A­
1
Overview
_______________________________________________________________
2
Interpretation
of
Standards
________________________________________________
4
Lead
______________________________________________________________________
5
Organics
___________________________________________________________________
6
Source
Analysis
_________________________________________________________
7
Industrial
Discharges_________________________________________________________
7
Combined
Sewer
Overflows
(
CSOs)
____________________________________________
8
Storm
water
________________________________________________________________
9
Types
of
Storm
water
Permits
___________________________________________
9
Storm
water
Pb
data
__________________________________________________
11
Estimate
of
Annual
Lead
Load
__________________________________________
13
Storm
water
Organics
Data
____________________________________________
16
Groundwater
______________________________________________________________
18
Monitoring
Well
Results_______________________________________________
19
Pollutant
Loading
Estimates____________________________________________
20
Contaminated
Sites
_________________________________________________________
20
NuWay
Oil
Site______________________________________________________
24
St.
Johns
Landfill
____________________________________________________
27
Sediment
Partitioning
_______________________________________________________
28
Air
Deposition
_____________________________________________________________
30
Oregon
Steel:
_______________________________________________________
31
Spills
_____________________________________________________________________
35
Illicit
Discharges____________________________________________________________
35
Summary
of
Pb
Loads
_______________________________________________________
36
References
____________________________________________________________
38
A­
2
Sources
of
Toxics
to
the
Columbia
Slough
Overview
The
Columbia
Slough
is
on
DEQ's
1994/
1996
303(
d)
list
of
water
quality­
limited
waterbodies
for
the
following
chemicals:

 
DDT
and
metabolites
 
Dioxins
 
Lead
 
PCBs
Impairment
of
beneficial
uses
by
DDT
and
its
metabolites,
dioxin
and
PCBs
is
demonstrated
by
occurrence
in
fish
tissue.
Review
of
fish
tissue
data
indicates
that
dieldrin
is
also
present
at
elevated
levels.
Water
column
data
provides
evidence
of
impairment
by
lead.
Because
of
their
presence
on
the
303(
d)
list,
these
chemicals
will
be
referred
to
as
303(
d)
chemicals.
General
information
on
the
sources,
fate
and
transport
of
each
is
provided
below.

DDT
and
its
metabolites
4,4'­
DDT,
also
known
simply
as
DDT,
is
a
low­
cost
broad­
spectrum
insecticide
that
was
banned
in
the
U.
S.
in
1972
although
it
is
still
being
used
in
some
tropical
countries.
Over
time
DDT
breaks
down
to
form
DDE
and
DDD,
which
are
also
associated
with
toxicological
effects.
All
are
subject
to
photodegradation
or
redeposition
by
rain
or
dry
deposition,
and
are
widely
dispersed
by
erosion,
runoff
and
volatilization.
On
land,
they
preferentially
bind
to
soil
and
sediment.
In
water
they
are
subject
to
sedimentation,
volatilization,
photodegradation,
and
uptake
into
the
food
chain.
Release
of
these
compounds
to
water
is
primarily
via
transport
of
particulates
contained
in
runoff.
Both
DDT
and
DDE
bioaccumulate
in
organisms,
particularly
in
fatty
tissues,
and
levels
are
subject
to
increase
as
they
advance
up
the
food
chain.

Due
to
extensive
past
use
of
DDT
worldwide
and
the
persistence
of
DDT
and
its
metabolites,
these
materials
are
virtually
ubiquitous
in
the
environment,
and
have
been
detected
in
virtually
all
media.
They
are
continually
being
transformed
and
redistributed
in
the
environment
(
EPA
1993,
Meyer
1990,
U.
S.
Public
Health
Service
1988).

Dieldrin
Dieldrin
was
widely
used
in
the
United
States
from
1950
to
1974
as
a
broad
spectrum
pesticide,
primarily
on
termites
and
other
soil­
dwelling
insects
and
on
cotton,
corn,
and
citrus
crops.
It
is
a
metabolite
of
aldrin,
thus
the
environmental
concentrations
of
dieldrin
are
a
cumulative
result
of
the
historic
use
of
both
aldrin
and
dieldrin.
EPA
A­
3
banned
the
production
and
most
major
uses
of
dieldrin
in
1974,
and
in
1987
all
uses
of
dieldrin
were
voluntarily
canceled
by
industry.
Dieldrin
is
extremely
persistent
in
the
environment,
and
by
means
of
bioaccumulation
it
is
concentrated
many
times
as
it
moves
up
the
food
chain.
Its
persistence
is
due
to
its
extremely
low
volatility
and
low
solubility
in
water
resulting
in
a
high
affinity
for
fat
(
EPA
1993,
Meyer
1990).

Dioxins
Dioxins
are
a
family
of
compounds,
the
most
hazardous
of
which
is
2,3,7,8­
TCDD.
Dioxins
may
be
produced
as
a
byproduct
of
incomplete
combustion
whenever
chlorine
is
contained
in
the
fuel
source.
Some
specific
examples
of
sources
include
chlorinebleaching
pulp
mills,
municipal
and
medical
waste
incinerators,
secondary
smelters
which
recover
metal
from
waste
products
such
as
scrap
automobiles,
and
wood
treaters
using
pentachlorophenol.
Dioxins
are
also
found
in
sludges
at
major
municipal
wastewater
treatment
plants.
These
are
most
likely
from
industrial
sources
discharging
to
the
treatment
plants
since
the
temperatures
associated
with
sewage
treatment
processes
are
not
sufficient
to
produce
dioxins.
Dioxins
found
in
treatment
plant
sludges
may
also
have
been
conveyed
there
by
storm
water.

Dioxins
have
been
a
contaminant
in
a
number
of
compounds
formerly
manufactured
as
broad
spectrum
herbicides,
the
best
known
being
Agent
Orange.
The
association
of
dioxins
with
certain
herbicides
has
provided
a
route
of
entry
into
the
environment
through
the
use
of
those
herbicides
and
by
the
improper
disposal
of
chemical
wastes
associated
with
herbicide
production.
Because
2,3,7,8­
TCDD
is
an
extremely
stable
substance
that
begins
to
thermally
decompose
only
when
heated
to
its
boiling
point,
930
°
F,
and
because
it
readily
dissolves
in
fatty
tissues,
it
is
highly
persistent
in
the
food
chain
(
EPA
1991,
1992,1993,
1994,
Meyer
1990).

Lead
Historically,
lead
has
had
a
number
of
industrial
uses.
It
has
been
used
in
paints,
in
solder
and
as
a
gasoline
additive.
As
recently
as
the
mid­
1980s,
the
primary
source
of
lead
in
the
environment
was
the
combustion
of
gasoline;
however,
use
of
lead
in
U.
S.
gasoline
has
fallen
sharply
in
recent
years.
The
maximum
amount
of
lead
now
allowed
in
unleaded
gasoline
is
0.1
g/
gal.
Because
lead
has
been
associated
with
the
combustion
of
gasoline,
it
is
found
in
urban
runoff.
About
75%
of
houses
and
apartments
built
before
1978
in
the
United
States
contain
lead
paint,
which
may
also
contribute
to
the
lead
found
in
urban
runoff.
At
present,
lead
is
used
primarily
in
batteries,
electric
cable
coverings,
some
exterior
paints,
ammunition,
and
sound
barriers.
Currently,
the
major
points
of
entry
of
lead
into
the
environment
are
from
mining
and
smelting
operations,
and
from
fly
ash
resulting
from
coal
combustion
(
EPA
1993,
Meyer
1990,
Dennis
O'Neill,
Metro,
pers.
comm.
).
A­
4
PCBs
PCBs
were
once
used
extensively
by
industry
as
insulating
fluids
in
electrical
transformers
and
capacitors,
as
plasticizers,
as
lubricants,
as
fluids
in
vacuum
pumps
and
compressors,
and
as
heat
transfer
and
hydraulic
fluids.
They
were
never
intended
to
be
released
directly
into
the
environment.
Prior
to
1979,
the
disposal
of
PCBs
and
PCB­
containing
equipment
was
not
subject
to
federal
regulation,
and
approximately
1.25
billion
pounds
was
purchased
by
U.
S.
industry.
Their
production
and
use
in
the
United
States
were
banned
by
the
EPA
in
July
1979.
PCBs
are
extremely
persistent
in
the
environment
and
are
bioaccumulated
throughout
the
food
chain
(
EPA
1993,
Meyer
1990).

DDT
(
and
by
extension,
its
metabolites),
dieldrin
and
PCBs
have
been
banned
by
the
EPA.
Their
presence
in
the
Slough
environment
is
likely
the
result
of
past
practices.
The
same
is
true
to
a
lesser
extent
for
lead
and
dioxin.
Car
emissions
contain
less
lead
than
they
used
to
owing
to
the
increased
use
of
unleaded
gasoline,
and
dioxin
production
associated
with
pulp
and
paper
mills
has
been
reduced
in
recent
years.

The
sources
analyzed
in
this
document
include
the
following:

 
industrial
discharges
 
combined
sewer
overflows
 
municipal
storm
water
 
industrial
storm
water
 
groundwater
 
contaminated
sites
 
contaminated
sediment
 
air
deposition
 
spills
 
illicit
discharges
Additional
sources
may
include:
agriculture
activities,
sumps,
septic
tanks
and
illegal
dumping.
Data
is
not
currently
available
to
quantify
the
loads
from
theses
sources.
TMDLs
include
a
margin
of
safety
to
account
for
this
uncertainty,
and
monitoring
requirements
will
be
established
to
provide
data
needed
to
reduce
uncertainty.

Interpretation
of
Standards
Lead
appears
on
the
303(
d)
list
for
the
Columbia
Slough
because
it
is
detected
in
the
water
column
at
levels
which
exceed
the
OAR
Table
20
chronic
criteria
for
the
protection
of
freshwater
aquatic
life.
The
organic
chemicals
appear
on
the
list
because
they
are
detected
in
fish
tissue
at
levels
which
exceed
screening
values
developed
from
the
OAR
Table
20
criteria.
These
values
were
developed
for
the
protection
of
human
health
from
exposure
to
contaminated
fish.
A­
5
The
specific
application
of
standards
for
each
of
the
303(
d)
parameter
and
the
interpretation
of
data
for
evaluating
sources
is
discussed
in
the
following
sections.

Lead
When
interpreting
information
on
sources
of
lead
to
the
Columbia
Slough,
it
is
important
to
consider
both
the
dissolved
and
total
lead
concentrations.
Lead
can
be
present
in
the
water
column
in
both
forms,
with
the
solid
form
being
adsorbed
onto
sediment
particles
in
the
water
column.
The
ratio
of
the
sorbed
to
dissolved
concentration
is
known
as
the
partition
coefficient
and
it
varies
with
the
presence
of
suspended
solids
according
to
the
following
equation
(
EPA
TMDL):

Kp
=
Cp/
SS
Cd
where
Kp
=
partitioning
coefficient
Cp
=
concentration
of
solids
Cd
=
concentration
in
solution
SS
=
suspended
solids
concentration
Because
lead
in
the
solid
form
adsorbs
onto
sediment
particles,
total
lead
levels
will
generally
be
higher
in
a
water
column
characterized
by
high
suspended
solids.
As
settling
occurs,
or
as
TSS
levels
in
the
water
column
otherwise
become
diluted,
lead
that
was
formerly
adsorbed
onto
particulate
matter
in
the
water
column
may
partition
into
the
dissolved
form.
Therefore
it
is
important
to
consider
both
total
lead
and
dissolved
lead
concentrations
when
evaluating
sources
of
lead
to
the
Slough.

When
total
lead
data
is
available
and
appropriate
partitioning
equations
are
available,
dissolved
lead
concentrations
can
be
calculated.
However,
to
develop
the
partitioning
coefficient
for
the
Columbia
Slough
lower
detection
limits
for
total
lead
are
needed.
For
this
reason,
dissolved
lead
values
are
evaluated
to
determine
compliance
with
the
chronic
criteria
for
the
protection
of
aquatic
life.
The
City
of
Portland
Bureau
of
Environmental
Services
(
BES)
has
collected
296
dissolved
Pb
and
hardness
samples
from
all
reaches
of
the
Slough,
throughout
all
seasons.

The
chronic
criteria
is
defined
as
the
four
day
average
concentration
not
to
be
exceeded
once
every
three
years.
There
is
insufficient
data
with
which
to
calculate
4
day
averages
directly,
so
the
existing
data
is
compared
directly
to
the
criteria.
Using
the
hardness
measured
with
each
sample,
a
total
lead
criteria
is
calculated
according
to
the
following
equation:

total
lead
criteria
(
Table
20)
=
e
(
1.273[
ln(
hardness)]­
4.705)

(
EPA
1986)
A­
6
EPA
recommends
the
use
of
the
dissolved
metal
criteria.
Total
metal
criteria
can
be
converted
to
a
dissolved
metal
criteria
via
the
use
of
a
conversion
factor
(
CF).
The
equation
for
Pb
is
as
follows:

CF
=
1.46203
­
[
ln(
hardness)(
0.145712)
(
EPA
1996).

Using
these
equations,
a
criteria
was
calculated
for
each
hardness
and
dissolved
Pb
sample.
From
the
frequency
distribution
of
the
criteria
the
5th
percentile
criteria
was
calculated
to
be
0.0012
mg/
L
dissolved
Pb.
The
5th
percentile
represents
a
"
worst
case"
assumption
(
EPA,
1995).

Figure
1:
dissolved
Pb
criteria
Dissolved
Pb
criteria,
frequency
distribution
0
10
20
30
40
50
60
0.0
01
0.0012
0.0014
0.0016
0.0018
0.002
0.0022
0.0024
0.0026
0.0028
0.003
Mo
r
e
frequency
0
20
40
60
80
100
120
Cumulative
frequency
Organics
The
303(
d)
list
organic
chemicals
are
detected
in
fish
tissue
rather
than
in
the
water
column.
The
appearance
of
these
organics
in
fish
tissue
is
the
result
of
bioconcentration
and
biomagnification.
Bioconcentration
is
the
term
used
to
describe
the
uptake
and
retention
of
pollutants
directly
from
the
water
mass
by
organisms,
through
tissues
such
as
the
gills
or
epithelial
tissues.
Biomagnification
is
the
process
whereby
pollutants
are
passed
from
one
trophic
level
to
another
and
exhibit
increasing
concentrations
in
organisms
related
to
their
trophic
status
(
Connell,
1984).

There
is
insufficient
information
at
present
to
allow
the
development
of
a
quantitative
relationship
between
water
column
concentrations
in
the
Columbia
Slough
and
concentrations
of
organics
in
fish
tissue.
Therefore,
for
this
phase
of
the
TMDL
process
it
will
be
assumed
that
if
the
OAR
Table
20
chronic
criteria
for
the
protection
of
aquatic
life
are
not
violated,
then
fish
tissue
concentrations
will
also
be
below
levels
necessary
to
demonstrate
impairment
of
beneficial
uses.
A­
7
Source
Analysis
Industrial
Discharges
Lead
is
the
only
303(
d)
chemical
which
is
monitored
as
a
requirement
under
industrial
discharge
permits
issued
in
the
Slough
watershed.

There
are
27
permitted
non
storm
water
industrial
discharges
to
the
Columbia
Slough.
Of
these,
22
have
general
permits
and
5
individual
permits.
General
permits
apply
to
industrial
categories
that
can
meet
the
general
conditions
assumed
to
cause
negligible
degradation
of
water
quality.

Table
1
contains
a
summary
of
the
active
industrial
in
the
Columbia
Slough
watershed.
Information
on
what
is
monitored
under
the
various
types
of
discharge
permits
is
included
for
completeness.

Table
1
Summary
of
General
Permits
for
Industrial
Discharges
to
the
Columbia
Slough
Permit
Type
Expiration
Date
Description
Parameters
Reported1
No.
of
Active
Permits
GEN01
7/
31/
2001
cooling
water/
heat
pumps
flow,
temperature,
pH,
chlorine
8
GEN02
12/
31/
1995
filter
backwash
settleable
solids,
pH
2
GEN13
12/
31/
1999
oily
storm
water
runoff
flow,
oil
and
grease,
oxygenated
fuel
additives
(
ethanol
and/
or
methyl­
t­
butyl
ether)
2
GEN15
6/
30/
2000
petroleum
hydrocarbons
cleanup
flow,
pH,
total
petroleum
hydrocarbons,
benzene,
BETX2,
lead3
4
GEN17
12/
31/
1997
vehicle
wash
water
pH
and
oil
&
grease
OR
pH,
arsenic,
chromium
VI,
copper,
lead,
zinc4
3
total
number
of
general
permits:
22
1All
metals
are
measured
as
total.
Requirements
to
measure
the
dissolved
portion
are
not
currently
in
place.
2BETX
stands
for
benzene,
ethylbenzene,
toluene
and
xylene.
3Monitoring
for
lead
is
not
required
for
all
permit
holders.
4The
latter
set
of
parameters
applies
to
cleaning
operations
using
strong
acids,
caustics,
or
other
metal
brighteners.
None
of
the
current
permit
holders
fall
into
this
category.

Only
the
GEN15
(
petroleum
hydrocarbons
cleanup)
and
GEN17
(
vehicle
wash
water)
permits
currently
require
monitoring
for
lead,
and
then
only
under
certain
circumstances.
Under
the
GEN15
permit,
ongoing
monitoring
for
lead
is
required
when
detectable
levels
of
lead
have
been
found
in
the
influent
to
the
treatment
system.
Under
the
GEN17
permit,
monitoring
is
required
for
those
facilities
that
have
cleaning
operations
using
strong
acids,
caustics,
or
other
metal
brighteners.
None
of
the
3
discharges
indicated
in
Table
2
fall
into
this
category,
therefore
they
are
exempt
from
monitoring
for
lead.

It
should
be
noted
that
while
monitoring
for
lead
can
be
required
under
these
permits,
the
permits
do
not
currently
contain
actual
limits
for
lead.
The
intent
of
the
monitoring
requirements
is
simply
to
collect
data
for
one
permit
cycle
and
then
the
need
for
an
A­
8
effluent
limit
will
be
evaluated
as
these
general
permits
come
up
for
renewal.
At
this
time,
it
is
anticipated
that
when
the
GEN17
permit
is
renewed
it
will
contain
permit
limits
for
lead.
Additional
detail
on
the
GEN15
permit
holders
discharging
to
the
Columbia
Slough
is
summarized
in
Table
2.

Table
2
Summary
of
GEN15A
Permits
in
the
Columbia
Slough
Watershed
Permit
Holder
Location
Comments
Case
Corporation
1745
NE
Columbia
Blvd.,
Portland
Site
is
impacted
by
gasoline
and
diesel.
No
lead
has
been
detected
at
this
site,
therefore
monitoring
for
lead
is
not
required1.

General
Motors
Corporation
9225
NE
Airport
Way,
Portland
This
facility
discharged
about
1
gpm
from
10/
95
to
10/
96.
100
ppb
of
total
lead
was
detected
in
one
of
the
on­
site
wells.
Jubitz
Truck
Stop
10210
N.
Vancouver
Way,
Portland
This
cleanup
site
involves
a
diesel
fuel
discharge
only.

Unocal
Station
#
6139
985
E.
Burnside
Street,
Gresham
Involves
a
diesel
fuel
discharge
only,
therefore
monitoring
for
lead
is
not
required.

1Don
Pettit,
DEQ,
pers.
comm.

Using
the
Pb
concentration
associated
with
the
discharge
that
existed
between
10/
95
and
10/
96,
an
annual
Pb
load
can
be
calculated
as
follows:

100
ug/
l
x
1
gpm
x
3.79
l/
gal
x
1400
min/
day
365
days/
yr
x
1
kg/
109
ug
=
0.19
kg/
yr
=
5x
10­
4
kg/
day
All
of
the
5
individual
permits
are
classified
as
minor
discharges
(
less
than
1
million
gallons
per
day)
and
none
require
monitoring
for
303(
d)
parameters.
Two
are
for
treated
groundwater,
and
require
testing
for
volatile
organic
compounds.
Both
of
these
permits
are
currently
under
review,
and
monitoring
requirements
may
be
expanded.
Two
more
of
the
5
discharges
go
to
the
City
of
Portland's
municipal
storm
water
system,
and
they
are
being
rerouted
to
the
City's
sanitary
system
(
Michael
Pronold,
BES,
pers.
comm.).

Combined
Sewer
Overflows
(
CSOs)

There
are
13
CSO
outfalls
located
on
the
Lower
Slough.
The
CSOs
are
currently
regulated
under
the
NPDES
program
as
well
as
an
Amended
Stipulation
and
Final
Order
(
ASFO)
which
the
Department
and
the
City
of
Portland
entered
into
in
1994.
Under
the
terms
of
the
ASFO,
the
CSOs
are
to
be
effectively
removed
from
the
Columbia
Slough
by
A­
9
December
1,
2000.
Because
the
justification
for
removing
CSOs
has
been
based
on
the
quantities
of
bacteria
they
discharge,
and
because
a
schedule
has
been
developed
for
CSO
removal,
little
monitoring
has
been
done
that
would
help
quantify
non­
bacterial
pollutant
loads
associated
with
CSOs.

In
April
of
1991,
samples
were
collected
from
one
CSO
outfall
to
the
Columbia
Slough.
Information
on
the
outfall
is
summarized
below.

Table
3
Monitored
Combined
Sewer
Overflow
Data
(
BES
1992)

Basin
Receiving
Stream
Size
(
acres)
Predominan
t
Land
Use
%
Impervio
us
Surface
Total
Pb
Vancouver
Columbia
Slough
255
residential
45
24.4
ug/
L
Monitoring
did
not
include
hardness
or
dissolved
lead
concentrations.
The
total
lead
value
exceeds
the
chronic
criteria
for
dissolved
lead
(=
1.2
ug/
l,)
by
a
substantial
margin.

Although
there
were
no
detects
of
DDT
and
its
metabolites,
dieldrin
or
PCBs
in
the
CSO
effluent,
the
detection
limits
for
all
of
these
chemicals
were
above
the
chronic
criteria
.
Since
sampling
of
these
chemicals
has
not
been
extensive
and
detection
limits
have
been
high,
it
cannot
be
concluded
that
they
are
not
present
in
any
quantities
in
CSOs
No
information
is
available
with
which
to
estimate
dioxin
loads
to
the
Slough.

In
addition
to
sampling
results
for
CSO
effluent,
modeling
of
CSO
pollutant
levels
has
been
done
by
OTAK
as
part
of
the
CSO
Management
Plan.
Results
of
this
modeling
estimate
the
annual
loading
rate
of
lead
to
the
Slough
to
be
149
lbs/
yr
(
BES
1993).
This
is
very
close
to
the
value
of
185
lb
provided
by
CH2MHill
in
the
Waterbody
Assessment,
Part
II
(
CH2MHill
1995).
An
average
of
these
values,
or
167
lbs/
yr
(
75.7
kg/
yr)
is
used
as
the
estimated
annual
total
lead
load
from
CSOs.

Storm
water
Types
of
Storm
water
Permits
Two
types
of
permits
are
issued
for
the
control
of
storm
water:
municipal
permits
and
industrial
permits.
In
addition,
in
a
few
cases,
NPDES
permits
issued
for
the
control
of
process
wastewater
have
been
modified
to
contain
storm
water
requirements.

Municipal
Separate
Storm
Sewer
System
(
MS4)
permits,
also
known
as
municipal
permits,
are
issued
to
municipalities,
drainage
districts
and
other
entities
with
jurisdiction
A­
10
over
separate
storm
sewer
systems
in
metropolitan
urban
areas.
MS4
permits
can
have
several
co­
applicants,
each
of
whom
will
be
responsible
for
some
portion
of
the
permitted
area.
Two
municipal
permits
have
been
issued
for
the
Columbia
Slough
watershed
and
will
be
referred
to
as
either
the
Portland
MS4
permit
or
the
Gresham
MS4
permit.

The
Portland
MS4
permit
holders
are
as
follows:

 
City
of
Portland
 
Multnomah
County
 
Port
of
Portland
 
Oregon
Department
of
Transportation
 
Multnomah
Drainage
District
#
1
 
Peninsula
Drainage
District
#
1
 
Peninsula
Drainage
District
#
2
The
Gresham
MS4
permit
holders
are
as
follows:

 
City
of
Gresham
 
City
of
Fairview
 
Multnomah
County
 
Oregon
Department
of
Transportation
Both
permits
were
issued
by
DEQ
on
September
7,
1995.
The
areas
covered
by
the
two
permits
are
summarized
below.

Table
4
Areas
Covered
by
MS4
Permits
in
the
Columbia
Slough
Watershed
Permit
Holder
Permit
Area
(
acres)
Col.
Sl.
Area
(
acres)
%
of
Col.
Sl.
Watershed
Source
of
Information
Portland
et
al
44,307
16,971
81%
MS4
Permit
App.,
Table
3­
37
Gresham
et
al
38,310
3,860
19%
MS4
Permit
App.,
Tables
5­
4
totals:
82,617
20,831
100%

Monitoring
requirements
for
MS4
permit
holders
are
described
in
the
MS4
permit
applications.
To
summarize,
catchments
representative
of
particular
land
uses
(
for
example,
commercial,
industrial,
or
residential)
are
monitored
during
3
winter
storm
events
and
one
summer
storm
event.
Parameters
measured
include
conventional
pollutants
as
well
as
metals.
The
1996
annual
reports
for
both
MS4
permits
issued
in
the
Slough
watershed
contain
the
results
of
all
monitoring
performed
since
1991.
A­
11
Industrial
storm
water
permits,
which
are
also
known
as
general
permits,
are
issued
for
particular
categories
of
activities
or
facilities,
such
as
construction
sites
or
metal
scrap
yards.
Whether
or
not
a
particular
industrial
activity
needs
a
permit
will
depend
on
its
SIC
(
Standard
Industrial
Classification)
code.
Monitoring
requirements
vary
by
permit
type,
but
generally
include
pH,
oil
and
grease,
BOD,
TSS
and
metals.
Metals
include
arsenic,
cadmium,
chromium,
copper,
iron,
lead,
manganese,
mercury,
nickel,
and
zinc.
Only
total
metal
concentrations
are
measured.

Storm
water
Pb
data
The
following
table
summarizes
the
extent
of
storm
water
monitoring
for
lead.

Table
5
Extent
of
Storm
water
Monitoring
for
Lead
Portland
MS4
Gresham
MS4
Industria
l
No.
of
Monitoring
Stations
10
4
741
No.
of
Storm
Events
Monitored
18
3
2/
yr
No.
samples
analyzed
for
total
lead
119
11
466
No.
samples
analyzed
for
dissolved
lead
119
none
none
No.
samples
analyzed
for
hardness
111
none
none
1Each
permit
holder
is
required
to
monitor
one
site.

Monitoring
under
the
Gresham
MS4
permit
and
the
industrial
permits
did
not
include
dissolved
lead.
These
results
can
be
converted
to
dissolved
lead
by
using
the
following
equation
that
gives
total
lead
in
terms
of
the
percentage
of
dissolved
lead.
This
equation
was
developed
from
data
collected
under
the
Portland
MS4
permit
(
DEQ,
1996.):

Pbdiss/
Pbtot
=
3.036
x
TSS^­
0.7846
(
eq.
1)
A­
12
Monitoring
results
for
municipal
and
industrial
storm
water
are
shown
below,
along
with
the
results
of
calculations
using
equation
(
1).

Table
6
Monitoring
Results
for
Lead
Portland
MS4
Gresham
MS4
Industrial
No.
Detects
(
rate,
%)
Total
Lead
118
(
99%)
11
(
100%)
425
(
100%)
Dissolved
Lead
79
(
66%)
not
analyzed
not
analyzed
Maximum
Total
Lead
0.290
0.031
7.001
Dissolved
Lead
0.100
N/
A
N/
A
Minimum
Concentration
Total
Lead
0.001
0.004
0.001
Dissolved
Lead
0.001
N/
A
N/
A
Mean
Total
Lead
0.048
0.023
0.112
Dissolved
Lead
0.005
N/
A
N/
A
Median
Total
Lead
0.029
0.009
0.023
Dissolved
Lead
0.003
N/
A
N/
A
1This
value
may
be
an
outlier.
The
next
highest
value
is
2.67
mg/
l.

Figure
2
shows
the
frequency
distributions
for
total
Pb
data
collected
by
the
MS4
and
industrial
permit
holders.
A­
13
Figure
2
Total
Pb
frequency
distribution
As
can
be
seen
from
Figure
2,
the
frequency
distributions
for
the
3
datasets
vary
markedly.
In
particular,
concentrations
associated
with
industrial
permits
are
significantly
higher
than
concentrations
associated
with
MS4
permits.

Estimate
of
Annual
Lead
Load
MS4
Pb
load
The
MS4
permit
applications
summarize
storm
water
loading
information
for
a
statistically
average
year.
The
following
table
summarizes
the
estimated
annual
Pb
load
to
the
Columbia
Slough.
Comparison
of
Frequency
Distributions
of
Total
Lead
Data
Note:
the
top
tw
o
values
for
the
industrial
permits
have
been
deleted
to
make
the
graph
more
readable.
The
values
are
7
mg/
l
and
2.67
mg/
l.

0
0.2
0.4
0.6
0.8
1
1.2
1.4
0.00
20.00
40.00
60.00
80.00
100.00
120.00
Frequency
Total
Lead
Concentration
(
mg/
l)
Gresham
MS4
Portland
MS4
Industrial
Permits
A­
14
Table
7
Summary
of
Total
Lead
Loads
As
Estimated
in
MS4
Annual
Reports
Permit
Holder
Columbia
Slough
(
lbs/
yr)
Entire
Permit
Area
(
lbs/
yr)
Source
of
Information
Portland
et
al
2196
(
est.)
(
996
kg/
yr)
4274
(
1939
kg/
yr)
Annual
Compliance
Report,
Section
VIII
Monitoring
Program,
Table
4­
7
Gresham
et
al
298
(
135
kg/
yr)
1,592
(
722
kg/
yr)
NPDES
MS4
Permit
No.
101315
Annual
Report,
Table
3­
8
A
specific
lead
load
to
the
Columbia
Slough
is
not
contained
in
the
Annual
Report
for
the
Portland
MS4
permit,
however
an
estimate
was
arrived
at
based
on
information
contained
in
the
permit
application.
The
permit
application
states
that
the
lead
load
from
the
entire
permit
area
is
4,640
lbs/
yr,
of
which
2387
lbs/
yr
is
discharged
to
the
Slough
(
Table
3­
37
of
the
permit
application).
In
the
1996
Annual
Compliance
Report,
the
lead
load
from
the
entire
permit
area
was
adjusted
to
4,274
lbs/
yr,
a
reduction
of
8%.
This
correction
yields
a
total
lead
load
to
the
Slough
from
the
area
covered
by
the
Portland
MS4
of
2196
lbs/
yr
(=
92%
of
2387
lbs/
yr).
The
lead
load
is
estimated
as
298
lb/
year
in
the
Gresham
permit
application.
The
estimate
is
based
on
an
event
mean
concentration
of
0.02
mg/
l
and
an
annual
runoff
volume
of
5,474
acre­
ft
per
year.
Combining
the
total
lead
load
from
both
permits,
an
annual
estimate
of
2494
lbs/
yr
(
1131
kg/
yr)
is
obtained.

This
is
very
close
to
the
modeled
total
lead
load
to
the
Columbia
Slough
reported
in
the
Waterbody
Assessment,
Part
II,
done
by
CH2MHill
in
1995.
The
total
value
obtained
from
Figures
6­
19,
20
and
21
is
2463.5
lbs/
yr.

Breakdown
by
Land
Use
The
Portland
MS4
permit
application
breaks
down
the
contributions
of
lead
by
land
use.
These
results
are
summarized
below.
It
should
be
noted
that
these
numbers
do
not
describe
the
watershed
as
a
whole,
since
the
Portland
MS4
only
covers
about
80%
of
the
total
watershed.
They
also
do
not
reflect
the
modifications
that
have
been
made
to
the
pollutant
loading
model
upon
which
the
MS4
permit
application
is
based.
This
table
is
intended
to
give
a
general
sense
of
the
relative
contributions
from
different
land
uses.
A­
15
Table
8
Lead
Loads
Associated
with
Various
Land
Uses
for
the
Portland
MS4
Permit
Area
Draining
to
the
Columbia
Slough
Land
Use
Category
Area
(
acres)
%
of
Total
Lead
Load
(
lbs/
yr)
%
of
Total
Residential
(
light)
1541.5
9
124.1
5
Residential
(
heavy)
171.8
1
22
1
Industrial
2322.6
14
724.8
30
Commercial
2827.7
17
1370.2
58
Parks
&
Open
Space
2303.5
14
7.6
0
Vacant
7220.3
43
24
1
Traffic
Corridor
379.5
3
110.4
5
totals:
16766.9
100
2383.1
100
Source:
Portland
MS4
permit
application,
Tables
B­
1
and
C­
1.

Industrial
Pb
Load
The
contribution
of
lead
from
permitted
industrial
sites
can
be
calculated
using
the
following
equation
(
EPA
1992):

Area
x
Annual
Rainfall
x
Runoff
Coefficient
x
Pollutant
Concentration
=
Annual
Pollutant
Load
The
annual
rainfall
for
the
watershed
is
given
in
Table
3­
12
of
the
Portland
MS4
permit
application
as
34.3
inches
per
year,
and
the
runoff
coefficient
for
industrial
areas
is
given
in
Table
3­
13
as
0.68.

A
search
of
the
files
for
general
storm
water
permits
resulted
in
areas
for
52
of
the
sites.
If
the
permit
area
associated
with
the
Port
of
Portland
is
excluded
because
the
Port
of
Portland
is
a
co­
applicant
of
the
Portland
MS4
permit,
the
total
area
associated
with
industrial
permits,
not
counting
those
issued
for
construction
projects,
is
977
acres.
This
calculation
assumes
that
the
area
represents
100%
of
the
facilities
that
require
industrial
storm
water
permits.

The
pollutant
load
associated
with
the
areas
that
are
currently
covered
by
general
industrial
permits
can
be
estimated
using
an
event
mean
concentration
for
industrial
areas.
The
mean
pollutant
concentration
reported
in
Table
3­
14
of
the
Portland
MS4
permit
application
is
0.059
mg/
l.
The
Gresham
MS4
permit
application
contains
monitoring
results
from
a
residential
area
and
an
area
that
is
half
industrial
and
half
residential,
and
A­
16
these
suggest
that
the
concentration
associated
with
industrial
areas
is
0.06
mg/
l.
For
this
phase
of
the
TMDL
process,
a
value
of
0.06
mg/
l
will
be
used
to
approximate
the
concentration
of
lead
found
in
runoff
from
industrial
areas.

Using
the
above
estimates,
the
annual
lead
load
associated
with
the
permitted
industrial
area
can
be
calculated
as
follows:

977
acres
x
34.3
inches/
yr
x
0.68
x
0.06
mg/
l
total
Pb
x
43560
sq.
ft/
acre
x
1
ft/
12
in
x
28.317
l/
cu
ft
x
1
kg/
106
mg
=
141
kg/
yr
Storm
water
Organics
Data
Monitoring
for
the
303(
d)
organics
has
been
conducted
primarily
by
the
DMAs
for
the
MS4
permits
and
the
St.
John's
landfill
closure.
There
are
currently
no
non
storm
water
discharges
of
303(
d)
organics
from
industrial
sources
to
the
Slough.
Monitoring
under
industrial
storm
water
permits
focuses
primarily
on
metals,
so
no
data
are
available
from
these
permittees
for
organic
pollutants.
Monitoring
under
the
municipal
permits
is
more
extensive.
Under
the
Gresham
MS4
permit,
testing
for
DDD,
DDE,
DDT,
dieldrin
and
PCBs
is
limited
to
one
storm
event
during
which
samples
were
collected
at
4
different
locations.
Dioxin
was
not
monitored.
There
were
no
detects
of
these
pollutants1
(
City
of
Gresham,
May
1993).
Monitoring
for
the
Portland
MS4
permit
includes
28
samples,
with
5
samples
above
the
detection
limit.
All
analyses
had
detection
limits
above
the
OAR
Table
20
criteria.
Results
are
presented
below:

Table
9:
Detects
of
303(
d)
Organics
in
Storm
water
Parameter
Land
Use
Concentration
(
det.
limit)
mg/
l
4,4'­
DDT
Residential
0.09
(
0.07)
4,4'­
DDT
Mixed
0.7
(
0.4)
4,4'­
DDE
Residential
0.04
(
0.04)
4,4'­
DDE
Mixed
0.15
(
0.1)
dieldrin
Mixed
0.1
(
0.1)

There
have
so
far
been
no
detects
of
PCBs
in
storm
water
monitored
under
the
Portland
MS4
permit.
The
detection
limits
for
PCBs
ranged
from
0.3
to
3.0
ug/
L.
As
part
of
the
Columbia
Slough
Sediment
Remediation
Project,
additional
monitoring
has
been
conducted
in
storm
water
pipes
draining
to
Buffalo
Slough.

1
detection
limits
were:
DDD
=
1.0
ug/
L,
DDE
=
0.5
ug/
L,
DDT
=
0.5
ug/
L,
dieldrin
=
0.5
ug/
L,
Aroclor
1221
=
3.0
ug/
L,
all
other
aroclor
=
1.0
ug/
L
A­
17
Sampling
occurred
during
dry
event
and
storm
event.
The
dry
event
sediment
samples
were
collected
in
mid
summer
when
no
storm
water
flows
were
present.
Sediment
sample
SW­
3
was
collected
and
composited
from
the
two
storm
water
catch
basins
that
discharge
into
the
storm
water
pipe.
These
results
are
summarized
in
Table
10.

Table
10:
Dry
Weather
Sediment
Sampling
Results
(
ug/
kg)
2
(
BES,
May
1997)

Parameter
SW­
3
dieldrin
2.92
(.
10)
DDE
14.20
(.
08)
DDD
ND
(.
07)
DDT
ND
(.
11)
PCBs
35.40
(
6.84)

The
storm
water
samples
were
collected
in
October
when
conditions
met
the
requirements
of
a
representative
storm
(
BES,
May
1997).
These
samples
were
collected
in
manholes
(
SW­
1,
SW­
2
and
SW­
6)
or
a
catch
basin
(
SW­
3)
above
the
outfalls.
There
was
no
receiving
water
inflow
in
these
samples
(
Chris
Prescott,
BES,
personal
communication,
1998).
Detection
limits
for
storm
water
were
on
the
order
of
1
ng/
l.
Typical
detection
limits
for
storm
water
are
1000
to
10,000
ng/
l.
These
results
are
summarized
below.

Table
11:
Storm
Water
Sampling
Results
(
ng/
L)
(
BES,
May
1997)
3
Parameter
SW­
1
SW­
2
SW­
3
SW­
6
dieldrin
ND
(.
51)
ND
(.
54)
2.32
(.
5)
ND
DDE
ND
(.
44)
1.17
(.
46)
5.60
(.
42)
ND
DDD
1.93
(
1.23)
ND
(
1.3)
3.62
(
1.19)
ND
DDT
1.28
(.
94)
12.89
(.
99)
24.05
(.
91)
ND
PCBs
ND
(
1.96­
3.92)
ND
(.
82­
4.13)
ND
(.
79­
3.79)
ND
The
storm
water
data
indicates
that
storm
water
is
a
source
of
pesticides.
Results
from
the
dry
weather
sediment
sample
at
SW­
3
indicate
that
sediment
associated
with
storm
water
is
contributing
PCBs
to
the
Buffalo
Slough
as
well
as
dieldrin
and
DDE.
Additional
monitoring
will
be
conducted
by
the
City
of
Portland
to
verify
this
conclusion.
Fugacity
modeling
has
been
conducted
using
the
results
of
the
Buffalo
Slough
monitoring.
The
fugacity
model
is
a
compartment
model
and
contaminants
are
assumed
to
be
in
compartments
that
represent
areas
of
the
environment,
such
as
surface
water,
algae
or
fish
tissue.
The
results
of
this
modeling
indicate
that
storm
water
sediment
is
the
likely
source
of
contamination
of
fish
tissue.
Without
storm
water
control
any
remediation
may
not
be
effective.
However,
this
modeling
was
based
on
one
sample
result
and
additional
modeling
will
be
conducted
when
additional
storm
water
samples
are
collected.

2
Detection
limit
in
parentheses
3
PCB
data
has
a
range
of
detection
limits
depending
on
Aroclor
analyzed,
SW­
6
detection
limits
not
recorded.
A­
18
Industrial
Storm
Water
Permits
­
Organics
Monitoring
Storm
water
monitoring
for
industrial
permits
focuses
primarily
on
metals,
and
does
not
include
303(
d)
organics.

Summary
of
Storm
water
Information
Based
on
information
obtained
under
the
general
storm
water
permits
and
the
MS4
permits
issued
in
the
Columbia
Slough
watershed,
the
following
observations
can
be
made:

 
The
total
lead
load
to
the
Columbia
Slough
is
estimated
in
the
MS4
permits
to
be
1131
kg/
yr.
Of
this,
141
kg/
yr
is
estimated
to
come
from
areas
covered
by
industrial
permits.

 
Sampling
for
the
other
parameters
found
to
impair
beneficial
uses
in
the
Columbia
Slough
has
been
infrequent,
and
so
far,
only
the
pesticides
have
been
detected.
Current
information
is
insufficient
for
developing
pollutant
loads
associated
with
any
of
the
303(
d)
organics.
With
lower
detection
limits,
it
may
be
possible
to
develop
pollutant
loads.

Groundwater
Several
of
the
303(
d)
parameters
are
hydrophobic,
which
means
they
tend
to
adsorb
strongly
to
soil
particles
and
are
comparatively
less
likely
to
be
found
in
groundwater.
DDT,
PCBs
and
dioxin
are
all
considered
to
be
hydrophobic.
This
characteristic
is
expressed
quantitatively
in
terms
of
the
retardation
factor.
In
a
report
"
Characterization
of
Subsoil
Properties
Affecting
the
Transport
of
Toxic
Metals,
Ammonia,
and
Hydrophobic
Organic
Compounds
at
the
St.
Johns
Landfill
Site"
(
Fish,
1994),
Dr.
William
Fish
states:

"
Calculated
retardation
factors
for
selected
priority­
pollutant
organic
compounds
range
from
less
than
20
for
the
more
soluble
compounds
such
as
toluene
or
chlorobenzene,
to
hundreds
or
even
thousands
for
hydrophobic
compounds
such
as
PAHs,
PCBs,
and
dioxins..."

In
the
same
report,
Dr.
Fish
points
out
that
lead
will
have
retardation
factors
much
larger
than
those
observed
for
nickel
and
copper,
which
are
typically
in
the
range
of
10
to
30.

It
should
be
noted
that
a
high
retardation
factor
does
not
preclude
the
possibility
of
contamination
by
a
hydrophobic
substance,
it
simply
reduces
the
rate
at
which
it
will
move
through
soil.
A­
19
General
Characterization
Groundwater
to
the
Slough
has
been
monitored
less
frequently
than
storm
water,
however
groundwater
quality
is
also
less
dynamic
than
storm
water.
Information
on
groundwater
quality
in
the
vicinity
of
the
Columbia
Slough
is
available
from
the
city
of
Portland
Water
Bureau.
Monitoring
has
also
been
performed
by
DEQ
and
USGS
on
a
more
limited
basis.
Information
on
groundwater
in
the
vicinity
of
contaminated
sites
is
also
available,
and
is
available
through
DEQ's
Environmental
Cleanup
Site
Information
(
ECSI)
database.
This
information
is
summarized
in
the
following
sections.

Monitoring
Well
Results
The
City
of
Portland
Water
Bureau
maintains
8
monitoring
wells
in
the
vicinity
of
the
Columbia
Slough.
These
wells
are
located
in
the
Troutdale
Sand
and
Gravel
Aquifer
(
TSA)
which
is
the
source
of
groundwater
to
the
Columbia
Slough.
Of
the
303(
d)
parameters,
only
total
lead
is
currently
monitored.

A
total
of
57
total
lead
samples
were
collected
in
these
wells
from
1984
through
1996,
with
between
2
and
11
samples
collected
at
each
site.
The
detection
limit
was
0.001
mg/
l,
and
lead
was
detected
in
8
of
the
57
samples.
Of
these
8
values,
5
were
at
the
detection
limit,
1
value
was
equal
to
0.002
mg/
l
and
2
values
were
equal
to
0.003
mg/
l.
According
to
Cathy
Casson
of
the
Water
Bureau,
lead
is
generally
only
detected
when
the
pumps
are
first
started
and
may
be
the
result
of
leaching
from
the
pumps
In
1991,
DEQ
collected
data
from
14
wells
located
in
East
Multnomah
County
in
the
vicinity
of
Fairview
Lake.
The
detection
limits
ranged
from
5
ug/
l
to
7
ug/
l.
The
results
are
summarized
below.

Table
12
Summary
of
DEQ
Well
Monitoring
Data
Parameter
No.
of
Samples
No.
of
Detects
Total
Lead
5
1
(=
5
ug/
l)
Dissolved
Lead
20
0
Dieldrin
27
0
DDT
27
0
DDE
27
0
DDD
27
0
The
lack
of
detects
may
reflect
the
relatively
high
detection
limits
associated
with
this
sampling
effort.

On
7/
27/
95,
the
USGS
collected
samples
from
five
wells
in
parks
along
N.
Columbia
Blvd.
from
about
N.
Portland
Rd.
to
NE
33rd
Drive
(
Nancy
Hendrickson,
BES,
pers.
comm.).
A­
20
The
results
for
dissolved
lead,
DDE
and
Dieldrin
showed
no
detects.
The
detection
limits
were
1
ug/
l,
6
ng/
l
and
1
ng/
l
respectively.
These
detection
limits
are
unusually
low,
and
are
well
below
the
chronic
criteria
for
these
chemicals.
No
tests
were
done
for
dioxin
or
PCBs.

Pollutant
Loading
Estimates
Loading
estimates
for
total
lead
can
be
developed
from
the
data
collected
by
the
USGS.
Using
values
set
at
½
the
detection
limit,
the
dissolved
lead
concentration
is
0.5
ug/
L.

In
Part
II
of
the
Waterbody
Assessment,
the
annual
flow
of
groundwater
to
the
Columbia
Slough
is
estimated
to
be
1.86x
109
cu
ft/
yr.
The
annual
rate
of
dissolved
lead
loading
is
calculated
as
follows:

(
0.5ug/
l)
x
(
1.86x
109
cu
ft/
yr)
x
(
28.317
l/
cu
ft)
x
(
1
kg/
106
mg)
x
(
1mg/
103ug)
=
26
kg/
yr
or
0.07
kg/
day.

Contaminated
Sites
As
of
August
28,
1996,
there
were
106
sites
listed
in
DEQ's
Environmental
Cleanup
Site
Information
System
(
ECSI)
for
the
Columbia
Slough
study
area.
In
addition
to
sites
from
which
a
release
of
hazardous
materials
has
been
confirmed,
this
list
also
contains
sites
that
have
since
been
found
to
not
pose
a
risk
to
groundwater
or
surface
water,
as
well
as
sites
that
have
been
cleaned
up.
It
also
contains
sites
that
upon
closer
examination
turn
out
to
not
drain
to
the
Columbia
Slough.
In
other
words,
not
all
106
sites
in
ECSI
are
likely
to
impact
water
quality
in
the
Columbia
Slough.

The
following
tables
contain
the
sites
listed
in
the
database
that
have
indications
of
the
presence
of
a
303(
d)
parameter.
The
status
line
describes
the
present
status
of
the
site,
i.
e.
the
site
actually
drains
to
the
Columbia
River,
or
data
review
indicated
insufficient
information
to
develop
a
load
estimate
at
this
time,
etc.
A­
21
PCBs
COMMON
NAME
ADDRESS
NAME
MEDIUM
Possible
Data
STATUS
Oregon
Waste
Systems
­
Proposed
Transfer
Station
11535
N
Force
ST
PCB
1221
GW
10.8
ppm
drains
to
Columbia
River
Portland
(
City
of)
­
Columbia
BLVD
POTW
5001
N
Columbia
BLVD
PCB
1254
OT
50.27
ppm
does
not
drain
to
Slough
Columbia
Slough
31.5
miles
of
waterway
PCBs
SE
520
ppb
(
LS)
load
developed
and
sediment
partitioning
allocation
in
TMDL
Columbia
Slough
Consolidation
Conduit
PCBs
SL
this
site
is
not
an
active
cleanup
site,
DEQ
has
been
working
with
the
City
of
Portland
to
characterize
any
areas
of
contamination
along
the
alignment
so
that
the
media
can
be
properly
managed
during
construction.

Lamm
Property
­
Site
2
4065
N
Suttle
RD
PCBs
SL
10
ppm
and
less
drains
to
Columbia
River
Malarkey
Roofing
Co.
3131
N
Columbia
BLVD
PCB
1242
SL
7.2
ppm
site
remediated
in
1989
and
1990
Morrison
Oil
Co.
3747
N
Suttle
RD
PCBs
SL
7
ppm
drains
to
Oregon
Slough
General
Electric
Industrial
Co.
2410
N
Columbia
BLVD
PCB
1221
SL
1
to
5
ppm
PCB
levels
lower
than
cleanup
action
level
of
0.7
mg/
kg
(
OARS
340­
122­
045)
(
average
PCB
1254
=.
28
mg/
kg,

PCB
1260
0.19
mg/
kg
data
from
7/
19/
96)

Schnitzer
Property
­
N
Kerby
AVE
8520
N
Kerby
AVE
PCB
1221
SL
0.8
ppm
PCB
from
soil
sample
taken
from
2
feet
below
surface,

below
asphalt
so
no
surface
runoff
contamination
possible,

no
groundwater
samples
were
taken,
no
load
calculated
NW
Cast/
Universal
Silver
9233
N
Calvert
Ave.
PCB
SL
Nu­
Way
Oil
Co.
7039
NE
46th
AVE
PCB
1242
SL
0.7
ppm
load
and
allocation
in
TMDL
Nu­
Way
Oil
Co.
7039
NE
46th
AVE
PCB
1260
SL
1.5
ppm
load
and
allocation
in
TMDL
N
Marine
DR
Extension
­
North
Portland
N
Marine
DR
PCBs
SL
drains
to
Columbia
River
Pacific
Meat
Co.
2701
N
Newark
St
PCB
SE/
SL
medium
codes:

GW
=
groundwater
OT
=
other
(
sludge)

SE=
instream
sediment
SL
=
soil
A­
22
DDT,
p,
p'­
COMMON
NAME
ADDRESS
MEDIUM
Possible
Data
STATUS
Rhone­
Poulenc
­
N
Marine
DR
4429
N
Suttle
RD
GW
up
to
88
ppb
does
not
drain
to
Columbia
Slough
Rhone­
Poulenc
­
N
Marine
DR
4429
N
Suttle
RD
SE
up
to
1,200
ppb
does
not
drain
to
Columbia
Slough
Rhone­
Poulenc
­
N
Marine
DR
4429
N
Suttle
RD
SL
up
to
3,100,000
ppb
does
not
drain
to
Columbia
Slough
Dieldrin
COMMON
NAME
ADDRESS
MEDIUM
Possible
Data
STATUS
Rhone­
Poulenc
­
N
Marine
DR
4429
N
Suttle
RD
SL
up
to
100,000
ppb
does
not
drain
to
Columbia
Slough
Rhone­
Poulenc
­
N
Marine
DR
4429
N
Suttle
RD
GW
up
to
1.9
ppb
does
not
drain
to
Columbia
Slough
medium
codes:

GW
=
groundwater
OT
=
other
(
sludge)

SE=
instream
sediment
SL
=
soil
A­
23
Lead
COMMON
NAME
ADDRESS
MEDIUM
Possible
Data
STATUS
Oregon
Waste
Systems
­
Proposed
Transfer
Station
11535
N
Force
ST
GW
1.2
­
41
ug/
L
drains
to
Columbia
River
St.
John's
Landfill
9363
N
Columbia
BLVD
GW
4.4
ppm
load
developed
and
allocation
in
TMDL
Oregon
National
Guard
­
PDX
Airport
#
1
Southwest
portion
of
airport
GW
2.175
ppm
in
1989
no
metals
were
detected
at
levels
above
regulatory
thresholds,
site
under
review
by
DEQ
DeWitt
Construction
10910
NE
Holman
ST
GW
1.08
PPM
data
from
an
unfiltered,
turbid
groundwater
sample.

Filtered
sample
was
a
non
detect
with
a
detection
limit
of
0.002
mg/
L
Nu­
Way
Oil
Co.
7039
NE
46th
AVE
GW
0.033
ppm
load
developed
and
allocation
in
TMDL
Schnitzer
Property
­
N
Kerby
AVE
8520
N
Kerby
AVE
GW
.006
ppm
groundwater
Pb
level
lower
than
drinking
water
standard,
no
load
calculated
St.
John's
Landfill
9363
N
Columbia
BLVD
OT
10.2
ppm
landfill
leachate
Nu­
Way
Oil
Co.
7039
NE
46th
AVE
SE
up
to
20,500
ppm
(
est)
this
data
from
lagoon,
which
has
since
been
remediated
load
developed
and
allocation
in
TMDL
using
data
from
8/
12/
97
for
other
sections
of
site
with
exposed
soil
JB's
Quality
Metal
Inc.
7715
NE
21st
AVE
SE
54­
1500
ppm
1500
ppm
sample
from
soils
removed
in
1992/
1993,
currently
has
no
further
action
status
in
cleanup
program
Columbia
Slough
31.5
miles
of
waterway
SE
510
ppm
(
LS)
load
developed
and
sediment
partitioning
allocation
in
TMDL
DeWitt
Construction
10910
NE
Holman
ST
SL
188
ppm
Pb
present
at
background
levels,
no
load
calculated
Fernley
Tire
Fire
5411
NE
Portland
Hwy
SL
240
ppm
Pb
present
at
background
soil
levels,
no
load
calculated
Flightcraft
7505
NE
Airport
WAY
SL
1.6
mg/
l
5/
94
data
showed
no
groundwater
contamination
Holman
Redevelopment
Area
­
Parcel
249
10835
NE
Holman
ST
SL
3,140
ppm
site
remediated
in
1992,
no
further
action
recommended
by
clean
up
staff
Lamm
1
4101
N
Suttle
RD
SL
414
ppm
drains
to
Columbia
River
Lamm
Property
­
Site
2
4065
N
Suttle
RD
SL
93
ppm
(
in
a
composite
drains
to
Columbia
River
of
4
surface
samples)

Malarkey
Roofing
Co.
3131
N
Columbia
BLVD
SL
1500
ppm
site
remediated
in
1989
and
1990
Mt.
Hood
Metals
9645
N
Columbia
Blvd
GW/
OT
active
voluntary
clean
up
project
Morrison
Oil
Co.
3747
N
Suttle
RD
SL
30
ppm
drains
to
Oregon
Slough
Oregon
National
Guard
­
PDX
Airport
#
1
Southwest
portion
of
airport
SL
46
ppm
Pb
present
at
background
soil
levels,
no
load
calculated,

site
under
review
by
DEQ
Oregon
Waste
Systems
­
Proposed
Transfer
Station
11535
N
Force
ST
SL
3.5
­
235
mg/
kg
drains
to
Columbia
River
Pacific
Meat
Co.
2701
N
Newark
St
SE
Redi­
Strip
of
Oregon
9940
N
Vancouver
WAY
SL
25
ppm
EP
Tox.
data
to
date
has
been
EP
toxicity,
so
no
load
developed
in
site
response
program,
sampling
will
occur
by
Spring
1998,
including
sampling
of
drainage
ditches
and
groundwater
Schnitzer
Property
­
N
Kerby
AVE
8520
N
Kerby
AVE
SL
290
ppm
Pb
present
at
background
soil
levels,
no
load
calculated
medium
codes:

GW
=
groundwater
OT
=
other
SE=
instream
sediment
SL
=
soil
A­
24
Where
sufficient
data
was
available
to
develop
a
load
and
allocation,
such
estimates
were
completed.
The
calculations
for
these
sites
follow.

The
NuWay
Oil
site
has
been
found
to
have
the
highest
concentration
of
both
lead
and
PCBs
reported
for
any
site
in
the
Slough
watershed.
The
maximum
detected
PCB
soil
concentration
is
29
mg/
kg
(
data
from
Bill
Dana,
DEQ,
9/
8/
97).
The
average
concentration
of
Pb
in
the
process
area
of
the
site
is
1532
mg/
kg
(
data
from
Bill
Dana,
DEQ,
9/
8/
97).

NuWay
Oil
Site
NuWay
Oil
Groundwater
Load
The
NuWay
Oil
site
is
located
immediately
adjacent
to
the
Whitaker
Slough
immediately
upstream
of
the
confluence
with
the
mainstem.
In
order
to
estimate
pollutant
loading
associated
with
groundwater
from
this
site,
it
is
first
necessary
to
establish
groundwater
velocity.
This
can
be
calculated
from
Darcy's
Law
(
Todd,
1980),
which
is
as
follows:

v
=
K
*
(
dh/
dL)

where
v
=
velocity
K
=
hydraulic
conductivity
dh/
dL
=
hydraulic
gradient
The
hydraulic
gradient
was
calculated
from
on­
site
well
information
(
NuWay)
to
be
3
x
10­
4
ft/
ft.
The
hydraulic
conductivity
is
a
function
of
soil
type.
The
site
was
found
to
have
soils
that
were
a
mixture
of
sand,
silt
and
clay.
The
hydraulic
conductivity
of
such
soils
is
typically
10­
2
to
10­
3
m/
day
(
Mavis
Kent,
DEQ,
pers.
comm.).
If
the
higher
value
is
used
in
order
to
be
conservative,
the
result
is:

v
=
(
10­
2
m/
day)
*
(
1ft
/
0.3048m)
*
(
3
x
10­
4
ft/
ft)
=
9.84
x
10­
6
ft/
day
The
rate
of
groundwater
flow
from
the
site
can
be
calculated
as
follows:

Q
=
v
*
length
of
site
along
the
Slough
*
depth
The
length
of
the
NuWay
site
along
the
Whitaker
Slough
is
about
400
ft.
If
the
contamination
is
assumed
to
run
the
entire
length
of
the
site
and
to
extend
to
a
depth
of
20
ft.,
then
the
rate
of
groundwater
flow
from
this
volume
of
soil
will
be:

Q
=
(
9.84
x
10­
6
ft/
day)
x
(
400
ft.)
x
(
20
ft.)
=
0.08
cu
ft/
day
Groundwater
data
from
April/
May
1997,
July
1997
and
November
1997
was
used
to
obtain
an
estimate
of
the
groundwater
load
of
Pb
and
PCBs
to
the
Slough.
Five
Pb
A­
25
samples
were
taken
during
this
time
and
had
two
non
detects
(
at
detection
limits
of
0.1
mg/
L
and
0.005
mg/
L,
respectively)
and
three
detects
at
12.2
ug/
L,
15
ug/
L
and
18.6
ug/
L.
With
the
non
detects
set
at
½
the
detection
limit,
the
average
Pb
concentration
is
0.02
mg/
L.

Using
the
average
groundwater
concentration,
the
loading
rate
is
calculated
as
follows:

Lead
loading
rate
=
(
0.08
cu
ft/
day)
x
(
0.02
mg/
l)
x
(
28.317
l/
cu
ft)
x
(
1
kg/
106
mg)=
4.53
x
10
­
8
kg/
day
or
1.65
x
10­
5
kg/
yr
total
Pb
PCB
data
from
the
same
time
period
were
non
detects
at
a
detection
limit
of
0.0001­
0.0003
mg/
L.
Using
½
the
detection
limit
of
0.00015
mg/
L,
the
annual
loading
rate
is
3.4x
10­
10
kg/
day
or
1.24
x
10­
7
kg/
year.
Retardation
factors
have
not
been
included
in
either
of
these
calculations.

From
this
analysis,
it
appears
that
the
loading
rate
of
lead
and
PCBs
from
NuWay
Oil
to
the
Columbia
Slough
via
groundwater
is
not
large,
even
if
retardation
factors
are
not
taken
into
account.
Yet
contamination
levels
at
this
site,
particularly
with
respect
to
lead;
are
very
high.

NuWay
Oil
Storm
water
Load
The
NuWay
Oil
Site
can
be
divided
into
two
sections;
the
lagoon
area
and
the
process
area.
The
lagoon
area
has
been
excavated
and
capped.
The
process
area
is
scheduled
for
remediation,
which
may
include
soil
excavation.
There
is
also
an
area
around
the
lagoon,
which
has
been
sampled
and
is
covered
with
gravel.
Annual
Pb
loads
from
surface
erosion
from
both
the
process
area
and
the
area
around
the
capped
lagoon
(
non
process
areas)
can
be
estimated
with
the
Universal
Soil
Loss
Equation
(
USLE)
and
the
measured
Pb
soil
levels.

Using
the
Universal
Soil
Loss
Equation,
the
soil
loss
from
the
site
is
calculated
as
follows
(
EPA,
1985):
X
=
1.29
E(
K)(
1s)
C(
P)
where:
X
=
average
annual
soil
loss
by
sheet
and
rill
erosion
in
t/
ha
E
=
rainfall/
runoff
erosivity
index
(
102
m­
tonne­
cm/
ha­
hr),
from
map
of
average
annual
erosivity
indices
(
pg.
163)
K
=
soil
erodibility
(
t/
ha
per
unit
of
E),
table
of
erodibility
per
soil
type
(
pg.
165)
1s
=
topographic
factor
C
=
cover
management
factor,
table
of
C
factors
for
a
construction
site
(
pg.
168)
P
=
supporting
practice
factor,
table
(
pg.
172)
The
topographic
factor,
1s,
is
calculated
as
follows
(
EPA,
1985):
1s
=
(
0.045x)
b(
65.41sin2 
+
4.56
sin 
+
0.065)
The
slope
angle
is
obtained
from
percent
slope,
s
by:
 
=
tan­
1
(
s/
100)
A­
26
(
percent
slope
estimates
from
Ken
Cameron,
DEQ,
personal
communication)

The
annual
watershed
solid
phase
chemical
load
in
rural
runoff
(
kg/
yr)
is
then
calculated
by:
Ls
=
.001(
Sd)(
Cs)(
X)(
A)
where:
Sd
is
the
sediment
delivery
ratio
and
is
a
function
of
the
drainage
area
=
0.35
(
pg.
178)
Cs
is
the
solid
phase
chemical
concentration
in
sediment
=
average
of
1073
mg/
kg
for
non
process
area
and
1532
mg/
kg
for
process
area
(
Bill
Dana,
DEQ,
personal
communication)
X
is
the
soil
loss
from
the
eroded
area,
calculated
using
the
USLE
A
is
the
acreage
of
the
eroded
area
=
30,000
ft2
==
0.28
ha
(
Ken
Cameron,
DEQ,
personal
communication)

The
following
table
summarizes
the
input
parameters
and
the
annual
Pb
load
from
the
process
and
non
process
areas:

Table
13
E
K
s
1s
C
P
X
Cs
A
Sd
Ls
process
86.75
.16
2%
0.162
8
1
1
2.916
1532
0.28
.35
.438
nonprocess
86.75
.16
0%
0.058
0.05
1
0.519
1073
0.28
.35
.005
The
USLE
predicts
soil
loss
from
sheet
and
rill
erosion,
but
does
not
predict
erosion
from
gullies,
streambanks
or
landslides.
(
Vesilind,
1982).

An
estimate
of
the
PCB
load
from
the
NuWay
Oil
Site
can
also
be
calculated
using
the
USLE.
Using
average
Aroclor
1260
concentrations
for
the
process
area
of
3.74
mg/
kg
and
non
process
area
of
1.65
mg/
kg
(
Bill
Dana,
DEQ,
personal
communication),
an
estimate
of
the
PCB
load
can
be
made.
Only
Aroclor
1260
data
was
used
as
the
other
PCBs
were
present
at
detection
levels.
The
Aroclor
1260
loads
are
then
8.4
x
10­
6
kg/
yr
and
1.1
x
10­
3
kg/
yr,
for
the
non
process
and
process
areas,
respectively.

Nu
Way
Oil
Sediment
Partitioning
Current
erosion
estimates
may
not
reflect
previous
loads,
as
much
of
the
site
has
been
excavated,
regraded
and
covered
with
gravel.
Instream
sediment
Pb
levels
are
high
(
BES
memo
to
DEQ,
9/
11/
97)
and
may
continue
to
contribute
to
violations
of
the
Pb
criteria
due
to
sediment
partitioning.
In
the
SLRA
(
Parametrix,
1995),
sediment
flux
from
contaminated
sediment
was
estimated.
The
maximum
estimated
sediment
flux
value
for
Pb
(
5.5
x
10­
4
mg/
L,
Parametrix
1995)
was
obtained
for
a
sample
from
Whitaker
Slough.
Using
this
value,
an
estimate
of
the
annual
load
to
Whitaker
Slough
is
possible.
The
SLRA
(
Parametrix,
1995)
estimates
the
average
flow
of
Whitaker
Slough
to
be
55
ft3/
sec
or
1.74
x
109
ft3/
yr.

(
5.5
x
10­
4
mg/
l)
x
(
1.74
x
109
cu
ft/
yr)
x
(
28.317
l/
cu
ft)
x
(
1
kg/
106
mg)
=
27.1
kg/
yr
A­
27
St.
Johns
Landfill
Priority
pollutants
are
monitored
yearly
at
9
wells
around
the
St.
Johns
Landfill.
Some
of
the
nine
wells
sampled
may
change
year
to
year.
Results
of
this
monitoring,
since
October
1993,
are
summarized
below
(
Paul
Vandenburg,
METRO,
pers.
comm.):
 
Lead
­
the
average
concentration
of
total
lead
found
in
monitoring
wells
is
0.0183
mg/
l
(
Metro
1995
and
Dennis
O'Neill,
pers.
comm.):
 
PCBs
­
have
not
been
detected
in
any
of
36
samples
that
have
been
tested
for
each
of
the
seven
Aroclor
(
PCB)
classes
(
detection
limit
was
0.5
ug/
L
for
Aroclors
other
than
1221,
Aroclor
1221
had
a
detection
limit
of
2
ug/
L,
Table
20
PCB
criteria
=
0.079
ng/
L)).
4
 
DDT,
DDE
and
DDD
­
none
of
these
compounds
have
been
detected
in
any
of
the
36
samples
tested
since
October
1993
(
detection
limit
for
DDT
was
0.1
ug/
L,
DDE
detection
limit
was
0.04
ug/
L,
DDD
detection
limit
was
0.05
ug/
L,
Table
20
DDT
criteria
=
0.024
ng/
L).

 
Dieldrin
­
no
dieldrin
has
been
detected
in
any
of
36
samples
tested
since
October
1993
(
detection
limit
was
0.04
ug/
L,
Table
20
criteria
=
0.071
ng/
L).

 
Dioxin
­
No
well
samples
have
been
taken
for
dioxin.
Fish
samples
taken
from
the
reach
of
the
Slough
near
the
landfill
showed
levels
of
dioxin
comparable
to
levels
in
fish
taken
from
other
parts
of
the
Slough
and
the
Columbia
and
Willamette
Rivers.
This
indicates
that
there
is
no
local
source
of
dioxin
in
the
area
of
the
landfill.
(
Parametrix,
July
1995)
(
Table
20
dioxin
criteria
=
1.3
x
10­
5
ng/
L).

The
lack
of
detects
with
respect
to
PCBs,
DDT
and
dieldrin
in
the
St.
Johns
Landfill
monitoring
wells
should
not
be
taken
as
evidence
that
they
are
not
present
at
the
site.
The
low
detection
frequency
is
more
likely
to
be
reflective
of
the
tendency
of
these
parameters
to
adsorb
onto
sediment
particles.
This
reduces
the
rate
at
which
they
are
likely
to
leave
the
site.
Initial
results
of
modeling
conducted
as
part
of
landfill
closure
indicate
that
with
the
cap
installed,
pollutant
loads
from
St.
Johns
Landfill
are
negligible.
Additional
work
is
currently
being
conducted
by
the
DEQ
solid
waste
program
to
verify
the
assumptions
of
the
model
and
the
accuracy
of
the
predictions.

Annual
Pb
load:
The
lateral
flow
rate
is
estimated
to
be
0.05
to
0.08
cfs.

0.08
ft3/
sec
X
0.0183
mg/
L
Pb
X
28.317
L/
ft3
X
(
1kg/
106
mg)
X
(
60
sec/
1
min)
X
(
60
min/
hr)
X
(
24
hr/
day)
=
3.6
x
10­
3
kg/
day
=
1.31
kg/
yr
of
lead
to
the
Slough
from
the
St.
Johns
Landfill.

4
Aroclor
1221
detection
limit
changed
to
0.4
ug/
L
in
August
1995,
for
all
other
Aroclors
the
detection
limit
changed
to
0.1
ug/
L
in
August
1995.
A­
28
Riedel
Site
DEQ
performed
limited
monitoring
from
1989
to
1993
at
7
different
locations
on
the
Nashpit
landfill.
This
landfill
was
closed
in
1991,
and
is
now
known
as
the
Riedel
site.
Results
of
monitoring
are
shown
below.

Table
14
Summary
of
Monitoring
at
Nashpit
Landfill
(
Riedel)

Parameter
No.
of
Samples
No.
of
Detects
Concentrations
(
mg/
l)
Total
Lead
10
3
0.011
to
0.018
Dissolved
Lead
33
0
NA
DDT,
DDE,
DDD
4
0
NA
Dieldrin
4
1
0.006
As
indicated
in
the
table,
lead
(
total)
and
dieldrin
have
all
been
detected
at
the
Riedel
site.
The
sample
found
to
contain
these
pollutants
was
collected
in
the
landfill
leachate
sump.
Leachate
from
this
sump
is
directed
to
the
Columbia
Blvd.
treatment
plant
and
is
highly
unlikely
to
impact
the
Slough.
The
source
of
the
dieldrin
may
not
be
the
landfill
itself,
but
rather
the
site
located
next
to
the
landfill
which
was
formerly
a
pesticide
storing
or
manufacturing
facility
(
Tim
Spencer,
DEQ,
pers.
comm.).

Lead
levels
appear
to
be
higher
than
those
associated
with
groundwater
samples
collected
from
the
city
groundwater
monitoring
wells
but
it
is
not
clear
at
this
time
whether
or
not
levels
seen
are
due
to
contamination
at
the
landfill.

To
summarize
the
information
available
on
the
Riedel
site,
at
this
time
it
appears
that
the
landfill
is
associated
with
higher
than
usual
levels
of
lead
and
that
dieldrin
may
be
associated
with
this
site.
There
is
insufficient
information
with
which
to
estimate
pollutant
loads
to
the
Slough.

Sediment
Partitioning
Sediments
within
the
Columbia
Slough
can
also
be
a
source
of
pollutants
because
some
of
the
pollutants
can
enter
the
water
column
via
partitioning.
Predictions
of
water
column
concentrations
of
various
pollutants
have
been
developed
(
SLRA
2/
95,
Chris
Prescott,
BES,
pers.
comm.).
Interstitial
water
concentrations
of
the
organic
chemicals
were
predicted
based
on
the
theory
that
organic
chemicals
tend
to
preferentially
bind
to
the
organic
carbon
fraction
of
sediment,
where
an
assumed
equilibrium
concentration
is
achieved
between
the
sediment
organic
carbon
and
interstitial
water
concentration
over
time.
The
organic
carbon
normalized
partition
coefficient
(
Koc)
was
used
to
estimate
the
organic
constituent
concentration
in
the
sediment
interstitial
water.
Surface
water
concentrations
were
calculated
based
on
the
flux
of
organic
constituents
from
the
A­
29
interstitial
water
to
the
surface
water.
(
SLRA,
2/
95,
Appendix
D).
By
multiplying
the
surface
water
concentrations
by
the
annual
flow
through
the
Columbia
Slough,
overall
mass
loads
can
be
developed.
The
Waterbody
Assessment
(
CH2MHill,
1995)
gives
the
total
annual
flow
to
the
Columbia
Slough,
not
counting
tidal
inflow
from
the
Willamette,
as
1.48
x
108
m3/
yr.
Water
column
concentrations
are
calculated
as
follows:

total
annual
inflow
(
m3
/
yr)
x
predicted
median
water
column
concentrations
(
mg/
L)
x
(
1000
L/
1
m3)
x
(
1
kg/
106
mg))
=
pollutant
load
(
kg/
yr)

Predicted
median
water
column
concentrations
and
associated
pollutant
loads
are
listed
below.

Table
15
Predicted
Median
Water
Column
Concentrations
and
Pollutant
Loads
Parameter
Predicted
Median
Water
Column
Conc.
(
mg/
l)
Pollutant
Load
kg/
yr
DDT
4.87
x
10­
13
DDE
7.17
x
10­
13
DDD
1.2
x
10­
12
total
value:
2.4
x
10­
12
3.55
x
10­
7
Dieldrin
2.67
x
10­
11
3.95
x
10­
6
Dioxin
no
value
available1
PCB
Aroclors
Aroclor
1016
9.1
x
10­
11
Aroclor
1221
1.14
x
10­
10
Aroclor
1232
5.14
x
10­
11
Aroclor
1248
4.08
x
10­
11
Aroclor
1254
4.76
x
10­
12
Aroclor
1260
9.59
x
10­
11
Aroclor
total
:
3.98
x
10­
10
1
x
10­
4
Lead
2.056
X
10­
7
0.030
1Sediments
have
not
been
tested
for
dioxin.

Due
to
the
toxicity
and
bioaccumulation
of
these
chemicals,
a
low
instream
concentration
causes
fish
tissue
concentrations
to
exceed
consumption
advisory
levels.
A­
30
Air
Deposition
Of
the
toxic
parameters
for
which
the
Slough
is
listed,
only
lead
and
dioxins
are
associated
with
current
as
well
as
past
air
emissions.
Other
parameters
were
associated
to
some
extent
with
past
emissions.
Specifically,
DDT
and
dieldrin
were
manufactured
by
Rhone­
Poulenc
on
North
Marine
Drive
until
the
early
1970s.
PCB
releases
were
likely
associated
with
the
burning
of
PCB­
contaminated
waste
oil,
prior
to
the
phasing
out
of
this
method
of
disposal
in
the
1970s.

Dioxin
Sources:
Of
the
activities
and
industries
that
could
result
in
air
emissions
of
dioxin,
the
EPA
currently
only
requires
monitoring
of
pulp
and
paper
industries.
Though
there
are
pulp
and
paper
plants
located
on
the
Columbia
River,
there
are
no
such
industries
located
along
the
Columbia
Slough.
The
nearest
facility
to
the
Columbia
Slough
would
be
the
James
River
facility
in
Camas,
Washington.
It
would
be
difficult
to
translate
an
air
emission
in
Camas
to
a
loading
rates
to
the
Columbia
Slough
because
of
the
multiple
transport
mechanisms.

Lead
Sources:
Though
the
airshed
for
the
Columbia
Slough
is
not
as
well
­
defined
as
the
watershed,
for
the
purposes
of
this
discussion
it
will
be
assumed
that
the
industries
and
activities
most
likely
to
impact
the
Slough
are
those
located
within
Multnomah
County.
The
industries
covered
by
the
Department's
ACPD
(
Air
Contaminant
Discharge
Permit)
that
are
likely
to
emit
lead
include
the
following:

 
metal
casting
(
foundry
operations)
 
battery
manufacturing
 
battery
recycling
 
metals
recycling
The
current
Source
List
maintained
by
DEQ's
Air
Quality
Division
lists
16
companies
located
in
Multnomah
County
as
falling
into
one
of
these
categories.
A
search
of
the
Air
Quality
Division
permit
files
revealed
that
most
of
these
companies
either
no
longer
exist
or
no
longer
engage
in
an
activity
associated
with
lead
emissions.
The
companies
that
are
currently
discharging
are
all
metal
casting/
foundry
operations,
and
they
are
listed
in
Table
23.
Only
Columbia
Steel
Casting
and
Oregon
Steel
Mills
are
actually
located
within
the
Columbia
Slough
watershed.
The
ESCO
plants
are
included
because
of
the
possibility
that
air
emissions
from
these
plants
may
migrate
into
the
Columbia
Slough
watershed.
A­
31
Table
16
List
of
Companies
with
Lead
Air
Emissions
AQ
File
No.
Name
Address
Process
Type
Est.
Lead
Emissions
1
26­
1869
Columbia
Steel
Casting
10425
N.
Bloss
Steel
Foundry
<
1200
26­
2067
ESCO,
Plant
3
2211
NW
Brewer
Steel
Foundry
<
1200
26­
2068
ESCO,
Plant
1
2141
NW
25th
Avenue
Steel
Foundry
<
1200
26­
1865
Oregon
Steel
Mills
14400
N
Rivergate
Blvd.
Steel
Foundry
<
2200
1Units
are
lbs/
yr.
Values
were
reported
as
tons
per
year,
but
have
been
converted.

Of
the
four
companies
listed,
only
Oregon
Steel
has
provided
an
actual
estimate
of
lead
emissions
to
DEQ.
The
values
provided
for
the
other
discharges
are
based
on
the
significant
emission
rate
for
lead
from
foundries,
which
has
been
estimated
by
EPA
to
be
less
than
1200
lbs/
yr.

The
reason
there
is
comparatively
little
information
on
lead
emissions
associated
with
these
facilities
is
that
lead
is
not
considered
by
the
EPA
to
be
a
pollutant
of
significance
for
metal
casting
operations
and
so
it
has
not
provided
an
emission
factor
for
lead
for
metal
casting
operations.
Since
DEQ
only
requires
monitoring
for
parameters
for
which
EPA
provides
emission
factors,
no
monitoring
data
is
available
for
most
of
the
foundries
listed
above.

Oregon
Steel:

DEQ
has
information
on
lead
emissions
from
Oregon
Steel
because
it
is
large
enough
to
be
required
to
apply
for
a
permit
under
Title
V.
Title
V
came
into
effect
under
the
Clean
Air
Act
Amendments
enacted
in
1990.
Title
V
sources
are
those
that
discharge
more
than
100
tons/
yr
of
the
criteria
pollutants,
or
more
than
10
tons/
yr
of
a
particular
criteria
pollutant,
or
more
than
25
tons/
yr
total
of
more
than
one
criteria
pollutant.
Lead
is
a
criteria
pollutant.
Title
V
sources
are
required
to
quantify
all
emissions
of
criteria
pollutants
in
excess
of
0.6
tons/
yr.

Oregon
Steel
applied
for
a
permit
in
1995.
Their
permit
application
states
that
they
currently
emit
2200
lbs/
yr
of
lead.
They
have
asked
to
be
permitted
to
discharge
4600
lbs/
year.
A­
32
The
plant
is
located
on
the
Willamette
River
approximately
1.5
miles
from
the
mouth
of
the
Columbia
Slough.
An
estimate
of
the
annual
Pb
load
to
the
Columbia
Slough
watershed
can
be
made
by
calculating
the
load
due
to
dry
and
wet
deposition
of
emitted
particulates.
Particulates,
if
sufficiently
large,
will
be
removed
from
the
air
by
simple
settling
due
to
gravity
(
dry
deposition).
The
settling
velocity
can
be
calculated
using
Stoke's
law.
Due
to
turbulence
in
the
atmosphere,
particles
less
than
20
um
will
seldom
settle
out
by
gravity
(
Vesilind
et
al,
1982).
Pollutants
may
also
be
removed
from
the
air
by
precipitation
(
wet
deposition);
rain
falls
through
the
air
and
the
air
pollutants
dissolve
in
the
rain
droplets.

Wet
deposition
may
be
estimated
by
the
following
equation:
(
EPA
1985)

L
=
10
C*
P*
A
where:
L
=
load
of
the
pollutant
delivered
to
the
receptor
area
as
wet
deposition
(
mass/
sec)
C
=
concentration
of
pollutant
in
precipitation
(
mass/
liter)
P
=
precipitation
rate
(
cm/
sec)
A
=
projected
receptor
area
(
m2)
10
=
conversion
factor
Quarterly
emission
reports
provided
by
Oregon
Steel
were
reviewed
for
input
data
(
1993­
1996).
The
report
contained
the
emission
rate
of
Pb
in
lb/
hr.
The
outlet
flowrate
from
the
stack
was
reported
as
cubic
foot/
minute
(
standard,
dry).
The
concentration
(
g/
L)
of
Pb
in
the
emission
was
calculated
as
emission
rate
divided
by
flow
rate:
(
lb/
hr)(
1hr/
60
min)(
min/
ft3)(
35.3
ft3/
m3)(
454
gr/
lb)(
1m3/
1000L)
=
g/
L
The
precipitation
was
calculated
as
the
annual
average
precipitation
for
the
period
of
1987­
1997.
The
projected
receptor
area
was
the
Columbia
Slough
drainage
basin,
40,
000
acres.
Using
the
EPA
equation,
the
annual
Pb
load
from
wet
deposition
was
calculated
as:
90%
=
10.6
kg/
yr
50%
=
4.4
kg/
yr
10%
=
0.99
kg/
yr
The
percentile
range
was
calculated
with
the
varying
flow
rates
and
Pb
emission
concentrations
as
reported
in
the
quarterly
emissions
reports.

Using
the
50%
annual
estimate,
an
estimate
of
the
quantity
of
Pb
that
would
land
on
the
Columbia
Slough
water
surface
may
be
calculated.
This
calculation
assumes
that
Pb
that
is
not
deposited
on
the
Slough
surface
water
is
deposited
on
land
and
accounted
for
in
the
storm
water
load.
As
stated
above,
the
Slough
drainage
basin
is
40,000
acres.
An
estimate
of
the
Columbia
Slough
surface
area
is
contained
in
a
memo
from
Scott
Wells
to
the
City
of
Portland
(
September
27,
1995).
At
approximately
6
feet
water
level,
the
surface
area
is
estimated
as
0.51
x
106
m2.
The
relative
area
of
surface
water
to
drainage
basin
is
calculated
as
follows:
A­
33
Surface
water:
0.51
x
106
m2
Drainage
basin:
40,000
acres
X
43560
ft2/
acre
X
1
m2/
10.76
ft2
=
1.62
x
108
m2
Ratio
=
0.51
x
106
m2/
1.62
x
108
m2
=
0.0031
The
annual
wet
deposition
to
the
surface
of
the
Columbia
Slough
is
4.4
kg/
yr
x
0.0031=
0.014
kg/
yr
The
wet
deposition
equation
was
used
with
the
following
assumptions:
1.
The
concentration
of
Pb
emitted
from
the
stack
is
the
concentration
of
Pb
in
the
precipitation,
i.
e.
100%
of
the
Pb
emitted
goes
to
the
precipitation.
2.
No
gradient
in
the
precipitation
concentration
is
assumed.
3.
The
airshed
actually
covered
by
the
plume
was
not
calculated,
therefore
all
the
Pb
emitted
may
not
fall
within
the
Columbia
Slough
watershed.
4.
The
emission
of
the
Pb
is
constant.
5.
The
average
annual
precipitation
was
used,
there
may
be
peak
loading
periods.

Dry
deposition
may
also
be
calculated
for
this
source
using
the
following
equation
(
EPA
1985):
L
=
Vd
*
Cp
*
A
*
f
where:
L
=
load
of
the
pollutant
delivered
to
the
receptor
surface
as
dry
deposition
(
mass/
sec)
Vd
=
settling
velocity
(
m/
sec)
Cp
=
concentration
of
atmospheric
particulates
(
mass/
m3)
A
=
projected
receptor
area
(
m2)
f
=
fraction
(
by
mass)
of
the
pollutant
in
the
particulates
Settling
velocity,
Vd,
is
calculated
using
Stoke's
law:
Vd
=
g(
ad)
2(
 
­
 a)
/
18
u
where:
Vd
=
settling
velocity
(
cm/
sec)
g
=
acceleration
of
gravity,
981.46
(
cm/
sec2)
d
=
particle
diameter
(
micro
meters)
 
=
particle
density
(~
2
g/
cm2)
 a
=
density
of
air
(
0.001243
g/
cm3
at
10C)
u
=
viscosity
of
air
(
0.000177
g/
cm­
sec
at
10C)

The
particle
diameters
are
<
10
um,
likely
2
um
(
Greg
Grunow,
DEQ,
personal
communication).
Using
these
diameters,
the
settling
velocity
varied
from
1.93
E
­
12
m/
sec
(
10
um)
to
7.71
E­
14
m/
sec
(
2
um).
Using
these
settling
velocities,
the
concentration
of
particulates
in
the
emissions
and
the
fraction
of
Pb
in
the
particulates,
the
dry
deposition
of
Pb
to
the
Columbia
Slough
drainage
basin
was
calculated.
The
results
are
summarized
below:
A­
34
Table
17:
Air
Deposition
of
Pb
percentil
e
2
um
10
um
10
%
3.82
X
10­
6
kg/
yr
9.55
X
10­
5
kg/
yr
50%
1.16
X
10­
5
kg/
yr
2.9
X
10­
4
kg/
yr
90%
1.64
X
10­
5
kg/
yr
4.1
X
10­
4
kg/
yr
Using
the
ratio
of
relative
area
of
Columbia
Slough
surface
water
to
the
drainage
area,
the
annual
dry
deposition
Pb
load
to
the
surface
water
can
be
calculated.
2.9
x
10­
4
kg/
yr
X
0.0031
=
8.99
x
10­
7
kg/
yr
The
dry
deposition
equation
was
used
with
the
following
assumptions:
1.
The
particle
density
was
not
known,
and
assumed
to
be
2
g/
cm3.
2.
The
viscosity
of
air
and
the
density
of
air
were
not
temperature
corrected.
3.
The
Pb
emitted
with
the
particulates
was
accounted
for
in
the
wet
deposition
calculation,
so
double
counting
of
Pb
load
from
the
source
may
occur.

Past
Lead
Sources:
Information
on
past
sources
is
contained
in
the
following
table.
Lead
emissions
again
reflect
the
Best
Professional
Judgment
of
DEQ
Air
Quality
staff.
The
sites
associated
with
these
closed
plants
may
release
airborne
dust
contaminated
with
lead.
Only
Zusman
Metals
Co.
is
actually
located
within
the
Columbia
Slough
watershed.
The
others
are
included
because
air
emissions
from
these
plants
may
have
migrated
into
the
Columbia
Slough
watershed.

Table
18:
List
of
Companies
with
Past
Lead
Emissions
AQ
File
No.
Name
Address
Process
Type
Est.
Lead
Emission
s
26­
1866
Gould's
Metals
5909
NW
61st
Lead
Oxide
Closed
1984
<
0.6
tpy
26­
1864
Pacific
Steel
Foundry
1979
NW
Vaughn
Foundry­
closed
in
1972
<
0.1
tpy
26­
2072
Zusman
Metals
Co.
(
Incinerator)
1525
NE
Columbia
Blvd.
Wire
Recycler
closed
1984
<
0.2
tpy
A­
35
Spills
DEQ
has
been
maintaining
records
on
reported
spill
events
since
1987.
A
computerized
database
has
been
developed
and
it
contains
records
of
all
spill
events
that
have
occurred
since
1994,
with
some
events
from
1994
as
well.
Since
1994,
38
spill
events
have
been
reported
in
the
Columbia
Slough
watershed.
The
substance
released
is
only
listed
for
5
of
these,
and
none
are
on
the
303(
d)
list
for
the
Slough.
The
substances
released
are
described
variously
as
food
waste,
oil
(
gasoline
and
diesel),
sewage
and
process
water.

No
pollutant
loads
for
303(
d)
toxics
can
be
associated
with
spills
based
on
this
information.

Illicit
Discharges
The
cities
of
Portland,
Fairview
and
Gresham
are
required
to
monitor
for
illicit
discharges
under
the
terms
of
the
MS4
(
Municipal
Separate
Storm
Sewer
System)
permit.
Though
these
programs
have
been
effective
in
reducing
pollutant
loads
to
the
Slough,
the
parameters
measured
under
them
do
not
include
303(
d)
parameters.
A­
36
Summary
of
Pb
Loads
Lead
loads
associated
with
various
sources
in
the
Columbia
Slough
are
summarized
below.

Table
19:
Summary
of
Total
Metal
Loads
to
the
Columbia
Slough
(
kg/
yr)
Source
Lead
Industrial
Discharges
0.19
Combined
Sewer
Overflows
75.7
Storm
water
(
total)
1131
MS4
area
only
9905
Industrial
permitted
area
only
141
Groundwater6
Overall
loading
26
NuWay
Oil
Site
(
to
Whitaker
Slough)
groundwater
sediment
partitioning
soil
erosion­
process
area
soil
erosion
­
non
process
area
1.65
x
10­
5
27.1
0.438
0.005
St.
John's
Landfill
1.31
Miscellaneous
Sediment
Partitioning
0.030
Air
Deposition7
Oregon
Steel
wet
deposition
Oregon
Steel
dry
deposition
0.014
8.99
x
10­
7
Spills
estimate
not
available
Illicit
Discharges
estimate
not
available
Total
of
Estimates:
1262
5
The
calculated
total
Pb
load
minus
the
load
associated
with
industrial
areas.
6
Dissolved
Pb
concentration
7
Using
the
50th
percentile
mass
load.
A­
37
Table
20
Summary
of
PCBs
Loads
to
the
Columbia
Slough
(
kg/
yr)

Source
PCBs
NuWay
Oil
Site
groundwater
1.24
x
10­
7
soil
erosion
­
process
area
(
Aroclor
1260)
1.1
x
10­
3
soil
erosion
­
non
process
area
(
Aroclor
1260)
8.4
x
10­
6
Sediment
Partitioning8
DDD,
DDE,
DDT
(
total
value)
3.55
x
10­
7
Dieldrin
3.95
x
10­
6
Aroclor
total
1
x
10­
4
8
Calculated
by
multiplying
the
daily
load
(
Table
15)
by
365
days/
year.
A­
38
References
BES
1992.
Combined
Sewer
Overflow
Management
Plan,
CSO
Characterization
Report,
City
of
Portland,
Bureau
of
Environmental
Services,
December
1992.

BES
1993.
Combined
Sewer
Management
Plan,
Volume
2,
Technical
Appendices,
Technical
Memorandum
5.3,
City
of
Portland,
Bureau
of
Environmental
Services,
June
1993.

BES
1997.
Columbia
Slough
Sediment
Project,
Focused
Feasibility
Study
Report
For
Buffalo
Slough,
May
1997,
Final
Draft,
City
of
Portland,
OR.

BES,
memo
to
DEQ,
Upstream
Contributions
to
Sediment
Contamination
at
the
NuWay
Oil
Site,
September
11,
1997.

Cameron,
Ken,
DEQ,
personal
communication
regarding
area,
slope
and
soil
characteristics
of
NUWay
Oil
Site,
9/
12/
97.

CH2MHill
92.
Water
Quality
Monitoring
Program
Results,
Technical
Memorandum
5.4A
to
the
City
of
Portland
from
CH2MHill,
9/
2/
92.

CH2MHill
1995.
Waterbody
Assessment,
Columbia
Slough
TMDL
Development,
Part
II,
prepared
by
CH2MHill
for
City
of
Portland,
1995.

Connell,
Deff,
W.,
Miller,
Gregory,
J.,
Chemistry
and
Toxicology
of
Pollution,
John
Wiley
and
Sons,
1984.

Dana,
Bill,
DEQ,
fax,
soil
sample
results
from
NuWay
Oil
Site,
9/
8/
97,
samples
analyzed
by
Ecology
and
Environment.

DEQ
1996.
Memo
from
Bob
Baumgartner
dated
1/
8/
96.

EPA
1985,
Water
Quality
Assessment:
A
Screening
Procedure
for
Toxic
and
Conventional
Pollutants
in
Surface
and
Ground
Water
­
Part
1,
September
1985,
EPA/
600/
6­
85/
002a.

EPA
1986.
EPA
Gold
Book.

EPA
1991.
Columbia
River
Dioxin
TMDL,
EPA
Region
10,
February
1991.

EPA
1992.
U.
S.
Environmental
Protection
Agency
(
EPA),
Office
of
Wastewater
Enforcement
and
Compliance.
November
1992.
Guidance
Manual
for
the
Preparation
of
A­
39
Part
2
of
the
NPDES
Permit
Applications
for
Discharges
from
Municipal
Separate
Storm
water
Systems.
Pre­
Print.
EPA
833­
B­
92­
002.
Washington,
D.
C.

EPA
1993.
Guidance
for
Assessing
Chemical
Contaminant
Data
for
Use
in
Fish
Advisories,
Volume
1,
Fish
Sampling
and
Analysis
EPA
823­
R­
93­
002.

EPA
1994.
Dioxin
Facts/
Scientific
Highlights
from
Draft
Reassessment,
USEPA,
September
1994.

EPA
1995.
Use
of
Ambient
Data
and
Antidegradation
in
Calculating
Wasteload
Allocations,
memo,
Wastewater
Management
and
Enforcement
Branch,
July
1995.

EPA
1996.
The
Metals
Translator:
Guidance
for
Calculating
A
Total
Recoverable
Permit
Limit
from
a
Dissolved
Criterion,
Office
of
Water,
EPA
823­
B­
96­
007,
June
1996.

EPA
TMDL.
EPA
TMDL
Regional
Workshop,
December
6­
8,
1994,
presented
for
US
EPA
Region
X,
Seattle,
Washington,
workshop
proceedings.

Fish,
William,
"
Characterization
of
Subsoil
Properties
Affecting
the
Transport
of
Toxic
Metals,
Ammonia,
and
Hydrophobic
Organic
Compounds
at
the
St.
Johns
Landfill
Site,
"
1994.

Gresham,
City
of,
Part
II,
National
Discharge
Elimination
System
Municipal
Storm
Water
Permit
Application,
Prepared
for
the
Oregon
Department
of
Environmental
Quality,
May
17,
1993.

Metro
1995.
"
Controlling
Seepage
from
St.
Johns
Landfill
to
Surrounding
Surface
Water",
Solid
Waste
Department,
Engineering
and
Analysis
Division.,
May
1995.

Meyer,
Eugene.
Chemistry
of
Hazardous
Materials,
2nd
Edition,
published
by
Brady
Prentice
Hall
Career
&
Technology,
New
Jersey,
1990.

Oregon
Steel
Mills,
Source
Evaluation
Reports,
Electric
Arc
Furnace
Baghouse
Outlet,
1993­
1996,
prepared
by
Horizon
Engineering
for
Oregon
Steel
Mills.

Parametrix,
Columbia
Slough
Sediment
Remedial
Investigation/
Feasibility
Studies,
Screening­
Level
Risk
Assessment
Addendum,
prepared
for
City
of
Portland,
Bureau
of
Environmental
Services,
July
5,
1995.

Portland
MS4.
Annual
Compliance
Report,
NPDES
MS4
Section
VIII
Monitoring
Program,
prepared
for
Oregon
DEQ,
September
1,
1996,
submitted
by
City
of
Portland
and
co­
applicants.
A­
40
Prescott,
Chris,
discussion
of
results
of
SLRA
report
and
Buffalo
Slough
Sediment
Remediation
Project,
April,
1997.

Pronold,
Michael,
BES,
personal
communication
regarding
storm
water
permits,
1996.

SLRA
2/
95.
Columbia
Slough
Sediment
Project,
Screening
Level
Risk
Assessment
Report,
prepared
by
Parametrix
for
City
of
Portland,
Bureau
of
Environmental
Services,
February
1995.

Todd,
David
Keith.
Groundwater
Hydrology,
Second
Edition,
published
by
John
Wiley
and
Sons
Incorporated,
1980.

U.
S.
Public
Health
Service.
Toxicological
Profile
for
p,
p­
DDT,
p,
p­
DDE,
p,
p­
DDD,
prepared
by
Clement
Associates
under
contract
no.
205­
88­
0608
for
the
Agency
for
Toxic
Substances
and
Disease
Registry,
U.
S.
Public
Health
Service
in
collaboration
with
the
U.
S.
Environmental
Public
Agency,
December
1988.
Draft
for
Public
Comment.

Vandenberg,
Paul,
METRO,
personal
communication
regarding
recent
(
since
10/
93)
priority
pollutant
sampling
at
the
St.
John's
Landfill,
June
17,
1997.

Vesiland,
P.
Aarne,
Peirce,
J.
Jeffrey,
Environmental
Engineering,
published
by
Ann
Arbor
Science
Publishers,
1982.

Wells,
Scott,
Berger,
Chris,
PSU
Civil
Engineering
Department,
Memo
to
Mary
Abrams,
BES,
Dawn
Saunders,
CH2MHill,
Sonja­
Biorn
Hansen,
DEQ,
Tim
Hayford,
MCDD1,
Re:
Upper
Columbia
Slough
Shading,
September
27,
1995.
