
step
(
mg/
L)
Calculated
in
Table
A­
9
yb,
t
Gas­
phase
constituent
concentration
in
the
bathroom
at
the
beginning
of
time
step
(
mg/
L)
Calculated
from
last
time
step
yb,
t+
ts
Gas­
phase
constituent
concentration
in
the
bathroom
at
the
end
of
time
step
(
mg/
L)
Calculated
in
Table
A­
10
ns
Number
of
time
steps
corresponding
to
time
spent
in
the
shower
(
dimensionless)
Summed
in
model
code
nb
Number
of
time
steps
corresponding
to
time
spent
in
the
bathroom
(
dimensionless)
Summed
in
model
code
1440
Minutes
per
day
(
min)

1000
Conversion
factor
(
L/
m3)
Conversion
factor
The
above
equations
are
used
to
calculate
the
time­
weighted
average
daily
indoor
air
concentration
to
which
a
receptor
is
exposed.
The
equation
assumes
that
receptors
are
only
exposed
to
contaminants
in
the
shower
and
bathroom.
Memo
Attachment
A
Page
10
of
10
Table
A­
12.
Model
parameters
for
exposure
Name
Description
Value
Reference
Comments
Bathroom
properties
Vb
Volume
of
the
bathroom
(
m^
3)
10
McKone,
T.,
1987
Exchange
rate
Qbh
Volumetric
exchange
rate
between
the
bathroom
and
the
house
(
L/
min)
300
RTI­
derived
value
Estimated
from
the
volume
and
flow
rate
in
McKone
(
1987)
such
that
the
exchange
rate
equals
the
volume
divided
by
the
residence
time
(
i.
e.,
10,000L/
30
min).

Qsb
Volumetric
exchange
rate
between
the
shower
and
the
bathroom
(
L/
min)
100
RTI­
derived
value
Estimated
from
the
volume
and
flow
rate
in
McKone
(
1987)
such
that
the
exchange
rate
equals
the
volume
divided
by
the
residence
time
(
i.
e.,
2000L/
20
min).

Exposure
time
ShowerStallTime
Time
in
shower
stall
after
showering
(
min)
0
NA
Only
assessing
exposure
from
time
spent
showering.

ShowerTime
Shower
time,
50th
percentile
(
min)
15
U.
S.
EPA,
1997
Table
15­
21,
50th
percentile
overall.

T_
bathroom
Time
spent
in
bathroom,
not
in
shower
(
min)
0
NA
Only
assessing
exposure
from
time
spent
showering.

Shower
properties
DropDiam
Diameter
of
shower
water
drop
(
cm)
0.098
RTI­
derived
value
Estimated
as
a
function
of
terminal
velocity
(
Coburn,
1996).

DropVel
Terminal
velocity
of
water
drop
(
cm/
s)
400
RTI­
derived
value
Estimated
by
correlating
to
existing
data
(
Coburn,
1996).

NozHeight
Height
of
shower
head
(
cm)
180
Little,
J.,
1992a
Selected
based
on
values
presented
in
Little.

ShowerRate
Rate
of
water
flow
from
shower
head
(
L/
min)
5.5
RTI­
derived
value
Calculated
based
on
droplet
diameter
and
nozzle
velocity.

Vs
Volume
of
shower
(
m^
3)
2
McKone,
T.,
1987
Groundwater
Cin
Constituent
concentration
in
incoming
water
(
mg/
L)
0.001
NA
Unit
concentration
selected.
Memo
Attachment
B
Contaminant­
Specific
Chemical
and
Physical
Properties
This
page
intentionally
left
blank.
Memo
Attachment
B
Page
1
of
9
Memo
Attachment
B
Contaminant­
Specific
Chemical
and
Physical
Properties
To
calculate
inhalation
HBNs,
the
shower
model
requires
input
of
several
chemicalspecific
properties,
including
Henry's
law
constant
(
HLC),
solubility
(
Sol),
and
diffusion
coefficients
in
air
(
Da)
and
water
(
Dw).
This
attachment
describes
the
data
sources
and
methodologies
used
to
collect
and
develop
these
properties.
Table
B­
1
(
at
the
end
of
this
attachment)
lists
by
contaminant
the
chemical­
specific
properties
used
to
calculate
inhalation
HBNs,
along
with
the
data
source
for
each
value.

B.
1
Data
Collection
Procedure
To
select
data
values
available
from
multiple
sources,
we
created
a
hierarchy
of
references
based
on
the
reliability
and
availability
of
data
in
such
sources.
Our
first
choice
for
data
collection
and
calculations
was
EPA
reports
and
software.
When
we
could
not
find
data
or
equations
from
EPA
publications,
we
consulted
highly
recognized
sources,
including
chemical
information
databases
on
the
Internet.
These
on­
line
sources
are
compilations
of
data
that
provide
the
primary
references
for
data
values.
The
specific
hierarchy
varied
among
properties
as
described
in
subsequent
sections.

For
dioxins,
the
preferred
data
source
in
all
cases
was
the
Exposure
and
Human
Health
Reassessment
of
2,3,7,8­
Tetrachlorodibenzo­
p­
Dioxin
(
TCDD)
and
Related
Compounds,
Part
1,
Vol.
3
(
Dioxin
Reassessment)
(
U.
S.
EPA,
2000).
We
used
the
Mercury
Study
Report
to
Congress
(
U.
S.
EPA,
1997a)
as
the
preferred
source
for
mercury
properties.
If
values
were
unavailable
from
these
sources,
we
followed
the
same
reference
hierarchy
that
was
used
for
other
contaminants.

All
data
entry
for
chemical
and
physical
properties
was
checked
by
comparing
each
entry
against
the
original
online
or
hardcopy
reference.
All
property
calculation
programs
were
checked
using
hand
calculations
to
ensure
that
they
were
functioning
correctly.

B.
2
Solubility
(
Sol)

For
solubility
(
Sol)
values,
we
looked
for
data
by
searching
the
following
sources
in
the
following
order:

1.
Superfund
Chemical
Data
Matrix
(
SCDM)
(
U.
S.
EPA,
1997b);
2.
CHEMFATE
Chemical
Search
(
SRC,
1999);
3.
Hazardous
Substances
Data
Bank
(
HSDB)
(
U.
S.
NLM,
2001);
4.
ChemFinder
(
CambridgeSoft
Corporation,
2001).
Memo
Attachment
B
Page
2
of
9
HLC
P
Sol
vp
=
For
mercury,
we
obtained
a
solubility
for
elemental
mercury
from
The
Merck
Index:
An
Encyclopedia
of
Chemicals,
Drugs,
and
Biologicals
(
Budavari,
1996).

B.
3
Henry's
Law
Constant
(
HLC)

Collection
of
Henry's
law
constant
(
HLC)
data
proceeded
by
searching
sources
in
the
following
order:

1.
SCDM;
2.
CHEMFATE;
3.
HSDB.

When
we
could
not
find
data
from
these
sources,
we
calculated
HLC
using
equation
15­
8
from
Lyman,
Reehl,
and
Rosenblatt
(
1990):

where
HLC
=
Henry's
law
constant
(
atm­
m3/
mole)
Pvp
=
vapor
pressure
(
atm)
Sol
=
solubility
(
mol/
m3).

B.
4
Diffusion
Coefficient
in
Water
(
Dw)

For
all
chemicals,
we
calculated
the
diffusion
coefficient
in
water
(
Dw)
by
hand
because
few
empirical
data
are
available.
The
preferred
calculation
was
equation
17­
6
from
the
WATER9
model
(
U.
S.
EPA,
2001):

D
T
MW
w
=
+

 
 
 
 
 
 
 
 
 
 
 
 
 

0
0001518
27316
29816
0
6
.
.
.
.

 
where
Dw
=
diffusion
coefficient
in
water
(
cm2/
s)
T
=
temperature
(
degrees
C)
MW
=
molecular
weight
(
g/
g­
mol)
D
=
density
(
g/
cc).

When
we
did
not
know
chemical
density,
we
used
equation
3.16
from
Process
Coefficients
and
Models
for
Simulating
Toxic
Organics
and
Heavy
Metals
in
Surface
(
Process
Coefficients)
(
U.
S.
EPA,
1987),
which
only
requires
molecular
weight:
Memo
Attachment
B
Page
3
of
9
Dw
MW
=
×
 
0
00022
2
3
.
/

Da
MW
=
×
 
19
2
3
.
/
(
)
D
T
MW
MW
MW
a
=
+
+
 

 
 
 
 
 
 
+
 
 
 
 
 
 
 
 
0
0029
27316
0
034
1
1
0
000015
25
18
1
5
2
0
333
2
.
(
.
)
.
.

.
.
.

.

 
where
Dw
=
diffusion
coefficient
in
water
(
cm2/
s)
MW
=
molecular
weight
(
g/
mol).

B.
5
Diffusion
Coefficient
in
Air
(
Da)

All
diffusion
coefficients
in
air
(
Da)
were
calculated
values
because
few
empirical
data
are
available.
Similar
to
Dw,
we
first
consulted
WATER9
and
then
used
U.
S.
EPA
(
1987).
Equation
17­
5
in
WATER9
calculates
diffusivity
in
air
as
follows:

where
Da
=
diffusion
coefficient
in
air
(
cm2/
s)
T
=
temperature
(
degrees
C)
MW
=
molecular
weight
(
g/
g­
mol)
D
=
density
(
g/
cc).

When
density
was
not
available,
we
used
equation
3.17
from
Process
Coefficients
(
U.
S.
EPA,
1987):

where
Da
=
diffusion
coefficient
in
air
(
cm2/
s)
MW
=
molecular
weight
(
g/
mol).

For
dioxins
and
dibenzofurans,
we
used
an
equation
from
the
Dioxin
Reassessment
(
U.
S.
EPA,
2000)
to
estimate
diffusion
coefficients
from
diphenyl's
diffusivity:

D
D
MW
MW
a
b
b
a
=
 
 
 
 
 
 
0
5
.

where
Da
=
diffusion
coefficient
of
constituent
in
air
(
cm2/
s)
Db
=
diffusion
coefficient
of
diphenyl
at
25
degrees
C
(
0.068
cm2/
s)
MWa
=
molecular
weight
of
constituent
(
g/
mole)
MWb
=
molecular
weight
of
diphenyl
(
154
g/
mole).
Memo
Attachment
B
Page
4
of
9
Table
B­
1.
Contaminant­
specific
Chemical
and
Physical
Properties
Contaminant
CASRN
Da
(
cm2/
s)
Dw
(
cm2/
s)
HLC
(
atm­
m3/
mol)
Sol
(
mg/
L)
Acetaldehyde
(
ethanal)
75­
07­
0
1.28E­
01
e
1.35E­
05
e
7.89e­
05
a
1.00e+
06
a
Acetone
(
2­
propanone)
67­
64­
1
1.06E­
01
e
1.15E­
05
e
3.88e­
05
a
1.00e+
06
a
Acetonitrile
(
methyl
cyanide)
75­
05­
8
1.34E­
01
e
1.41E­
05
e
3.46e­
05
a
1.00e+
06
a
Acrolein
107­
02­
8
1.12E­
01
e
1.22E­
05
e
1.22e­
04
a
2.13e+
05
a
Acrylamide
79­
06­
1
1.07E­
01
e
1.26E­
05
e
1.00e­
09
a
6.40e+
05
a
Acrylic
acid
(
propenoic
acid)
79­
10­
7
1.03E­
01
e
1.20E­
05
e
1.17e­
07
a
1.00e+
06
a
Acrylonitrile
107­
13­
1
1.14E­
01
e
1.23E­
05
e
1.03e­
04
a
7.40e+
04
a
Aldrin
309­
00­
2
2.28E­
02
e
5.84E­
06
e
1.70e­
04
a
1.80e­
01
a
Aniline
(
benzeneamine)
62­
53­
3
8.30E­
02
e
1.01E­
05
e
1.90e­
06
a
3.60e+
04
a
Benz(
a)
anthracene
56­
55­
3
5.09E­
02
b
5.89E­
06
b
3.35e­
06
a
9.40e­
03
a
Benzene
71­
43­
2
8.95E­
02
e
1.03E­
05
e
5.55e­
03
a
1.75e+
03
a
Benzidine
92­
87­
5
3.55E­
02
e
7.59E­
06
e
3.88e­
11
a
5.00e+
02
a
Benzo(
a)
pyrene
50­
32­
8
2.55E­
02
e
6.58E­
06
e
1.13e­
06
a
1.62e­
03
a
Benzo(
b)
fluoranthene
205­
99­
2
4.76E­
02
b
5.51E­
06
b
1.11e­
04
a
1.50e­
03
a
Benzyl
chloride
100­
44­
7
6.34E­
02
e
8.81E­
06
e
4.15e­
04
a
5.25e+
02
a
Bis(
2­
ethylhexyl)
phthalate
117­
81­
7
1.73E­
02
e
4.18E­
06
e
1.02e­
07
a
3.40e­
01
a
Bis(
2­
chloroethyl)
ether
111­
44­
4
5.67E­
02
e
8.71E­
06
e
1.80e­
05
a
1.72e+
04
a
Bis(
2­
chloroisopropyl)
ether
39638­
32­
9
4.01E­
02
e
7.40E­
06
e
1.34e­
04
d
1.31e+
03
a
Bromodichloromethane
75­
27­
4
5.63E­
02
e
1.07E­
05
e
1.60e­
03
a
6.74e+
03
a
Bromomethane
(
methyl
bromide)
74­
83­
9
1.00E­
01
e
1.35E­
05
e
6.24e­
03
a
1.52e+
04
a
Butadiene,
1,3­
106­
99­
0
1.00E­
01
e
1.03E­
05
e
7.36e­
02
a
7.35e+
02
a
Carbon
tetrachloride
56­
23­
5
5.71E­
02
e
9.78E­
06
e
3.04e­
02
a
7.93e+
02
a
Carbon
disulfide
75­
15­
0
1.06E­
01
e
1.30E­
05
e
3.03e­
02
a
1.19e+
03
a
Chlordane
57­
74­
9
2.15E­
02
e
5.45E­
06
e
4.86e­
05
a
5.60e­
02
a
Chloro­
1,3­
butadiene,
2­
(
Chloroprene)
126­
99­
8
8.41E­
02
e
1.00E­
05
e
1.19e­
02
f
1.74e+
03
a
Chlorobenzene
108­
90­
7
7.21E­
02
e
9.48E­
06
e
3.70e­
03
a
4.72e+
02
a
Chlorobenzilate
510­
15­
6
2.18E­
02
e
5.48E­
06
e
7.24e­
08
f
1.11e+
01
a
Chlorodibromomethane
124­
48­
1
3.66E­
02
e
1.06E­
05
e
7.83e­
04
a
2.60e+
03
a
Chloroethane
(
ethyl
chloride)
75­
00­
3
1.04E­
01
e
1.16E­
05
e
8.82e­
03
a
5.68e+
03
a
Chloroform
67­
66­
3
7.70E­
02
e
1.09E­
05
e
3.67e­
03
a
7.92e+
03
a
Chloromethane
(
methyl
chloride)
74­
87­
3
1.24E­
01
e
1.36E­
05
e
8.82e­
03
a
5.33e+
03
a
Chlorophenol,
2­
95­
57­
8
6.61E­
02
e
9.48E­
06
e
3.91e­
04
a
2.20e+
04
a
Chloropropene,
3­
(
allyl
chloride)
107­
05­
1
9.36E­
02
e
1.08E­
05
e
1.10e­
02
a
3.37e+
03
a
Chrysene
218­
01­
9
2.61E­
02
e
6.75E­
06
e
9.46e­
05
a
1.60e­
03
a
Cresol,
o­
95­
48­
7
7.59E­
02
e
9.86E­
06
e
1.20e­
06
a
2.60e+
04
a
Cresol,
m­
108­
39­
4
7.29E­
02
e
9.32E­
06
e
8.65e­
07
a
2.27e+
04
a
(
continued)
Table
B­
1.
(
continued)
Memo
Attachment
B
Contaminant
CASRN
Da
(
cm2/
s)
Dw
(
cm2/
s)
HLC
(
atm­
m3/
mol)
Sol
(
mg/
L)

Page
5
of
9
Cresol,
p­
106­
44­
5
7.24E­
02
e
9.24E­
06
e
7.92e­
07
a
2.15e+
04
a
Cresols
(
total)
1319­
77­
3
7.37E­
02
e
9.48E­
06
e
9.52e­
07
a
2.34e+
04
a
Cumene
98­
82­
8
6.02E­
02
e
7.85E­
06
e
1.16e+
00
a
6.13e+
01
a
Cyclohexanol
108­
93­
0
7.59E­
02
e
9.35E­
06
e
1.02e­
04
f
4.30e+
04
f
DDT,
p,
p'­
50­
29­
3
1.83E­
02
e
4.44E­
06
e
8.10e­
06
a
2.50e­
02
a
Dibenz(
a,
h)
anthracene
53­
70­
3
2.36E­
02
e
6.02E­
06
e
1.47e­
08
a
2.49e­
03
a
Dibromo­
3­
chloropropane,
1,2­
96­
12­
8
3.21E­
02
e
8.90E­
06
e
1.47e­
04
a
1.23e+
03
a
Dichlorobenzene,
1,2­
95­
50­
1
5.62E­
02
e
8.92E­
06
e
1.90e­
03
a
1.56e+
02
a
Dichlorobenzene,
1,4­
106­
46­
7
5.50E­
02
e
8.68E­
06
e
2.40e­
03
a
7.38e+
01
a
Dichlorobenzidine,
3,3'­
91­
94­
1
4.75E­
02
b
5.50E­
06
b
4.00e­
09
a
3.11e+
00
a
Dichlorodifluoromethane
(
Freon
12)
75­
71­
8
7.60E­
02
e
1.08E­
05
e
3.43e­
01
a
2.80e+
02
a
Dichloroethane,
1,1­
75­
34­
3
8.36E­
02
e
1.06E­
05
e
5.62e­
03
a
5.06e+
03
a
Dichloroethane,
1,2­
107­
06­
2
8.54E­
02
e
1.09E­
05
e
9.79e­
04
a
8.52e+
03
a
Dichloroethylene,
1,1­
75­
35­
4
8.63E­
02
e
1.10E­
05
e
2.61e­
02
a
2.25e+
03
a
Dichloropropane,
1,2­
78­
87­
5
7.33E­
02
e
9.73E­
06
e
2.80e­
03
a
2.80e+
03
a
Dichloropropene,
trans­
1,3­
10061­
02­
6
7.63E­
02
e
1.01E­
05
e
1.80e­
03
i
2.72e+
03
a
Dichloropropene,
1,3­
(
isomer
mixture)
542­
75­
6
7.63E­
02
e
1.01E­
05
e
1.77e­
02
a
2.80e+
03
a
Dichloropropene,
cis­
1,3­
10061­
01­
5
7.65E­
02
e
1.02E­
05
e
2.40e­
03
i
2.72e+
03
a
Dieldrin
60­
57­
1
2.33E­
02
e
6.01E­
06
e
1.51e­
05
a
1.95e­
01
a
Dimethyl
formamide,
N,
N­
(
DMF)
68­
12­
2
9.72E­
02
e
1.12E­
05
e
7.39e­
08
i
1.00e+
06
f
Dimethylbenz(
a)
anthracene,
7,12­
57­
97­
6
4.71E­
02
b
5.45E­
06
b
3.11e­
08
a
2.50e­
02
a
Dinitrotoluene,
2,4­
121­
14­
2
3.75E­
02
e
7.90E­
06
e
9.26e­
08
a
2.70e+
02
a
Dioxane,
1,4­
123­
91­
1
8.74E­
02
e
1.05E­
05
e
4.80e­
06
a
1.00e+
06
a
Diphenylhydrazine,
1,2­
122­
66­
7
0.0343
e
7.25E­
06
e
1.53e­
06
a
6.80e+
01
a
Epichlorohydrin
106­
89­
8
0.0888
e
1.11E­
05
e
3.04e­
05
a
6.59e+
04
a
Epoxybutane,
1,2­
106­
88­
7
9.32E­
02
e
1.05E­
05
e
1.80e­
04
f
9.50e+
04
f
Ethoxyethanol
acetate,
2­
111­
15­
9
5.70E­
02
e
7.98E­
06
e
1.80e­
06
i
2.29e+
05
i
Ethoxyethanol
,
2­
110­
80­
5
8.19E­
02
e
9.76E­
06
e
1.23e­
07
a
1.00e+
06
a
Ethylbenzene
100­
41­
4
6.86E­
02
e
8.48E­
06
e
7.88e­
03
a
1.69e+
02
a
Ethylene
dibromide
(
1,2­
dibromoethane)
106­
93­
4
4.31E­
02
e
1.05E­
05
e
7.43e­
04
a
4.18e+
03
a
Ethylene
glycol
107­
21­
1
1.17E­
01
e
1.36E­
05
e
6.00e­
08
a
1.00e+
06
a
Ethylene
thiourea
96­
45­
7
8.69E­
02
b
1.01E­
05
b
3.08e­
10
a
6.20e+
04
a
Ethylene
oxide
75­
21­
8
1.34E­
01
e
1.46E­
05
e
1.48e­
04
f
1.00e+
06
g
Formaldehyde
50­
00­
0
1.67E­
01
e
1.74E­
05
e
3.36e­
07
a
5.50e+
05
a
Furfural
98­
01­
1
8.53E­
02
e
1.07E­
05
e
4.00e­
06
a
1.10e+
05
a
HCH,
gamma­
(
Lindane)
58­
89­
9
2.74E­
02
e
7.30E­
06
e
1.40e­
05
a
6.80e+
00
a
(
continued)
Table
B­
1.
(
continued)
Memo
Attachment
B
Contaminant
CASRN
Da
(
cm2/
s)
Dw
(
cm2/
s)
HLC
(
atm­
m3/
mol)
Sol
(
mg/
L)

Page
6
of
9
HCH,
beta­
319­
85­
7
0.0277
e
7.40E­
06
e
7.43e­
07
a
2.40e­
01
a
HCH,
alpha­
319­
84­
6
2.75E­
02
e
7.35E­
06
e
1.06e­
05
a
2.00e+
00
a
Heptachlor
epoxide
1024­
57­
3
2.19E­
02
e
5.58E­
06
e
9.50e­
06
a
2.00e­
01
a
Heptachlor
76­
44­
8
2.23E­
02
e
5.70E­
06
e
1.10e­
03
a
1.80e­
01
a
Hexachloro­
1,3­
butadiene
87­
68­
3
2.67E­
02
e
7.03E­
06
e
8.15e­
03
a
3.23e+
00
a
Hexachlorobenzene
118­
74­
1
2.90E­
02
e
7.85E­
06
e
1.32e­
03
a
5.00e­
03
a
Hexachlorocyclopentadiene
77­
47­
4
2.72E­
02
e
7.22E­
06
e
2.70e­
02
a
1.80e+
00
a
Hexachlorodibenzo­
p­
dioxins
(
HxCDDs)
34465­
46­
8
4.27E­
02
j
4.12E­
06
b
1.10e­
05
c
4.40e­
06
c
Hexachlorodibenzofurans
(
HxCDFs)
55684­
94­
1
4.36E­
02
j
4.23E­
06
b
1.10e­
05
c
1.30e­
05
c
Hexachloroethane
67­
72­
1
3.21E­
02
e
8.89E­
06
e
3.89e­
03
a
5.00e+
01
a
Hexane,
n­
110­
54­
3
7.28E­
02
e
8.12E­
06
e
1.43e­
02
a
1.24e+
01
a
Indeno(
1,2,3­
cd)
pyrene
193­
39­
5
4.48E­
02
b
5.19E­
06
b
1.60e­
06
a
2.20e­
05
a
Isophorone
78­
59­
1
5.25E­
02
e
7.53E­
06
e
6.64e­
06
a
1.20e+
04
a
Mercury
7439­
97­
6
7.15E­
02
e
3.01E­
05
e
7.10e­
03
k
5.62e­
02
h
Methacrylonitrile
126­
98­
7
9.64E­
02
e
1.06E­
05
e
2.47e­
04
a
2.54e+
04
a
Methanol
67­
56­
1
1.58E­
01
e
1.65E­
05
e
4.55e­
06
a
1.00e+
06
a
Methoxyethanol
acetate,
2­
110­
49­
6
6.59E­
02
e
8.71E­
06
e
3.11e­
07
d
1.00e+
06
i
Methoxyethanol,
2­
109­
86­
4
0.0952
e
1.10E­
05
e
8.10e­
08
f
1.00e+
06
g
Methyl
methacrylate
80­
62­
6
7.53E­
02
e
9.25E­
06
e
3.37e­
04
a
1.50e+
04
a
Methyl
tert­
butyl
ether
(
MTBE)
1634­
04­
4
7.55E­
02
e
8.63E­
06
e
5.87e­
04
f
5.13e+
04
f
Methyl
isobutyl
ketone
108­
10­
1
6.98E­
02
e
8.36E­
06
e
1.38e­
04
a
1.90e+
04
a
Methyl
ethyl
ketone
78­
93­
3
9.17E­
02
e
1.02E­
05
e
5.59e­
05
a
2.23e+
05
a
Methylcholanthrene,
3­
56­
49­
5
2.41E­
02
e
6.14E­
06
e
9.40e­
07
a
3.23e­
03
a
Methylene
chloride
(
dichloromethane)
75­
09­
2
9.99E­
02
e
1.25E­
05
e
2.19e­
03
a
1.30e+
04
a
N­
Nitrosomethylethylamine
10595­
95­
6
8.41E­
02
e
9.99E­
06
e
1.40e­
06
i
1.97e+
04
a
N­
Nitrosodimethylamine
62­
75­
9
9.88E­
02
e
1.15E­
05
e
1.20e­
06
a
1.00e+
06
a
N­
Nitrosopiperidine
100­
75­
4
6.99E­
02
e
9.18E­
06
e
2.80e­
07
a
7.65e+
04
a
N­
Nitrosodiphenylamine
86­
30­
6
2.84E­
02
e
7.19E­
06
e
5.00e­
06
a
3.51e+
01
a
N­
Nitrosodiethylamine
55­
18­
5
7.38E­
02
e
9.13E­
06
e
3.63e­
06
a
9.30e+
04
a
N­
Nitroso­
di­
n­
butylamine
924­
16­
3
4.22E­
02
e
6.83E­
06
e
3.16e­
04
a
1.27e+
03
a
N­
Nitrosopyrrolidine
930­
55­
2
8.00E­
02
e
1.01E­
05
e
1.20e­
08
a
1.00e+
06
a
N­
Nitroso­
di­
n­
propylamine
621­
64­
7
5.64E­
02
e
7.76E­
06
e
2.25e­
06
a
9.89e+
03
a
Naphthalene
91­
20­
3
6.05E­
02
e
8.38E­
06
e
4.83e­
04
a
3.10e+
01
a
Nitrobenzene
98­
95­
3
6.81E­
02
e
9.45E­
06
e
2.40e­
05
a
2.09e+
03
a
Nitropropane,
2­
79­
46­
9
8.47E­
02
e
1.02E­
05
e
1.23e­
04
a
1.70e+
04
a
(
continued)
Table
B­
1.
(
continued)
Memo
Attachment
B
Contaminant
CASRN
Da
(
cm2/
s)
Dw
(
cm2/
s)
HLC
(
atm­
m3/
mol)
Sol
(
mg/
L)

Page
7
of
9
Pentachlorodibenzo­
p­
dioxins
(
PeCDDs)
36088­
22­
9
4.47E­
02
j
4.38E­
06
b
2.60e­
06
c
1.18e­
04
c
Pentachlorodibenzofurans
(
PeCDFs)
30402­
15­
4
4.57E­
02
j
4.51E­
06
b
5.00e­
06
c
2.40e­
04
c
Pentachlorophenol
87­
86­
5
2.95E­
02
e
8.01E­
06
e
2.44e­
08
a
1.95e+
03
a
Phenol
108­
95­
2
8.34E­
02
e
1.03E­
05
e
3.97e­
07
a
8.28e+
04
a
Phthalic
anhydride
85­
44­
9
5.95E­
02
e
9.75E­
06
e
1.63e­
08
a
6.20e+
03
a
Polychlorinated
biphenyls
(
Aroclors)
1336­
36­
3
2.33E­
02
e
5.98E­
06
e
2.60e­
03
a
7.00e­
02
a
Propylene
oxide
(
1,2­
epoxypropane)
75­
56­
9
1.10E­
01
e
1.21E­
05
e
1.23e­
04
f
4.05e+
05
f
Pyridine
110­
86­
1
9.31E­
02
e
1.09E­
05
e
8.88e­
06
a
1.00e+
06
a
Styrene
100­
42­
5
7.13E­
02
e
8.81E­
06
e
2.75e­
03
a
3.10e+
02
a
TCDD,
2,3,7,8­
1746­
01­
6
4.70E­
02
j
4.68E­
06
b
3.29e­
05
c
1.93e­
05
c
Tetrachlorodibenzo­
p­
dioxins
(
TCDDs)
41903­
57­
5
4.70E­
02
j
4.68E­
06
b
1.70e­
05
c
3.30e­
04
c
Tetrachlorodibenzofurans
(
TCDFs)
55722­
27­
5
4.82E­
02
j
4.84E­
06
b
1.40e­
05
c
4.20e­
04
c
Tetrachloroethane,
1,1,2,2­
79­
34­
5
4.89E­
02
e
9.29E­
06
e
3.45e­
04
a
2.97e+
03
a
Tetrachloroethane,
1,1,1,2­
630­
20­
6
4.82E­
02
e
9.10E­
06
e
2.42e­
03
a
1.10e+
03
a
Tetrachloroethylene
127­
18­
4
5.05E­
02
e
9.45E­
06
e
1.84e­
02
a
2.00e+
02
a
Toluene
108­
88­
3
7.80E­
02
e
9.23E­
06
e
6.64e­
03
a
5.26e+
02
a
Toluenediamine
2,4­
95­
80­
7
7.72E­
02
b
8.94E­
06
b
7.92e­
10
a
3.37e+
04
a
Toluidine,
o­
95­
53­
4
7.24E­
02
e
9.18E­
06
e
2.72e­
06
a
1.66e+
04
a
Toxaphene
(
chlorinated
camphenes)
8001­
35­
2
2.16E­
02
e
5.48E­
06
e
6.00e­
06
a
7.40e­
01
a
Tribromomethane
(
bromoform)
75­
25­
2
3.58E­
02
e
1.04E­
05
e
5.35e­
04
a
3.10e+
03
a
Trichloro­
1,2,2­
trifluoro­
ethane,
1,1,2­
76­
13­
1
3.76E­
02
e
8.59E­
06
e
4.81e­
01
a
1.70e+
02
a
Trichlorobenzene,
1,2,4­
120­
82­
1
3.96E­
02
e
8.40E­
06
e
1.42e­
03
a
3.46e+
01
a
Trichloroethane,
1,1,2­
79­
00­
5
6.69E­
02
e
1.00E­
05
e
9.13e­
04
a
4.42e+
03
a
Trichloroethane,
1,1,1­
71­
55­
6
6.48E­
02
e
9.60E­
06
e
1.72e­
02
a
1.33e+
03
a
Trichloroethylene
(
TCE)
79­
01­
6
6.87E­
02
e
1.02E­
05
e
1.03e­
02
a
1.10e+
03
a
Trichlorofluoromethane
(
Freon
11)
75­
69­
4
6.55E­
02
e
1.01E­
05
e
9.70e­
02
a
1.10e+
03
a
Trichlorophenol,
2,4,6­
88­
06­
2
3.14E­
02
e
8.09E­
06
e
7.79e­
06
a
8.00e+
02
a
Trichloropropane,
1,2,3­
96­
18­
4
5.75E­
02
e
9.24E­
06
e
4.09e­
04
a
1.75e+
03
a
Triethylamine
121­
44­
8
6.63E­
02
e
7.84E­
06
e
1.38e­
04
f
5.50e+
04
f
Vinyl
acetate
108­
05­
4
8.51E­
02
e
1.00E­
05
e
5.11e­
04
a
2.00e+
04
a
Vinyl
chloride
75­
01­
4
1.07E­
01
e
1.20E­
05
e
2.70e­
02
a
2.76e+
03
a
Xylene,
p­
106­
42­
3
6.84E­
02
e
8.45E­
06
e
7.66e­
03
a
1.85e+
02
a
Xylene,
o­
95­
47­
6
6.91E­
02
e
8.56E­
06
e
5.19e­
03
a
1.78e+
02
a
Xylene,
m­
108­
38­
3
6.85E­
02
e
8.47E­
06
e
7.34e­
03
a
1.61e+
02
a
Xylenes
(
total)
1330­
20­
7
6.87E­
02
e
8.49E­
06
e
6.73e­
03
a
1.75e+
02
a
(
continued)
Table
B­
1.
(
continued)
Memo
Attachment
B
Page
8
of
9
Da
=
air
diffusivity;
Dw
=
water
diffusivity;
HLC
=
Henry's
law
constant;
Sol
=
aqueous
solubility
CASRN
=
Chemical
Abstract
Service
Registry
Number
Data
Sources:
a
SCDM
(
U.
S.
EPA,
1997b).
b
Calculated
based
on
U.
S.
EPA,
1987.
c
U.
S.
EPA,
2000.
d
Calculated
based
on
Lyman,
Reehl,
and
Rosenblatt,
1990.
e
Calculated
based
on
WATER9
(
U.
S.
EPA,
2001).
f
CHEMFATE
(
SRC,
1999).
g
ChemFinder.
com
(
CambridgeSoft
Corporation,
2001).
h
The
Merck
Index
(
Budavari,
1996).
i
HSDB
(
NLM,
2001).
j
Calculated
based
on
U.
S.
EPA,
2000.
k
U.
S.
EPA,
1997a.

B.
6
References
Budavari,
S.
(
ed).
1996.
The
Merck
Index:
An
Encyclopedia
of
Chemicals,
Drugs,
and
Biologicals.
12th
edition.
Whitehouse
Station,
NJ:
Merck
and
Co.

CambridgeSoft
Corporation.
2001.
ChemFinder.
com
database
and
internet
searching.
http://
chemfinder.
cambridgesoft.
com.
Accessed
July
2001.

Lyman,
W.
J.,
W.
F.
Reehl,
and
D.
H.
Rosenblatt.
1990.
Handbook
of
Chemical
Property
Estimation
Methods:
Environmental
Behavior
of
Organic
Compounds.
Washington,
DC:
American
Chemical
Society.

Syracuse
Research
Corporation
(
SRC).
1999.
CHEMFATE
Chemical
Search,
Environmental
Science
Center,
Syracuse,
NY.
http://
esc.
syrres.
com/
efdb/
Chemfate.
htm.
Accessed
July
2001.

U.
S.
Environmental
Protection
Agency
(
EPA).
1987.
Process
Coefficients
and
Models
for
Simulating
Toxic
Organics
and
Heavy
Metals
in
Surface
Waters.
Office
of
Research
and
Development.
Washington,
DC:
U.
S.
Government
Printing
Office
(
GPO).

U.
S.
Environmental
Protection
Agency
(
EPA).
1997a.
Mercury
Study
Report
to
Congress.
Volume
IV:
An
Assessment
of
Exposure
to
Mercury
in
the
United
States.
EPA­
452/
R­
97­
006.
Office
of
Air
Quality
Planning
and
Standards
and
Office
of
Research
and
Development.
Washington,
DC:
GPO.

U.
S.
Environmental
Protection
Agency
(
EPA).
1997b.
Superfund
Chemical
Data
Matrix
(
SCDM).
SCDMWIN
1.0
(
SCDM
Windows
User's
Version),
Version
1.
Office
of
Solid
Waste
and
Emergency
Response,
Washington
DC:
GPO.
http://
www.
epa.
gov/
superfund/
resources/
scdm/
index.
htm.
Accessed
July
2001.
Memo
Attachment
B
Page
9
of
9
U.
S.
Environmental
Protection
Agency
(
EPA).
2000.
Exposure
and
Human
Health
Reassessment
of
2,3,7,8­
Tetrachlorodibenzo­
p­
Dioxin
(
TCDD)
and
Related
Compounds,
Part
1,
Vol.
3.
Office
of
Research
and
Development,
Washington,
DC:
GPO.

U.
S.
Environmental
Protection
Agency
(
EPA).
2001.
WATER9.
Office
of
Air
Quality
Planning
and
Standards,
Research
Triangle
Park,
NC.
http://
www.
epa.
gov/
ttn/
chief/
software/
water/
index.
html.
Accessed
July
2001.

U.
S.
National
Library
of
Medicine
(
NLM).
2001.
Hazardous
Substances
Data
Bank
(
HSDB).
http://
toxnet.
nlm.
nih.
gov/
cgi­
bin/
sis/
htmlgen?
HSDB.
Accessed
July
2001.
This
page
intentionally
left
blank.
Attachment
A­
2
Listing
of
Input
Specifications
for
Each
Unit
from
WATER9
This
page
intentionally
left
blank.
Page
1
of
17
Attachment
A.
1
Listing
of
Input
Specifications
for
Each
Unit
from
WATER9
Non­
aerated
units
Run
1
(
Tank
and
SI)

Type
of
unit
is
storage
tank
1
Description
of
unit
12
RUN1
TANK
2
Wastewater
temperature
(
C)
24.52
3
Open
surface
area
of
tank
(
m2)
0.9
4
Density
of
liquid
in
tank
(
g/
cc)
1
5
tank
waste
Mwt,
water=
18
18
6
tank
storage
time
(
days)
0
7
tank
paint
factor
1
8
tank
diameter
(
m)
1.1
9
tank
vapor
space
height
(
m)
0
10
diurnal
temp.
change
(
deg.
C)
11
11
tank
height
(
m)
2
12
oil
in
composite
wastewater
(
wt.
%)
0
Type
of
unit
is
lagoon
1
Description
of
unit
13
RUN1
SI
2
Wastewater
temperature
(
C)
24.52
3
Length
of
impoundment
(
m)
6
4
Depth
of
impoundment
(
m)
0.1
5
Width
of
impoundment
(
m)
6
6
active
biomass,
impoundment
(
g/
l)
0
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
14
RUN1
TANK
SOLIDS
2
flow
diversion
rate
(
l/
s)
3.66E­
06
3
fraction
solids
in
waste
diverted
0.63
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
16
RUN1
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
17
RUN1
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
18
RUN1
SI
SOLIDS
2
flow
diversion
rate
(
l/
s)
3.66E­
06
3
fraction
solids
in
waste
diverted
0.63
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
20
RUN1
SI
PIPE
Page
2
of
17
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
21
RUN1
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Page
3
of
17
Non­
aerated
Units
Run
2
(
SI
only)

Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
24
RUN2
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
25
RUN2
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
lagoon
1
Description
of
unit
26
RUN2
SI
2
Wastewater
temperature
(
C)
24.52
3
Length
of
impoundment
(
m)
8
4
Depth
of
impoundment
(
m)
0.2
5
Width
of
impoundment
(
m)
8
6
active
biomass,
impoundment
(
g/
l)
0.03
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
27
RUN2
SI
SOLIDS
2
flow
diversion
rate
(
l/
s)
6.39E­
06
3
fraction
solids
in
waste
diverted
0.63
Page
4
of
17
Non­
aerated
Units
Run
3
(
Tank
and
SI)

Type
of
unit
is
storage
tank
1
Description
of
unit
12
RUN3
TANK
2
Wastewater
temperature
(
C)
24.52
3
Open
surface
area
of
tank
(
m2)
6.6
4
Density
of
liquid
in
tank
(
g/
cc)
1
5
tank
waste
Mwt,
water=
18
18
6
tank
storage
time
(
days)
0
7
tank
paint
factor
1
8
tank
diameter
(
m)
2.9
9
tank
vapor
space
height
(
m)
0
10
diurnal
temp.
change
(
deg.
C)
11
11
tank
height
(
m)
2.6
12
oil
in
composite
wastewater
(
wt.
%)
0
Type
of
unit
is
lagoon
1
Description
of
unit
13
RUN3
SI
2
Wastewater
temperature
(
C)
24.52
3
Length
of
impoundment
(
m)
48
4
Depth
of
impoundment
(
m)
0.9
5
Width
of
impoundment
(
m)
48
6
active
biomass,
impoundment
(
g/
l)
0
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
14
RUN3
TANK
SOLIDS
2
flow
diversion
rate
(
l/
s)
0.00134
3
fraction
solids
in
waste
diverted
0.63
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
16
RUN3
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
17
RUN3
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
18
RUN3
SI
SOLIDS
2
flow
diversion
rate
(
l/
s)
0.00134
3
fraction
solids
in
waste
diverted
0.63
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
20
RUN3
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
Page
5
of
17
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
21
RUN3
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Page
6
of
17
Non­
aerated
Units
Run
4
(
SI
only)

Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
24
RUN4
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
25
RUN4
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
lagoon
1
Description
of
unit
26
RUN4
SI
2
Wastewater
temperature
(
C)
24.52
3
Length
of
impoundment
(
m)
17
4
Depth
of
impoundment
(
m)
0.4
5
Width
of
impoundment
(
m)
17
6
active
biomass,
impoundment
(
g/
l)
0.03
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
27
RUN4
SI
SOLIDS
2
flow
diversion
rate
(
l/
s)
0.00137
3
fraction
solids
in
waste
diverted
0.63
Page
7
of
17
Non­
aerated
Units
Run
5
(
Tank
and
SI)

Type
of
unit
is
storage
tank
1
Description
of
unit
12
RUN5
TANK
2
Wastewater
temperature
(
C)
24.52
3
Open
surface
area
of
tank
(
m2)
6
4
Density
of
liquid
in
tank
(
g/
cc)
1
5
tank
waste
Mwt,
water=
18
18
6
tank
storage
time
(
days)
0
7
tank
paint
factor
1
8
tank
diameter
(
m)
2.7
9
tank
vapor
space
height
(
m)
0
10
diurnal
temp.
change
(
deg.
C)
11
11
tank
height
(
m)
2.5
12
oil
in
composite
wastewater
(
wt.
%)
0
Type
of
unit
is
lagoon
1
Description
of
unit
13
RUN5
SI
2
Wastewater
temperature
(
C)
24.52
3
Length
of
impoundment
(
m)
8
4
Depth
of
impoundment
(
m)
0.2
5
Width
of
impoundment
(
m)
8
6
active
biomass,
impoundment
(
g/
l)
0
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
14
RUN5
TANK
SOLIDS
2
flow
diversion
rate
(
l/
s)
1.84E­
06
3
fraction
solids
in
waste
diverted
0.99
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
16
RUN5
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
17
RUN5
TANK
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
18
RUN5
SI
SOLIDS
2
flow
diversion
rate
(
l/
s)
1.84E­
06
3
fraction
solids
in
waste
diverted
0.99
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
20
RUN5
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
Page
8
of
17
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
21
RUN5
SI
PIPE
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Page
9
of
17
Aerated
Treatment
Train
Run
7
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
1
inlet
pipe
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
2
transfer
pipe
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
primary
municipal
clarifier
1
Description
of
unit
4
Primary
clarifier
2
Wastewater
temperature
(
C)
25
3
primary
clarifier
diameter
(
m)
1
4
primary
clarifier
depth
(
m)
2
5
clarifier
solids
removal
efficiency
0.6
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
8
Center
well
present,
=
1
1
10
number
of
identical
units
in
parallel
0
15
vent
air
emission
control
factor
0
16
cover
vent
rate
(
m3/
s
per
m2
surface)
0.0005
17
If
covered,
then
enter
1
0
Type
of
unit
is
activated
sludge
1
Description
of
unit
5
Activated
Sludge
2
Wastewater
temperature
(
C)
25
3
length
of
aeration
unit
(
m)
1
4
width
of
aeration
unit
(
m)
1
5
depth
of
aeration
unit
(
m)
3.5
6
Area
of
agitation
(
each
aerator,
m2)
1
7
Total
number
of
agitators
in
the
unit
1
8
Power
of
agitation
(
each
aerator,
HP)
0.014
9
Impeller
diameter
(
cm)
60
10
Impeller
rotation
(
RPM)
1200
11
Agitator
mechanical
efficiency
0.83
12
aerator
effectiveness,
alpha
0.83
13
if
there
is
plug
flow,
enter
1
0
14
Overall
biorate
(
mg/
g
bio­
hr)
19
15
Aeration
air
flow
(
m3/
s)
0.001
16
activated
sludge
biomass(
g/
l)
2.5
17
If
covered,
then
enter
1
0
18
agitator
pump
rate(
m3/
s
each)
0
Type
of
unit
is
circular
clarifier
1
Description
of
unit
6
Secondary
Clarifier
2
Wastewater
temperature
(
C)
25
3
secondary
clarifier
diameter
(
m)
1
4
secondary
clarifier
depth
(
m)
3
5
clarifier
solids
removal
efficiency
0.99
Page
10
of
17
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
7
SecClar
sludge
split
2
flow
diversion
rate
(
l/
s)
0.12
3
fraction
solids
in
waste
diverted
0.99
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
8
SecClar
sludge
split
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
9
Sludge
recycle
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
divert
flow
1
Description
of
unit
10
SecClar
wasted
sludge
2
flow
diversion
rate
(
l/
s)
0.007
4
fraction
waste
flow
diverted
0
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
11
SecClar
wasted
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
12
PrimClar
sludge
2
flow
diversion
rate
(
l/
s)
0.007
3
fraction
solids
in
waste
diverted
0.6
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
13
PrimClar
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
40
Act
sludge
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
Page
11
of
17
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
41
SecClar
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Page
12
of
17
Aerated
Treatment
Train
Run
8
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
42
inlet
pipe
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
43
transfer
pipe
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
primary
municipal
clarifier
1
Description
of
unit
45
primary
clarifier
2
Wastewater
temperature
(
C)
25
3
primary
clarifier
diameter
(
m)
3
4
primary
clarifier
depth
(
m)
3.8
5
clarifier
solids
removal
efficiency
0.6
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
8
Center
well
present,
=
1
1
10
number
of
identical
units
in
parallel
0
15
vent
air
emission
control
factor
0
16
cover
vent
rate
(
m3/
s
per
m2
surface)
0.0005
17
If
covered,
then
enter
1
0
Type
of
unit
is
activated
sludge
1
Description
of
unit
46
Activated
Sludge
2
Wastewater
temperature
(
C)
25
3
length
of
aeration
unit
(
m)
5.2
4
width
of
aeration
unit
(
m)
3.5
5
depth
of
aeration
unit
(
m)
5
6
Area
of
agitation
(
each
aerator,
m2)
47
7
Total
number
of
agitators
in
the
unit
1
8
Power
of
agitation
(
each
aerator,
HP)
0.34
9
Impeller
diameter
(
cm)
60
10
Impeller
rotation
(
RPM)
1200
11
Agitator
mechanical
efficiency
0.83
12
aerator
effectiveness,
alpha
0.83
13
if
there
is
plug
flow,
enter
1
0
14
Overall
biorate
(
mg/
g
bio­
hr)
19
15
Aeration
air
flow
(
m3/
s)
0.026
16
activated
sludge
biomass(
g/
l)
2.5
17
If
covered,
then
enter
1
0
18
agitator
pump
rate(
m3/
s
each)
0
Type
of
unit
is
circular
clarifier
1
Description
of
unit
47
Secondary
Clarifie
2
Wastewater
temperature
(
C)
25
3
secondary
clarifier
diameter
(
m)
4
4
secondary
clarifier
depth
(
m)
4
5
clarifier
solids
removal
efficiency
0.99
Page
13
of
17
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
48
SecClar
sludge
split
2
flow
diversion
rate
(
l/
s)
0.12
3
fraction
solids
in
waste
diverted
0.99
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
49
SecClar
sludge
split
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Total
water
added
at
the
unit
(
l/
s)
50
SecClar
sludge
recycle
2
Area
of
openings
at
unit
(
cm2)
50
3
Radius
of
drop
pipe
(
cm)
5
4
Drop
length
to
conduit
(
cm)
61
5
Humidity
of
inlet
air
(%)
60
6
Temperature
of
air
(
C)
10.16
7
Drain
air
velocity
(
ft/
min)
84
8
manhole
air
velocity
(
ft/
min)
128
9
Conduit
air
velocity
(
ft/
min)
66
10
Wind
velocity
(
cm/
s
at
10
m)
377
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
.015
13
friction
factor
liquid
.016
14
friction
factor
gas
.006
15
radius
of
underflow
conduit
(
cm)
12
16
Underflow
T
(
C)
25
17
oscillation
cycle
time
(
min)
5
18
design
collection
velocities
(
ft/
s)
2
Type
of
unit
is
divert
flow
1
Description
of
unit
51
SecClar
wasted
sludge
8
oil
molecular
weight
180
9
oil
density
(
g/
cc)
.8
10
NaUT
1=
municipal
2=
industrial
0
11
NaUT
1=
mass
tr.
2=
equil
0
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
52
SecClar
wasted
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
53
PrimClar
sludge
2
flow
diversion
rate
(
l/
s)
0.007
3
fraction
solids
in
waste
diverted
0.6
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
54
PrimClar
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
Page
14
of
17
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
81
Act
sludge
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
82
SecClar
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Page
15
of
17
Aerated
Treatment
Train
Run
9
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
1
inlet
pipe
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
2
transfer
pip
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
primary
municipal
clarifier
1
Description
of
unit
4
primary
clarifier
2
Wastewater
temperature
(
C)
25
3
primary
clarifier
diameter
(
m)
1
4
primary
clarifier
depth
(
m)
2
5
clarifier
solids
removal
efficiency
0.6
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
8
Center
well
present,
=
1
1
10
number
of
identical
units
in
parallel
0
15
vent
air
emission
control
factor
0
16
cover
vent
rate
(
m3/
s
per
m2
surface)
0.0005
17
If
covered,
then
enter
1
0
Type
of
unit
is
activated
sludge
1
Description
of
unit
5
Activated
Sludge
2
Wastewater
temperature
(
C)
25
3
length
of
aeration
unit
(
m)
0.8
4
width
of
aeration
unit
(
m)
0.8
5
depth
of
aeration
unit
(
m)
2.5
6
Area
of
agitation
(
each
aerator,
m2)
1
7
Total
number
of
agitators
in
the
unit
1
8
Power
of
agitation
(
each
aerator,
HP)
0.006
9
Impeller
diameter
(
cm)
60
10
Impeller
rotation
(
RPM)
1200
11
Agitator
mechanical
efficiency
0.83
12
aerator
effectiveness,
alpha
0.83
13
if
there
is
plug
flow,
enter
1
0
14
Overall
biorate
(
mg/
g
bio­
hr)
19
15
Aeration
air
flow
(
m3/
s)
0.00044
16
activated
sludge
biomass(
g/
l)
2.5
17
If
covered,
then
enter
1
0
18
agitator
pump
rate(
m3/
s
each)
0
Type
of
unit
is
circular
clarifier
1
Description
of
unit
6
Secondary
Clarifier
2
Wastewater
temperature
(
C)
25
3
secondary
clarifier
diameter
(
m)
1
4
secondary
clarifier
depth
(
m)
3
5
clarifier
solids
removal
efficiency
0.99
Page
16
of
17
6
waterfall
drop
height
(
cm)
20
7
clarifier
weir/
circumference
0.5
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
7
SecClar
sludge
split
2
flow
diversion
rate
(
l/
s)
0.12
3
fraction
solids
in
waste
diverted
0.99
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
8
SecClar
sludge
split
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
9
SecClar
Sludge
recycle
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
divert
flow
1
Description
of
unit
10
SecClar
wasted
sludge
2
flow
diversion
rate
(
l/
s)
0.007
4
fraction
waste
flow
diverted
0
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
11
SecClar
wasted
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
solids
removal
stream
1
Description
of
unit
12
PrimClar
sludge
2
flow
diversion
rate
(
l/
s)
0.007
3
fraction
solids
in
waste
diverted
0.6
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
13
PrimClar
sludge
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
40
Act
sludge
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
Page
17
of
17
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
Type
of
unit
is
hard
piped,
no
headspace
1
Description
of
unit
41
SecClar
effluent
2
Underflow
T
(
C)
25
3
Total
water
added
at
the
unit
(
l/
s)
0
7
Open
surface=
1
0
8
Subsurface
entrance=
1
1
9
subsurface
exit
=
1
1
10
radius
of
underflow
conduit
(
cm)
12
11
distance
to
next
unit
(
cm)
500
12
slope
of
underflow
conduit
0.015
This
page
intentionally
left
blank.
Attachment
A­
3
Toxicity
Benchmarks
Used
in
the
Industrial
Waste
Evaluation
Model
(
IWEM)
This
page
intentionally
left
blank.
Page
1
of
23
RESEARCH
TRIANGLE
INSTITUTE
MEMORANDUM
DATE:
August
27,
2001
TO:
Ann
Johnson
FROM:
Susan
N.
Wolf,
Robert
S.
Truesdale
SUBJECT:
Toxicity
benchmarks
used
in
the
Industrial
Waste
Evaluation
Model
(
IWEM)
(
revised)

Human
health
benchmarks
for
chronic
oral
and
inhalation
exposures
were
used
in
the
Industrial
Waste
Evaluation
Model
(
IWEM).
The
U.
S.
Environmental
Protection
Agency
(
EPA)
uses
reference
doses
(
RfDs)
and
reference
concentrations
(
RfCs)
to
evaluate
noncancer
risk
from
oral
and
inhalation
exposures,
respectively.
Oral
cancer
slope
factors
(
CSFs),
inhalation
unit
risk
factors
(
URFs),
and
inhalation
CSFs
are
used
to
evaluate
risk
for
carcinogens.

This
memorandum
provides
the
toxicity
benchmarks
used
in
IWEM.
Section
1.0
describes
the
data
sources
and
general
hierarchy
used
to
collect
these
benchmarks.
Section
2.0
provides
the
benchmarks
along
with
discussions
of
individual
human
health
benchmarks
extracted
from
a
variety
of
sources.

1.0
Methodology
and
Data
Sources
Several
sources
of
health
benchmarks
are
available.
Human
health
benchmarks
were
obtained
from
these
sources
in
the
following
order
of
preference:

#
Integrated
Risk
Information
System
(
IRIS)
#
Superfund
Technical
Support
Center
Provisional
Benchmarks
#
Health
Effects
Assessment
Summary
Tables
(
HEAST)
#
Agency
for
Toxic
Substances
and
Disease
Registry
(
ATSDR)
minimal
risk
levels
(
MRLs)
#
California
Environmental
Protection
Agency
(
CalEPA)
chronic
inhalation
reference
exposure
levels
(
RELs)
and
cancer
potency
factors.
#
EPA
health
assessment
documents
#
Various
other
EPA
health
benchmark
sources.

For
dioxins
and
dibenzofurans,
World
Health
Organization
(
WHO)
toxicity
equivalency
factors
(
TEFs)
from
Van
den
Berg
et
al.
(
1998)
were
applied
to
the
HEAST
CSF
for
2,3,7,8­
TCDD
to
get
CSFs
for
all
other
dioxins
and
furans
(
see
Section
2.4).
Page
2
of
23
#
Integrated
Risk
Information
System
(
IRIS)

Benchmarks
in
IRIS
are
prepared
and
maintained
by
EPA,
and
values
from
IRIS
were
used
in
IWEM
whenever
available.
IRIS
is
EPA's
electronic
database
containing
information
on
human
health
effects
(
U.
S.
EPA,
2001a).
Each
chemical
file
contains
descriptive
and
quantitative
information
on
potential
health
effects.
Health
benchmarks
for
chronic
noncarcinogenic
health
effects
include
RfDs
and
RfCs.
Cancer
classification,
oral
CSFs,
and
inhalation
URFs
are
included
for
carcinogenic
effects.
IRIS
is
the
official
repository
of
Agencywide
consensus
of
human
health
risk
information.

Inhalation
CSFs
are
not
available
from
IRIS,
so
they
were
calculated
from
inhalation
URFs
(
which
are
available
from
IRIS)
using
the
following
equation:

In
this
equation,
70
kg
represents
average
body
weight;
20
m3/
d
represents
average
inhalation
rate;
and
1000
:
g/
mg
is
a
units
conversion
factor
(
U.
S.
EPA,
1997).
These
standard
estimates
of
body
weight
and
inhalation
rate
are
used
by
EPA
in
the
calculation
of
the
URF,
and,
therefore,
the
values
were
used
to
calculate
inhalation
CSFs.

1.2
Superfund
Provisional
Benchmarks
The
Superfund
Technical
Support
Center
(
EPA's
National
Center
for
Environmental
Assessment
[
NCEA])
derives
provisional
RfCs,
RfDs,
and
CSFs
for
certain
chemicals.
These
provisional
health
benchmarks
can
be
found
in
Risk
Assessment
Issue
Papers.
Some
of
the
provisional
values
have
been
externally
peer
reviewed,
and
some
(
e.
g.,
trichloroethylene,
tetrachloroethylene)
come
from
previously
published
EPA
Health
Assessment
Documents.
These
provisional
values
have
not
undergone
EPA's
formal
review
process
for
finalizing
benchmarks
and
do
not
represent
Agency­
wide
consensus
information.
Specific
provisional
values
used
in
IWEM
are
described
in
Section
2.5.

1.3
Health
Effects
Summary
Tables
(
HEAST)

HEAST
is
a
listing
of
provisional
noncarcinogenic
and
carcinogenic
health
toxicity
values
(
RfDs,
RfCs,
URFs,
and
CSFs)
derived
by
EPA
(
U.
S.
EPA,
1997).
Although
the
health
toxicity
values
in
HEAST
have
undergone
review
and
have
the
concurrence
of
individual
EPA
program
offices,
either
they
have
not
been
reviewed
as
extensively
as
those
in
IRIS
or
their
data
set
is
not
complete
enough
to
be
listed
in
IRIS.
HEAST
benchmarks
have
not
been
updated
in
several
years
and
do
not
represent
Agency­
wide
consensus
information.
Page
3
of
23
1.4
ATSDR
Minimal
Risk
Levels
The
ATSDR
MRLs
are
substance­
specific
health
guidance
levels
for
noncarcinogenic
endpoints
(
ATSDR,
2001).
An
MRL
is
an
estimate
of
the
daily
human
exposure
to
a
hazardous
substance
that
is
likely
to
be
without
appreciable
risk
of
adverse
noncancer
health
effects
over
a
specified
duration
of
exposure.
MRLs
are
based
on
noncancer
health
effects
only
and
are
not
based
on
a
consideration
of
cancer
effects.
MRLs
are
derived
for
acute,
intermediate,
and
chronic
exposure
durations
for
oral
and
inhalation
routes
of
exposure.
Inhalation
and
oral
MRLs
are
derived
in
a
manner
similar
to
EPA's
RfCs
and
RfDs,
respectively
(
i.
e.,
ATSDR
uses
the
noobserved
adverse­
effect­
level/
uncertainty
factor
(
NOAEL/
UF)
approach);
however,
MRLs
are
intended
to
serve
as
screening
levels
and
are
exposure
duration­
specific.
Also,
ATSDR
uses
EPA's
1994
inhalation
dosimetry
methodology
in
the
derivation
of
inhalation
MRLs.
A
chronic
inhalation
MRL
for
mixed
xylenes
was
used
as
a
surrogate
for
each
of
the
xylene
isomers.

1.5
CalEPA
Cancer
Potency
Factors
and
Reference
Exposure
Levels
CalEPA
has
developed
cancer
potency
factors
for
chemicals
regulated
under
California's
Hot
Spots
Air
Toxics
Program
(
CalEPA,
1999a).
The
cancer
potency
factors
are
analogous
to
EPA's
oral
and
inhalation
CSFs.
CalEPA
has
also
developed
chronic
inhalation
RELs,
analogous
to
EPA's
RfC,
for
120
substances
(
CalEPA,
1999b,
2000).
CalEPA
used
EPA's
1994
inhalation
dosimetry
methodology
in
the
derivation
of
inhalation
RELs.
The
cancer
potency
factors
and
inhalation
RELs
have
undergone
internal
peer
review
by
various
California
agencies
and
have
been
the
subject
of
public
comment.
A
chronic
inhalation
REL
for
mixed
cresols
was
used
as
a
surrogate
for
each
of
the
cresol
isomers.

1.6
Other
EPA
Health
Benchmarks
EPA
has
also
derived
health
benchmark
values
in
other
risk
assessment
documents,
such
as
Health
Assessment
Documents
(
HADs),
Health
Effect
Assessments
(
HEAs),
Health
and
Environmental
Effects
Profiles
(
HEEPs),
Health
and
Environmental
Effects
Documents
(
HEEDs),
Drinking
Water
Criteria
Documents,
and
Ambient
Water
Quality
Criteria
Documents.
Evaluations
of
potential
carcinogenicity
of
chemicals
in
support
of
reportable
quantity
adjustments
were
published
by
EPA's
Carcinogen
Assessment
Group
(
CAG)
and
may
include
cancer
potency
factor
estimates.
Health
toxicity
values
identified
in
these
EPA
documents
are
usually
dated
and
are
not
recognized
as
Agency­
wide
consensus
information
or
verified
benchmarks,
however,
and
as
a
result
they
are
used
in
the
hierarchy
only
when
values
are
not
available
from
IRIS,
HEAST,
Superfund
provisional
values,
ATSDR,
or
CalEPA.
Section
2.6
describes
the
specific
values
from
these
alternative
EPA
sources
that
were
used
in
IWEM.

2.0
IWEM
Human
Health
Benchmarks
The
chronic
human
health
benchmarks
used
to
calculate
the
health­
based
numbers
(
HBNs)
in
IWEM
are
summarized
in
Table
1,
which
provides
the
Chemical
Abstract
Service
Registry
Number
(
CASRN),
constituent
name,
RfD
(
mg/
kg­
d),
RfC
(
mg/
m3),
oral
CSF
1A
twofold
increase
of
the
oral
CSF
to
1.4
per
mg/
kg­
d
to
account
for
continuous
lifetime
exposure
from
birth
was
also
recommended
but
was
not
used
for
IWEM.

2A
twofold
increase
to
8.8E­
6
per
:
g/
m3
for
the
inhalation
URF,
to
account
for
continuous
lifetime
exposure
from
birth,
was
also
recommended
but
was
not
used
for
IWEM.

Page
4
of
23
(
mg/
kg­
d­
1),
inhalation
URF
[(:
g/
m3)­
1],
inhalation
CSF
(
mg/
kg­
d­
1),
and
reference
for
each
benchmark.
A
key
to
the
references
cited
and
abbreviations
used
is
provided
at
the
end
of
the
table.

For
a
majority
of
IWEM
constituents,
human
health
benchmarks
were
available
from
IRIS
(
U.
S.
EPA,
2001a),
Superfund
Provisional
Benchmarks,
or
HEAST
(
U.
S.
EPA,
1997).
Benchmarks
also
were
obtained
from
ATSDR
(
2001)
or
CalEPA
(
1999a,
1999b,
2000).
This
section
describes
benchmarks
obtained
from
other
sources,
along
with
the
Superfund
Provisional
values
and
special
uses
(
e.
g.,
benzene,
vinyl
chloride)
of
IRIS
benchmarks.

2.1
Benzene
The
cancer
risk
estimates
for
benzene
are
provided
as
ranges
in
IRIS.
The
oral
CSF
for
benzene
is
1.5E­
02
to
5.5E­
02
(
mg/
kg/
d)­
1
and
the
inhalation
URF
is
2.2E­
06
to
7.8E­
06
(
µ
g/
m3)­
1
(
U.
S.
EPA,
2001a).
For
IWEM,
the
upper
range
estimates
were
used
(
i.
e.,
5.5E­
02
(
mg/
kg/
d)­
1
and
7.8E­
06
(
µ
g/
m3)­
1
for
the
oral
CSF
and
inhalation
URF,
respectively).

2.2
Vinyl
Chloride
Based
on
use
of
the
linearized
multistage
model,
IRIS
recommends
an
oral
CSF
of
7.2E­
1
per
mg/
kg­
d
for
vinyl
chloride
to
account
for
continuous
lifetime
exposure
during
adulthood;
this
value
was
used
for
IWEM.
1
Based
on
use
of
the
linearized
multistage
model,
an
inhalation
URF
of
4.4E­
6
per
:
g/
m3
to
account
for
continuous,
lifetime
exposure
during
adulthood
was
recommended
for
vinyl
chloride
and
was
used
for
IWEM;
an
inhalation
CSF
of
1.5E­
2
per
mg/
kg­
d
was
calculated
from
the
URF.
2
2.3
Polychlorinated
Biphenyls
There
are
two
inhalation
CSFs
available
from
IRIS
for
polychlorinated
biphenyls
(
PCBs):
0.4
per
mg/
kg­
d
for
evaporated
congeners
and
2.0
per
mg/
kg­
d
for
dust
or
aerosol
(
high
risk
and
persistence).
The
inhalation
CSF
for
evaporated
congeners
will
be
used
for
IWEM.
Page
5
of
23
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Acenaphthene
83­
32­
9
6.0E­
02
I
Acetaldehyde
(
ethanal)
75­
07­
0
9.0E­
03
I
2.2E­
06
I
7.7E­
03
calc
Acetone
(
2­
propanone)
67­
64­
1
1.0E­
01
I
3.1E+
01
A
Acetonitrile
(
methyl
cyanide)
75­
05­
8
6.0E­
02
I
Acetophenone
98­
86­
2
1.0E­
01
I
Acrolein
107­
02­
8
2.0E­
02
H
2.0E­
05
I
Acrylamide
79­
06­
1
2.0E­
04
I
4.5E+
0
I
1.3E­
03
I
4.6E+
00
calc
Acrylic
acid
(
propenoic
acid)
79­
10­
7
5.0E­
01
I
1.0E­
03
I
Acrylonitrile
107­
13­
1
1.0E­
03
H
5.4E­
1
I
2.0E­
03
I
6.8E­
05
I
2.4E­
01
calc
Aldrin
309­
00­
2
3.0E­
05
I
1.7E+
01
I
4.9E­
03
I
1.7E+
01
calc
Allyl
alcohol
107­
18­
6
5.0E­
03
I
Aniline
(
benzeneamine)
62­
53­
3
5.7E­
3
I
1.0E­
03
I
1.6E­
06
C99a
5.6E­
03
calc
Anthracene
120­
12­
7
3.0E­
01
I
Antimony
7440­
36­
0
4.0E­
04
I
Arsenic
7440­
38­
2
3.0E­
04
I
1.5E+
00
I
Barium
7440­
39­
3
7.0E­
02
I
Benz{
a}
anthracene
56­
55­
3
1.2E+
00
C99a
1.1E­
04
C99a
3.9E­
01
calc
Benzene
71­
43­
2
5.5E­
02
I
6.0E­
02
C00
7.8E­
06
I
2.7E­
02
calc
Benzidine
92­
87­
5
3.0E­
03
I
2.3E+
02
I
6.7E­
02
I
2.3E+
02
I
Benzo{
a}
pyrene
50­
32­
8
7.3E+
00
I
1.1E­
03
C99a
3.9E+
00
calc
Benzo{
b}
fluoranthene
205­
99­
2
1.2E+
00
C99a
1.1E­
04
C99a
3.9E­
01
calc
Benzyl
chloride
100­
44­
7
1.7E­
01
I
4.9E­
05
C99a
1.7E­
01
calc
Benzyl
alcohol
100­
51­
6
3.0E­
01
H
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
6
of
23
Beryllium
7440­
41­
7
2.0E­
03
I
Bis(
2­
chloroethyl)
ether
111­
44­
4
1.1E+
00
I
3.3E­
04
I
1.2E+
00
calc
Bis(
2­
chloroisopropyl)
ether
39638­
32­
9
4.0E­
02
I
7.0E­
02
H
1.0E­
05
H
3.5E­
02
calc
Bis(
2­
ethylhexyl)
phthalate
117­
81­
7
2.0E­
02
I
1.4E­
02
I
1.0E­
02
C99b
2.4E­
06
C99a
8.4E­
03
calc
Bromodichloromethane
75­
27­
4
2.0E­
02
I
6.2E­
2
I
1.8E­
05
AC
6.2E­
02
AC
Bromomethane
(
methyl
bromide)
74­
83­
9
1.4E­
03
I
5.0E­
03
I
Butadiene,
1,3­
106­
99­
0
2.0E­
02
C00
2.8E­
04
I
9.8E­
01
calc
Butanol
71­
36­
3
1.0E­
01
I
Butyl
benzyl
phthalate
85­
68­
7
2.0E­
01
I
Butyl­
4,6­
dinitrophenol,
2­
sec­
(
Dinoseb)
88­
85­
7
1.0E­
03
I
Cadmium
7440­
43­
9
5.0E­
04
I
Carbon
tetrachloride
56­
23­
5
7.0E­
04
I
1.3E­
1
I
7.0E­
03
SF
1.5E­
05
I
5.3E­
02
calc
Carbon
disulfide
75­
15­
0
1.0E­
01
I
7.0E­
01
I
Chlordane
57­
74­
9
5.0E­
04
I
3.5E­
01
I
7.0E­
04
I
1.0E­
04
I
3.5E­
01
calc
Chloro­
1,3­
butadiene,
2­
(
Chloroprene)
126­
99­
8
2.0E­
02
H
7.0E­
03
H
Chloroaniline,
p­
106­
47­
8
4.0E­
03
I
Chlorobenzene
108­
90­
7
2.0E­
02
I
6.0E­
02
SF
Chlorobenzilate
510­
15­
6
2.0E­
02
I
2.7E­
01
H
7.8E­
05
H
2.7E­
01
calc
Chlorodibromomethane
124­
48­
1
2.0E­
02
I
8.4E­
2
I
2.4E­
05
AC
8.4E­
02
AC
Chloroethane
(
ethyl
chloride)
75­
00­
3
1.0E+
01
I
Chloroform
67­
66­
3
1.0E­
02
I
1.0E­
01
A
Chloromethane
(
methyl
chloride)
74­
87­
3
1.3E­
2
H
9.0E­
02
I
1.8E­
06
H
6.3E­
03
calc
Chlorophenol,
2­
95­
57­
8
5.0E­
03
I
1.4E­
03
AC
Chloropropene,
3­
(
allyl
chloride)
107­
05­
1
1.0E­
03
I
6.0E­
06
C99a
2.1E­
02
calc
Chromium
(
III)
16065­
83­
1
1.5E+
00
I
Chromium
(
VI)
18540­
29­
9
3.0E­
03
I
Chrysene
218­
01­
9
1.2E­
01
C99a
1.1E­
05
C99a
3.9E­
02
calc
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
7
of
23
Cobalt
7440­
48­
4
2.0E­
02
SF
Copper
7440­
50­
8
*
MCL
only
Cresol,
p­
106­
44­
5
5.0E­
03
H
6.0E­
01
surr
(
C00)

Cresol,
o­
95­
48­
7
5.0E­
02
I
6.0E­
01
surr
(
C00)

Cresol,
m­
108­
39­
4
5.0E­
02
I
6.0E­
01
surr
(
C00)

Cresols
(
total)
1319­
77­
3
5.0E­
02
surr
(
I)
6.0E­
01
C00
Cumene
98­
82­
8
1.0E­
01
I
4.0E­
01
I
Cyclohexanol
108­
93­
0
1.7E­
05
solv
2.0E­
05
solv
Cyclohexanone
108­
94­
1
5.0E+
00
I
DDD
72­
54­
8
2.4E­
01
I
DDE
72­
55­
9
3.4E­
01
I
DDT,
p,
p'­
50­
29­
3
5.0E­
04
I
3.4E­
01
I
9.7E­
05
I
3.4E­
01
calc
Di­
n­
butyl
phthalate
84­
74­
2
1.0E­
01
I
Di­
n­
octyl
phthalate
117­
84­
0
2.0E­
02
H
Diallate
2303­
16­
4
6.1E­
02
H
Dibenz{
a,
h}
anthracene
53­
70­
3
7.3E+
00
TEF
1.2E­
03
C99a
4.2E+
00
calc
Dibromo­
3­
chloropropane,
1,2­
96­
12­
8
1.4E+
0
H
2.0E­
04
I
6.9E­
07
H
2.4E­
03
calc
Dichlorobenzene,
1,2­
95­
50­
1
9.0E­
02
I
2.0E­
01
H
Dichlorobenzene,
1,4­
106­
46­
7
2.4E­
2
H
8.0E­
01
I
1.1E­
05
C99a
3.9E­
02
calc
Dichlorobenzidine,
3,3'­
91­
94­
1
4.5E­
01
I
3.4E­
04
C99a
1.2E+
00
calc
Dichlorodifluoromethane
(
Freon
12)
75­
71­
8
2.0E­
01
I
2.0E­
01
H
Dichloroethane,
1,2­
107­
06­
2
9.1E­
2
I
2.4E+
00
A
2.6E­
05
I
9.1E­
02
calc
Dichloroethane,
1,1­
75­
34­
3
1.0E­
01
H
5.0E­
01
H
1.6E­
06
C99a
5.6E­
03
calc
Dichloroethylene,
1,1­
75­
35­
4
9.0E­
03
I
6.0E­
1
I
7.0E­
02
C00
5.0E­
05
I
1.8E­
01
calc
Dichloroethylene,
trans­
1,2­
156­
60­
5
2.0E­
02
I
Dichloroethylene,
cis­
1,2­
156­
59­
2
1.0E­
02
H
Dichlorophenol,
2,4­
120­
83­
2
3.0E­
03
I
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
8
of
23
Dichlorophenoxyacetic
acid,
2,4­
(
2,4­
D)
94­
75­
7
1.0E­
02
I
Dichloropropane,
1,2­
78­
87­
5
9.0E­
02
A
6.8E­
2
H
4.0E­
03
I
Dichloropropene,
trans­
1,3­
10061­
02­
6
3.0E­
02
I
1.0E­
1
I
2.0E­
02
surr
(
I)
4.0E­
06
surr
(
I)
1.4E­
02
calc
Dichloropropene,
cis­
1,3­
10061­
01­
5
3.0E­
02
I
1.0E­
1
I
2.0E­
02
surr
(
I)
4.0E­
06
surr
(
I)
1.4E­
02
calc
Dichloropropene,
1,3­
(
mixture
of
isomers)
542­
75­
6
3.0E­
02
I
1.0E­
01
I
2.0E­
02
I
4.0E­
06
I
1.4E­
02
calc
Dieldrin
60­
57­
1
5.0E­
05
I
1.6E+
01
I
4.6E­
03
I
1.6E+
01
calc
Diethyl
phthalate
84­
66­
2
8.0E­
01
I
Diethylstilbestrol
56­
53­
1
4.7E+
03
H
Dimethoate
60­
51­
5
2.0E­
04
I
Dimethoxybenzidine,
3,3'­
119­
90­
4
1.4E­
02
H
Dimethyl
phthalate
131­
11­
3
Dimethyl
formamide,
N,
N­
(
DMF)
68­
12­
2
1.0E­
01
H
3.0E­
02
I
Dimethylbenz{
a}
anthracene,
7,12­
57­
97­
6
7.1E­
02
C99a
2.5E+
02
calc
Dimethylbenzidine,
3,3'­
119­
93­
7
9.2E+
00
H
Dimethylphenol,
2,4­
105­
67­
9
2.0E­
02
I
Dimethylphenol,
3,4­
95­
65­
8
1.0E­
03
I
Dinitrobenzene,
1,3­
99­
65­
0
1.0E­
04
I
Dinitrophenol,
2,4­
51­
28­
5
2.0E­
03
I
Dinitrotoluene,
2,6­
606­
20­
2
1.0E­
03
H
6.8E­
01
surr
(
I)

Dinitrotoluene,
2,4­
121­
14­
2
2.0E­
03
I
6.8E­
01
surr
(
I)
8.9E­
05
C99a
3.1E­
01
calc
Dioxane,
1,4­
123­
91­
1
1.1E­
2
I
3.0E+
00
C00
7.7E­
06
C99a
2.7E­
02
calc
Diphenylamine
122­
39­
4
2.5E­
02
I
Diphenylhydrazine,
1,2­
122­
66­
7
8.0E­
1
I
2.2E­
04
I
7.7E­
01
calc
Disulfoton
298­
04­
4
4.0E­
05
I
Endosulfan
(
Endosulfan
I
and
II,
mixture)
115­
29­
7
6.0E­
03
I
Endrin
72­
20­
8
3.0E­
04
I
Epichlorohydrin
106­
89­
8
2.0E­
03
H
9.9E­
3
I
1.0E­
03
I
1.2E­
06
I
4.2E­
03
calc
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
9
of
23
Epoxybutane,
1,2­
106­
88­
7
2.0E­
02
I
Ethoxyethanol
acetate,
2­
111­
15­
9
3.0E­
01
H
3.0E­
01
C00
Ethoxyethanol,
2­
110­
80­
5
4.0E­
01
H
2.0E­
01
I
Ethyl
acetate
141­
78­
6
9.0E­
01
I
Ethyl
ether
60­
29­
7
2.0E­
01
I
Ethyl
methacrylate
97­
63­
2
9.0E­
02
H
Ethyl
methanesulfonate
62­
50­
0
2.9E+
02
RQ
Ethylbenzene
100­
41­
4
1.0E­
01
I
1.0E+
00
I
1.1E­
06
SF
3.9E­
03
calc
Ethylene
oxide
75­
21­
8
1.0E+
0
H
3.0E­
02
C00
1.0E­
04
H
3.5E­
01
calc
Ethylene
dibromide
(
1,2­
dibromoethane)
106­
93­
4
8.5E+
1
I
2.0E­
04
H
2.2E­
04
I
7.7E­
01
calc
Ethylene
glycol
107­
21­
1
2.0E+
00
I
4.0E­
01
C00
Ethylene
thiourea
96­
45­
7
8.0E­
05
I
1.1E­
01
H
1.3E­
05
C99a
4.6E­
02
calc
Fluoranthene
206­
44­
0
4.0E­
02
I
Fluorene
86­
73­
7
4.0E­
02
I
Fluoride
16984­
48­
8
6.0E­
02
surr
(
I)

Formaldehyde
50­
00­
0
2.0E­
01
I
9.8E­
03
A
1.3E­
05
I
4.6E­
02
calc
Formic
acid
64­
18­
6
2.0E+
00
H
Furan
110­
00­
9
1.0E­
03
I
Furfural
98­
01­
1
3.0E­
03
I
5.0E­
02
H
HCH,
beta­
319­
85­
7
1.8E+
00
I
5.3E­
04
I
1.9E+
00
calc
HCH,
gamma­
(
Lindane)
58­
89­
9
3.0E­
04
I
1.3E+
00
H
3.1E­
04
C99a
1.1E+
00
calc
HCH,
alpha­
319­
84­
6
8.0E­
03
A
6.3E+
00
I
1.8E­
03
I
6.3E+
00
calc
Heptachlor
76­
44­
8
5.0E­
04
I
4.5E+
00
I
1.3E­
03
I
4.6E+
00
calc
Heptachlor
epoxide
1024­
57­
3
1.3E­
05
I
9.1E+
00
I
2.6E­
03
I
9.1E+
00
calc
Hexachloro­
1,3­
butadiene
87­
68­
3
3.0E­
04
SF
7.8E­
2
I
2.2E­
05
I
7.7E­
02
calc
Hexachlorobenzene
118­
74­
1
8.0E­
04
I
1.6E+
0
I
4.6E­
04
I
1.6E+
00
calc
Hexachlorocyclopentadiene
77­
47­
4
6.0E­
03
I
2.0E­
04
I
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
10
of
23
Hexachlorodibenzo­
p­
dioxins
(
HxCDDs)
34465­
46­
8
1.5E+
04
WHO98
3.3E+
00
WHO98
1.5E+
04
WHO98
Hexachlorodibenzofurans
(
HxCDFs)
55684­
94­
1
1.5E+
04
WHO98
3.3E+
00
WHO98
1.5E+
04
WHO98
Hexachloroethane
67­
72­
1
1.0E­
03
I
1.4E­
2
I
4.0E­
06
I
1.4E­
02
calc
Hexachlorophene
70­
30­
4
3.0E­
04
I
Hexane,
n­
110­
54­
3
1.1E+
01
SF
2.0E­
01
I
Indeno{
1,2,3­
cd}
pyrene
193­
39­
5
1.2E+
00
C99a
1.1E­
04
C99a
3.9E­
01
calc
Isobutyl
alcohol
78­
83­
1
3.0E­
01
I
Isophorone
78­
59­
1
2.0E­
01
I
9.5E­
4
I
2.0E+
00
C99b
Kepone
143­
50­
0
5.0E­
04
A
Lead
7439­
92­
1
*
MCL
only
Manganese
7439­
96­
5
4.7E­
02
I
Mercury
7439­
97­
6
1.0E­
04
surr
(
I)
3.0E­
04
I
Methacrylonitrile
126­
98­
7
1.0E­
04
I
7.0E­
04
H
Methanol
67­
56­
1
5.0E­
01
I
4.0E+
00
C00
Methoxychlor
72­
43­
5
5.0E­
03
I
Methoxyethanol,
2­
109­
86­
4
1.0E­
03
H
2.0E­
02
I
Methoxyethanol
acetate,
2­
110­
49­
6
2.0E­
03
H
9.0E­
02
C00
Methyl
parathion
298­
00­
0
2.5E­
04
I
Methyl
methacrylate
80­
62­
6
1.4E+
00
I
7.0E­
01
I
Methyl
isobutyl
ketone
108­
10­
1
8.0E­
02
H
8.0E­
02
H
Methyl
ethyl
ketone
78­
93­
3
6.0E­
01
I
1.0E+
00
I
Methyl
tert­
butyl
ether
(
MTBE)
1634­
04­
4
3.0E+
00
I
Methylcholanthrene,
3­
56­
49­
5
6.3E­
03
C99a
2.2E+
01
calc
Methylene
bromide
(
dibromomethane)
74­
95­
3
1.0E­
02
H
Methylene
Chloride
(
dichloromethane)
75­
09­
2
6.0E­
02
I
7.5E­
3
I
3.0E+
00
H
4.7E­
07
I
1.6E­
03
calc
Molybdenum
7439­
98­
7
5.0E­
03
I
N­
Nitroso­
di­
n­
butylamine
924­
16­
3
5.4E+
0
I
1.6E­
03
I
5.6E+
00
calc
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
11
of
23
N­
Nitroso­
di­
n­
propylamine
621­
64­
7
7.0E+
00
I
2.0E­
03
C99a
7.0E+
00
calc
N­
Nitrosodiethylamine
55­
18­
5
1.5E+
2
I
4.3E­
02
I
1.5E+
02
calc
N­
Nitrosodimethylamine
62­
75­
9
8.00E­
06
SF
5.1E+
01
I
1.4E­
02
I
4.9E+
01
calc
N­
Nitrosodiphenylamine
86­
30­
6
2.00E­
02
SF
4.9E­
03
I
2.6E­
06
C99a
9.1E­
03
calc
N­
Nitrosomethylethylamine
10595­
95­
6
2.2E+
01
I
6.3E­
03
C99a
3.7E+
00
C99a
N­
Nitrosopiperidine
100­
75­
4
2.7E­
03
C99a
9.5E+
00
calc
N­
Nitrosopyrrolidine
930­
55­
2
2.1E+
0
I
6.1E­
04
I
2.1E+
00
calc
Naphthalene
91­
20­
3
2.0E­
02
I
3.0E­
03
I
Nickel
7440­
02­
0
2.0E­
02
I
Nitrobenzene
98­
95­
3
5.0E­
04
I
2.0E­
03
H
Nitropropane,
2­
79­
46­
9
2.0E­
02
I
2.7E­
03
H
9.5E+
00
calc
Octamethyl
pyrophosphoramide
152­
16­
9
2.0E­
03
H
Parathion
(
ethyl)
56­
38­
2
6.0E­
03
H
Pentachlorobenzene
608­
93­
5
8.0E­
04
I
Pentachlorodibenzo­
p­
dioxins
(
PeCDDs)
36088­
22­
9
1.5E+
05
WHO98
3.3E+
01
WHO98
1.5E+
05
WHO98
Pentachlorodibenzofurans
(
PeCDFs)
30402­
15­
4
7.5E+
04
WHO98
1.7E+
01
WHO98
7.5E+
04
WHO98
Pentachloronitrobenzene
(
PCNB)
82­
68­
8
3.0E­
03
I
2.6E­
01
H
Pentachlorophenol
87­
86­
5
3.0E­
02
I
1.2E­
01
I
5.1E­
06
C99a
1.8E­
02
calc
Phenol
108­
95­
2
6.0E­
01
I
Phenyl
mercuric
acetate
62­
38­
4
8.0E­
05
I
Phenylenediamine,
1,3­
108­
45­
2
6.0E­
03
I
Phorate
298­
02­
2
2.0E­
04
H
Phthalic
anhydride
85­
44­
9
2.0E+
00
I
1.2E­
01
H
Polychlorinated
biphenyls
(
Aroclors)
1336­
36­
3
2.0E­
05
surr
(
I)
4.0E­
01
I
1.0E­
04
I
4.0E­
01
I
Pronamide
23950­
58­
5
7.5E­
02
I
Propylene
oxide
(
1,2­
epoxypropane)
75­
56­
9
2.4E­
1
I
3.0E­
02
I
3.7E­
06
I
1.3E­
02
calc
Pyrene
129­
00­
0
3.0E­
02
I
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
12
of
23
Pyridine
110­
86­
1
1.0E­
03
I
7.0E­
03
EPA86
Safrole
94­
59­
7
1.8E­
01
RQ
Selenium
7782­
49­
2
5.0E­
03
I
Silver
7440­
22­
4
5.0E­
03
I
Strychnine
and
salts
57­
24­
9
3.0E­
04
I
Styrene
100­
42­
5
2.0E­
01
I
1.0E+
00
I
Tetrachlorobenzene,
1,2,4,5­
95­
94­
3
3.0E­
04
I
Tetrachlorodibenzo­
p­
dioxin
(
TCDD),

2,3,7,8­
1746­
01­
6
1.0E­
09
A
1.5E+
5
H
3.3E+
01
H
1.5E+
05
H
Tetrachlorodibenzo­
p­
dioxins
(
TCDDs)
41903­
57­
5
1.5E+
05
surr
(
H)
3.3E+
01
surr
(
H)
1.5E+
05
surr
(
H)

Tetrachlorodibenzofurans
(
TCDFs)
55722­
27­
5
1.5E+
04
WHO98
3.3E+
00
WHO98
1.5E+
04
WHO98
Tetrachloroethane,
1,1,2,2­
79­
34­
5
6.0E­
02
SF
2.0E­
1
I
5.8E­
05
I
2.0E­
01
calc
Tetrachloroethane,
1,1,1,2­
630­
20­
6
3.0E­
02
I
2.6E­
2
I
7.4E­
06
I
2.6E­
02
calc
Tetrachloroethylene
127­
18­
4
1.0E­
02
I
5.2E­
02
HAD
3.0E­
01
A
5.8E­
07
HAD
2.0E­
03
HAD
Tetrachlorophenol,
2,3,4,6­
58­
90­
2
3.0E­
02
I
Tetraethyl
dithiopyrophosphate
(
Sulfotep)
3689­
24­
5
5.0E­
04
I
Thallium
7440­
28­
0
8.0E­
05
surr
(
I)

Thiram
(
Thiuram)
137­
26­
8
5.0E­
03
I
Toluene
108­
88­
3
2.0E­
01
I
4.0E­
01
I
Toluenediamine,
2,4­
95­
80­
7
3.2E+
00
H
1.1E­
03
C99a
3.9E+
00
calc
Toluidine,
o­
95­
53­
4
2.4E­
1
H
6.9E­
05
AC
2.4E­
01
AC
Toluidine,
p­
106­
49­
0
1.9E­
01
H
Toxaphene
(
chlorinated
camphenes)
8001­
35­
2
1.1E+
00
I
3.2E­
04
I
1.1E+
00
calc
Tribromomethane
(
bromoform)
75­
25­
2
2.0E­
02
I
7.9E­
03
I
1.1E­
06
I
3.9E­
03
calc
Trichloro­
1,2,2­
trifluoroethane,
1,1,2­
76­
13­
1
3.0E+
01
I
3.0E+
01
H
Trichlorobenzene,
1,2,4­
120­
82­
1
1.0E­
02
I
2.0E­
01
H
Trichloroethane,
1,1,1­
71­
55­
6
2.8E­
01
SF
2.2E+
00
SF
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Constituent
Name
CASRN
RfD
(
mg/
kg­
d)
RfD
Ref
CSFo
(
per
mg/
kg­
d)
CSFo
Ref
RfC
(
mg/
m3)
RfC
Ref
URF
(
per
ug/
m3)
URF
Ref
CSFi
(
per
mg/
kg­
d)
CSFi
Ref
Page
13
of
23
Trichloroethane,
1,1,2­
79­
00­
5
4.0E­
03
I
5.7E­
02
I
1.6E­
05
I
5.6E­
02
calc
Trichloroethylene
(
1,1,2­
trichloroethylene)
79­
01­
6
1.1E­
02
HAD
6.0E­
01
C00
1.7E­
06
HAD
6.0E­
03
HAD
Trichlorofluoromethane
(
Freon
11)
75­
69­
4
3.0E­
01
I
7.0E­
01
H
Trichlorophenol,
2,4,5­
95­
95­
4
1.0E­
01
I
Trichlorophenol,
2,4,6­
88­
06­
2
1.1E­
02
I
3.1E­
06
I
1.1E­
02
calc
Trichlorophenoxy)
propionic
acid,
2­(
2,4,5­

(
Silvex)
93­
72­
1
8.0E­
03
I
Trichlorophenoxyacetic
acid,
2,4,5­
93­
76­
5
1.0E­
02
I
Trichloropropane,
1,2,3­
96­
18­
4
6.0E­
03
I
7.0E+
00
H
5.0E­
03
SF
Triethylamine
121­
44­
8
7.0E­
03
I
Trinitrobenzene,
sym­

(
1,3,5­
Trinitrobenzene)
99­
35­
4
3.0E­
02
I
Tris(
2,3­
dibromopropyl)
phosphate
126­
72­
7
9.8E+
00
RQ
Vanadium
7440­
62­
2
7.0E­
03
H
Vinyl
acetate
108­
05­
4
1.0E+
00
H
2.0E­
01
I
Vinyl
chloride
75­
01­
4
3.0E­
03
I
7.2E­
01
I
1.0E­
01
I
4.4E­
06
I
1.5E­
02
calc
Xylene,
p­
106­
42­
3
2.0E+
00
surr
(
H)
4.0E­
01
surr
(
A)

Xylene,
m­
108­
38­
3
2.0E+
00
H
4.0E­
01
surr
(
A)

Xylene,
o­
95­
47­
6
2.0E+
00
H
4.0E­
01
surr
(
A)

Xylenes
(
total)
1330­
20­
7
2.0E+
00
I
4.0E­
01
A
Zinc
7440­
66­
6
3.0E­
01
I
Key:
CASRN
=
Chemical
Abstract
Service
registry
number.
CSFo
=
oral
cancer
slope
factor.

RfD
=
reference
dose.
CSFi
=
inhalation
cancer
slope
factor.

RfC
=
reference
concentration.
URF
=
unit
risk
factor.
Table
1.
Human
Health
Benchmarks
Used
in
IWEM
(
continued)

Page
14
of
23
a
Sources:

A
=
ATSDR
MRLs
(
ATSDR,
2001)
I
=
IRIS
(
U.
S.
EPA,
2001a)

AC
=
developed
for
the
Air
Characteristic
Study
(
U.
S.
EPA,
1999g)
RQ
=
reportable
quantity
adjustments
(
U.
S.
EPA,
1998d,
e,
f)

calc
=
calculated
SF
=
Superfund
Risk
Issue
Paper
(
U.
S.
EPA,
1998a,
b;
1999a,
b,
c,
d,
e,
f;

C99a
=
CalEPA
cancer
potency
factor
(
CalEPA,
1999a)
2000,
2001b,
c,
d)

C99b
=
CalEPA
chronic
REL
(
CalEPA,
1999b)
solv
=
63
FR
64371­
0402
(
U.
S.
EPA,
1998c)

C00
=
CalEPA
chronic
REL
(
CalEPA,
2000)
surr
=
surrogate
(
source
in
parentheses;
see
section
2.8)

HAD
=
Health
Assessment
Document
(
U.
S.
EPA,
1986a,
1987)
TEF
=
toxicity
equivalency
factor
(
U.
S.
EPA,
1993)

H
=
HEAST
(
U.
S.
EPA,
1997)
WHO98=
World
Health
Organization
(
WHO)
1998
toxicity
equivalency
factor
scheme
(
Van
den
Berg
et
al.,
1998)
Page
15
of
23
2.4
Dioxin­
like
Compounds
Cancer
slope
factors
for
some
dioxin­
like
compounds
were
calculated
by
using
the
toxic
equivalency
factor
(
TEF)
approach
(
Van
den
Berg
et
al.,
1998).
For
the
TEF
approach,
the
toxicity
of
a
group
of
chemically
related
constituents
that
typically
occur
in
the
environment
as
mixtures
is
based
on
estimates
of
the
toxic
potency
of
each
constituent
as
compared
with
a
reference
compound
within
the
group.
TEF
estimates
are
based
on
a
knowledge
of
the
mechanism
of
action,
available
experimental
data,
and
other
structure­
activity
information.
TEFs
have
been
established
for
a
number
of
polychlorinated
dibenzodioxins,
polychlorinated
dibenzofurans,
and
polychlorinated
biphenyl
(
PCB)
congeners
thought
to
have
dioxin­
like
toxicity
(
Van
den
Berg
et
al.,
1998).
The
TEFs
listed
in
Table
2
were
used
for
the
dioxin
and
furan
congeners
in
IWEM.

Table
2.
TEFs
Used
for
Dioxin
and
Furan
Congeners
Constituent
Name
CASRN
CSFo
(
mkd)­
1
CSFo
Source
URF
(:
g/
m3)­
1
URF
Source
CSFi
(
mkd)­
1
CSFi
Source
TEF
Dioxins
Pentachlorodibenzo­
p­
dioxin,
1,2,3,7,8­
40321­
76­
4
1.5E+
05
WHO
1998
3.3E+
01
WHO
1998
1.5E+
05
WHO
1998
1
Tetrachlorodibenzo­
p­
dioxin,
2,3,7,8­
1746­
01­
6
1.5E+
5
EPA,
1997
3.3E+
1
EPA,
1997
1.5E+
5
EPA,
1997
1
Hexachlorodibenzo­
p­
dioxin,
1,2,3,4,7,8­
70648­
26­
9
1.5E+
4
WHO
1998
3.3E+
0
WHO
1998
1.5E+
4
WHO
1998
0.1
Furans
Hexachlorodibenzofuran,
1,2,3,4,7,8­
70648­
26­
9
1.5E+
4
WHO
1998
3.3E+
0
WHO
1998
1.5E+
4
WHO
1998
0.1
Pentachlorodibenzofuran,
2,3,4,7,8­
57117­
31­
4
7.5E+
4
WHO
1998
1.7E+
1
WHO
1998
7.5E+
4
WHO
1998
0.5
Tetrachlorodibenzofuran,
2,3,7,8­
51207­
31­
9
1.5E+
4
WHO
1998
3.3E+
0
WHO
1998
1.5E+
4
WHO
1998
0.1
WHO
98
=
Van
den
Berg
et
al.
(
1998)
EPA,
1997
=
HEAST
(
U.
S.
EPA,
1997).

The
human
health
benchmarks
calculated
using
the
TEFs
for
1,2,3,4,7,8­
hexachlorodibenzo­
p­
dioxin
and
1,2,3,4,7,8­
hexachlorodibenzofuran
were
surrogates
for
hexachlorodibenzo­
p­
dioxins
(
HxCDDs)
and
hexachlorodibenzofurans
(
HxCDFs),
respectively.
The
human
health
benchmarks
for
1,2,3,7,8­
pentachlorodibenzo­
p­
dioxin
and
2,3,4,7,8­
pentachlorodibenzofuran
were
used
to
represent
pentachlorodibenzodioxins
(
PeCDDs)
and
pentachlorodibenzofurans
(
PeCDFs),
respectively.
The
human
health
benchmarks
for
2,3,7,8­
tetrachlorodibenzo­
p­
dioxin
(
2,3,7,8­
TCDD)
and
2,3,7,8­
tetrachlorodibenzofuran
were
used
to
represent
tetrachlorodibenzo­
p­
dioxins
(
TCDDs)
and
tetrachlorodibenzofurans
(
TCDFs),
Page
16
of
23
respectively.
When
TEFs
varied
within
a
class
of
dioxin­
like
compounds
(
i.
e.,
pentachlorodibenzofurans),
the
TEF
most
protective
of
human
health
was
used.

2.5
Superfund
Technical
Support
Center
Provisional
Benchmarks
Table
3
list
the
provisional
human
health
benchmarks
from
the
Superfund
Technical
Support
Center
that
were
used
for
some
IWEM
constituents.
A
provisional
subchronic
RfC
of
2.0E­
2
mg/
m3
was
developed
by
the
Superfund
Technical
Support
Center
(
U.
S.
EPA,
1999a)
for
carbon
tetrachloride;
a
provisional
chronic
RfC
of
7.0E­
3
mg/
m3
was
derived
from
this
value
by
applying
an
uncertainty
factor
of
3
to
account
for
the
use
of
a
subchronic
study.

Table
3.
Provisional
Human
Health
Benchmarks
Developed
by
the
Superfund
Technical
Support
Center
CASRN
Chemical
Name
Benchmark
Type
Benchmark
Value
Units
Reference
108­
90­
7
Chlorobenzene
RfC
6.0E­
02
mg/
m3
U.
S.
EPA,
1998a
7440­
48­
4
Cobalt
(
and
compounds)
RfD
2.0E­
02
mg/
kg­
d
U.
S.
EPA,
2001b
100­
41­
4
Ethylbenzene
URF
1.1E­
06
(:
g/
m3)­
1
U.
S.
EPA,
1999b
87­
68­
3
Hexachlorobutadiene
RfD
3.0E­
04
mg/
kg­
d
U.
S.
EPA,
1998b
110­
54­
3
Hexane,
n­
RfD
1.1E+
01
mg/
kg­
d
U.
S.
EPA,
1999c
62­
75­
9
N­
Nitrosodimethylamine
(
N­
methyl­
N­
nitrosomethanamine
RfD
8.0E­
06
mg/
kg­
d
U.
S.
EPA,
2001c
86­
30­
6
N­
Nitrosodiphenylamine
RfD
2.0E­
02
mg/
kg­
d
U.
S.
EPA,
2001d
79­
34­
5
Tetrachloroethane,
1,1,2,2­
RfD
6.0E­
02
mg/
kg­
d
U.
S.
EPA,
2000
71­
55­
6
Trichloroethane,
1,1,1­
RfD
2.8E­
01
mg/
kg­
d
U.
S.
EPA,
1999d
71­
55­
6
Trichloroethane,
1,1,1­
RfC
2.2E+
00
mg/
m3
U.
S.
EPA,
1999e
96­
18­
4
Trichloropropane,
1,2,3­
RfC
5.0E­
03
mg/
m3
U.
S.
EPA,
1999f
2.6
Benchmarks
From
Other
EPA
Sources
For
some
IWEM
constituents,
human
health
benchmarks
were
not
available
from
IRIS,
the
Superfund
Technical
Support
Center,
HEAST,
ATSDR,
or
CalEPA,
but
were
available
from
other
EPA
sources:

#
The
provisional
oral
CSF
of
5.2E­
2
per
mg/
kg­
d,
provisional
inhalation
URF
of
5.8E­
7
per
:
g/
m3,
and
the
provisional
inhalation
CSF
of
2.0E­
3
per
mg/
kg­
d
developed
for
tetrachloroethylene
by
EPA
in
a
Health
Assessment
Document
(
HAD)
(
U.
S.
EPA,
1986a)
were
used.
Page
17
of
23
#
For
trichloroethylene,
provisional
cancer
benchmarks
developed
by
EPA
in
a
HAD
(
U.
S.
EPA,
1987)
were
used
and
include
the
oral
CSF
of
1.1E­
2
per
mg/
kgd
inhalation
URF
of
1.7E­
6
per
:
g/
m3,
and
inhalation
CSF
of
6.0E­
3
per
mg/
kg­
d.

#
A
provisional
RfD
of
1.7E­
5
mg/
kg­
d
and
a
provisional
RfC
of
2.0E­
5
mg/
m3
were
derived
for
cyclohexanol
in
the
final
listing
rule
for
solvents
(
63
FR
64371)
and
were
used
(
U.
S.
EPA,
1998c).

#
An
acceptable
daily
intake
(
ADI)
of
2.0E­
03
mg/
kg­
d
from
inhalation
(
7.0E­
3
mg/
m3)
was
identified
for
pyridine
(
U.
S.
EPA,
1986b).

#
EPA
calculated
an
oral
cancer
potency
factor
of
293
per
mg/
kg­
d
for
ethyl
methanesulfonate
in
a
reportable
quantity
adjustment
evaluation
(
U.
S.
EPA,
1998d).

#
EPA
calculated
an
oral
cancer
potency
factor
of
0.18
per
mg/
kg­
d
for
safrole
in
a
reportable
quantity
adjustment
evaluation
(
U.
S.
EPA,
1998e).

#
EPA
calculated
an
oral
cancer
potency
factor
of
9.8
per
mg/
kg­
d
for
tris(
2,3­
dibromopropyl)
phosphate
in
a
reportable
quantity
adjustment
evaluation
(
U.
S.
EPA,
1998f).

#
The
cancer
slope
factor
for
dibenzo(
a,
h)
anthracene
was
calculated
by
using
the
TEF
approach
and
a
TEF
of
1
(
U.
S.
EPA,
1993).
The
oral
CSF
for
dibenzo(
a,
h)
anthracene
was
therefore
the
same
as
the
IRIS
(
U.
S.
EPA,
2001a)
value
for
benzo(
a)
pyrene:
7.3.
E+
00
(
mg/
kg­
d)­
1.

2.7
Air
Characteristic
Study
Provisional
Benchmarks
Provisional
inhalation
health
benchmarks
were
developed
in
the
Air
Characteristic
Study
(
U.
S.
EPA,
1999g)
for
several
constituents
lacking
IRIS,
HEAST,
alternative
EPA,
or
ATSDR
values.
For
2­
chlorophenol,
a
provisional
RfC
was
developed
using
route­
to­
route
extrapolation
of
the
oral
RfD.
Using
route­
to­
route
extrapolations
based
on
oral
CSFs
from
IRIS
and
HEAST,
the
Air
Characteristic
Study
developed
provisional
inhalation
URFs
and
inhalation
CSFs
for
bromodichloromethane,
chlorodibromomethane,
and
o­
Toluidine.

These
provisional
inhalation
benchmark
values
are
summarized
in
Table
4
below.
Additional
details
on
the
derivation
of
these
inhalation
benchmarks
can
be
found
in
the
Revised
Risk
Assessment
for
the
Air
Characteristic
Study
(
U.
S.
EPA,
1999g).
Page
18
of
23
Table
4.
Provisional
Inhalation
Benchmarks
Developed
in
the
Air
Characteristic
Study
CASRN
Chemical
Name
RfC
(
mg/
m3)
RfC
Target
Effect
URF
(:
g/
m3)­
1
CSFi
(
mg/
kg­
d)­
1
75­
27­
4
Bromodichloromethane
(
dichlorobromomethane)
1.8E­
05
6.2E­
02
124­
48­
1
Chlorodibromomethane
(
dibromochloromethane)
2.4E­
05
8.4E­
02
95­
57­
8
2­
Chlorophenol
(
o­)
1.4E­
03
Reproductive,
developmental
95­
53­
4
o­
Toluidine
(
2­
methylaniline)
6.9E­
05
2.4E­
01
2.8
Surrogate
Health
Benchmarks
For
several
IWEM
constituents,
IRIS
benchmarks
for
similar
chemicals
were
used
as
surrogate
data.
The
rationale
for
these
recommendations
is
as
follows:

#
cis­
1,3­
Dichloropropylene
and
trans­
1,3­
dichloropropylene
were
based
on
1,3­
dichloropropene.
The
studies
cited
in
the
IRIS
file
for
1,3­
dichloropropene
used
a
technical­
grade
chemical
that
contained
about
a
50/
50
mixture
of
the
cis­
and
trans­
isomers.
The
RfD
is
3E­
02
mg/
kg­
d
and
the
RfC
is
2E­
02
mg/
m3.
The
oral
CSF
for
1,3­
dichloropropene
is
0.1
(
mg/
kg­
d)­
1
and
the
inhalation
URF
is
4E­
06
(
µ
g/
m3)­
1.

#
The
IRIS
oral
CSF
for
the
2,4­/
2,6­
dinitrotoluene
mixture
(
6.8E­
01
per
mg/
kg­
d)
was
used
as
the
oral
CSFs
for
2,4­
dinitrotoluene
and
2,6­
dinitrotoluene.

#
The
RfDs
for
o­
and
m­
cresol
(
both
5E­
02
mg/
kg/
d)
are
cited
on
IRIS.
The
provisional
RfD
for
p­
cresol
(
5E­
03
mg/
kg/
d)
is
from
HEAST.
Cresol
mixtures
contain
all
three
cresol
isomers.
Based
on
the
hierarchy
described
above
(
i.
e.,
IRIS
is
preferred
over
HEAST
because
IRIS
is
EPA's
official
repository
of
Agency­
wide
consensus
human
health
risk
information),
the
RfD
for
m­
cresol
(
5E­
02
mg/
kg­
d)
was
used
as
a
surrogate
for
cresol
mixtures.

#
Fluoride
was
based
on
fluorine.
The
IRIS
RfD
for
fluorine
(
6E­
02
mg/
kg­
d)
is
based
on
soluble
fluoride.

#
The
RfD
for
methyl
mercury
(
1E­
04
mg/
kg­
d)
was
used
as
a
surrogate
for
elemental
mercury.

#
The
RfD
for
Arochlor
1254
(
2E­
05
mg/
kg­
d)
was
used
as
a
surrogate
for
PCBs.
Page
19
of
23
#
Thallium
was
based
on
thallium
chloride.
There
are
several
thallium
salts
that
have
RfDs
in
IRIS.
The
lowest
value
among
the
thallium
salts
(
8E­
05
mg/
kg­
d)
is
routinely
used
to
represent
thallium
in
risk
assessments.

#
p­
Xylene
was
based
on
total
xylenes.
An
RfD
of
2
mg/
kg­
d
is
listed
for
total
xylenes,
m­
xylene,
and
o­
xylene
in
IRIS.
Total
xylenes
contain
a
mixture
of
all
three
isomers;
therefore,
the
RfD
likely
is
appropriate
for
p­
xylene.

2.9
Chloroform
EPA
has
classified
chloroform
as
a
Group
B2,
Probable
Human
Carcinogen,
based
on
an
increased
incidence
of
several
tumor
types
in
rats
and
mice
(
U.
S.
EPA,
2001a).
However,
based
on
an
evaluation
initiated
by
EPA's
Office
of
Water
(
OW),
the
Office
of
Solid
Waste
(
OSW)
now
believes
the
weight
of
evidence
for
the
carcinogenic
mode
of
action
for
chloroform
does
not
support
a
mutagenic
mode
of
action;
therefore,
a
nonlinear
low­
dose
extrapolation
is
more
appropriate
for
assessing
risk
from
exposure
to
chloroform.
EPA's
Science
Advisory
Board
(
SAB),
the
World
Health
Organization
(
WHO),
the
Society
of
Toxicology,
and
EPA
all
strongly
endorse
the
nonlinear
approach
for
assessing
risks
from
chloroform.

Although
OW
conducted
its
evaluation
of
chloroform
carcinogenicity
for
oral
exposure,
a
nonlinear
approach
for
low­
dose
extrapolation
would
apply
to
inhalation
exposure
to
chloroform
as
well,
because
chloroform's
mode
of
action
is
understood
to
be
the
same
for
both
ingestion
and
inhalation
exposures.
Specifically,
tumorigenesis
for
both
ingestion
and
inhalation
exposures
is
induced
through
cytotoxicity
(
cell
death)
produced
by
the
oxidative
generation
of
highly
reactive
metabolites
(
phosgene
and
hydrochloric
acid),
followed
by
regenerative
cell
proliferation
(
U.
S.
EPA,
1998g).
Chloroform­
induced
liver
tumors
in
mice
have
only
been
seen
after
bolus
corn
oil
dosing
and
have
not
been
observed
following
administration
by
other
routes
(
i.
e.,
drinking
water
and
inhalation).
As
explained
in
EPA
OW's
March
31,
1998,
and
December
16,
1998,
Federal
Register
notices
pertaining
to
chloroform
(
U.
S.
EPA,
1998g
and
1998h,
respectively),
EPA
now
believes
that
"
based
on
the
current
evidence
for
the
mode
of
action
by
which
chloroform
may
cause
tumorigenesis,
...
a
nonlinear
approach
is
more
appropriate
for
extrapolating
low­
dose
cancer
risk
rather
than
the
low­
dose
linear
approach..."(
U.
S.
EPA,
1998g).
OW
determined
that,
given
chloroform's
mode
of
carcinogenic
action,
liver
toxicity
(
a
noncancer
health
effect)
actually
"
is
a
more
sensitive
effect
of
chloroform
than
the
induction
of
tumors"
and
that
protecting
against
liver
toxicity
"
should
be
protective
against
carcinogenicity
given
that
the
putative
mode
of
action
understanding
for
chloroform
involves
cytotoxicity
as
a
key
event
preceding
tumor
development"
(
U.
S.
EPA,
1998g).

The
recent
evaluations
conducted
by
OW
concluded
that
protecting
against
chloroform's
noncancer
health
effects
protects
against
excess
cancer
risk.
EPA
now
believes
that
the
noncancer
health
effects
resulting
from
inhalation
of
chloroform
would
precede
the
development
of
cancer
and
would
occur
at
lower
doses
than
would
tumor
development.
Although
EPA
has
not
finalized
a
noncancer
health
benchmark
for
inhalation
exposure
(
i.
e.,
an
RfC),
ATSDR
has
developed
an
inhalation
MRL
for
chloroform.
Therefore,
ATSDR's
chronic
inhalation
MRL
for
chloroform
(
0.1
mg/
m3)
was
used
in
IWEM.
Page
20
of
23
3.0
References
ATSDR
(
Agency
for
Toxic
Substances
and
Disease
Registry).
2001.
Minimal
Risk
Levels
(
MRLs)
for
Hazardous
Substances.
http://
atsdr1.
atsdr.
cdc.
gov:
8080/
mrls.
html
CalEPA
(
California
Environmental
Protection
Agency).
1999a.
Air
Toxics
Hot
Spots
Program
Risk
Assessment
Guidelines:
Part
II.
Technical
Support
Document
for
Describing
Available
Cancer
Potency
Factors.
Office
of
Environmental
Health
Hazard
Assessment,
Berkeley,
CA.
Available
online
at
http://
www.
oehha.
org/
scientific/
hsca2.
htm.

CalEPA
(
California
Environmental
Protection
Agency).
1999b.
Air
Toxics
Hot
Spots
Program
Risk
Assessment
Guidelines:
Part
III.
Technical
Support
Document
for
the
Determination
of
Noncancer
Chronic
Reference
Exposure
Levels.
SRP
Draft.
Office
of
Environmental
Health
Hazard
Assessment,
Berkeley,
CA.
Available
online
at
http://
www.
oehha.
org/
hotspots/
RAGSII.
html.

CalEPA
(
California
Environmental
Protection
Agency).
2000.
Air
Toxics
Hot
Spots
Program
Risk
Assessment
Guidelines:
Part
III.
Technical
Support
Document
for
the
Determination
of
Noncancer
Chronic
Reference
Exposure
Levels.
Office
of
Environmental
Health
Hazard
Assessment,
Berkeley,
CA.
Available
online
(
in
3
sections)
at
http://
www.
oehha.
org/
air/
chronic_
rels/
22RELS2k.
html,
http://
www.
oehha.
org/
air/
chronic_
rels/
42kChREL.
html,
http://
www.
oehha.
org/
air/
chronic_
rels/
Jan2001ChREL.
html.

U.
S.
EPA
(
Environmental
Protection
Agency).
1986a.
Addendum
to
the
Health
Assessment
Document
for
Tetrachloroethylene
(
Perchloroethylene).
Updated
Carcinogenicity
Assessment
for
Tetrachloroethylene
(
Perchloroethylene,
PERC,
PCE).
External
Review
Draft.
EPA/
600/
8­
82­
005FA.
Office
of
Health
and
Environmental
Assessment,
Office
of
Research
and
Development,
Washington
DC.

U.
S.
EPA
(
Environmental
Protection
Agency).
1986b.
Health
and
Environmental
Effects
Profile
for
Pyridine.
EPA/
600/
x­
86­
168.
Environmental
Criteria
and
Assessment
Office,
Office
of
Research
and
Development,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1987.
Addendum
to
the
Health
Assessment
Document
for
Trichloroethylene.
Updated
Carcinogenicity
Assessment
for
Trichloroethylene.
External
Review
Draft.
EPA/
600/
8­
82­
006FA.
Office
of
Health
and
Environmental
Assessment,
Office
of
Research
and
Development,
Washington
DC.

U.
S.
EPA
(
Environmental
Protection
Agency).
1993.
Provisional
Guidance
for
Quantitative
Risk
Assessment
of
Polycyclic
Aromatic
Hydrocarbons.
Office
of
Health
and
Environmental
Assessment,
Environmental
Criteria
and
Assessment
Office,
Cincinnati,
OH.
EPA/
600/
R­
93­
089.
Page
21
of
23
U.
S.
EPoviA
(
Environmental
Protection
Agency).
1994.
Methods
for
Derivation
of
Inhalation
Reference
Concentrations
and
Application
of
Inhalation
Dosimetry.
EPA/
600/
8­
90­
066F.
Environmental
Criteria
and
Assessment
Office,
Office
of
Health
and
Environmental
Assessment,
Office
of
Research
and
Development,
Research
Triangle
Park,
NC.

U.
S.
EPA
(
Environmental
Protection
Agency).
1997.
Health
Effects
Assessment
Summary
Tables
(
HEAST).
EPA­
540­
R­
97­
036.
FY
1997
Update.
Office
of
Solid
Waste
and
Emergency
Response,
Washington,
DC.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998a.
Risk
Assessment
Issue
Paper
for:
Derivation
of
a
Provisional
Chronic
RfC
for
Chlorobenzene
(
CASRN
108­
90­
7).
98­
020/
09­
18­
98.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998b.
Risk
Assessment
Paper
for:
Evaluation
of
the
Systemic
Toxicity
of
Hexachlorobutadiene
(
CASRN
87­
68­
3)
Resulting
from
Oral
Exposure.
98­
009/
07­
17­
98.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998c.
Hazardous
waste
management
system;
identification
and
listing
of
hazardous
waste;
solvents;
final
rule.
Federal
Register
63
FR
64371­
402.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998d.
Evaluation
of
the
Potential
Carcinogenicity
of
Ethyl
Methanesulfonate
(
62­
50­
0)
in
Support
of
Reportable
Quantity
Adjustments
Pursuant
to
CERLCA
Section
102.
Prepared
by
Carcinogen
Assessment
Group,
Office
of
Health
and
Environmental
Assessment,
Washington,
D.
C.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998e.
Evaluation
of
the
Potential
Carcinogenicity
of
Safrole
(
94­
59­
7)
in
Support
of
Reportable
Quantity
Adjustments
Pursuant
to
CERLCA
Section
102.
Prepared
by
Carcinogen
Assessment
Group,
Office
of
Health
and
Environmental
Assessment,
Washington,
D.
C.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998f.
Evaluation
of
the
Potential
Carcinogenicity
of
Tris(
2,3­
dibromopropyl)
phosphate
(
126­
72­
7)
in
Support
of
Reportable
Quantity
Adjustments
Pursuant
to
CERLCA
Section
102.
Prepared
by
Carcinogen
Assessment
Group,
Office
of
Health
and
Environmental
Assessment,
Washington,
D.
C.

U.
S.
EPA
(
Environmental
Protection
Agency).
1998g.
National
primary
drinking
water
regulations:
disinfectants
and
disinfection
byproducts
notice
of
data
availability;
Proposed
Rule.
Federal
Register
63
(
61):
15673­
15692.
March
31.
Page
22
of
23
U.
S.
EPA
(
Environmental
Protection
Agency).
1998h.
National
primary
drinking
water
regulations:
disinfectants
and
disinfection
byproducts;
final
rule.
Federal
Register
63
(
241):
69390­
69476.
December
16.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999a.
Risk
Assessment
Paper
for:
The
Derivation
of
a
Provisional
Subchronic
RfC
for
Carbon
Tetrachloride
(
CASRN
56­
23­
5).
98­
026/
6­
14­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999b.
Risk
Assessment
Issue
Paper
for:
Evaluating
the
Carcinogenicity
of
Ethylbenzene
(
CASRN
100­
41­
4).
99­
011/
10­
12­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999c.
Risk
Assessment
Paper
for:
An
Updated
Systemic
Toxicity
Evaluation
of
n­
Hexane
(
CASRN
110­
54­
3).
98­
019/
10­
1­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999d.
Risk
Assessment
Issue
Paper
for:
Derivation
of
Provisional
Oral
Chronic
RfD
and
Subchronic
RfDs
for
1,1,1­
Trichloroethane
(
CASRN
71­
55­
6).
98­
025/
8­
4­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999e.
Risk
Assessment
Issue
Paper
for:
Derivation
of
Provisional
Chronic
and
Subchronic
RfCs
for
1,1,1­
Trichloroethane
(
CASRN
71­
55­
6).
98­
025/
8­
4­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999f.
Risk
Assessment
Paper
for:
Derivation
of
the
Systemic
Toxicity
of
1,2,3­
Trichloropropane
(
CASRN
96­
18­
4).
98­
014/
8­
13­
99.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
1999g.
Revised
Risk
Assessment
for
the
Air
Characteristic
Study.
EPA­
530­
R­
99­
019a.
Volume
2.
Office
of
Solid
Waste,
Washington,
DC.

U.
S.
EPA
(
Environmental
Protection
Agency).
2000.
Risk
Assessment
Paper
for:
Derivation
of
a
Provisional
RfD
for
1,1,2,2­
Tetrachloroethane
(
CASRN
79­
34­
5).
00­
122/
12­
20­
00.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.
Page
23
of
23
U.
S.
EPA
(
Environmental
Protection
Agency).
2001a.
Integrated
Risk
Information
System
(
IRIS).
National
Center
for
Environmental
Assessment,
Office
of
Research
and
Development,
Washington,
DC.
Available
online
at
http://
www.
epa.
gov/
iris/

U.
S.
EPA
(
Environmental
Protection
Agency).
2001b.
Risk
Assessment
Paper
for:
Derivation
of
a
Provisional
RfD
for
Cobalt
and
Compounds
(
CASRN
7440­
48­
4).
00­
122/
3­
16­
01.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
2001c.
Risk
Assessment
Paper
for:
Derivation
of
a
Provisional
RfD
for
N­
Nitrosodimethylamine
(
CASRN
62­
75­
9).
00­
122/
3­
16­
01.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

U.
S.
EPA
(
Environmental
Protection
Agency).
2001d.
Risk
Assessment
Paper
for:
Derivation
of
a
Provisional
RfD
for
N­
Nitrosodiphenylamine
(
CASRN
86­
30­
6).
00­
122/
3­
16­
01.
National
Center
for
Environmental
Assessment.
Superfund
Technical
Support
Center,
Cincinnati,
OH.

Van
den
Berg,
M.,
L.
Birnbaum,
A.
T.
C.
Bosveld,
et
al.
1998.
Toxic
equivalency
factors
(
TEFs)
for
PCBs,
PCDDs,
PCDFs
for
humans
and
wildlife.
Environmental
Health
Perspectives
106:
775­
792.
This
page
intentionally
left
blank.
Appendix
B
Modifications
Made
to
WATER9
to
Calculate
Sludge
Concentrations
This
page
intentionally
left
blank.
Appendix
B
Modifications
Made
to
WATER9
to
Calculate
Sludge
Concentrations
B­
3
Appendix
B
Modifications
Made
to
WATER9
to
Calculate
Sludge
Concentrations
Several
modifications
to
the
WATER9
model
that
are
currently
under
review
were
used
in
the
Headworks
analysis;
the
model
with
these
modification
is
referred
to
as
WATER9b.
Most
of
these
revisions
deal
with
how
sorption
to
solids
is
modeled.
This
appendix
describes
briefly
the
modifications
to
WATER9
to
create
WATER9b.
In
addition,
Attachment
B.
1
is
the
WATER9
documentation
of
changes
to
solids
sorption
calculations
from
WATER8;
this
document
is
included
here
for
the
reader's
convenience.
This
attachment
has
been
updated
from
the
existing
WATER9
documentation
to
reflect
the
WATER9b
changes
and
model
validation
undertaken
for
the
Headworks
analysis,
but
is
otherwise
presented
as
is
from
the
WATER9
documentation.

The
primary
modification,
as
it
pertains
to
the
Headworks
analysis,
is
the
segregation
of
the
interstitial
fluid
from
the
solids
sorption
balance.
The
currently
released
version
of
WATER9
assumes
that
the
solid
matter
in
the
wastewater
treatment
system
contains
99
parts
water
to
1
part
solid
material.
This
assumption
was
made
to
account
for
contaminant
dissolved
in
the
interstitial
fluid
of
microorganism
present
in
the
wastewater.
The
"
solid­
to­
liquid"
phase
adsorption
coefficient
related
the
concentration
of
the
dissolved
liquid
phase
(
mass
per
volume)
to
the
total
mass
of
contaminant
in
the
cell
(
both
sorbed
and
dissolved
contaminant
inside
the
cell)
per
mass
of
solid
matter
(
on
a
dry
basis).
This
assumption
of
99
mass
percent
water
inherent
in
the
wastewater
solid
limited
the
utility
of
the
WATER9
model
to
predict
the
fate
of
contaminant
when
inert
solid
material
(
rather
than
biomass)
is
present
or
when
sludge
dewatering
is
performed
on
the
biosolids,
reducing
the
water
content
of
the
solids
stream
to
below
99
percent.

In
both
WATER9
and
WATER9b
versions,
solid­
liquid
partitioning
is
based
on
the
following
equation
from
Matter­
Muller:

(
)
ksl
Kow
=
×
 
10
0
67
2
61
.
log
.

where
ksl
=
the
partitioning
of
the
compound
into
biomass
solids
(
g/
Kg
biomass
per
g/
m3)
Kow
=
octanol­
water
partition
coefficient
(
unitless)
Appendix
B
Modifications
Made
to
WATER9
to
Calculate
Sludge
Concentrations
B­
4
WATER9b
uses
this
equation
directly
to
calculate
the
concentration
of
contaminant
sorbed
onto
the
solids
on
a
dry
basis.
WATER9
had
modified
the
Matter­
Muller
equation
by
adding
a
0.099
to
ksl,
as
defined
above,
so
that
the
partition
coefficient
specifically
includes
that
mass
of
contaminant
in
the
interstitial
fluid.
That
is,
WATER9
considered
the
mass
sorbed
as
being
the
sorbed
contaminant
plus
the
dissolved
contaminant
in
the
cell
per
dry
weight
of
cell.
This
term
has
been
dropped
in
WATER9b
along
with
ancillary
equations
to
account
for
the
mass
sorbed
being
the
mass
sorbed
the
dry
matter
only
(
with
no
correction
for
interstitial
water).
These
modifications
to
WATER9
are
currently
being
peer­
reviewed,
and
it
is
anticipated
that
the
WATER9
modifications
used
in
the
Headworks
analysis
will
be
publically
available
in
the
next
release
of
the
WATER9
model.
Attachment
B­
1
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
This
page
intentionally
left
blank.
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
1
of
27
May
6,
2002
Technical
Note
SUBJECT:
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments.
FROM:
C.
Allen,
RTI
TO:
J.
Baskir,
RTI
Purpose
This
is
a
memorandum
describing
the
modeling
of
the
fate
of
a
compound
in
impoundment
units
and
in
tank
units
for
the
programs
WATER8
and
WATER9.
The
scope
of
the
memorandum
includes
differences
between
WATER8
and
WATER9
in
equations
that
are
used
for
fate
modeling,
and
verification
of
the
identical
predictions
of
compound
fate
for
both
WATER8
and
WATER9.

This
memorandum
is
organized
in
the
following
sections:

Purpose
Summary
of
relevant
changes
to
modeling
approach
from
WATER8
to
WATER9
Summary
of
verification
of
WATER9
for
cases
relevant
to
the
headworks
project
a.
WATER8/
WATER9
comparison
for
non­
sorption
components
(
i.
e.
showing
similarities
of
WATER8
and
WATER9)
b.
WATER9
comparison
to
hand
calculations
c.
WATER8
to
WATER9
comparison
for
sorption
components
(
i.
e.
showing
differences
between
WATER8
and
WATER9)
 
Chemdat8
nonaerated
impoundment
 
Chemdat8
disposal
impoundment
d.
Material
balance
(
internal
check
of
model)
Documentation
of
details
WATER9
sorption
routines
Partitioning
of
the
compound
at
a
unit.
Equation
for
partitioning
in
oil
Example
calculation
of
fraction
in
oil
for
benzene
Equation
for
partitioning
in
solids
Equation
for
overall
partitioning
among
the
four
phases
Example
calculation
of
fraction
in
solids
for
benzene
Documentation
of
details
of
WATER8/
WATER9
comparisons
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
2
of
27
Documentation
of
details
of
WATER9/
Hand
calculations
comparisons
Subroutine
providing
the
details
of
the
calculations
used
by
WATER9
for
the
tank
unit
Subroutine
providing
the
details
of
the
calculations
used
by
WATER9
for
the
impoundment
or
the
lagoon
unit
Case
1:
Detailed
Model
Results
Case
2:
Detailed
Model
Results
Case
3:
Detailed
Model
Results
Summary
of
relevant
changes
to
modeling
approach
from
WATER8
to
WATER9
This
is
primarily
a
summary
of
the
information
that
is
discussed
in
detail
in
the
sorption
equations
documentation,
plus
other
changes
relevant
to
the
headworks
project.

In
the
tank
unit
of
WATER9,
the
following
feature
was
added,
relative
to
WATER8.
The
storage
tank
model,
as
an
option,
can
be
modeled
as
a
closed
constant
level
tank
if
the
depth
of
the
tank
is
set
to
zero.
The
quantity
of
waste
processed
in
the
tank
is
then
defined
from
the
flow
rate
on
the
inlet
waste
stream.
This
option
would
eliminate
the
working
loss
from
a
closed
tank,
but
would
not
eliminate
the
breathing
losses.

In
WATER8
the
sorption
of
the
compounds
on
biomass,
solids,
oils,
and
other
material
is
calculated
external
to
WATER8.
The
bulk
concentration
of
the
wastewater
in
the
unit
is
calculated,
and
hand
calculations
or
computer
programs
are
used
to
estimate
the
partitioning
in
the
different
phases.
In
WATER9,
the
concentration
of
biomass,
solids,
oils,
and
water
is
tracked
throughout
the
system.
The
biomass
is
generated
in
some
of
the
biologically
active
units,
and
the
solids
and
oils
are
added
with
the
waste
to
the
system.
The
partitioning
of
the
components
in
these
four
phases
is
automatically
calculated
by
WATER9,
unlike
WATER8.

Additional
optional
features
of
WATER9
that
are
not
present
in
WATER8
include
the
following:
°
Adjustment
of
Henry's
law
constant
due
to
partitioning
on
solids
or
oils,
°
Equilibrium
hydrolysis
due
to
pH
sensitive
ionization,
and
°
Selective
removal
of
oils
or
solids
from
a
unit.

Summary
of
verification
of
WATER9
for
cases
relevant
to
the
headworks
project
a.
WATER8/
WATER9
comparison
for
non­
sorption
components
(
i.
e.
showing
similarities
of
WATER8
and
WATER9)
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
3
of
27
Surface
Impoundment
or
Lagoon
Unit
Case
1
SURFIMP.
CDW,
a
WATER8
distribution
file
Modification(
s)
Specified
time
for
emissions,
0.1
months
Results
WATER8
WATER9
Fraction
volatilized
0.1444
0.1444
Fraction
biodegraded
0.8528
0.8528
Fraction
remaining
0.0028
0.00278
Storage
Tank
Open
Case
2
TANKB.
CDW,
a
WATER8
distribution
file
Modification(
s)
Contents
Mwt,
18
(
aqueous
waste)

Results
WATER8
WATER9
Fraction
volatilized
0.5549
0.5549
Fraction
biodegraded
0.0
0.0
Fraction
remaining
0.4451
0.4451
Storage
Tank
Closed
Case
3
TANKB.
CDW,
a
WATER8
distribution
file
Modification(
s)
Contents
Mwt,
18
(
aqueous
waste)
Closed
tank
Results
WATER8
WATER9
Breathing
fraction
0.1486
0.1486
Working
fraction
0.1663
0.1663
Fraction
biodegraded
0.0
0.0
Fraction
remaining
0.7098
0.7098
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
4
of
27
b.
WATER9
comparison
to
hand
calculations
The
hand
calculations
are
equivalent
to
the
computer
calculations
of
WATER8
and
WATER9
for
Case
1,
Case
2,
and
Case
3
that
are
presented
in
the
preceding
sections.
WATER9
provides
a
printout
of
the
details
of
the
site­
specific
calculations
for
each
compound
in
each
unit.
This
report
is
important
and
should
be
used
for
site
specific
verification
of
the
WATER9
calculations
for
important
projects.
This
report
does
not
always
provide
full
details
for
some
of
the
intermediate
calculations.
The
reports
for
Case
1
and
Case
2
are
edited
to
provide
additional
details
of
the
intermediate
calculations.

See
the
section
below
Documentation
of
details
of
WATER9/
Hand
calculations
comparisons
for
the
following
information:

The
annotated
source
code
with
inputs,
units
of
inputs,
and
actual
equations
and
logic
used
by
WATER9
for
calculations.
°
A
detailed
printout
of
the
calculations
used
for
the
WATER9
projects:
Case
1,
Case
2,
and
Case
3.
°
Additional
comments
and
equations
to
provide
additional
hand
calculation
details
not
automatically
provided
by
WATER9
for
Case
1
and
Case
3.

c.
WATER8
to
WATER9
comparison
for
sorption
components
(
i.
e.
showing
differences
between
WATER8
and
WATER9)

Using
the
surface
impoundment
model
Case
4,
from
the
file
headworks
project
2,
the
overall
concentration
of
benzene
exiting
the
impoundment
was
0.96977
g/
M3.

Surface
Impoundment
Case
4:
headworks
project
2,
a
WATER9
project
file
Type
of
unit
Impoundment
aqueous
waste
with
1%
solids
Results
Hand
calculation
WATER9b
Fraction
effluent
benzene
in
solids
0.406
0.4036
Fraction
effluent
benzene
in
water
0.594
0.5963
Concentration
in
water
phase
0.5663
0.5663
The
fraction
of
benzene
in
the
water
is
1­
fsolids,
or
1­
0.4061
=
0.5939.
The
concentration
of
the
benzene
in
the
aqueous
phase
is
the
total
concentration,
0.9535
g/
M3
times
the
overall
waste
flow
rate
0.030
M3/
s
times
the
fraction
of
benzene
in
the
aqueous
phase,
0.5939,
divided
by
the
flow
of
water,
0.0297
M3/
s,
or
0.572
ppmw.
The
concentration
of
the
benzene
in
the
aqueous
phase
based
upon
the
total
flow
(
aqueous+
solids)
is
the
total
concentration
in
the
combined
phase,
0.9535
g/
M3
times
the
fraction
of
benzene
in
the
aqueous
phase,
0.5939,
or
0.5663
ppmw.
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
5
of
27
WATER8
does
not
estimate
the
partitioning
of
the
benzene
in
the
surface
impoundment.
The
hand
calculation
methodology
presented
here
could
be
used
with
the
WATER8
exit
concentrations.

Hand
calculations
of
the
above
are
presented
in
the
section
Example
calculation
of
fraction
in
solids
for
benzene
The
WATER9
results
are
presented
for
Case
4
in
the
section
Documentation
of
details
of
WATER8/
WATER9
comparisons
 
Chemdat8
nonaerated
impoundment
In
Chemdat8
the
non­
aerated
impoundment
model
provided
an
estimate
of
sorption
on
biomass
generated
in
the
unit.
For
sorption
considered
in
Case
1
modified
as
a
flow
through
impoundment,
WATER9
provides
partitioning
of
benzene
consistent
with
Chemdat8
and
the
nonaerated
impoundment.

Flow
through
Impoundment
Case
1b:
Case
1
modified
as
a
WATER9
project
file
Surfimp
Type
of
unit
Flow
through
impoundment
aqueous
waste
with
1000
ppm
dissolved
solids
Results
Chemdat8
WATER9b
Fraction
volatilized
0.121
0.1205
Fraction
biologically
removed
0.733
0.7305
Fraction
sorbed
0.000838
0.00464
Fraction
remaining
0.145
0.149
One
difference
in
the
above
output
is
that
Chemdat8
separates
the
fraction
remaining
in
the
water
from
the
sorbed
fraction,
and
WATER9
includes
the
sorbed
fraction
in
the
reported
remaining
amount.

 
Chemdat8
disposal
impoundment
In
Chemdat8
the
disposal
impoundment
model
provides
an
estimate
of
sorption
on
biomass
generated
in
the
unit.
For
sorption
considered
in
Case
1
modified
as
a
disposal
impoundment,
WATER9
provides
partitioning
of
benzene
similar
to
Chemdat8
with
the
disposal
impoundment.
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
6
of
27
Disposal
Impoundment
Case
1b:
Case
1
modified
as
a
WATER9
project
file
Surfimp
Type
of
unit
Disposal
impoundment
aqueous
waste
with
1000
ppm
dissolved
solids.

Results
Chemdat8
WATER9
Fraction
volatilized
0.139
0.1383
Fraction
biologically
removed
0.848
0.8482
Fraction
sorbed
0.011
0.0533
Fraction
remaining
0.003
0.00822
WATER9
and
WATER8
use
a
very
different
calculation
algorithm
for
solving
for
the
exit
concentration.
The
Chemdat8
procedure
is
a
direct
calculation
with
an
approximation
equation,
and
WATER8/
WATER9
use
an
iterative
numerical
procedure.

d.
Material
balance
(
internal
check
of
model)

The
following
report
provides
a
material
balance
on
the
units
in
the
project
file
headworks
project
2.
There
was
no
error
reported
for
the
system.

UNIT
MATERIAL
BALANCE
04­
01­
2002
BENZENE
Part
1
Balance
by
unit
No.
in
out
air,
remove
sum
(
g/
s)
(
g/
s)
(
g/
s)
(
g/
s)

1
air:
0.
E+
00
0.
E+
00
0.
E+
00
water
0.
E+
00
0.
E+
00
0.
E+
00
0.
E+
00
2
air:
0.
E+
00
0.
E+
00
2.47
E­
04
water
3.
E­
02
2.98
E­
02
0.
E+
00
0.
E+
00
3
air:
0.
E+
00
0.
E+
00
0.
E+
00
water
1.67
E­
02
1.67
E­
02
0.
E+
00
0.
E+
00
4
air:
0.
E+
00
0.
E+
00
1.32
E­
04
water
3.
E­
02
2.91
E­
02
7.75
E­
04
­
1.46
E­
09
5
air:
0.
E+
00
0.
E+
00
0.
E+
00
water
1.67
E­
02
1.67
E­
02
0.
E+
00
0.
E+
00
6
air:
0.
E+
00
0.
E+
00
0.
E+
00
water
2.91
E­
02
2.91
E­
02
0.
E+
00
0.
E+
00
7
air:
0.
E+
00
0.
E+
00
0.
E+
00
water
1.3
E­
02
1.3
E­
02
0.
E+
00
0.
E+
00
________
TOTAL
AIR
3.79
E­
04
TOTAL
REMOVAL
7.75
E­
04
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
7
of
27
Part
2
Overall
balance
No.
waste
in
air
remove
flow
out
(
g/
s)
(
g/
s)
(
g/
s)
(
g/
s)

Loss
from
open
unit
surface
.00025
g/
s.
2:
34
3.
E­
02
2.47
E­
04
0.
E+
00
0.
E+
00
3:
49
0.
E+
00
0.
E+
00
0.
E+
00
0.
E+
00
Loss
from
open
unit
surface
.00013
g/
s.
4:
36
3.
E­
02
1.32
E­
04
7.75
E­
04
0.
E+
00
5:
14
0.
E+
00
0.
E+
00
0.
E+
00
1.67
E­
02
6:
14
0.
E+
00
0.
E+
00
0.
E+
00
2.91
E­
02
7:
14
0.
E+
00
0.
E+
00
0.
E+
00
1.3
E­
02
________
TOTALS
3.79
E­
04
7.75
E­
04
Total
inlet
loading
of
compound
from
waste
6.
E­
02
g/
s.
Fraction
lost
to
the
air
.006324
Error
in
overall
material
balance
­
5.1805e­
09
g/
s
Fraction
error
in
overall
material
balance
.

Documentation
of
details
WATER9
sorption
routines
Partitioning
of
the
compound
at
a
unit.
The
compound
is
partitioned
into
the
following
four
phases
in
each
unit:
°
Aqueous
phase
°
Oil
phase
°
Solids
phase
°
Biomass
solids
phase
Initially
the
loading
of
each
of
these
phases
is
defined
by
the
composition
of
the
waste
stream,
with
the
exception
of
the
biomass
solids.
The
biomass
solids
exiting
a
unit
is
defined
by
the
material
balance
in
the
unit
for
the
creation
of
biomass
within
the
unit.
The
rate
of
generation
of
biomass
is
one
half
the
product
of
the
biomass
solids
concentrations,
the
overall
biorate,
and
the
amount
of
dissolved
solids.

The
sorption
of
components
on
solids
in
WATER9
is
currently
the
same
for
solids
and
biomass
solids.
The
organic
fraction
and
the
sorption
characteristics
of
solids
are
not
defined
in
WATER9.
If
you
have
special
sorption
characteristics
of
the
solids,
adjust
your
specifications
of
the
concentrations
of
the
solids
concentration
in
the
waste
as
biomass
equivalent
solids.

Equation
for
partitioning
in
oil
The
partitioning
into
the
oil
is
assumed
to
be
defined
by
the
octanol­
water
partition
coefficient.

owr
=
owpc
*
oilfract
/
(
1
­
oilfract)
where:
owr
=
the
oil
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water;
owpc
=
the
octanol­
water
partition
coefficient,
the
ratio
of
the
concentration
in
the
oil
to
the
concentration
in
the
water;
and
oilfract=
the
fraction
of
oil
present
in
the
wastewater.
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
8
of
27
Example
calculation
of
fraction
in
oil
for
benzene
It
is
assumed
for
this
calculation
that
only
water
and
oil
are
present
with
a
trace
amount
of
benzene,
with
9
parts
oil
to
1
part
water.

The
benzene
octanol
water
partition
coefficient
(
owpc)
is
141.
oilfract
=
0.9.
owr
(
g
in
oil
/
g
in
water)=
owpc
*
oilfract
/
(
1
­
oilfract)
owr
(
g
in
oil
/
g
in
water)=
141
*
0.9
/
(
1
­
0.9)
owr
(
g
in
oil
/
g
in
water)=
1269
frinoil
=
owr
/
(
1
+
owr)
'
frinoil
is
the
fraction
in
the
oil
phase
frinoil
=
0.99921
Equation
for
partitioning
in
solids
The
partitioning
into
the
biomass
and
solids
is
assumed
to
be
defined
by
the
octanol­
water
partition
coefficient.

ksl
=
10
^
(
0.67
*
low
­
2.61)

where:
ksl
=
the
partitioning
of
the
compound
into
biomass
solids,
(
g/
Kg
biomass
per
g/
m3);
and
low
=
the
logarithm
base
10
of
the
octanol­
water
partition
coefficient.
swr
=
ksl
*
(
solids
+
biomass)
/
water
where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water;
ksl
=
the
partitioning
of
the
compound
into
biomass
solids,
(
g/
Kg
biomass
per
g/
m3);
water
=
the
water
in
the
unit
(
L/
s);
solids
=
the
solids
in
the
unit
as
defined
by
the
waste
characteristics
(
g/
s),
assumed
to
have
the
same
sorptive
capacity
as
the
biomass;
and
biomass
=
the
biomass
in
the
unit
(
g/
s).

Equation
for
overall
partitioning
among
the
four
phases
The
partitioning
into
the
biomass
and
solids
is
assumed
to
be
defined
by
the
octanol­
water
partition
coefficient.

Fraction
in
water
=
1
/
(
1
+
owr
+
swr)

where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water;
and
owr
=
the
oil
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water.

Fraction
in
oil
=
owr
/
(
1
+
owr
+
swr)
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
9
of
27
where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water;
and
owr
=
the
oil
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water.

Fraction
in
solids
=
swr
/
(
1
+
owr
+
swr)
x
[
solids/(
biomass+
solids)]

where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water;
and
owr
=
the
oil
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water;
solids
=
the
solids
in
the
unit
as
defined
by
the
waste
characteristics
(
g/
s),
assumed
to
have
the
same
sorptive
capacity
as
the
biomass;
and
biomass
=
the
biomass
in
the
unit
(
g/
s).

Fraction
in
biomass
=
swr
/
(
1
+
owr
+
swr)
x
[
biomass/(
biomass+
solids)]

where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water;
and
owr
=
the
oil
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water;
solids
=
the
solids
in
the
unit
as
defined
by
the
waste
characteristics
(
g/
s),
assumed
to
have
the
same
sorptive
capacity
as
the
biomass;
and
biomass
=
the
biomass
in
the
unit
(
g/
s).

If
the
unit
is
an
API
separator
then
the
partitioning
into
the
oil
is
already
defined
by
the
unit
calculations;
however,
the
partitioning
into
the
solids
may
be
estimated
with
the
above
procedures.

In
the
case
of
a
lagoon
(
generally
without
forced
agitation
or
aeration)
the
solids
and
other
sorptive
material
can
settle
to
the
base
of
the
lagoon
and
will
not
be
available
for
biodegradation,
volatilization,
or
discharge
with
the
components
of
the
waste
that
remain
suspended
in
the
lagoon.
A
special
sorption
flag
is
available
to
simulate
this
condition.

Example
calculation
of
fraction
in
solids
for
benzene
This
example
is
from
the
project
file:
headworks
project
2.
Benzene
is
in
the
impoundment
water
with
a
concentration
of
0.96977
g/
M3
and
a
solids
concentration
of
10000
ppmw.
The
flow
rate
of
the
waste
stream
is
30
L/
s,
with
a
flow
of
water
of
29.7
L/
s
(
99%
water,
1%
solids).
The
solids
flow
rate
is
300
g/
s
for
this
example.

First
ksl,
a
partitioning
factor
is
estimated
from
the
correlation
used
by
WATER9
for
biomass
solids.

ksl
=
10
^
(
0.67
*
low
­
2.61)
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
10
of
27
where:
ksl
=
the
partitioning
of
the
compound
into
biomass
solids,
(
0.06769
g/
Kg
biomass
per
g/
m3);
and
low
=
the
logarithm
base
10
of
the
octanol­
water
partition
coefficient
of
benzene,
2.15.

swr
=
ksl
*
(
solids
+
biomass)
/
water
where:
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water
0.6837;
ksl
=
the
partitioning
of
the
compound
into
biomass
solids,
(
0.06769
g/
Kg
biomass
per
g/
m3);
water
=
the
water
in
the
unit
(
29.7
L/
s);
solids
=
the
solids
in
the
unit
as
defined
by
the
waste
characteristics
(
300
g/
s),
assumed
to
have
the
same
sorptive
capacity
as
the
biomass;
and
biomass
=
the
biomass
in
the
unit
(
0
g/
s).

To
estimate
the
fraction
of
benzene
sorbed
on
the
solids,
the
following
equation
is
used:

fsolids
=
swr
/
(
1
+
swr
+
owr)
*
solids
/
(
solids
+
sludge)

where:
fsolids
=
The
fraction
of
benzene
that
is
sorbed
on
the
solids
in
the
waste
stream,
0.4061.
swr
=
the
solids
to
water
ratio,
the
ratio
of
the
mass
in
the
solids
to
the
mass
in
the
water
0.6837;
owr
=
the
oil
to
water
ratio,
the
ratio
of
the
mass
in
the
oil
to
the
mass
in
the
water
0;
there
is
no
oil
phase
in
this
example.
solids
=
the
solids
in
the
unit
as
defined
by
the
waste
characteristics
(
300
g/
s),
assumed
to
have
the
same
sorptive
capacity
as
the
biomass;
and
sludge
=
the
biomass
flow
rate
in
the
waste
stream
(
0
g/
s).

The
fraction
of
benzene
in
the
water
is
1­
fsolids,
or
1­
0.4061
=
0.5939.
The
concentration
of
the
benzene
in
the
aqueous
phase
is
the
total
concentration,
0.9535
g/
M3
times
the
overall
waste
flow
rate
0.030
M3/
s
times
the
fraction
of
benzene
in
the
aqueous
phase,
0.5939,
divided
by
the
flow
of
water,
0.0297
M3/
s,
or
0.572
ppmw.
The
concentration
of
the
benzene
in
the
aqueous
phase
based
upon
the
total
flow
(
aqueous+
solids)
is
the
total
concentration
in
the
combined
phase,
0.9535
g/
M3
times
the
fraction
of
benzene
in
the
aqueous
phase,
0.5939,
or
0.5663
ppmw.

This
calculation
of
benzene
partitioning
may
be
compared
with
the
WATER9
results
presented
in
the
following
section.
The
last
line
in
the
following
section
provides
the
direct
comparison
to
the
hand
calculation
of
0.5663
ppmw
benzene
in
the
aqueous
phase.
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
11
of
27
Documentation
of
details
of
WATER8/
WATER9
comparisons
The
following
information
provides
detailed
information
about
the
estimation
of
benzene
sorption
onto
solids
in
a
surface
impoundment.
The
unit
calculations
for
the
lagoon
are
presented
first,
followed
by
WATER9
estimates
of
the
benzene
partitioning.

WASTEWATER
TREATMENT
UNIT
4
05­
07­
2002
File
Headworks
testrun
2:
BENZENE
Type
of
unit
is
lagoon
1
Description
of
unit
4
default
2
Wastewater
temperature
(
C)
25
3
Length
of
impoundment
(
m)
7.5
4
Depth
of
impoundment
(
m)
2
5
Width
of
impoundment
(
m)
7.5
6
active
biomass,
impoundment
(
g/
l)
0.05
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0
9
Overall
biorate
(
mg/
g
bio­
hr)
19
10
sorption
flag
for
solids
settling
=
1
0
COMPOUND
PROPERTIES
OF
BENZENE
at
25
deg.
C
Type
of
compound
A8
density
(
g/
cc)
0.874
molecular
weight
78.11
diffusion
coef.
water
(
cm2/
s)
1.02e­
05
diffusion
coef.
air
(
cm2/
s)
0.088
vapor
pressure
(
mm
Hg)
95.26
Henry's
law
constant
(
atm­
m3/
mol)
0.00555
y/
x=
308.34
Reference
for
Henry's
law:
Yaws
and
Yang,
1992
S
vapor
pressure
temp.
coefficients
6.905
1211.033
220.8
The
enthalpy
of
vaporization
90.614
cal/
cc.
zero
order
biorate
constant
(
mg/
g­
hr)
19.1
first
order
biorate
constant
(
l/
g­
hr)
1.4
octanol
water
partition
coefficient
2.15
solubility
ppmw
1796.573
UNIFAC
code
16:
00000000000
CAS
code
71­
43­
2
The
estimated
vapor
pressure
is
95.33174
mm
Hg.
DETAILED
CALCULATIONS
at
Unit
4
default
Type:
lagoon
COMPOUND:
BENZENE
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
12
of
27
The
oil
corrected
aqueous
HL
in
the
dropping
waste
stream
is
3.083e+
02
(
y/
x)
Closed
or
sealed
waste
drop
into
the
unit.__________
waste
1
testruns
Properties
of
BENZENE
at
25.
deg.
C
hl=
0.00555
atm­
m3/
mol
vp=
95.26
mmHg
k1=
0.
L/
g­
hr
dl=
1.02e­
05
cm2/
s
dv=
0.088
cm2/
s
The
residence
time
in
the
unit
is
1.0417
hr.
(
0.0434
days.)
The
fetch
to
depth
ratio
(
effective
width/
depth)
is
4.2325.
__
Sorption
partitioning
of
component_______
The
fraction
sorbed
on
solids
is
0..
solids
fraction
sorbed
0.
biomass
fraction
sorbed
0.
oil
fraction
sorbed
0.
kg
is
estimated
as
0.00838
m/
s.
Springer
correlation
does
not
apply,
use
Mackay
and
Yeun
(
1983).
The
friction
velocity
is
13.347cm/
s.
The
Schmidt
number
is
980.392.
kl
is
estimated
as
6.477e­
06
m/
s.
Waste
rate
in
the
unit
30.
(
L/
s)
0.6848
(
MGD)
concentration
into
the
unit
1.
(
mg/
L)
compound
rate
into
the
unit
0.03
(
g/
s)
0.2381
(
lb/
hr)
compound
rate
recovered
by
controls
0.
(
g/
s)
0.
(
lb/
hr)
fraction
recovered
by
controls
0.
KG
surface
(
m/
s)
0.00854
KL
surface
(
m/
s)
6.477e­
06
KL
OVERALL
SURFACE
(
m/
s)
6.455e­
06
TOTAL
FRACTION
VOLATILIZED
0.00685
FRACTION
BIOLOGICALLY
REMOVED
0.03965
FRACTION
SUBMERGED
VOLATILIZED
0.

FRACTION
ABSORBED
0.3872
TOTAL
AIR
EMISSIONS
(
g/
s)
0.00021
(
Mg/
year)
0.00648
EMISSION
FACTOR
(
g/
cm2­
s)
3.656e­
10
UNIT
EXIT
CONCENTRATION
(
ppmw)
0.5663
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
13
of
27
Documentation
of
details
of
WATER9/
Hand
calculations
comparisons
Subroutine
providing
the
details
of
the
calculations
used
by
WATER9
for
the
tank
unit.

Sub
TANK(
nt%)
'
edited
3­
25­
2002
Call
sets8(
nt%,
n%,
ci,
Vel,
q,
temp)
'
n%=
number
of
identical
tanks
'
ci=
inlet
concentration,
ppmw.
'
vel=
windspeed
cm/
s
'
q=
inlet
flow
rate
m3/
s
'
T=
temperature
in
the
tank,
deg
C
'
unit
inputs
__________________________
areareal
=
asgn8(
3)
DENS
=
asgn8(
4)
'
g/
cc
mwt
=
asgn8(
5)
storetime
=
asgn8(
6)
'
days
Fp
=
asgn8(
7)
'
paint
factor
wid
=
asgn8(
8)
'
diameter
m
h
=
asgn8(
9)
'
vapor
space
m
dt
=
asgn8(
10)
*
1.8
'
deg
F
AREA
=
(
wid)
^
2
*
3.141592
/
4
'
m2
le(
nt%).
AREA
=
AREA
depth
=
asgn8(
11)
'
m
specified
as
tank
height
vol
=
depth
*
AREA
'
m3
oilfract
=
asgn8(
12)
/
100
'
see
subroutine
fractionoil
for
details
If
oilfract
=
0
Then
'
oil
fraction
not
specified,
estimated
from
inflow
Call
fractionoil(
oilfract,
owpc,
owr,
frinoil,
nt%,
hlcor)
Else
Call
fractionoil(
oilfract,
owpc,
owr,
frinoil,
0,
hlcor)
End
If
'
oilfraction=
fraction
of
oil
in
the
tank
'
owpc
=
oil
water
partition
coefficient
'
owr
=
oil
water
ratio
'
frinoil
=
fraction
of
compound
in
the
oil
phase
'
hlcor
=
henry's
law
constant
correction
for
oil
partitioning.

fair
=
0:
fairs
=
0:
fairb
=
0:
fairw
=
0
If
storetime
=
0
And
q
=
0
Then
Exit
Sub
ElseIf
storetime
=
0
Then
storetime
=
vol
*
n%
/
q
/
3600
/
24
End
If
If
storetime
=
0
Then
Exit
Sub
qan
=
n%
*
ci
*
vol
*
DENS
/
storetime
*
365
'
g
yearly
throughput
If
depth
=
0
Then
qan
=
n%
*
ci
*
DENS
*
q
*
24
*
3600
*
365
'
g
yearly
throughput
If
showprint
=
1
Then
ppprnt
"
The
depth
in
the
tank
is
zero,
constant
level
option."
End
If
End
If
nturn
=
365
/
storetime
Call
Tcorr(
k1,
vmax,
dl,
dv,
vp,
Hl,
temp,
nt%)
cmwt
=
aa.
mwt:
If
cmwt
=
0
Then
cmwt
=
80
If
nturn
<=
36
Then
Kn
=
1
Else
Kn
=
(
180
+
nturn)
/
6
/
nturn
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
14
of
27
If
mwt
=
18
Or
oilfract
=
0
Then
'
aqueous
p
=
14.7
*
Hl
*
ci
/
cmwt
*
hlcor
'
psia
pmax
=
vp
/
760
*
14.7
If
p
>
pmax
Then
p
=
pmax
aqueous$
=
"
Aqueous
matrix"
If
showprint
=
1
Then
ppprnt
"
The
oil
corrected
aqueous
HL
is
"
+
Format$(
Hl
*
hlcor
*
55555,
"#.###
e+
00
(
y/
x)")
xw
=
0
Else
coil
=
ci
*
frinoil
/
oilfract
xw
=
frinoil
*
coil
/
cmwt
/
(
coil
/
cmwt
+
(
1000000!
­
coil)
/
mwt)
p
=
xw
*
vp
*
14.7
/
760
'
psia
aqueous$
=
"
Oily
matrix"
End
If
If
p
<
0
Then
p
=
0
conc
=
p
/
14.7
/
1000000!
'
ppmv
If
showprint
=
1
Then
'
print
summary
of
inputs
ppprnt
"
The
concentration
in
the
tank
inlet
is
"
+
Format$(
ci,
"#.###
e+
00
ppmw")
ppprnt
"
The
flowrate
of
liquid
is
"
+
Format$(
q,
"#.###
e+
00")
+
"
M3/
s"
ppprnt
"
liquid
flowrate
(
from
tank
holding)
is
"
+
Format$(
vol
/
storetime
/
24
/
3600,
"#.###
e+
00")
+
"
M3/
s"
ppprnt
"
The
total
loading
of
the
compound
is
"
+
Format$(
qan,
"#.##
e+
00")
+
"
g/
yr."
End
If
If
areareal
>
0
Then
'
this
section
is
for
an
open
tank
If
depth
=
0
Then
depth
=
0.3
fd
=
wid
/
depth
kg
=
KGC8(
Vel,
wid
*
100,
dv,
2)
kl
=
KLC8(
Vel,
fd,
dl,
temp,
6,
0,
1)
ko
=
1
/
(
1
/
kl
+
1
/
(
Hl
*
hlcor)
/
55555
/
kg)
restime
=
storetime
*
24
*
3600
Mtr
=
ko
*
0.18
/
depth
*
restime
fairs
=
1
­
Exp(­
Mtr)
fair
=
fairs
Call
setx8(
kg,
kl,
ko,
fairs,
0,
0,
0)
Else
'_____
calculation
of
working
losses
If
depth
=
0
Then
'
assumes
constant
level
tank,
fixed
roof
fairw
=
0
Else
G
=
q
*
1000
/
3.75
*
3600
*
24
'
gal/
day
v
=
vol
*
1000
/
3.785
'
gal
lw
=
0.0000000109
*
aa.
mwt
*
p
*
v
*
Kn
'
Mg/
turnover
If
ci
>
0
Then
fairw
=
1000000!
*
lw
/
(
ci
*
vol
*
DENS)
Else
fairw
=
0
fairw
=
fairw
/
(
1
+
fairw)
If
showprint
=
1
Then
ppprnt
"
The
working
volume
is
"
+
Format$(
vol,
"#.###
e+
00
m3;")
+
Format$(
v,
"#.###
e+
00
gal")
ppprnt
"
The
mass
lost
per
turnover
is
"
+
Format$(
lw,
"#.###
e+
00")
+
"
Mg/
turnover"
ppprnt
"
The
vapor
pressure
of
the
compound
in
solution
is
"
+
Format$(
p,
"#.######")
+
"
psia."
End
If
End
If
'_____
calculation
of
breathing
losses
dia
=
wid
*
3.28
'
ft
h
=
h
*
3.28
'
ft
If
dia
>
30
Then
c
=
1
Else
c
=
0.0771
*
dia
­
0.0013
*
dia
^
2
­
0.1334
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
15
of
27
Lb2
=
0.0000102
*
aa.
mwt
*
(
p
/
(
14.7
­
p))
^
0.68
*
dia
^
1.73
Lb
=
n%
*
Lb2
*
h
^
0.51
*
dt
^
0.5
*
Fp
*
c
'
Mg/
year
If
qan
>
0
Then
fairb
=
1000000
*
Lb
/
qan
Else
fairb
=
0
'
summary
information
fairb
=
fairb
/
(
1
+
fairb)
'
fraction
to
air
from
breathing
fair
=
fairb
+
fairw
*
(
1
­
fairb)
'
total
fraction
to
air
'
printing
information_______________
Call
setx8(
0,
0,
0,
0,
0,
0,
0)
If
showprint
=
1
Then
ppprnt
"
MWT
=
"
+
Format$(
aa.
mwt,
"###.#")
+
"
dia=
"
+
Format$(
dia,
"####.#
ft.")
ppprnt
"
Breathing:
Lb
=
0.0000102
*
MWT
*
(
p
/
(
14.7
­
p))
^
0.68
*
dia
^
1.73
"
ppprnt
"
mass
emissions=
Lb
*
h
^
0.51
*
dt
^
0.5
*
Fp
*
c
Mg/
yr"
ppprnt
"
c
=
"
+
Format$(
c,
"#.###")
+
"
h=
"
+
Format$(
h,
"####.#
ft.")
ppprnt
"
dt
=
"
+
Format$(
dt,
"##.##
")
+
"
deg.
F
Fp=
"
+
Format$(
Fp,
"##.###")
ppprnt
"
mass
emissions=
"
+
Format$(
Lb,
"##.##
E+
00
")
+
"
Mg/
yr"
End
If
End
If
If
showprint
=
1
Then
ppprnt
"
The
temperature
in
the
tank
is
"
+
Format$(
temp,
"###.#")
+
"
deg.
C"
ppprnt
"
The
type
of
liquid
is
"
+
aqueous$
ppprnt
"
The
concentration
in
the
liquid
waste
is
"
+
Format$(
ci,
"#.###
e+
00
g/
m3")
ppprnt
"
The
fraction
in
the
oil
is
"
+
Format$(
frinoil,
"#.#######")
ppprnt
"
The
vapor
pressure
(
p)
is
"
+
Format$(
p,
"#.###
e+
00
psia;
")
+
"("
+
Format$(
vp,
"#.###
e+
00
mmHg")
+
")"
ppprnt
"
The
fraction
of
the
compound
in
oil
phase
is
"
+
Format$(
frinoil,
"#.#####")
+
"."
ppprnt
"
The
residence
time
in
the
tank
is
"
+
Format$(
storetime,
"###.###")
+
"
days."
End
If
Call
setx1(
storetime,
Kn,
fairw,
fairb,
fairs,
concg,
frinoil,
0,
0,
0)
'
nt%,
fair,
fbio,
fads,
ta,
percontrol
Call
sumrates8(
nt%,
fair,
0,
0,
AREA,
0,
0)
ASGN2(
192)
=
ci
*
(
1
­
fair
­
fbio
­
fads)

End
Sub
Subroutine
providing
the
details
of
the
calculations
used
by
WATER9
for
the
impoundment
or
the
lagoon
unit.

Sub
IMPOUND8(
nt%)
'
surface
impoundment
model
'
input
parameters
Call
sets8(
nt%,
n%,
ci,
v,
q,
T)
'
n%=
number
of
impoundments
'
ci=
inlet
concentration,
ppmw.
'
v=
windspeed
cm/
s
'
q=
inlet
flow
rate
m3/
s
'
T=
temperature
in
the
impoundment
deg
C
l1
=
asgn8(
3)
'
length,
m
d
=
asgn8(
4)
'
depth,
m
If
d
=
0
Then
Exit
Sub
wid
=
asgn8(
5)
'
width,
m
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
16
of
27
xw
=
asgn8(
6)
'
g
biomass
/
l
If
asgn8(
7)
=
1
Then
plugflow
=
1
holdingtime
=
asgn8(
8)
'
months.
if
residence
time
is
specified
by
waste
flow,
set
to
0.
overallbiorate
=
asgn8(
9)
sorptionflag
=
asgn8(
10)

AREA
=
wid
*
l1
'
surface
of
impoundment
m2
le(
nt%).
AREA
=
AREA
'
see
subroutine
Tcorr
for
details
Call
Tcorr(
k1,
vmax,
dl,
dv,
vp,
Hl,
T,
nt%)
'
compound
properties
adjusted
for
temperature
T(
Cel.)
'
k1=
first
order
biorate
constant
L/
g­
hr
'
dl,
dv
diffusion
constant
liquid
and
vapor,
cm2/
s
'
vp
vapor
pressure
mm
Hg
'
Hl
Henry's
law
constant
atm­
m3/
mol
volume
=
AREA
*
d
'
m3
dia
=
Sqr(
AREA
*
4
/
3.14)
'
width
m
If
holdingtime
>
0
Then
'
modified
4­
4­
02
if
q
=
0
Then
'
model
is
the
same
for
either
plugflow
=
1
'
plug
flow
or
disposal
restime
=
holdingtime
*
365.25
/
12
*
24
'
holding
time,
hr
checkflowrate
holdingtime,
volume,
q,
nt%
qavg
=
volume
/
restime
/
3600
'
m3/
s
q
=
qavg
L(
nt%).
wflow
=
q
*
1000
'
permits
only
one
warning
from
checkflowrate
If
showprint
=
1
Then
ppprnt
"
The
average
flow
for
specified
holding
time
is
volume/
residence
time
"
+
FORMP(
qavg)
+
"
m3/
s.
"
End
If
Else
restime
=
l1
*
wid
*
d
/
q
*
n%
/
3600
'
holding
time,
hr
End
If
totalin
nt%,
sumsolids,
sumBiomass,
sumOil,
sumDiss
'
g/
s
'
sumsolids=
solids
added
to
impoundment,
g/
s
average
'
sumbiomass=
biomass
solids
added
to
impoundment,
g/
s
average
'
sumoil=
oil
added
to
impoundment,
g/
s
average
'
sumDiss=
dissolved
solids
added
to
impoundment,
g/
s
average
inletsolids
=
(
sumsolids
+
sumBiomass
+
sumOil)
'
g/
s
fractionsorbed
=
le(
nt%).
fsludge
+
le(
nt%).
fsolids
+
le(
nt%).
foil
fractionwater
=
1
­
fractionsorbed
settle
oilremove,
solidRemain,
waterRemove,
solidRemove,
nt%
If
le(
nt%).
cin
>
0
Then
fractionsorbed
=
(
oilremove
+
solidRemain
+
waterRemove
+
solidRemove)
/
le(
nt%).
cin
fs2
=
(
solidRemain
+
solidRemove)
/
le(
nt%).
cin
Else
fs2
=
0
fractionsorbed
=
0
End
If
'
add
biomass
generation
'
g/
s
=
gbio/
L
mg/
gbio­
hr
m3
hr/
s
L/
m3
g/
mg
bioadd
=
xw
*
overallbiorate
*
volume
/
3600
*
1000
/
1000
/
2
'
g/
s
=
g/
s
maxbioadd
=
sumDiss
/
2
If
bioadd
>
maxbioadd
Then
bioadd
=
maxbioadd
*
0.95
ksl
=
10
^
(
0.67
*
aa.
low
­
2.61)
'
g/
Kg
biomass
per
g/
m3
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
17
of
27
If
sorptionflag
=
1
Then
If
(
sumsolids
+
sumBiomass)
>
0
Then
fractionbioadd
=
(
le(
nt%).
fsludge
+
le(
nt%).
fsolids)
*
bioadd
/
(
sumsolids
+
sumBiomass)
Else
'
only
new
biomass
'
kg/
m3
=
gbio/
s
kg/
g
m3/
s
If
q
>
0
Then
concsolids
=
bioadd
/
1000
/
q
*
n%
'
+
xb
'
kg/
M3
fractionbioadd
=
ksl
*
concsolids
/
(
ksl
*
concsolids
+
1)
'
assumes
solids
and
oil
are
similar
to
biomass
ElseIf
bioadd
=
0
Then
concsolids
=
0
fractionbioadd
=
0
Else
MsgBox
"
error
in
specification
for
unit
"
+
Str$(
nt%)
End
If
End
If
Else
fractionsorbed
=
0
End
If
'
ld(
50).
xstart
is
an
internal
flag
that
specifies
that
Hl
is
corrected
for
sorption
If
ld(
50).
xstart
=
1
Then
Hl
=
Hl
*
(
1
­
fractionsorbed)
'
sorption
correction
of
HL
If
bioadd
>
0
And
maxbioadd
>
0
Then
le(
nt%).
Mrds
=
(
bioadd
/
maxbioadd)
Else
le(
nt%).
Mrds
=
0
le(
nt%).
bios
=
bioadd
'
g
new
biomass/
s
fd!
=
dia
/
d
'
Fetch
to
depth
ratio
If
showprint
=
1
Then
ppprnt
"
The
residence
time
in
the
unit
is
"
+
FORMP(
restime)
+
"
hr.
("
+
FORMP(
restime
/
24)
+
"
days.)"
If
q
=
0
Then
ppprnt
"
The
residence
time
was
specified."
ppprnt
"
The
fetch
to
depth
ratio
(
effective
width/
depth)
is
"
+
FORMP(
fd!)
+
"."
If
sorptionflag
=
1
Then
ppprnt
"
The
solids
are
assumed
to
settle
in
the
lagoon
base."
ppprnt
"
The
fraction
sorbed
(
solids+
water)
is
"
+
FORMP(
fractionsorbed)
End
If
ppprnt
"__
Sorption
partitioning
of
component_______"
ppprnt
"
The
fraction
sorbed
on
solids
is
"
+
FORMP(
fs2)
+
"."
sumsolids2
=
le(
nt%).
fsolids
+
le(
nt%).
fsludge
+
le(
nt%).
foil
If
sumsolids
>
0
Then
ppprnt
"
solids
fraction
sorbed
"
+
FORMP(
fs2
*
le(
nt%).
fsolids
/
sumsolids2)
ppprnt
"
biomass
fraction
sorbed
"
+
FORMP(
fs2
*
le(
nt%).
fsludge
/
sumsolids2)
ppprnt
"
oil
fraction
sorbed
"
+
FORMP(
fs2
*
le(
nt%).
foil
/
sumsolids2)
End
If
End
If
'
see
the
details
under
the
functions
kgc8,
klc8
kg
=
KGC8(
v,
dia
*
100,
dv,
2)
'
gm/
c2­
s
kl
=
KLC8(
v,
fd!,
dl,
T,
6,
0,
1)
ko
=
1
/
(
1
/
kl
+
1
/
Hl
/
55555
/
kg)
kair
=
ko
*
0.18
/
d
*
3600
'
hr­
1
If
sorptionflag
=
1
Then
'
solids
dropped
at
base
of
unit
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
18
of
27
kads
=
0
'
not
considered
when
solids
drop
Else
'
solids
proceed
through
system
'
1/
hr
gbio/
s
s/
hr
kg/
g
g/
Kg
biomass
per
g/
m3
/
m3
kads
=
(
bioadd
+
inletsolids)
*
3600
*
0.001
*
ksl
/
volume
'
/
hr
kads
=
(
1
­
fractionwater)
/
restime
/
fractionwater
'
5­
7­
02
End
If
kother
=
kair
+
kads
hydrolysisk
kother,
khydrolysis
solids
=
0
dissol
=
0
'
see
the
details
under
the
subroutine
fract28
Call
fract28(
ci
*
(
1
­
fractionsorbed),
xw,
vmax,
kother,
kair,
solids,
dissol,
restime,
Co,
fbio,
fair,
fraleft,
plugflow,
0,
fads,
cair)

total
=
ci
*
volume
'
g
in
impound
'__
summarize
results_______
If
sorptionflag
=
1
Then
'
solids
dropped
at
base
of
unit
fads
=
0
'
fractionsorbed
'
fraction
that
is
adsorbed
and
not
available
for
volatilization
or
biodegradation
Else
'
solids
proceed
through
system
If
kother
>
0
Then
fdiff
=
kdiff
/
kother
*
fair
fads
=
kads
/
kother
*
fair
fhydrolysis
=
khydrolysis
/
kother
*
fair
fair
=
kair
/
kother
*
fair
Else:
fdiff
=
0:
fads
=
0
End
If
End
If
fhydrolysis
=
fhydrolysis
*
(
1
­
fractionsorbed)
fair
=
fair
*
(
1
­
fractionsorbed)
'
fraction
that
is
lost
to
the
air
fdiff
=
fdiff
*
(
1
­
fractionsorbed)
'
fraction
that
is
biodegraded
fbio
=
fbio
*
(
1
­
fractionsorbed)
'
fraction
that
is
biodegraded
fraleft
=
(
1
­
fractionsorbed)
­
fair
­
fbio
­
fdiff
If
showprint
=
1
And
khydrolysis
>
0
Then
ppprnt
"
Hydrolysis______________________________________"
ppprnt
"
The
hydrolysis
rate
is
"
+
FORMP(
khydrolysis)
+
"/
hr."
ppprnt
"
The
fraction
removed
by
hydrolysis
is
"
+
FORMP(
fhydrolysis)
ppprnt
"
The
hydrolysis
rate
is
included
with
the
biorate"
ppprnt
"
The
fraction
removed
bio
without
hydrolysis
is
"
+
FORMP(
fbio)
fbio
=
fbio
+
fhydrolysis
ppprnt
"
The
fraction
removed
bio
plus
hydrolysis
is
"
+
FORMP(
fbio)
End
If
'__
print
results_______
Call
setx8(
kg,
kl,
ko,
fair,
fbio,
fdiff,
fads)
If
restime
>
0
Then
le(
nt%).
cin
=
total
/
restime
/
3600
'
g/
s
Call
sumrates8(
nt%,
fair,
fbio,
0,
AREA,
0,
fractionsorbed)
If
restime
>
0
Then
le(
nt%).
e
=
total
*
fair
/
restime
/
3600
ASGN2(
192)
=
ci
*
(
1
­
fair
­
fbio
­
fads)
End
Sub
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
19
of
27
Case
1:
Detailed
Model
Results
WASTEWATER
TREATMENT
UNIT
1
04­
01­
2002
Disposal
impoundment
with
1ppmw
benzene
BENZENE
Type
of
unit
is
lagoon
1
Description
of
unit
1
2
Wastewater
temperature
(
C)
25
3
Length
of
impoundment
(
m)
95
4
Depth
of
impoundment
(
m)
1.8
5
Width
of
impoundment
(
m)
95
6
active
biomass,
impoundment
(
g/
l)
0.05
7
if
there
is
plug
flow,
enter
1
0
8
time
for
emissions
in
lagoon
(
months)
0.1
9
Overall
biorate
(
mg/
g
bio­
hr)
19
10
sorption
flag
for
solids
settling
=
1
0
COMPOUND
PROPERTIES
OF
BENZENE
at
25
deg.
C
Type
of
compound
A
density
(
g/
cc)
0.87
molecular
weight
78.1
diffusion
coef.
water
(
cm2/
s)
9.8e­
06
diffusion
coef.
air
(
cm2/
s)
0.088
vapor
pressure
(
mm
Hg)
95.2
Henry's
law
constant
(
atm­
m3/
mol)
0.00555
y/
x=
308.34
Reference
for
Henry's
law:
no
database
value
vapor
pressure
temp.
coefficients
6.905
1211.033
220.79
The
enthalpy
of
vaporization
90.218
cal/
cc.
zero
order
biorate
constant
(
mg/
g­
hr)
19.
first
order
biorate
constant
(
l/
g­
hr)
1.4
octanol
water
partition
coefficient
2.15
solubility
ppmw
1780.
UNIFAC
code
16:
00000000000
CAS
code
71­
43­
2
The
estimated
vapor
pressure
is
95.256044
mm
Hg.

DETAILED
CALCULATIONS
at
Unit
1
Type:
lagoon
COMPOUND:
BENZENE
The
residence
time
was
specified
as
0.1
month.
The
residence
time
in
the
unit
is
73.05
hr.
(
3.0438
days.)

Estimate
the
equivalent
diameter
from
the
area
(
95
x
95
m2)
dia
=
Sqr(
95*
95
*
4
/
3.14)
dia=
107.2
m
kg
=
0.00482(
v/
100)^
0.78/(
dia)^
0.11*(
0.000181/
0.0012/
dv)^­
0.67*
0.00409
v
=
447
m/
s
windspeed
dia
=
107.22
equivalent
length
m
Dv
=
0.088
cm2/
s
gas
diffusivity
Kg
=
2.6417
e­
5
gas
mass
transfer
coefficient
gm/
c2­
s
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
20
of
27
The
fetch
to
depth
ratio
is
107.22/
1.8
=
59.55
Since
the
fetch
to
depth
ratio
is
greater
than
51.11
Then
kl
=
0.0000002611
*
v
*
v
/
10000
*
(
dl
/
0.0000085)
^
0.66666
v
=
447
cm/
s
windspeed
dl
=
9.8
e­
6
cm2/
s
liquid
diffusivity
Kl
=
3.187
e­
5
gm/
c2­
s
liquid
mass
transfer
coefficient
ko
=
1
/
(
1
/
kl
+
1
/
Hl
/
55555
/
kg)

Hl
=
0.00555
atm/(
g/
m3)
Henry's
law
kg
=
2.642
e­
5
gm/
c2­
s
gas
phase
coef.
Kl
=
3.187
e­
5
gm/
c2­
s
liquid
phase
coef.
ko
=
3.1743
e­
5
gm/
c2­
s
overall
mass
transfer
coef.

ko
is
estimated
as
(
3.1743
e­
5)*
0.18
=
5.7146
e­
6
kair
=
ko
*
0.18
/
d
*
3600
ko
=
3.1743
e­
5
gm/
c2­
s
overall
mass
transfer
d
=
1.8
m
depth
of
impoundment
kair
=
0.011428
hr­
1
kads
=
(
bioadd
+
inletsolids)
*
3600
*
0.001
*
ksl
/
volume
'
/
hr
kads
=
0,
because
bioadd
and
inletsolids
equal
0.

kother
=
kair
+
kads
kother
=
0.011428
hr­
1
WATER8
subroutine
Call
fract28(
ci
*
(
1
­
fractionsorbed),
xw,
vmax,
kother,
kair,
solids,
dissol,
restime,
Co,
fbio,
fair,
fraleft,
plugflow,
0,
fads,
cair)

Input
values:
Ci
=
1
g/
m3,
inlet
concentration
of
benzene
Fractionsorbed
=
0
Xw
=
0.05
biomass,
g/
L
vmax
=
19
kother
=
0.011428
hr­
1
kair
=
0.011428
hr­
1
solids
=
0
dissol
=
0
restime
=
73
hr.
plugflow
=
1
plug
flow,
because
the
holding
time
is
specified
kair
=
0.011428
hr­
1
Output
values:
Co
=
0.00278
g/
m3
fbio
=
0.8528
fair
=
0.14439
fraleft
=
0.00278
fads
=
0.0
Details
of
subroutine
ks
=
aa.
biov
/
aa.
k1
aa.
biov
=
19
aa.
k1
=
1.4
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
21
of
27
ks
=
13.57
An
iterative
procedure
is
used
to
estimate
the
exit
concentration
for
the
wastewater
as
it
is
retained
in
the
basin
for
the
specified
0.1
months.
The
exit
concentration
c
is
0.00278
g/
m3.

fbio
=
(
ci
­
fother
­
c)
/
ci
ci
=
1
g/
m3.
fother
=
0.14439
c
=
0.00278
g/
m3
fbio
=
0.8528.

fair
=
kair
/
kother
*
fother
/
ci
ci
=
1
g/
m3.
kair
=
0.011428
hr­
1
kother
=
0.011428
hr­
1
fother
=
0.14439
fair
=
0.14439
g/
m3.

fads
=
(
1
­
ratio)
*
c
/
ci
ratio
=
0.
fads
=
0
fraleft
=
c
/
ci
ci
=
1
g/
m3.
c
=
0.00278
g/
m3
fraleft
=
0.00278
g/
m3.

WATER9
summary
KG
surface
(
m/
s)
0.00646
KL
surface
(
m/
s)
5.736e­
06
KL
OVERALL
SURFACE
(
m/
s)
5.714e­
06
TOTAL
FRACTION
VOLATILIZED
0.1444
FRACTION
BIOLOGICALLY
REMOVED
0.8528
FRACTION
SUBMERGED
VOLATILIZED
0.
FRACTION
ABSORBED
0.

TOTAL
AIR
EMISSIONS
(
g/
s)
0.00892
(
Mg/
year)
0.2813
EMISSION
FACTOR
(
g/
cm2­
s)
9.883e­
11
UNIT
EXIT
CONCENTRATION
(
ppmw)
0.00278
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
22
of
27
Case
2:
Detailed
Model
Results
WASTEWATER
TREATMENT
UNIT
2
03­
25­
2002
Example
calculation
Section
9.6.3
BENZENE
Type
of
unit
is
storage
tank
1
Description
of
unit
2
open
storage
tank
2
Wastewater
temperature
(
C)
25
3
Open
surface
area
of
tank
(
m2)
2
4
Density
of
liquid
in
tank
(
g/
cc)
1
5
tank
waste
Mwt,
water=
18
18
6
unit
storage
time
(
days)
8.3
7
tank
paint
factor
1
8
tank
diameter
(
m)
5.79
9
tank
vapor
space
height
(
m)
1.37
10
diurnal
temp.
change
(
deg.
C)
11
11
tank
height
(
m)
2.7
12
oil
in
composite
wastewater
(
wt.
%)
0
COMPOUND
PROPERTIES
OF
BENZENE
at
25
deg.
C
Type
of
compound
density
(
g/
cc)
0.874
molecular
weight
78.11
diffusion
coef.
water
(
cm2/
s)
9.8e­
06
diffusion
coef.
air
(
cm2/
s)
0.088
vapor
pressure
(
mm
Hg)
95.26
Henry's
law
constant
(
atm­
m3/
mol)
0.00555
y/
x=
308.33
Reference
for
Henry's
law:
Yaws
and
Yang,
1992
S
vapor
pressure
temp.
coefficients
6.905
1211.033
220.8
The
enthalpy
of
vaporization
90.614
cal/
cc.
zero
order
biorate
constant
(
mg/
g­
hr)
19.1
first
order
biorate
constant
(
l/
g­
hr)
1.4
octanol
water
partition
coefficient
2.13
solubility
ppmw
1790.
UNIFAC
code
16:
00000000000
CAS
code
71­
43­
2
The
estimated
vapor
pressure
is
95.33174
mm
Hg.
DETAILED
CALCULATIONS
at
Unit
2
open
storage
tank
Type:
storage
tank
COMPOUND:
BENZENE
The
oil
corrected
aqueous
HL
is
3.083e+
02
(
y/
x)
The
concentration
in
the
tank
inlet
is
30
ppmw
The
flowrate
of
liquid
is
1.
e­
04
M3/
s
liquid
flowrate
(
from
tank
holding)
is
9.913e­
05
M3/
s
The
total
loading
of
the
compound
is
9.38e+
04
g/
yr.

Estimate
the
equivalent
diameter
is
the
specified
diameter,
5.79
m.

kg
=
0.00482(
v/
100)^
0.78/(
dia)^
0.11*(
0.000181/
0.0012/
dv)^­
0.67*
0.00409
v
=
200
cm/
s
windspeed
dia
=
5.79
equivalent
length
m
Dv
=
0.088
cm2/
s
gas
diffusivity
Kg
=
1.945
e­
5
gas
mass
transfer
coefficient
gm/
c2­
s
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
23
of
27
The
fetch
to
depth
ratio
is
5.79/
2.7
=
2.144
Since
the
windspeed
(
200
cm/
s)
is
less
than
350
cm/
s,
the
following
correlation
is
used.
kl
=
0.00000278
*
(
dl
/
0.0000085)
^
0.66666
v
=
200
cm/
s
windspeed
dl
=
9.8
e­
6
cm2/
s
liquid
diffusivity
Kl
=
3.057
e­
6
gm/
c2­
s
liquid
mass
transfer
coefficient
ko
=
1
/
(
1
/
kl
+
1
/
Hl
/
55555
/
kg)

Hl
=
0.00555
atm/(
g/
m3)
Henry's
law
Kg
=
1.945
e­
5
gas
mass
transfer
coefficient
gm/
c2­
s
Kl
=
3.057
e­
6
gm/
c2­
s
liquid
phase
coef.
ko
=
1.693
e­
5
gm/
c2­
s
overall
mass
transfer
coef.

ko
is
estimated
as
(
1.693
e­
5)*
0.18
=
5.7146
e­
6
m/
s
restime
=
STORETIME
*
24
*
3600
storetime
=
8.3
days
restime
=
717120
sec.

Mtr
=
ko
*
0.18
/
depth
*
restime
*
areareal
/
AREA
'
4­
8­
02
ko
=
1.693
e­
5
gm/
c2­
s
overall
mass
transfer
d
=
2.7
m
depth
of
liquid
Mtr
=
0.809552
fairs
=
1
­
Exp(­
Mtr)

Mtr
=
0.809552
fairs
=
0.55494
The
temperature
in
the
tank
is
25.
deg.
C
The
type
of
liquid
is
Aqueous
matrix
p
=
14.7
*
Hl
*
ci
/
cmwt
*
hlcor
ci
=
30
g/
m3
inlet
concentration
of
component
hl
=
0.00555
atm­
m3/
mol
cmwt
=
78.11
compound
molecular
weight
hlcor
=
1
correction
for
oil
sorption,
not
needed
p
=
0.03133
vapor
pressure,
psia
The
residence
time
in
the
tank
is
8.3
days.
Waste
rate
in
the
unit
0.1
(
L/
s)
0.00228
(
MGD)
concentration
into
the
unit
30.
(
mg/
L)
compound
rate
into
the
unit
0.003
(
g/
s)
0.02381
(
lb/
hr)
compound
rate
recovered
by
controls
0.
(
g/
s)
0.
(
lb/
hr)
fraction
recovered
by
controls
0.
unit
storage
time
(
days)
8.3
Tank
turnover
factor
0.8489
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
24
of
27
Tank
working
loss
(
fraction)
0.

Tank
breathing
loss
(
fraction)
0.

Open
tank
volatilization
loss
0.5549
concentration
in
headspace
(
ppmv)
0.

fraction
of
compound
in
oil
phase
0.

TOTAL
FRACTION
VOLATILIZED
0.5549
FRACTION
BIOLOGICALLY
REMOVED
0.

TOTAL
AIR
EMISSIONS
(
g/
s)
0.00166
(
Mg/
year)
0.0525
EMISSION
FACTOR
(
g/
cm2­
s)
6.323e­
09
UNIT
EXIT
CONCENTRATION
(
ppmw)
13.352
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
25
of
27
Case
3:
Detailed
Model
Results
WASTEWATER
TREATMENT
UNIT
1
04­
01­
2002
Example
calculation
Section
9.6.3
BENZENE
Type
of
unit
is
storage
tank
1
Description
of
unit
1
closed
tank
2
Wastewater
temperature
(
C)
25
3
Open
surface
area
of
tank
(
m2)
0
4
Density
of
liquid
in
tank
(
g/
cc)
1
5
tank
waste
Mwt,
water=
18
18
6
unit
storage
time
(
days)
8.3
7
tank
paint
factor
1
8
tank
diameter
(
m)
5.79
9
tank
vapor
space
height
(
m)
1.37
10
diurnal
temp.
change
(
deg.
C)
11
11
tank
height
(
m)
2.7
12
oil
in
composite
wastewater
(
wt.
%)
0
COMPOUND
PROPERTIES
OF
BENZENE
at
25
deg.
C
Type
of
compound
density
(
g/
cc)
0.874
molecular
weight
78.11
diffusion
coef.
water
(
cm2/
s)
9.8e­
06
diffusion
coef.
air
(
cm2/
s)
0.088
vapor
pressure
(
mm
Hg)
95.26
Henry's
law
constant
(
atm­
m3/
mol)
0.00555
y/
x=
308.33
Reference
for
Henry's
law:
Yaws
and
Yang,
1992
S
vapor
pressure
temp.
coefficients
6.905
1211.033
220.8
The
enthalpy
of
vaporization
90.614
cal/
cc.
zero
order
biorate
constant
(
mg/
g­
hr)
19.1
first
order
biorate
constant
(
l/
g­
hr)
1.4
octanol
water
partition
coefficient
2.13
solubility
ppmw
1790.
UNIFAC
code
16:
00000000000
CAS
code
71­
43­
2
The
estimated
vapor
pressure
is
95.33174
mm
Hg.

DETAILED
CALCULATIONS
at
Unit
1
closed
tank
Type:
storage
tank
COMPOUND:
BENZENE
Properties
of
BENZENE
at
25.
deg.
C
hl=
0.00555
atm­
m3/
mol
vp=
95.26
mmHg
k1=
0.
L/
g­
hr
dl=
9.8e­
06
cm2/
s
dv=
0.088
cm2/
s
p
=
14.7
*
Hl
*
ci
/
cmwt
*
hlcor
ci
=
30
g/
m3
inlet
concentration
of
component
hl
=
0.00555
atm­
m3/
mol
cmwt
=
78.11
compound
molecular
weight
hlcor
=
1
correction
for
oil
sorption,
not
needed
p
=
0.03133
vapor
pressure,
psia
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
26
of
27
qan
=
ci
*
vol
*
DENS
/
storetime
*
365
ci
=
30
g/
m3
inlet
concentration
of
component
vol
=
71.09
m3
tank
working
volume
dens
=
1
liquid
density
g/
cc
storetime=
8.3
days
specified
retention
time
in
tank
qan
=
93788
g
yearly
throughput
nturn
=
365
/
storetime
storetime
=
8.3
days
specified
retention
time
in
tank
nturn
=
44
number
of
turnovers
in
a
year
If
nturn
<=
36
Then
Kn
=
1
Else
Kn
=
(
180
+
nturn)
/
6
/
nturn
Kn
=
(
180
+
nturn)
/
6
/
nturn
nturn
=
44
number
of
turnovers
in
a
year
Kn
=
0.8489
v
=
vol
*
1000
/
3.785
'
gal
vol
=
71.09
m3
tank
working
volume
v
=
18782
volume
working
gal
lw
=
0.0000000109
*
aa.
mwt
*
p
*
v
*
Kn
v
=
18782
volume
working
gal
Kn
=
0.8489
p
=
0.03133
vapor
pressure,
psia
aa.
mwt
=
78.11
compound
molecular
weight
lw
=
4.2534
e­
4
Mg/
turnover
fairw
=
1000000!
*
lw
/
(
ci
*
vol
*
DENS)
ci
=
30
g/
m3
inlet
concentration
of
component
vol
=
71.09
m3
tank
working
volume
dens
=
1
liquid
density
g/
cc
lw
=
8.3
days
specified
retention
time
in
tank
fairw
=
0.19944
g
yearly
throughput
fairwc
=
fairw
/
(
1
+
fairw)
'
fraction
to
air
from
breathing
fairw
=
0.19944
g
yearly
throughput
fairwc
=
0.16628
g
yearly
throughput
The
concentration
in
the
tank
inlet
is
30
ppmw
The
flowrate
of
liquid
is
1.
e­
04
M3/
s
liquid
flowrate
(
from
tank
holding)
is
9.913e­
05
M3/
s
The
total
loading
of
the
compound
is
9.38e+
04
g/
yr.
The
working
volume
is
7.109e+
01
m31.878e+
04
gal
The
mass
lost
per
turnover
is
4.253e­
04
Mg/
turnover
The
vapor
pressure
of
the
compound
in
solution
is
.031335
psia.
MWT
=
78.1
dia=
19.
ft.

dia
=
wid
*
3.28
dia
=
18.99
diameter,
feet
wid
=
5.79
diameter,
meters
hf
=
h
*
3.28
hf
=
4.494
vapor
height,
feet
h
=
1.37
vapor
height,
meters
WATER8
and
WATER9
Modeling
of
Tanks
and
Impoundments
Page
27
of
27
If
dia
>
30
Then
c
=
1
Else
c
=
0.0771
*
dia
­
0.0013
*
dia
^
2
­
0.1334
dia
=
18.99
diameter,
feet
c
=
0.8620
Lb2
=
0.0000102
*
mwt
*
(
p
/
(
14.7
­
p))
^
0.68
*
dia
^
1.73
p
=
0.03133
vapor
pressure,
psia
dia
=
18.99
diameter,
feet
mwt
=
78.11
compound
molecular
weight
lb2
=
0.0019831
Lb
=
Lb2
*
hf
^
0.51
*
dt
^
0.5
*
Fp
*
c
'
Mg/
year
lb2
=
0.0019831
hf
=
4.494
vapor
height,
feet
dt
=
19.8
diurnal
temp.
change
(
deg.
F)
equals
change
in
temp.
deg
C
x
1.8
c
=
0.8620
Fp
=
1
tank
paint
factor
Lb
=
0.016368
fairb
=
1000000
*
Lb
/
qan
Lb
=
0.016368
qan
=
93788
g
yearly
throughput
fairb
=
0.17452
fairbc
=
fairb
/
(
1
+
fairb)
'
fraction
to
air
from
breathing
fairb
=
0.17452
fairbc
=
0.14859
Overall
loss
working
and
breathing
fair
=
fairb
+
fairwc
*
(
1
­
fairbc)
fairbc
=
0.14859
fraction
working
fairwc
=
0.16628
fraction
breathing
fair
=
0.29016
fraction
breathing
plus
working
The
temperature
in
the
tank
is
25.
deg.
C
The
type
of
liquid
is
Aqueous
matrix
The
concentration
in
the
liquid
waste
is
30
g/
m3
The
fraction
in
the
oil
is
zero,
there
is
no
oil.
The
vapor
pressure
(
p)
is
3.133e­
02
psia(
9.526e+
01
mmHg)
The
fraction
of
the
compound
in
oil
phase
is
..
The
residence
time
in
the
tank
is
8.3
days.
Waste
rate
in
the
unit
0.1
(
L/
s)
0.00228
(
MGD)
concentration
into
the
unit
30.
(
mg/
L)
compound
rate
into
the
unit
0.003
(
g/
s)
0.02381
(
lb/
hr)
compound
rate
recovered
by
controls
0.
(
g/
s)
0.
(
lb/
hr)
fraction
recovered
by
controls
0.

WATER9
summary
for
closed
top
tank
unit
storage
time
(
days)
8.3
Tank
turnover
factor
0.8489
Tank
working
loss
(
fraction)
0.1663
Tank
breathing
loss
(
fraction)
0.1486
Open
tank
volatilization
loss
0.
TOTAL
AIR
EMISSIONS
(
g/
s)
0.00087
(
Mg/
year)
0.02745
EMISSION
FACTOR
(
g/
cm2­
s)
3.306e­
09
UNIT
EXIT
CONCENTRATION
(
ppmw)
21.295
This
page
intentionally
left
blank.
Appendix
C
Detailed
Phase
II
Groundwater
Results
This
page
intentionally
left
blank.
C­
3
Appendix
C
Detailed
Phase
II
Groundwater
Results
Table
C­
1.
Adjusted
IWEM
Protective
Concentrations
for
Risk
=
1E­
6
and
HQ
=
1
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1e­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
1
Benzene
SI
A
RUN2
CT
CT
CT
CT
2.0E­
02
1.2E­
01
1.0E­
01
8.8E­
01
7.8E­
01
2
Benzene
SI
D
RUN2
CT
HE
HE
CT
2.0E­
02
4.5E­
03
4.0E­
03
6.2E­
03
5.5E­
03
3
Benzene
SI
F
RUN2
CT
HE
CT
HE
2.0E­
02
8.4E­
03
7.5E­
03
1.3E­
02
1.2E­
02
4
Benzene
SI
G
RUN2
CT
CT
HE
HE
2.0E­
02
2.7E­
02
2.4E­
02
1.7E­
01
1.5E­
01
5
Benzene
SI
B
RUN1
HE
HE
CT
CT
5.1E­
02
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
6
Benzene
SI
C
RUN1
HE
CT
HE
CT
5.1E­
02
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
7
Benzene
SI
E
RUN1
HE
CT
CT
HE
5.1E­
02
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
8
Benzene
SI
B
RUN3
HE
HE
CT
CT
2.3E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
9
Benzene
SI
C
RUN3
HE
CT
HE
CT
2.3E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
10
Benzene
SI
E
RUN3
HE
CT
CT
HE
2.3E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
11
Benzene
SI
B
RUN4
HE
HE
CT
CT
5.4E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
12
Benzene
SI
C
RUN4
HE
CT
HE
CT
5.4E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
13
Benzene
SI
E
RUN4
HE
CT
CT
HE
5.4E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
14
Benzene
SI
B
RUN5
HE
HE
CT
CT
3.1E­
02
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
15
Benzene
SI
C
RUN5
HE
CT
HE
CT
3.1E­
02
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
16
Benzene
SI
E
RUN5
HE
CT
CT
HE
3.1E­
02
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
20
Benzene
Tank
B
RUN1
HE
HE
CT
CT
5.9E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
21
Benzene
Tank
C
RUN1
HE
CT
HE
CT
5.9E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
22
Benzene
Tank
E
RUN1
HE
CT
CT
HE
5.9E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
23
Benzene
Tank
B
RUN3
HE
HE
CT
CT
9.8E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
(
continued)
C­
4
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1e­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
1.
(
continued)

24
Benzene
Tank
C
RUN3
HE
CT
HE
CT
9.8E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
25
Benzene
Tank
E
RUN3
HE
CT
CT
HE
9.8E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
26
Benzene
Tank
B
RUN5
HE
HE
CT
CT
3.8E­
02
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
27
Benzene
Tank
C
RUN5
HE
CT
HE
CT
3.8E­
02
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
28
Benzene
Tank
E
RUN5
HE
CT
CT
HE
3.8E­
02
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
29
Benzene
PrimClar
A
RUN7
CT
CT
CT
CT
9.6E­
01
1.2E­
01
1.0E­
01
8.8E­
01
7.8E­
01
30
Benzene
PrimClar
D
RUN7
CT
HE
HE
CT
9.6E­
01
4.5E­
03
4.0E­
03
6.2E­
03
5.5E­
03
31
Benzene
PrimClar
F
RUN7
CT
HE
CT
HE
9.6E­
01
8.4E­
03
7.5E­
03
1.3E­
02
1.2E­
02
32
Benzene
PrimClar
G
RUN7
CT
CT
HE
HE
9.6E­
01
2.7E­
02
2.4E­
02
1.7E­
01
1.5E­
01
33
Benzene
PrimClar
B
RUN8
HE
HE
CT
CT
9.7E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
34
Benzene
PrimClar
C
RUN8
HE
CT
HE
CT
9.7E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
35
Benzene
PrimClar
E
RUN8
HE
CT
CT
HE
9.7E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
36
Benzene
PrimClar
B
RUN9
HE
HE
CT
CT
9.6E­
01
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
37
Benzene
PrimClar
C
RUN9
HE
CT
HE
CT
9.6E­
01
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
38
Benzene
PrimClar
E
RUN9
HE
CT
CT
HE
9.6E­
01
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
55
Benzene
SecClar
A
RUN7
CT
CT
CT
CT
2.7E­
02
1.2E­
01
1.0E­
01
8.8E­
01
7.8E­
01
56
Benzene
SecClar
D
RUN7
CT
HE
HE
CT
2.7E­
02
4.5E­
03
4.0E­
03
6.2E­
03
5.5E­
03
57
Benzene
SecClar
F
RUN7
CT
HE
CT
HE
2.7E­
02
8.4E­
03
7.5E­
03
1.3E­
02
1.2E­
02
58
Benzene
SecClar
G
RUN7
CT
CT
HE
HE
2.7E­
02
2.7E­
02
2.4E­
02
1.7E­
01
1.5E­
01
59
Benzene
SecClar
B
RUN8
HE
HE
CT
CT
2.6E­
02
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
60
Benzene
SecClar
C
RUN8
HE
CT
HE
CT
2.6E­
02
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
(
continued)
C­
5
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1e­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
1.
(
continued)

61
Benzene
SecClar
E
RUN8
HE
CT
CT
HE
2.6E­
02
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
62
Benzene
SecClar
B
RUN9
HE
HE
CT
CT
5.7E­
02
1.3E­
02
1.2E­
02
2.1E­
02
1.8E­
02
63
Benzene
SecClar
C
RUN9
HE
CT
HE
CT
5.7E­
02
4.2E­
02
3.7E­
02
2.6E­
01
2.3E­
01
64
Benzene
SecClar
E
RUN9
HE
CT
CT
HE
5.7E­
02
7.5E­
02
6.7E­
02
5.6E­
01
5.0E­
01
68
Ethoxyethanol,
2­
SI
A
RUN2
CT
CT
CT
CT
1.9E+
00
4.0E+
02
1.2E+
05
3.1E+
03
9.2E+
05
69
Ethoxyethanol,
2­
SI
B
RUN1
HE
HE
CT
CT
2.2E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
70
Ethoxyethanol,
2­
SI
B
RUN3
HE
HE
CT
CT
2.4E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
71
Ethoxyethanol,
2­
SI
B
RUN4
HE
HE
CT
CT
2.2E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
72
Ethoxyethanol,
2­
SI
B
RUN5
HE
HE
CT
CT
2.0E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
74
Ethoxyethanol,
2­
Tank
B
RUN1
HE
HE
CT
CT
2.5E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
75
Ethoxyethanol,
2­
Tank
B
RUN3
HE
HE
CT
CT
2.5E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
76
Ethoxyethanol,
2­
Tank
B
RUN5
HE
HE
CT
CT
2.4E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
77
Ethoxyethanol,
2­
PrimClar
A
RUN7
CT
CT
CT
CT
2.5E+
01
4.0E+
02
1.2E+
05
3.1E+
03
9.2E+
05
78
Ethoxyethanol,
2­
PrimClar
B
RUN8
HE
HE
CT
CT
2.5E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
79
Ethoxyethanol,
2­
PrimClar
B
RUN9
HE
HE
CT
CT
2.5E+
01
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
85
Ethoxyethanol,
2­
SecClar
A
RUN7
CT
CT
CT
CT
1.2E+
00
4.0E+
02
1.2E+
05
3.1E+
03
9.2E+
05
86
Ethoxyethanol,
2­
SecClar
B
RUN8
HE
HE
CT
CT
1.2E+
00
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
87
Ethoxyethanol,
2­
SecClar
B
RUN9
HE
HE
CT
CT
2.6E+
00
4.6E+
01
1.4E+
04
7.2E+
01
2.1E+
04
89
Trichloroethane,
1,1,2­
SI
A
RUN2
CT
CT
CT
CT
2.4E­
02
7.9E­
02
5.1E­
02
7.2E­
01
4.7E­
01
90
Trichloroethane,
1,1,2­
SI
D
RUN2
CT
HE
HE
CT
2.4E­
02
2.7E­
03
1.8E­
03
4.3E­
03
2.7E­
03
91
Trichloroethane,
1,1,2­
SI
B
RUN1
HE
HE
CT
CT
5.1E­
02
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
(
continued)
C­
6
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1e­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
1.
(
continued)

92
Trichloroethane,
1,1,2­
SI
C
RUN1
HE
CT
HE
CT
5.1E­
02
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
93
Trichloroethane,
1,1,2­
SI
B
RUN3
HE
HE
CT
CT
2.4E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
94
Trichloroethane,
1,1,2­
SI
C
RUN3
HE
CT
HE
CT
2.4E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
95
Trichloroethane,
1,1,2­
SI
B
RUN4
HE
HE
CT
CT
6.2E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
96
Trichloroethane,
1,1,2­
SI
C
RUN4
HE
CT
HE
CT
6.2E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
97
Trichloroethane,
1,1,2­
SI
B
RUN5
HE
HE
CT
CT
3.1E­
02
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
98
Trichloroethane,
1,1,2­
SI
C
RUN5
HE
CT
HE
CT
3.1E­
02
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
101
Trichloroethane,
1,1,2­
Tank
B
RUN1
HE
HE
CT
CT
6.0E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
102
Trichloroethane,
1,1,2­
Tank
C
RUN1
HE
CT
HE
CT
6.0E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
103
Trichloroethane,
1,1,2­
Tank
B
RUN3
HE
HE
CT
CT
9.8E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
104
Trichloroethane,
1,1,2­
Tank
C
RUN3
HE
CT
HE
CT
9.8E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
105
Trichloroethane,
1,1,2­
Tank
B
RUN5
HE
HE
CT
CT
4.0E­
02
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
106
Trichloroethane,
1,1,2­
Tank
C
RUN5
HE
CT
HE
CT
4.0E­
02
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
107
Trichloroethane,
1,1,2­
PrimClar
A
RUN7
CT
CT
CT
CT
9.7E­
01
7.9E­
02
5.1E­
02
7.2E­
01
4.7E­
01
108
Trichloroethane,
1,1,2­
PrimClar
D
RUN7
CT
HE
HE
CT
9.7E­
01
2.7E­
03
1.8E­
03
4.3E­
03
2.7E­
03
109
Trichloroethane,
1,1,2­
PrimClar
B
RUN8
HE
HE
CT
CT
9.7E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
110
Trichloroethane,
1,1,2­
PrimClar
C
RUN8
HE
CT
HE
CT
9.7E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
111
Trichloroethane,
1,1,2­
PrimClar
B
RUN9
HE
HE
CT
CT
9.7E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
112
Trichloroethane,
1,1,2­
PrimClar
C
RUN9
HE
CT
HE
CT
9.7E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
123
Trichloroethane,
1,1,2­
SecClar
A
RUN7
CT
CT
CT
CT
5.3E­
02
7.9E­
02
5.1E­
02
7.2E­
01
4.7E­
01
124
Trichloroethane,
1,1,2­
SecClar
D
RUN7
CT
HE
HE
CT
5.3E­
02
2.7E­
03
1.8E­
03
4.3E­
03
2.7E­
03
(
continued)
C­
7
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1e­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
1.
(
continued)

125
Trichloroethane,
1,1,2­
SecClar
B
RUN8
HE
HE
CT
CT
4.8E­
02
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
126
Trichloroethane,
1,1,2­
SecClar
C
RUN8
HE
CT
HE
CT
4.8E­
02
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
127
Trichloroethane,
1,1,2­
SecClar
B
RUN9
HE
HE
CT
CT
1.1E­
01
7.9E­
03
5.1E­
03
1.4E­
02
9.2E­
03
128
Trichloroethane,
1,1,2­
SecClar
C
RUN9
HE
CT
HE
CT
1.1E­
01
2.9E­
02
1.9E­
02
2.2E­
01
1.4E­
01
C­
8
Appendix
C
Detailed
Phase
II
Groundwater
Results
Table
C­
2.
Adjusted
IWEM
Protective
Concentrations
for
Risk
=
1E­
5
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
1
Benzene
SI
A
RUN2
CT
CT
CT
CT
2.0E­
02
1.2E+
00
1.0E+
00
8.8E+
00
7.8E+
00
2
Benzene
SI
D
RUN2
CT
HE
HE
CT
2.0E­
02
4.5E­
02
4.0E­
02
6.2E­
02
5.5E­
02
3
Benzene
SI
F
RUN2
CT
HE
CT
HE
2.0E­
02
8.4E­
02
7.5E­
02
1.3E­
01
1.2E­
01
4
Benzene
SI
G
RUN2
CT
CT
HE
HE
2.0E­
02
2.7E­
01
2.4E­
01
1.7E+
00
1.5E+
00
5
Benzene
SI
B
RUN1
HE
HE
CT
CT
5.1E­
02
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
6
Benzene
SI
C
RUN1
HE
CT
HE
CT
5.1E­
02
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
7
Benzene
SI
E
RUN1
HE
CT
CT
HE
5.1E­
02
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
8
Benzene
SI
B
RUN3
HE
HE
CT
CT
2.3E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
9
Benzene
SI
C
RUN3
HE
CT
HE
CT
2.3E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
10
Benzene
SI
E
RUN3
HE
CT
CT
HE
2.3E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
11
Benzene
SI
B
RUN4
HE
HE
CT
CT
5.4E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
12
Benzene
SI
C
RUN4
HE
CT
HE
CT
5.4E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
13
Benzene
SI
E
RUN4
HE
CT
CT
HE
5.4E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
14
Benzene
SI
B
RUN5
HE
HE
CT
CT
3.1E­
02
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
15
Benzene
SI
C
RUN5
HE
CT
HE
CT
3.1E­
02
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
16
Benzene
SI
E
RUN5
HE
CT
CT
HE
3.1E­
02
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
20
Benzene
Tank
B
RUN1
HE
HE
CT
CT
5.9E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
21
Benzene
Tank
C
RUN1
HE
CT
HE
CT
5.9E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
22
Benzene
Tank
E
RUN1
HE
CT
CT
HE
5.9E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
23
Benzene
Tank
B
RUN3
HE
HE
CT
CT
9.8E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
24
Benzene
Tank
C
RUN3
HE
CT
HE
CT
9.8E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
(
continued)
C­
9
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
2.
(
continued)

25
Benzene
Tank
E
RUN3
HE
CT
CT
HE
9.8E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
26
Benzene
Tank
B
RUN5
HE
HE
CT
CT
3.8E­
02
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
27
Benzene
Tank
C
RUN5
HE
CT
HE
CT
3.8E­
02
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
28
Benzene
Tank
E
RUN5
HE
CT
CT
HE
3.8E­
02
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
29
Benzene
PrimClar
A
RUN7
CT
CT
CT
CT
9.6E­
01
1.2E+
00
1.0E+
00
8.8E+
00
7.8E+
00
30
Benzene
PrimClar
D
RUN7
CT
HE
HE
CT
9.6E­
01
4.5E­
02
4.0E­
02
6.2E­
02
5.5E­
02
31
Benzene
PrimClar
F
RUN7
CT
HE
CT
HE
9.6E­
01
8.4E­
02
7.5E­
02
1.3E­
01
1.2E­
01
32
Benzene
PrimClar
G
RUN7
CT
CT
HE
HE
9.6E­
01
2.7E­
01
2.4E­
01
1.7E+
00
1.5E+
00
33
Benzene
PrimClar
B
RUN8
HE
HE
CT
CT
9.7E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
34
Benzene
PrimClar
C
RUN8
HE
CT
HE
CT
9.7E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
35
Benzene
PrimClar
E
RUN8
HE
CT
CT
HE
9.7E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
36
Benzene
PrimClar
B
RUN9
HE
HE
CT
CT
9.6E­
01
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
37
Benzene
PrimClar
C
RUN9
HE
CT
HE
CT
9.6E­
01
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
38
Benzene
PrimClar
E
RUN9
HE
CT
CT
HE
9.6E­
01
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
55
Benzene
SecClar
A
RUN7
CT
CT
CT
CT
2.7E­
02
1.2E+
00
1.0E+
00
8.8E+
00
7.8E+
00
56
Benzene
SecClar
D
RUN7
CT
HE
HE
CT
2.7E­
02
4.5E­
02
4.0E­
02
6.2E­
02
5.5E­
02
57
Benzene
SecClar
F
RUN7
CT
HE
CT
HE
2.7E­
02
8.4E­
02
7.5E­
02
1.3E­
01
1.2E­
01
58
Benzene
SecClar
G
RUN7
CT
CT
HE
HE
2.7E­
02
2.7E­
01
2.4E­
01
1.7E+
00
1.5E+
00
59
Benzene
SecClar
B
RUN8
HE
HE
CT
CT
2.6E­
02
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
60
Benzene
SecClar
C
RUN8
HE
CT
HE
CT
2.6E­
02
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
61
Benzene
SecClar
E
RUN8
HE
CT
CT
HE
2.6E­
02
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
62
Benzene
SecClar
B
RUN9
HE
HE
CT
CT
5.7E­
02
1.3E­
01
1.2E­
01
2.1E­
01
1.8E­
01
63
Benzene
SecClar
C
RUN9
HE
CT
HE
CT
5.7E­
02
4.2E­
01
3.7E­
01
2.6E+
00
2.3E+
00
(
continued)
C­
10
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
2.
(
continued)

64
Benzene
SecClar
E
RUN9
HE
CT
CT
HE
5.7E­
02
7.5E­
01
6.7E­
01
5.6E+
00
5.0E+
00
89
Trichloroethane,
1,1,2­
SI
A
RUN2
CT
CT
CT
CT
2.4E­
02
7.9E­
01
5.1E­
01
7.2E+
00
4.7E+
00
90
Trichloroethane,
1,1,2­
SI
D
RUN2
CT
HE
HE
CT
2.4E­
02
2.7E­
02
1.8E­
02
4.3E­
02
2.7E­
02
91
Trichloroethane,
1,1,2­
SI
B
RUN1
HE
HE
CT
CT
5.1E­
02
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
92
Trichloroethane,
1,1,2­
SI
C
RUN1
HE
CT
HE
CT
5.1E­
02
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
93
Trichloroethane,
1,1,2­
SI
B
RUN3
HE
HE
CT
CT
2.4E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
94
Trichloroethane,
1,1,2­
SI
C
RUN3
HE
CT
HE
CT
2.4E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
95
Trichloroethane,
1,1,2­
SI
B
RUN4
HE
HE
CT
CT
6.2E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
96
Trichloroethane,
1,1,2­
SI
C
RUN4
HE
CT
HE
CT
6.2E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
97
Trichloroethane,
1,1,2­
SI
B
RUN5
HE
HE
CT
CT
3.1E­
02
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
98
Trichloroethane,
1,1,2­
SI
C
RUN5
HE
CT
HE
CT
3.1E­
02
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
101
Trichloroethane,
1,1,2­
Tank
B
RUN1
HE
HE
CT
CT
6.0E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
102
Trichloroethane,
1,1,2­
Tank
C
RUN1
HE
CT
HE
CT
6.0E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
103
Trichloroethane,
1,1,2­
Tank
B
RUN3
HE
HE
CT
CT
9.8E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
104
Trichloroethane,
1,1,2­
Tank
C
RUN3
HE
CT
HE
CT
9.8E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
105
Trichloroethane,
1,1,2­
Tank
B
RUN5
HE
HE
CT
CT
4.0E­
02
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
106
Trichloroethane,
1,1,2­
Tank
C
RUN5
HE
CT
HE
CT
4.0E­
02
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
107
Trichloroethane,
1,1,2­
PrimClar
A
RUN7
CT
CT
CT
CT
9.7E­
01
7.9E­
01
5.1E­
01
7.2E+
00
4.7E+
00
108
Trichloroethane,
1,1,2­
PrimClar
D
RUN7
CT
HE
HE
CT
9.7E­
01
2.7E­
02
1.8E­
02
4.3E­
02
2.7E­
02
109
Trichloroethane,
1,1,2­
PrimClar
B
RUN8
HE
HE
CT
CT
9.7E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
110
Trichloroethane,
1,1,2­
PrimClar
C
RUN8
HE
CT
HE
CT
9.7E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
111
Trichloroethane,
1,1,2­
PrimClar
B
RUN9
HE
HE
CT
CT
9.7E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
112
Trichloroethane,
1,1,2­
PrimClar
C
RUN9
HE
CT
HE
CT
9.7E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
(
continued)
C­
11
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Leachate
Conc
(
ppm)
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
2.
(
continued)

123
Trichloroethane,
1,1,2­
SecClar
A
RUN7
CT
CT
CT
CT
5.3E­
02
7.9E­
01
5.1E­
01
7.2E+
00
4.7E+
00
124
Trichloroethane,
1,1,2­
SecClar
D
RUN7
CT
HE
HE
CT
5.3E­
02
2.7E­
02
1.8E­
02
4.3E­
02
2.7E­
02
125
Trichloroethane,
1,1,2­
SecClar
B
RUN8
HE
HE
CT
CT
4.8E­
02
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
126
Trichloroethane,
1,1,2­
SecClar
C
RUN8
HE
CT
HE
CT
4.8E­
02
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
127
Trichloroethane,
1,1,2­
SecClar
B
RUN9
HE
HE
CT
CT
1.1E­
01
7.9E­
02
5.1E­
02
1.4E­
01
9.2E­
02
128
Trichloroethane,
1,1,2­
SecClar
C
RUN9
HE
CT
HE
CT
1.1E­
01
2.9E­
01
1.9E­
01
2.2E+
00
1.4E+
00
NA
=
not
applicable.
For
2­
ethoxyethanol,
only
values
for
HQ
=
1
were
calculated,
and
these
are
shown
in
Table
C­
1.
C­
12
Appendix
C
Detailed
Phase
II
Groundwater
Results
Table
C­
3.
Ratio
of
Leachate
Concentration
to
Adjusted
IWEM
Protective
Concentration
for
Risk
=
1E­
6
or
HQ
=
1
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
1
Benzene
SI
A
RUN2
CT
CT
CT
CT
1.7E­
01
1.9E­
01
2.2E­
02
2.5E­
02
2
Benzene
SI
D
RUN2
CT
HE
HE
CT
4.4E+
00
4.9E+
00
3.2E+
00
3.6E+
00
3
Benzene
SI
F
RUN2
CT
HE
CT
HE
2.3E+
00
2.6E+
00
1.5E+
00
1.7E+
00
4
Benzene
SI
G
RUN2
CT
CT
HE
HE
7.3E­
01
8.3E­
01
1.2E­
01
1.3E­
01
5
Benzene
SI
B
RUN1
HE
HE
CT
CT
3.8E+
00
4.3E+
00
2.4E+
00
2.8E+
00
6
Benzene
SI
C
RUN1
HE
CT
HE
CT
1.2E+
00
1.4E+
00
1.9E­
01
2.2E­
01
7
Benzene
SI
E
RUN1
HE
CT
CT
HE
6.7E­
01
7.6E­
01
9.0E­
02
1.0E­
01
8
Benzene
SI
B
RUN3
HE
HE
CT
CT
1.8E+
01
2.0E+
01
1.1E+
01
1.3E+
01
9
Benzene
SI
C
RUN3
HE
CT
HE
CT
5.5E+
00
6.3E+
00
8.8E­
01
1.0E+
00
10
Benzene
SI
E
RUN3
HE
CT
CT
HE
3.1E+
00
3.5E+
00
4.2E­
01
4.7E­
01
11
Benzene
SI
B
RUN4
HE
HE
CT
CT
4.1E+
01
4.7E+
01
2.6E+
01
3.0E+
01
12
Benzene
SI
C
RUN4
HE
CT
HE
CT
1.3E+
01
1.5E+
01
2.1E+
00
2.3E+
00
13
Benzene
SI
E
RUN4
HE
CT
CT
HE
7.2E+
00
8.1E+
00
9.7E­
01
1.1E+
00
14
Benzene
SI
B
RUN5
HE
HE
CT
CT
2.3E+
00
2.7E+
00
1.5E+
00
1.7E+
00
15
Benzene
SI
C
RUN5
HE
CT
HE
CT
7.3E­
01
8.3E­
01
1.2E­
01
1.3E­
01
16
Benzene
SI
E
RUN5
HE
CT
CT
HE
4.1E­
01
4.6E­
01
5.5E­
02
6.2E­
02
20
Benzene
Tank
B
RUN1
HE
HE
CT
CT
NA
NA
2.9E+
01
3.2E+
01
21
Benzene
Tank
C
RUN1
HE
CT
HE
CT
NA
NA
2.2E+
00
2.5E+
00
22
Benzene
Tank
E
RUN1
HE
CT
CT
HE
NA
NA
1.1E+
00
1.2E+
00
23
Benzene
Tank
B
RUN3
HE
HE
CT
CT
NA
NA
4.7E+
01
5.4E+
01
24
Benzene
Tank
C
RUN3
HE
CT
HE
CT
NA
NA
3.7E+
00
4.2E+
00
(
continued)
C­
13
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
3.
(
continued)

25
Benzene
Tank
E
RUN3
HE
CT
CT
HE
NA
NA
1.7E+
00
2.0E+
00
26
Benzene
Tank
B
RUN5
HE
HE
CT
CT
NA
NA
1.8E+
00
2.1E+
00
27
Benzene
Tank
C
RUN5
HE
CT
HE
CT
NA
NA
1.4E­
01
1.6E­
01
28
Benzene
Tank
E
RUN5
HE
CT
CT
HE
NA
NA
6.7E­
02
7.6E­
02
29
Benzene
PrimClar
A
RUN7
CT
CT
CT
CT
NA
NA
1.1E+
00
1.2E+
00
30
Benzene
PrimClar
D
RUN7
CT
HE
HE
CT
NA
NA
1.6E+
02
1.8E+
02
31
Benzene
PrimClar
F
RUN7
CT
HE
CT
HE
NA
NA
7.3E+
01
8.2E+
01
32
Benzene
PrimClar
G
RUN7
CT
CT
HE
HE
NA
NA
5.7E+
00
6.4E+
00
33
Benzene
PrimClar
B
RUN8
HE
HE
CT
CT
NA
NA
4.7E+
01
5.3E+
01
34
Benzene
PrimClar
C
RUN8
HE
CT
HE
CT
NA
NA
3.7E+
00
4.1E+
00
35
Benzene
PrimClar
E
RUN8
HE
CT
CT
HE
NA
NA
1.7E+
00
1.9E+
00
36
Benzene
PrimClar
B
RUN9
HE
HE
CT
CT
NA
NA
4.7E+
01
5.3E+
01
37
Benzene
PrimClar
C
RUN9
HE
CT
HE
CT
NA
NA
3.7E+
00
4.1E+
00
38
Benzene
PrimClar
E
RUN9
HE
CT
CT
HE
NA
NA
1.7E+
00
1.9E+
00
55
Benzene
SecClar
A
RUN7
CT
CT
CT
CT
2.3E­
01
2.6E­
01
3.0E­
02
3.4E­
02
56
Benzene
SecClar
D
RUN7
CT
HE
HE
CT
5.9E+
00
6.7E+
00
4.3E+
00
4.9E+
00
57
Benzene
SecClar
F
RUN7
CT
HE
CT
HE
3.2E+
00
3.6E+
00
2.0E+
00
2.3E+
00
58
Benzene
SecClar
G
RUN7
CT
CT
HE
HE
1.0E+
00
1.1E+
00
1.6E­
01
1.8E­
01
59
Benzene
SecClar
B
RUN8
HE
HE
CT
CT
1.9E+
00
2.2E+
00
1.2E+
00
1.4E+
00
60
Benzene
SecClar
C
RUN8
HE
CT
HE
CT
6.1E­
01
6.9E­
01
9.7E­
02
1.1E­
01
61
Benzene
SecClar
E
RUN8
HE
CT
CT
HE
3.4E­
01
3.8E­
01
4.6E­
02
5.1E­
02
62
Benzene
SecClar
B
RUN9
HE
HE
CT
CT
4.3E+
00
4.9E+
00
2.7E+
00
3.1E+
00
63
Benzene
SecClar
C
RUN9
HE
CT
HE
CT
1.3E+
00
1.5E+
00
2.1E­
01
2.4E­
01
(
continued)
C­
14
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
3.
(
continued)

64
Benzene
SecClar
E
RUN9
HE
CT
CT
HE
7.6E­
01
8.5E­
01
1.0E­
01
1.1E­
01
68
Ethoxyethanol,
2­
SI
A
RUN2
CT
CT
CT
CT
4.7E­
03
1.6E­
05
6.0E­
04
2.0E­
06
69
Ethoxyethanol,
2­
SI
B
RUN1
HE
HE
CT
CT
4.7E­
01
1.6E­
03
3.0E­
01
1.0E­
03
70
Ethoxyethanol,
2­
SI
B
RUN3
HE
HE
CT
CT
5.3E­
01
1.8E­
03
3.4E­
01
1.1E­
03
71
Ethoxyethanol,
2­
SI
B
RUN4
HE
HE
CT
CT
4.7E­
01
1.6E­
03
3.0E­
01
1.0E­
03
72
Ethoxyethanol,
2­
SI
B
RUN5
HE
HE
CT
CT
4.3E­
01
1.4E­
03
2.7E­
01
9.2E­
04
74
Ethoxyethanol,
2­
Tank
B
RUN1
HE
HE
CT
CT
NA
NA
3.5E­
01
1.2E­
03
75
Ethoxyethanol,
2­
Tank
B
RUN3
HE
HE
CT
CT
NA
NA
3.5E­
01
1.2E­
03
76
Ethoxyethanol,
2­
Tank
B
RUN5
HE
HE
CT
CT
NA
NA
3.4E­
01
1.1E­
03
77
Ethoxyethanol,
2­
PrimClar
A
RUN7
CT
CT
CT
CT
NA
NA
8.0E­
03
2.7E­
05
78
Ethoxyethanol,
2­
PrimClar
B
RUN8
HE
HE
CT
CT
NA
NA
3.5E­
01
1.2E­
03
79
Ethoxyethanol,
2­
PrimClar
B
RUN9
HE
HE
CT
CT
NA
NA
3.5E­
01
1.2E­
03
85
Ethoxyethanol,
2­
SecClar
A
RUN7
CT
CT
CT
CT
2.9E­
03
9.9E­
06
3.8E­
04
1.3E­
06
86
Ethoxyethanol,
2­
SecClar
B
RUN8
HE
HE
CT
CT
2.5E­
02
8.5E­
05
1.6E­
02
5.4E­
05
87
Ethoxyethanol,
2­
SecClar
B
RUN9
HE
HE
CT
CT
5.6E­
02
1.9E­
04
3.6E­
02
1.2E­
04
89
Trichloroethane,
1,1,2­
SI
A
RUN2
CT
CT
CT
CT
3.0E­
01
4.7E­
01
3.3E­
02
5.2E­
02
90
Trichloroethane,
1,1,2­
SI
D
RUN2
CT
HE
HE
CT
8.8E+
00
1.4E+
01
5.6E+
00
8.7E+
00
91
Trichloroethane,
1,1,2­
SI
B
RUN1
HE
HE
CT
CT
6.5E+
00
1.0E+
01
3.6E+
00
5.6E+
00
92
Trichloroethane,
1,1,2­
SI
C
RUN1
HE
CT
HE
CT
1.8E+
00
2.8E+
00
2.4E­
01
3.7E­
01
93
Trichloroethane,
1,1,2­
SI
B
RUN3
HE
HE
CT
CT
3.0E+
01
4.6E+
01
1.7E+
01
2.6E+
01
94
Trichloroethane,
1,1,2­
SI
C
RUN3
HE
CT
HE
CT
8.3E+
00
1.3E+
01
1.1E+
00
1.7E+
00
95
Trichloroethane,
1,1,2­
SI
B
RUN4
HE
HE
CT
CT
7.8E+
01
1.2E+
02
4.4E+
01
6.8E+
01
96
Trichloroethane,
1,1,2­
SI
C
RUN4
HE
CT
HE
CT
2.2E+
01
3.3E+
01
2.9E+
00
4.4E+
00
(
continued)
C­
15
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
6
or
HQ
=
1
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
3.
(
continued)

97
Trichloroethane,
1,1,2­
SI
B
RUN5
HE
HE
CT
CT
4.0E+
00
6.1E+
00
2.2E+
00
3.4E+
00
98
Trichloroethane,
1,1,2­
SI
C
RUN5
HE
CT
HE
CT
1.1E+
00
1.7E+
00
1.5E­
01
2.2E­
01
101
Trichloroethane,
1,1,2­
Tank
B
RUN1
HE
HE
CT
CT
NA
NA
4.2E+
01
6.5E+
01
102
Trichloroethane,
1,1,2­
Tank
C
RUN1
HE
CT
HE
CT
NA
NA
2.8E+
00
4.3E+
00
103
Trichloroethane,
1,1,2­
Tank
B
RUN3
HE
HE
CT
CT
NA
NA
6.9E+
01
1.1E+
02
104
Trichloroethane,
1,1,2­
Tank
C
RUN3
HE
CT
HE
CT
NA
NA
4.6E+
00
7.0E+
00
105
Trichloroethane,
1,1,2­
Tank
B
RUN5
HE
HE
CT
CT
NA
NA
2.8E+
00
4.3E+
00
106
Trichloroethane,
1,1,2­
Tank
C
RUN5
HE
CT
HE
CT
NA
NA
1.8E­
01
2.8E­
01
107
Trichloroethane,
1,1,2­
PrimClar
A
RUN7
CT
CT
CT
CT
NA
NA
1.3E+
00
2.1E+
00
108
Trichloroethane,
1,1,2­
PrimClar
D
RUN7
CT
HE
HE
CT
NA
NA
2.3E+
02
3.5E+
02
109
Trichloroethane,
1,1,2­
PrimClar
B
RUN8
HE
HE
CT
CT
NA
NA
6.9E+
01
1.1E+
02
110
Trichloroethane,
1,1,2­
PrimClar
C
RUN8
HE
CT
HE
CT
NA
NA
4.5E+
00
7.0E+
00
111
Trichloroethane,
1,1,2­
PrimClar
B
RUN9
HE
HE
CT
CT
NA
NA
6.8E+
01
1.1E+
02
112
Trichloroethane,
1,1,2­
PrimClar
C
RUN9
HE
CT
HE
CT
NA
NA
4.5E+
00
6.9E+
00
123
Trichloroethane,
1,1,2­
SecClar
A
RUN7
CT
CT
CT
CT
6.7E­
01
1.0E+
00
7.4E­
02
1.1E­
01
124
Trichloroethane,
1,1,2­
SecClar
D
RUN7
CT
HE
HE
CT
1.9E+
01
3.0E+
01
1.2E+
01
1.9E+
01
125
Trichloroethane,
1,1,2­
SecClar
B
RUN8
HE
HE
CT
CT
6.1E+
00
9.4E+
00
3.4E+
00
5.3E+
00
126
Trichloroethane,
1,1,2­
SecClar
C
RUN8
HE
CT
HE
CT
1.7E+
00
2.6E+
00
2.2E­
01
3.5E­
01
127
Trichloroethane,
1,1,2­
SecClar
B
RUN9
HE
HE
CT
CT
1.4E+
01
2.1E+
01
7.6E+
00
1.2E+
01
128
Trichloroethane,
1,1,2­
SecClar
C
RUN9
HE
CT
HE
CT
3.8E+
00
5.8E+
00
5.0E­
01
7.8E­
01
NA
=
not
applicable.
Values
are
NA
for
scenarios
that
were
not
evaluated
(
e.
g.,
leachate
from
tanks
or
primary
clarifiers).
C­
16
Appendix
C
Detailed
Phase
II
Groundwater
Results
Table
C­
4.
Ratio
of
Leachate
Concentration
to
Adjusted
IWEM
Protective
Concentration
for
Risk
=
1E­
5
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
1
Benzene
SI
A
RUN2
CT
CT
CT
CT
1.7E­
02
1.9E­
02
2.2E­
03
2.5E­
03
2
Benzene
SI
D
RUN2
CT
HE
HE
CT
4.4E­
01
4.9E­
01
3.2E­
01
3.6E­
01
3
Benzene
SI
F
RUN2
CT
HE
CT
HE
2.3E­
01
2.6E­
01
1.5E­
01
1.7E­
01
4
Benzene
SI
G
RUN2
CT
CT
HE
HE
7.3E­
02
8.3E­
02
1.2E­
02
1.3E­
02
5
Benzene
SI
B
RUN1
HE
HE
CT
CT
3.8E­
01
4.3E­
01
2.4E­
01
2.8E­
01
6
Benzene
SI
C
RUN1
HE
CT
HE
CT
1.2E­
01
1.4E­
01
1.9E­
02
2.2E­
02
7
Benzene
SI
E
RUN1
HE
CT
CT
HE
6.7E­
02
7.6E­
02
9.0E­
03
1.0E­
02
8
Benzene
SI
B
RUN3
HE
HE
CT
CT
1.8E+
00
2.0E+
00
1.1E+
00
1.3E+
00
9
Benzene
SI
C
RUN3
HE
CT
HE
CT
5.5E­
01
6.3E­
01
8.8E­
02
1.0E­
01
10
Benzene
SI
E
RUN3
HE
CT
CT
HE
3.1E­
01
3.5E­
01
4.2E­
02
4.7E­
02
11
Benzene
SI
B
RUN4
HE
HE
CT
CT
4.1E+
00
4.7E+
00
2.6E+
00
3.0E+
00
12
Benzene
SI
C
RUN4
HE
CT
HE
CT
1.3E+
00
1.5E+
00
2.1E­
01
2.3E­
01
13
Benzene
SI
E
RUN4
HE
CT
CT
HE
7.2E­
01
8.1E­
01
9.7E­
02
1.1E­
01
14
Benzene
SI
B
RUN5
HE
HE
CT
CT
2.3E­
01
2.7E­
01
1.5E­
01
1.7E­
01
15
Benzene
SI
C
RUN5
HE
CT
HE
CT
7.3E­
02
8.3E­
02
1.2E­
02
1.3E­
02
16
Benzene
SI
E
RUN5
HE
CT
CT
HE
4.1E­
02
4.6E­
02
5.5E­
03
6.2E­
03
20
Benzene
Tank
B
RUN1
HE
HE
CT
CT
NA
NA
2.9E+
00
3.2E+
00
21
Benzene
Tank
C
RUN1
HE
CT
HE
CT
NA
NA
2.2E­
01
2.5E­
01
22
Benzene
Tank
E
RUN1
HE
CT
CT
HE
NA
NA
1.1E­
01
1.2E­
01
23
Benzene
Tank
B
RUN3
HE
HE
CT
CT
NA
NA
4.7E+
00
5.4E+
00
(
continued)
C­
17
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
4.
(
continued)

24
Benzene
Tank
C
RUN3
HE
CT
HE
CT
NA
NA
3.7E­
01
4.2E­
01
25
Benzene
Tank
E
RUN3
HE
CT
CT
HE
NA
NA
1.7E­
01
2.0E­
01
26
Benzene
Tank
B
RUN5
HE
HE
CT
CT
NA
NA
1.8E­
01
2.1E­
01
27
Benzene
Tank
C
RUN5
HE
CT
HE
CT
NA
NA
1.4E­
02
1.6E­
02
28
Benzene
Tank
E
RUN5
HE
CT
CT
HE
NA
NA
6.7E­
03
7.6E­
03
29
Benzene
PrimClar
A
RUN7
CT
CT
CT
CT
NA
NA
1.1E­
01
1.2E­
01
30
Benzene
PrimClar
D
RUN7
CT
HE
HE
CT
NA
NA
1.6E+
01
1.8E+
01
31
Benzene
PrimClar
F
RUN7
CT
HE
CT
HE
NA
NA
7.3E+
00
8.2E+
00
32
Benzene
PrimClar
G
RUN7
CT
CT
HE
HE
NA
NA
5.7E­
01
6.4E­
01
33
Benzene
PrimClar
B
RUN8
HE
HE
CT
CT
NA
NA
4.7E+
00
5.3E+
00
34
Benzene
PrimClar
C
RUN8
HE
CT
HE
CT
NA
NA
3.7E­
01
4.1E­
01
35
Benzene
PrimClar
E
RUN8
HE
CT
CT
HE
NA
NA
1.7E­
01
1.9E­
01
36
Benzene
PrimClar
B
RUN9
HE
HE
CT
CT
NA
NA
4.7E+
00
5.3E+
00
37
Benzene
PrimClar
C
RUN9
HE
CT
HE
CT
NA
NA
3.7E­
01
4.1E­
01
38
Benzene
PrimClar
E
RUN9
HE
CT
CT
HE
NA
NA
1.7E­
01
1.9E­
01
55
Benzene
SecClar
A
RUN7
CT
CT
CT
CT
2.3E­
02
2.6E­
02
3.0E­
03
3.4E­
03
56
Benzene
SecClar
D
RUN7
CT
HE
HE
CT
5.9E­
01
6.7E­
01
4.3E­
01
4.9E­
01
57
Benzene
SecClar
F
RUN7
CT
HE
CT
HE
3.2E­
01
3.6E­
01
2.0E­
01
2.3E­
01
58
Benzene
SecClar
G
RUN7
CT
CT
HE
HE
1.0E­
01
1.1E­
01
1.6E­
02
1.8E­
02
59
Benzene
SecClar
B
RUN8
HE
HE
CT
CT
1.9E­
01
2.2E­
01
1.2E­
01
1.4E­
01
60
Benzene
SecClar
C
RUN8
HE
CT
HE
CT
6.1E­
02
6.9E­
02
9.7E­
03
1.1E­
02
61
Benzene
SecClar
E
RUN8
HE
CT
CT
HE
3.4E­
02
3.8E­
02
4.6E­
03
5.1E­
03
(
continued)
C­
18
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
4.
(
continued)

62
Benzene
SecClar
B
RUN9
HE
HE
CT
CT
4.3E­
01
4.9E­
01
2.7E­
01
3.1E­
01
63
Benzene
SecClar
C
RUN9
HE
CT
HE
CT
1.3E­
01
1.5E­
01
2.1E­
02
2.4E­
02
64
Benzene
SecClar
E
RUN9
HE
CT
CT
HE
7.6E­
02
8.5E­
02
1.0E­
02
1.1E­
02
89
Trichloroethane,
1,1,2­
SI
A
RUN2
CT
CT
CT
CT
3.0E­
02
4.7E­
02
3.3E­
03
5.2E­
03
90
Trichloroethane,
1,1,2­
SI
D
RUN2
CT
HE
HE
CT
8.8E­
01
1.4E+
00
5.6E­
01
8.7E­
01
91
Trichloroethane,
1,1,2­
SI
B
RUN1
HE
HE
CT
CT
6.5E­
01
1.0E+
00
3.6E­
01
5.6E­
01
92
Trichloroethane,
1,1,2­
SI
C
RUN1
HE
CT
HE
CT
1.8E­
01
2.8E­
01
2.4E­
02
3.7E­
02
93
Trichloroethane,
1,1,2­
SI
B
RUN3
HE
HE
CT
CT
3.0E+
00
4.6E+
00
1.7E+
00
2.6E+
00
94
Trichloroethane,
1,1,2­
SI
C
RUN3
HE
CT
HE
CT
8.3E­
01
1.3E+
00
1.1E­
01
1.7E­
01
95
Trichloroethane,
1,1,2­
SI
B
RUN4
HE
HE
CT
CT
7.8E+
00
1.2E+
01
4.4E+
00
6.8E+
00
96
Trichloroethane,
1,1,2­
SI
C
RUN4
HE
CT
HE
CT
2.2E+
00
3.3E+
00
2.9E­
01
4.4E­
01
97
Trichloroethane,
1,1,2­
SI
B
RUN5
HE
HE
CT
CT
4.0E­
01
6.1E­
01
2.2E­
01
3.4E­
01
98
Trichloroethane,
1,1,2­
SI
C
RUN5
HE
CT
HE
CT
1.1E­
01
1.7E­
01
1.5E­
02
2.2E­
02
101
Trichloroethane,
1,1,2­
Tank
B
RUN1
HE
HE
CT
CT
NA
NA
4.2E+
00
6.5E+
00
102
Trichloroethane,
1,1,2­
Tank
C
RUN1
HE
CT
HE
CT
NA
NA
2.8E­
01
4.3E­
01
103
Trichloroethane,
1,1,2­
Tank
B
RUN3
HE
HE
CT
CT
NA
NA
6.9E+
00
1.1E+
01
104
Trichloroethane,
1,1,2­
Tank
C
RUN3
HE
CT
HE
CT
NA
NA
4.6E­
01
7.0E­
01
105
Trichloroethane,
1,1,2­
Tank
B
RUN5
HE
HE
CT
CT
NA
NA
2.8E­
01
4.3E­
01
106
Trichloroethane,
1,1,2­
Tank
C
RUN5
HE
CT
HE
CT
NA
NA
1.8E­
02
2.8E­
02
107
Trichloroethane,
1,1,2­
PrimClar
A
RUN7
CT
CT
CT
CT
NA
NA
1.3E­
01
2.1E­
01
108
Trichloroethane,
1,1,2­
PrimClar
D
RUN7
CT
HE
HE
CT
NA
NA
2.3E+
01
3.5E+
01
109
Trichloroethane,
1,1,2­
PrimClar
B
RUN8
HE
HE
CT
CT
NA
NA
6.9E+
00
1.1E+
01
(
continued)
C­
19
Appendix
C
Detailed
Phase
II
Groundwater
Results
RunID
Chemical
WMU
Scenario
Water9
Run
High
End
Parameters
Risk
=
1E­
5
Leachate
from
WW
Unit
Sludge
in
Landfill
Source
Fate
Exp
Dose
Ingestion
Inhalation
Ingestion
Inhalation
Table
C­
4.
(
continued)

110
Trichloroethane,
1,1,2­
PrimClar
C
RUN8
HE
CT
HE
CT
NA
NA
4.5E­
01
7.0E­
01
111
Trichloroethane,
1,1,2­
PrimClar
B
RUN9
HE
HE
CT
CT
NA
NA
6.8E+
00
1.1E+
01
112
Trichloroethane,
1,1,2­
PrimClar
C
RUN9
HE
CT
HE
CT
NA
NA
4.5E­
01
6.9E­
01
123
Trichloroethane,
1,1,2­
SecClar
A
RUN7
CT
CT
CT
CT
6.7E­
02
1.0E­
01
7.4E­
03
1.1E­
02
124
Trichloroethane,
1,1,2­
SecClar
D
RUN7
CT
HE
HE
CT
1.9E+
00
3.0E+
00
1.2E+
00
1.9E+
00
125
Trichloroethane,
1,1,2­
SecClar
B
RUN8
HE
HE
CT
CT
6.1E­
01
9.4E­
01
3.4E­
01
5.3E­
01
126
Trichloroethane,
1,1,2­
SecClar
C
RUN8
HE
CT
HE
CT
1.7E­
01
2.6E­
01
2.2E­
02
3.5E­
02
127
Trichloroethane,
1,1,2­
SecClar
B
RUN9
HE
HE
CT
CT
1.4E+
00
2.1E+
00
7.6E­
01
1.2E+
00
128
Trichloroethane,
1,1,2­
SecClar
C
RUN9
HE
CT
HE
CT
3.8E­
01
5.8E­
01
5.0E­
02
7.8E­
02
NA
=
not
applicable.
Values
are
NA
for
scenarios
that
were
not
evaluated
(
e.
g.,
leachate
from
tanks
or
primary
clarifiers).

For
2­
ethoxyethanol,
only
values
for
HQ
=
1
were
calculated,
and
these
are
shown
in
Table
C­
3.