Exhibit
K
Biotic Assessment of Water Quality
in a
Reach
of the Sangamon River Receiving
From
the Sanitary District of Decatur
Eastern Illinois University Report
ent
2007
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
effluent from
the San
R obert
Department of Biological
Sciences
Eastem
Illinois University
Charleston.
Illinois 61920
Sangamon River
tary
District of Decatur
ischer. Ph.D.
and Charles L.. Pederson Ph.D.
r-,- District of Decatur
501 Dipper Dries
Decatur. Illinois
625??
EXECUTIVE SUMMARY
ions associated with operation of SDD that Nvere easily
ified by prominent landmarks xvithin the City of Decatur. Illinois. USA and have log.>2ed
GPS coordinates for those sites. Sites were established initially in 1995 during an assessment of
potential impacts of discharges from combined se-wage overflo%v (CSC) facilities as well as the
main treatment plant. All sites were located in the mainstem of the Sangamon River extending
from just downstream of the dam. which impounds Lake Decatur to the
Wyckles
Road Bridge on
the west edge of Decatur. Sites 1. 13.
4. 5. 6. 7. and S are within the
UPSTREAM reach
extendin,, from the dam to the discharge
of the main treatment plant. and
Sites 9. 11 . 1? are
located
in
the DQWaSTREANI
reach which extends from the main treatment
plant discharge to
the Wvckles
Road
bridge. Throughout this reports. we will refer to general locations
as either
UPSTREAM
or DOMINSTREAN1
of the SDD main treatment plant discharge.
Form 2003
through 2005. samples also v,-ere
collected from the Sangamon
River
at
an additional
DOWNSTREAM site (P, 1-I) located 1 km
north
of
the intersection
of C R 600E and CR SOON.
near the Lincoln Trail Homestead State Park. Site 2 (an open channel entering the Sangamon
r from the Lincoln Park CSC)
and
Site 10 (located in Stevens Creek in Fainiew Park) are
distinct from other sites largely due to their location outside of the mainstem of the San=Lamon
River. Because these Sites are more or less isolated from reservoir or sanitary
have not included since 200`_'.
~
Levels of 12 water quality variables were determined form eleven mainstem sites in
?006. Previously, we documents that UPSTREAM and DOWNSTREAM reaches are
distinct
on the basis of their physical and chemical characteristics. Discharge from Lake Decatur is the
UPSTRE AINI reach. resulting in our observation of relatively
instream
o f the SDD facilitate development of more
overall nature of the UPSTREAM and
ng periods of high reserv
oir
discharge.
zed by lower pH. perhaps resulting from addition
.down of organic matter in the wastewater treatment process.
greater potential for instrearn primary
productivity
as a result of
loading
as
indexed by higher levels of dissolved solids. conductivity. total alkaltriltv.
o x 'di7
i ,ed
nitroaen.
I
and phosphorus. Suspended organic material including phytoplartkton algae
r om the reservoir may be supporting heterotrophs in the upstream reach. 'ýN'e have
established a new research effort that seeks to confirm that SDD discharge may be facilitating
a shift from a stream system that relies on
allochthonous
input of
algae to
one
that relies
on
autochthonous instream primary productivity. Improvement of
conditions
in
the
STREAM reach could be realized by maintenance of flo-,v with the range of 200-400 cfs,
measured at the Route 48 bridge.
Collection of diatoms assemblage
data was
hampered by disappearance of greater than
half of the artificial substrates that were deployed- either through vandalism or natural
disturbance. Loss of the majority of samplers is a drawback to this aspect of the study arid
d for upcoming sampling efforts to evaluate utilization of natural substrates to
culties.
A total of
I 1 1-1 ester- Den dv
Nfultiplate samplers were placed along the main
stem of the
Samaamon River associated
with the Sanitan District of
Decatur for deterrnirration of`
macroinvertebrate
communities. For the
eleven sampling locations eye were only able to collect
data from eight
sites along the stretch of
the Sanaamon River associated with the Sanitary
t of Decatur.
a total of 58-18 organisms
represen rag 19 macro invertebrate
taxa were
collected.
The 110131 values ranged from
5.79 to 6.94 Nv
collected
representing? insects in the
order Diptera. MBI scores
tfall of the SDD.
assessed
in 2006 were consistent with
MBi values obtained during 1998 and
2001-2005. NIBI
over all the ,ears
for UPSTREAM and DOWNSTREAM sites were
7.1 and
ivelv. Both of these
overall scores warrant a "goodlfair
rating." However. two-factor
ANOVA revealed the difference
in NIBI values to be significant
(p<0.05) between upstream and
downstrearn sites, indicated
that stream habitat quality is better at the DOWNSTREAyl
sites.
our observations
with data collected in 1988 (IEPA
report). and 1992
(IEPA
report). MBI values for
the
Sangamon
River associated with the Sanitan District of
Decatur
-,were significantly lower
than values obtained during the 1988 survey but
were aenerally
]ties obtained in the
1992 report. In addition. when comparing present
NIBI scores
scores determined during
a 1998 stream assessment conducted by Eastern
Illinois
n -. a continuation of
the
trend of improved biotic
irate
2 006. As
in the previous sample
periods the fish community in 2006 again vas
Stream qualiný in the Sangamon
River basin cvas evaluated by fish
population sampl
and the Index; of
Biotic Intearit-\-. A total of 2'317
fish of 26 species were collected as I
I s
dominated by
the family C"yprinidae (minnows
and carp). Significant differences were not
observed (>0.05) in
community-based measures
of diversity between UPSTREAM and
DOW?ý'STREAM
reaches. Stream quality
in the Sangamon River basin as evaluated
population samples
and the Index of Biotic
Intearitv ram.ýed between 26 (site 6)
to 44 (Site 12).
especial
quality of poor to
good.
Overall
mean IBIs for data polled form
-2006 ,were
31 and 34 for the L`PSTREAM
and DOW NSTREAM reaches. respectively
.
rences were observed
in community based
measures of diversity between UPS
suo4gesting= that overall habitat
gtrality based on the fish
the DOWNSTREAM reach.
DOWNSTREAM sites associated
Nvith the main treatment plant outfall
from the Sanitary District
of Decatur may have increased
IBI rating
due to the predictable instrearn
lows an
p
due in part to nutrient
loading. In addition.
all mamstr
d autochthonous
primary production
chest percent of organisms
or the 8 main
channel sites
as those received in the
previous basin sunevs
conducted in I
fish community
metrics, there has been
no reduction in the quali
d on
ated near
the Sanitary District of
Decatur in the last 20 years.
: rýczzi::cx:iriri:ýcicýc.csexxaýxýr:eicxiraczcc-.`rirzaczzzieýczx:r7eirsexxxzxi:ýe7cxiexzýc;ci:
O
verall. biotic community structure
and habitat character]
erpass i
s
tern.
Established
biocriteria includin4-
fish and macr
t
fined similar quality
the SanLamon
. IL is a homogeneous
brate indices
su-gest that
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
discharge from the SDD
main treatment plant
actually enhances qualitA of this stream resource.
Although fauna
may be responding positively
to elevated primary production derived from
nputs to the stream- biotic communities
of the Sangamon River most likely benefit
from
the more constant instream
flows resulting from discharge of treated effluent. Data on benthic
diatom community structure
confirms that. this group of organisms
likely is the
most
sensitive to
variable stream habitat quality. In
future vears. emphasis will be placed on evaluating
the
presumed positive impact
of the SDD on stream communities relative
to what
«e txiieve
might
iinental
effect of extremely variable flows
upstream of the plant resulting from the
unpredictable releases
of water from Lake Decatur.
In addition. we specifically intend to revisit
u ti -1'7
-1'7
I 'on
'on
of water hardness as a va n 'able for establish'
i in(, v.,ater quality especialk, as it relates
to
concentrations of cations such as nickel
and zinc. In ?007 and beyond-
we
will be making
additional biotic
collections in effort to determine
the bioconcentrations of these elements in
macro in vertebrates and fish. 'We
have little doubt that enhancement of the flow
regime in the Sanýýamon
River due to the
SDD more than compensates for an\ impact. real or
perceived. that may
arise from loading of nutrients or
solids into the stream.
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
n
Impoundm
hers to create reservoirs
used for irrration purposes. ass urban
water supplies_
and recreation. is commonplace. However. impoundments may impact downstream aquatic
and their
surrounding
terrestrial habitats. Diminished water quality and availability.
closures of fisheries. extirpation of species. groundwater
depletion. and
more frequent and
intense flooding are increasingly distiný.tuished as consequences of current river management
associated
with
impoundments (Abramovitz 1996. Collier et cal 1996. Nairnan ct al 1915).
Specifically. dams can affect riverine systems by
altering flow regime.
changing nutrient and
loads. and modlfvinv= enerav flow
(hi--on
et al 1995). As
a
result. river reaches
doýti-nstream from
a dam may no longer able to support native species. which will be reflected by
reduced inte rity of biotic communities. (Nalman
et al 1995. NRC
1992).
A natural flow re,_,irne is critical for sustaining
ecosystem inte--rit-v and nati
rivers (Foff.
et
al. 1197). Dams can have
vaniný7
ef `eets on downstream aquatic habitats
depending on the purpose for which the dam was built. Impormdmertts used for urban water
supplies reduce flow rates below the
dam throughout the entire year (Finlayson et al. 1990 as
well as increased daily and seasonal variability in flow
regime (Finlayson et al. 1994.
McMahon
?003). In addition. abiotic variables including temperature.
turbidity. pH. conductivit-v and solids concentrations are altered in the downstream ri
(e.g_ (Finla\-son et al. 1990.
AlonL with stream impoundments. point source
and non-point
source
pollution can
have
profound effects on the ecological integrity
include agriculture. livestock --razin
'
waste are examples of po
ý.
Non-point sources of pollution may
d industrial
Quality Act of 19721 encouraged wastewater treatment plants to upgr
to r
result. many communities were
forced to build advanced tertian water treatment
et al 1985). Yet these treatment facilities still ex
Carpenter and W'aite (2000) documented
that concentrations of phosphorus vyere highest in
streams draininu agricultural basins and at sites influenced by wastewater discharges. .N-
al (?002) reported that selvage
effluent inputs had elevated nitrate levels. These
enhanced nutrient inputs can be expected to increase
productivity- ,vithin a river because
detrital
processing usually are limited by loxv ambient stream nutrient
concentrations (Stockner and Shortreed 1978. Elwood et al I
Physical habitat (e.a.. flow regime. bottom substrate composition. instrearn coyer. etc.) and
chemical water quality must be suitable for support of
individual species in lotic systems and
maintenance of the integrity of aquatic communities. The Sangamon
River
offers art
opN
to study these relationships it) a stream influenced by impoundment as well as point source
T
aamon River Basin
is a 14.000km2 watershed covenn<= all or portions of
eir7hteen counties in central Illinois. ,More than 35.10 km of streams within the basin course
throu«h glacial and alluvial deposits creating rypically lotiv gradient stream with sand and gravel
substrates. Streams within the basin have been
impacted for most of the past century. recei
is from both point and non-point sources. Current land
use is
80%
agricultural
of
which
85%1's corn or so%'beans. The
great expanses of prairie that once existed in Illinois have been
reduced to isolated hill and sand prairies coupled
with remnants along highway and railroad
right-of-ways
and
native
deciduous woodlands now are limited
to
stream
riparian
areas. Major
metropolitan areas associated with the San<amon
River are Blooming-ton. Decatur. and
Springfield representing a combined population
of more than 500.000 residents. Impoundments
associated with urbanization include Lake Taylon-ille. Lake
Sangehris. and Lake Springfield on
the
South
Fork
of
the
Sangamon.-
Clinton Lake on Salt Creek: as well as Lake Decatur.
h such influential factors at play the status
of the biotic integrity of the San >amon River
onstantly in flux. In 1998-99 and continuing
from 2001-2006. an intensive sampling
program vas initiated to document,
temporal and spatial heterogeneiný of an 8.5 km urban reach
of the Sangamon River
beginning
just below the Lake Decatur Dam
and extending,
downstream
to incorporate discharges from the Sanitary,
District of Decatur (SDD). This study has been
nded to characterize stream habitat quality and
to assess impacts resulting from ongoing
municipal and reset-voir management by evaluating biotic integrity at various trophic levels in
the
context of the physical and chemical nature
of the Sangamon River.
Histo
ling locations associated with
operation of SDD that were
prominent landmarks within
the
Ciry
of Decatur. Illinois. USA and have logged GPS coordinates
sites (Table 1). Sites were established
initiall-v in 1998 during an assessment of
I impacts of discharges from combined sewage overflow (CSO)
facilities as
well
a the
main treatment plant. All sites were located
in the mainstern of the Sangamon River eaten
tream of the dam. which impounds
Lake Decatur to the WycUes Road Bridge on
of Decatur. Sites 1. 3.
4 . 5 . 6. 7. and 8 are within the UP
t he
main treatment plant- and Sites 9. 1 1 and 12
h extends from the main treatment
plant
discharge
to
allout this re
yM of
the
SDD
main treatment
l
ted from the Sangamon
intersection
of
Homestead State
R 600E and CR 8
1 entering
the
Sat
as either
g 2003.
kiVI site
In Trail
d Site 10 (located in Stevens
largely due to their location outside
are more or less isolated from
reservoir or sanitan
protocol after 2003.
features considered
are
f the Sangamon River.
coln
other sites
e these Sites
in
sample
Assessment
Procedure (SHAP). which evaluates lone habitat quality using
mportant
to biotic integrity. vas performed by
us during the month of JUIV it
1998. 2001. and 2002 throuo7 2006. At each stream
site. t- o individuals independently ~
s related to substrate and instrearn
coyer. channel
morpholo-!L,,N,
and hydrology. and
III
th,
our
habitat quality types using guidelines established by the
y
(1994). The
mean total score of the 15 metrics lýotms
overall habitat
quality rating for the stream reach under consideration. Habitat
quality of the UPS"
rid HOWNST
oor:
59
- 100 =
hes were
categorized on the basis of its
ir: 100 - 14
2 =
Good
e llent.
Average SNAP scores
for UPSTREAM
and DON"S T REANI sites were 82
respectively. Nonetheless.
physical habitat structure
based on SHAP still results in classification
of all mainstern sites as "fair"
quality stream reaches indicating
that the physical structure of the
homogeneous.
11
,physical
structure
provides a backdrop for
the ability of the study reach to support a
flora and fauna. Routine
assessment of characteristic water quality variables
superimposed on
substrate characteristics.
channel rnorpholom and bank features can aid in
understandng the functioning
of stream svstems. Given
that organisms exist within often-
narrow ranges of tolerance
for certain physical and chemical characteristics of
their environment.
analysis of
these variables is imperative for
understanding? the potential for anthropogenic
impacts to decrease biotic
integrity of natural systems. As
a result, "ve incorporated routine
of various physical
and chemical features of the Sangamon River
sites studied dur
2002.
xvl-ich based
on principal components analysis.
revealed significant differences between
the LtPSTREAiti=1 and DO'vt`NSTREAN1
reaches. Ivlonitorirrg of
relevant variables continues
through 2007.
Qualitative judgements (good vs.
bad) based on established biocritena
using data
2000 -2006 were inconsistent.
The f/lacroinvertebrate
Biotic Index classified both reaches as
GOOD/FAIR. although conditions
are improved significantly DOWNSTREANI of the,discharge
ent. And the Fish Index
of Biotic Integrity calculated from 1998. 2001
ified both reaches
as FAIR. but ryas able to detect
~a
si
DOWNSTREANI of the
m ain treatment. Also,
since 20102
we have continued
to refine our sampling protocol for
e nthic al;ae
for monitoring stream habitat quality. Indices of
diatom
re did not differ between
UPSTREAM and
DOWNSTREAM
reaches
based on analysis of spring
and fall sample periods. Hovveyer,
qualitative comparisons of
shifts in community
dominance Nverc possible
and clearly indicated pro
for biomo
M ethods
Field data collection
and water chemistry determination
collected
even- tAvo to four weeks from
February to November. 2006.
Sampling
ryas initiated at the Lake Decatur
dam and preceded downstream. While in the field,
additional
abiotic variables (dissolved
oxygen. pH. conductivity. and
temperature were
a :Amphibian and 'vlanta multiprove. Surface
water samples -were
collected at 0.3 m below
the surface aid returned
to the laboraton- on ice and analyzed
within
generally
accepted time limits. All samplinv
and analyses were conducted according,
to Standard
i%4ethods for Examination
of VVate, and V astewater (APHA.
199j).
In the laboratory.
suspended and total solids
determinations were made by drvim-, residue
collected on standard tLdass Fiber filters
as well as unfiltered samples
placed into tared porcelain
crucibles
at
103-105
"C. Total dissolved solids were
calculated by difference. Total phosphorus
(following frersulfate digestion) and
soluble reactive phosphorus (utilizing
filtered. undigested,
sample aliquots)
were determine
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* * * * * PCB 2009-125 * * * * *
for determination of ammonia nitrogen.
and total oxidized mtro4zen (N0,-N ý N0ý-?°t) was
determined via the cadmium reduction method.
Colorimetrv of all nutrient analyses was
determined
usinu a Beckman DU Sao Life
measured by titration
to colonme
:e UV/Vis Spectrophotometer. Alkalimr was
ds. For all chemical artah-ses. due
consideration
was
given
to
quality
control and q
urance procedures. including, but not
el analyses of labormorv
standards.
Hacroin
vertebrates
Macroinvertebrate samples were
collected from 8 of the -1 I sites using modified multiplate
samplers (I-lester and Dendv 196'). Substrates
were placed on the stream bottom Ior periods of
six weeks. beLLinnim.,
July 1~0. ?006 to allow colonization. Samplers were collected with
aid of
dip-net. in order to avoid loss of invertebrates.
and placed in wide-mouth plastic containers. All
organisms
were preserved in the held with 95% ethanol containing
rose bengal. After so
macro invertebrates were identified
to the lowest possible taxonomic level and data
were
used
to
calculate a Nla
each
taxon is
literature and pr
is Index (MBI) according
to Hilsenhoff(1982). In this method.
d a pollution tolerance value
ranging from zero to eleven based on available
held experience.
Based on present assessment methods. M
reflect water qualitti as follows (IFPA 1988):
<
5.0 - Excellent: 5.0 - 6.0 - Very g
GoodJFair: 7.6 -- 10.0
K
Poor: => 10.0 - Ven- Poor. Macro invertibrate Biotic Index,
scores for ?006
were compared to those data. which were pooled
from 1998. ?001 through 2005.
Fish
Fish were sampled on
effort at each site. Fish were
identified to spe
possible. although voucher s
1
were not practical. specimens Nvere preserv
laboraton-. Species richness
and evenness (Pielou_ 1977) were used as fundamental measures
of
diversitx. Fish communitti data also were
used to determine the community-based
0130. Which uses
twelve metrics in three categories
to appraise
fish
cornmunities
(Karr et al.. 1986). Values of 1. 3. and 5
are assigned for each metric. and the values for
the
individual metrics are
then summed to generate a score
from I`' to 60. Calculation of IBI values
was aided by an in
utility of
I
follows: 51-60 - excellent: comparable
to best situati
er
v e characterization of streams. as
pis to standardize sampling
nan disturbance.
4 1-50.
good: good fishen for
gamefish: species richness may
31--f0.9 - fair:
bullheads. sunfish.
and carp predominate: diversi
intolerants reduced. 211 -30ý 9 - poor: fish
dominated by omnivores and tolerant forms: diversity
notably reduced. <21 - yen- poor: few fish
of any species present. no sport
fishery exists. Fish IBI scores for ?006
were compared to those
were pooled from
1998. ?001 and ?00? through 2005.
B enthic algal (diatom) samples
Artificial substrates
were
continuousIv
exposed at I I sites in the main channel
of the Sarazarnon
River from 10 July - a
1 July during= 2007. Substrates
were I a 3 inch clean v.,lass microscope
ded at the surface of
the
stream
in comznerciaily available periphvtometers (
"'i1
telv,
all but -' substrates
were
lost
due either to natural occurrence (i.e.. high
discharge events) or
due to vandalism.
As such. fart
pursued as results
would have been
uninformative or inconclusive.
Results
w
ere
riot
bit ater chenristrt-
Levels of 1? separate
water quality
variables were determined for
eleven mainstem sites in `?006
(Table 3). The trend
established in prior sampling
rears continued
throuiXhout this recent
sampling period.
with levels for
each of the variables being
generally higher in DOG ?NISTREAM
locations. Most
notably. higher concentrations
of forms of phosphorus
and nitrogen were
observed along with a Caeneral
trend of elevated conductivity.
presumably resulting
ge from the main treatment plant
of the Sanitary District of
Decatur. Water cherrristrY
continued to be relatively-
homogeneous over
the entire study reach
during periods of hi
rarge from the darn which impounds
Lake Decatur.
Macroin vertebrates
A
total of I I Hester-Dendy
Multiplate samplers were placed
along the main stern of the
San<amon River associated
with the Sanitary
District of Decatur for detemxirration
of
vertebrate communities.
For the eleven sampling
locations eve %vere o
fected data for eight
sites along the stretch
of the Sangamon River associated
ýtith the
Sanitary
ct of Decatur. a total of 5828
orLanisms representing
19 macro invertebrate taxa
were
collected
(Table I ). The MBI values ranged
percent of organisms
collected representing?
5.77 to 6.94 for
the
in the order Diptera.
armel
sites assessed in `'
for
-')ý Both of
revealed the
a nd ?001 - 2005. MBI scores
averaged over the see
difference in NIBI values
to be
irtdicatinL7
that stream
aoodf`fair ran
ficant
(p<-
ites were 7.1 and 5.9_ respecti%
pstream
and downstrearn sites.
°UAcM sites.
Fish
A total of '317 fish of
?6 species from 10
families were collected
at I I sites during July 2006
(Table 3 ). As in the previous sample
periods the fish community
in ?006 again was
dominated
by the family Cyprinidae (minnows
and carp).
Significant differences were
not observed
(p>0.05) in cornmunitN-based
measures ol'dl%-erslr%
between UPSTREAM
and
DOWNSTRB,VM
reaches.
Stream quality
in the Sangarrion River
basin as evaluated by fish
P
ulat'on samples
and the Index of Biotic
Integrit-v rariged from 28
(Sites 6) to 4-4 (Site
12).
OP I
I
I
'era]] strcýam quality
of poor to {good.
Overall mean IBIs for data
pooled frorn 1998.
?001-?006 were _31
and 34 for the UPSTREAM
and
rtfirmed
this difference
to
be
habitat quality, based on
the fish community.
is improved in
r eaches- r espectively.
<0.05).
suggesting that overall
ed in the stream
were recovered. further
anaIN sis
diatom assemblage
was not attempted.
Discussion
Overall. the SanLarnon
River extending from
the darn. which impounds
Lake Decatur to the
W-v&les Road Bridge. can be
considered a fair quality
aquatic system with minimal
habi
variety.
Althouah there is sianificant
variation in ph-sical
habitats UPSTREAM and
DOWNSTRE.AA1 of
the SDD. variability
in SHAD ratings were
primarily dependent upon such
factors as substrate stability.
pool variability and
quality due to stream flow. arid loss or
reduc
of riparian zone
vegetation that had
occurred at each specific
site, The primary difference
between
UPSTREAM
arid
DOWNSTREAM
reaches is attributable indirectly
to
metrics
related
to flow. The DOWNSTRE
ANI reach
receives continuous floe-
from SDD. whereas
UPSTREAN1
flow varies CLreatly due
to unpredictable reservoir
discharges. Such alterations
have lead to simplification
of stream habitat
with concomitant reduction in species
diversity and
biotic
inte.rin and an overall
decline in quality of
the aquatic resource.
Based
on physical habitat stricture
as measured
by SNAP. the reaches of the Sangamon
which %ve studied.
are indistinguishable.
Flowever. PCA confirms
that UPSTREAM and
DOWNSTREAM
reaches are
distinct or, the basis of
their physical and chemical characteristics.
Discharge from Lake
Decatur is the primary
input to the UPSTREAM
reach. resulting in our
observation
of relatively higher
variabilin in fjOW and nutrient
concentrations. Conversely.
stable and predictable
instrearn flows observed
in
rive s-,-sterns (Sanders
c-t al. 1985:
Walde 1
988).
'Ke also
believe that drastic reduction
o
discharge is detrimental
to habitat quality
in the
UPS
I KLAM reach.
uyeratt. results
a threshold exists
with respect to flow. i.e.
periods when discharge is
en flow is below this
threshold. the UPSTREAM
and DON"STREAM
reG
ý,lhile they appear to behave
as a con
suggests that water quality
is comprom
ides
as confirmed by work conducted
in
983: Peckarskv 1983:
Vti'ardy &. Stan
inuum when discharae
exceeds -IOU cfs.
downstream
from the darn to the discharge
of
-ion River extending
air treatment
plant of the Sanitary District
of
Decatur
as a result of management
to maintain
resenýoir levels by eliminating
o
-e management
ofý Sangamon
River tray require maintenance
of instrearrr floýý
above the proposed
threshold (100 cfs) by
continuous discharge from
Lake Decatur.
of SDD
are characterized
by lower pH. perhaps resulting
from addition
of CO, due to respiratory
breakdown of organic
matter in the wastewater
treatment process.
These sites may also have greater
potential for instream
priman productivity
aýs a result of
indexed by higher levels
of dissolved solids.
conductivity, total alkali nit".
horns. Elevated concentrations
of suspended solids
and chi orophyll
ites indicate
that suspended organic
material including
phvtoplankton algae
derived from the
rese5 oir may
be
supporting
heterotrophs in
the upstrearn
reach. In
contrast. DOWNSTREANI
sites ar-e maintained
by autochthonous primary
productivity that is
supported by relativel\
higher concentrations
of plant nutrients
derived from
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
the sanitary discharge.
V,*e
conclude that SDD
discharge may be facilitatini, a shin from a stream
system that relies on
allochthonous input of algae to
one that relies on autochthonous instream
ductivity.
Qualitative evaluation of the two stream reaches
requires assessment of stream biota to determine
whether or not
differences in the tWo stream reaches are reflected b\
higher trophic
levels.
Such
an evaluation of overall stream
habitat quality can be made via biotic indices involving
macroinvertebrates and fish. taxa that have
become widely used for biotic assessments.
DOWNSTREAM sites were
characterized during 1998, ?001-?006 by si<gniicantly lower ,VIBI
scores and higher IBI values- indicative of
improved habitat quality capable of Supporting diverse
and a variety of different
trophic levels. DOWNSTREAM sites associated with the main
treatment plant outfall from the SDD may have
increased Integrity due to predictable instrearn
flows and increased
autochthonous primary production due in part to nutrient loading.
When comparing our obsenýatiorts made during the ?006 sampling
period with data collected in
(Sanitary
District of Decatur) and ?001-?005 (Sanitary District of'
Decatur) both IBI and
MBI values for DOWN STREA:'vt sites associated with the maim treatment
plant outfall were generally similar or slightly improved
compared to values obtained during, all
previous sampling periods. Thus
the upgrades performed to the main plant in 1990 and
the
Lincoln CSO in 19x1`' by the sanitation district have
lead di
gamon River which has been maintained
over the past seven years.
onallv. there has been no reduction
in the quality of the San<gamon River section located
near the Sanitary- District of Decatur in the last
?0 years.
r biological
monitoring was confirmed b% our extensive analysis of
oiled on artificial substrates
during ?00`? and 2003. However. y
d to be reconsidered. Exce
re to utilize collections from naturally occurrirr<,7
substrates.
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 1. List of the
13
sites utilized by tine
Department of Biolog
D
is
conducted on renc
o ln Park - above out-fall
Site . ý' - Lincoln Park - oucfall canal
r of the
San
anron
Rs-,-er
associated
b elow outfall
Site 4-4 - Oakland (L.incoLn Park Drive) - above
Oakland
(Linncoln
Park
Drive) -
below outfall
7`n Ward - upstream of outfall
Site -7 - 7`}' Ward - downstream
of ourfall
ain Treatment Plant - upstream, of main outfall
49 - SDD Main treatment Plant - downstream of main outf
k
in
Fairview
Park
Site
'-,I
I - San2amon
Site '-t-"
-
Sanaarnon
of stevens
Creek
near the Lincoln Trail Homestead State Park. I Lm north
of the intersection
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 2. Measured water
quality
variables
far 11 mainstern sites in the Sangamon River associated with the SL1D.
total
TDS
6
2 /23/06
4'20/06
5/9/06
6 /6/06
6 129/06
8 /9/06
9/15/06
10/13/06
11/16106
2006
Average
2!21'06
2/23/06
4/20106
5/9/06
6/6/06
/08
8/9/06
9/15/06
10/13/06
_
11/16/06
2006
Average
1 19.9
1 29.8
1
9.9
1 7.5
1 6.3
1 7.9
1 9.4
1 12.6
1 7.1
1 12.6
1 8.5
23.8
24.7
26.7
22.6
11.6
7 ,8
19.3
313
602
5 44
521
507
341
531
606
9.0 711
7.8 593
0 .44
5,60
2 49
0.56
197
7.97
131
6.44 0.27
249
0.39 0.22
158
0.96 0.48
276
7.80 0.35
236
0.08 0.06
249
3.67 0.14
227
3.39
12.92
DL
0.17
0,18
0.22
389.3 383.3
DL 8.8 400.0 391.2
0.04 10,0
422.7 412.7
0.07 30.0 370.7
340.7
0.01 31.0 350.0 329.0
0.02 13,0 302.7 289.7
0.35
0.23 25.0 225.3 200.3
0.42
0,22 11.0 144.0 133.0
0.12
0.04 17.0 376,0 359.0
0,11
DL 22.0 372.0 350,0
0.18
0.05
17.4
336.3 318.9
3 14.0
2.4 4,5 1276
263
0.47
0.05
DL 6.8 384.0 377.2
2 .5 4.5
364
236
5.84
DL
DL 8.8 401.3 392.5
18.4 10.4
602
164
0.55
0.16
0.03 12.0 445.3 433.3
3 10,2 18.5 8.3 544
197
8.55
0.19
DL 31.0 366.7 335,7
3 6.8
23.8
8.0 520
197
7.00 0.21
0.25
0.02 30.0
357,3 327.3
3 6.7 24.4 8,3 518
223
0.42 0.12
0.21
0,02 18.0
314.7
296.7
3 7.9 26.7 7,8 345
184
1.36 0.44
0.36
0.28 27.0 217.3 1903
3 9.0
22.3
8.5 542
263
8,34
0.38
0.40
0,25 7.0 160.0 153,0
3 13,1
10.9
8.4 513
289
0.21
0.07
0.17
0,06
20.0
378.7 358.7
3 7.2
7,8 9.0 709
315
3.97 0.16
0.11
DL 23.0 374.7 351.7
3 12.0 19.1 7.8 603
233
3.67
15.37
0.19
0.05 18.4 340.0 321.6
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 2. (coat.)
total
06
4/20/06
5/9/06
6/6/06
6129106
819/06
9/15/06
1 0/13/06
11/16/06
2006
Average
4 28.1
'18,4 10.4 603
236
4 9.5
18,4
8.2 552
210
4 7.5 23.5 8,1
528
223
4 7.0 24.4 8.3 516
210
4 8.0 26.3 7.7 353
158
4 9.2 21.9 8.5 545
263
4 11.8
9.8 7.7 566
263
4 7.2
7.8
9.1
710
315
4 11.8 18.8 7.5 589
230
212!06
5
10.1
2123106
5 18.3
4120106
5/9/06
6/6106
6 /29106
819/06
9/15/06
10113/06
11116/06
5 9.6
5
7.8
5
6.9
5 7.9
5 8.9
5 8.5
5 7.1
2006 Average
5
11.4
NFi3 P04 - TP P04 - SRP TSS TS
TDS
0.48
0.05
DL 4.0 381.3 377.3
6.11
DL
DL 9.6 397.3 387.7
0.52
0.17
0.04 19.0 434.7 415.7
8.49
0.17
DL 32.0 392.0 360.0
7.30 0.32
0.24
0.00 34.0 366.7 332.7
0.41
0.13
0.22
0.03 21.0 329,3 308,3-
1.33 0.23
0,36
0.26
34.0
230.7
196.7
8.37 0.43
0.36
0,23 13.0 162.7 149.7
0.59 0.10
0,25
0.09 18.0
372-0 354,0
4.03 0.21
0.11
DL 22.0 354.7 332.7
3.76 10.07
0.19
0.05
20.7
342.1 321.5
2 .4 3.4 1206
276
0.47
0.05
DL
6.0 397.3 391.3
2.4 4.2 362
197
5.87
DL
DL 11.2 393.3
382.1
8 .3
2 3.7 8 .0
2 4.4 8.3
2 6,1
6 03
210
0.54
0.16
0.04 9.0
422.7 413,7
5 47
210
8.49
0.17
DL 39,0 340.7 351.7
522
210
6.94 0.26
0.25
DL 30.0 362.7 332.7
515
210
0.41 0.16
0.20
0.02 20.0 309.3 289.3
346
158
1.30 0.43
0.35
0.26 36.0 242.7
206.7
545
263
8.29
0.42
0.39
0.24 15.0 180.0 165.0
9.5 7.8 565
236
0.61 0.10
0.25
0.10 16.0 356.0 340.0
7.8 9.1 710
289
3.79 0.21
0.12
DL 25.0 376.0 351.0
1 8.8 7.5
592
226
3.67 9.63
0.19
0.05 20.7 343.1
322.3
Table 2. (coat.)
t otal
6
2/23/06
4120/06
5 /9/06
6/6106
6/29106
8/9/06
9/15/06
10/13/06
11/16/06
lkalinlty
TON
NH3 P04 - TP P04 - SRP TSS TS TDS
6
9.1
2 .2 4.0 362
6 7.1
23.5
6 6.5 24.4
6 6.6
26.2
6 9.3
10.5
8.2
8.0
8,2
7.6
8.3
6 6.8
7.9 9,0
603
546
523
524
366
553
728
686
0 .06
DL 6.4 384.0 377.6
2 76
5.81
DL
DL
10.4 410.7 400.3
249
0.53
0.17
0.03
9.0 422.7 413.7
197
8.37
0.19
DL 39,¬7 390.7 351.7
6 .85 0.28
0.28
0.00 39.0 377.3 338.3
249
0.42 0.33
0.24
0.01
18.0
346.7 328.7
158
1.30 0.50
0.38
0.28 30.0
240.0 210.0
2 89
7,91 0.35
0.38
0.20
5.0 181.3
276
0.30
0.06
0.09
0.00 20.0 458,7
289
3.52 0.12
0.10
DL 22.0 364.0
342.0
6 11.2
18.9 7.6 595
253
3.55 6.84
0.19
0.03 19.9 357.6 337.7
2/2/06
7 9.4
3.3 3.3 1063
263
0.47
0.05
DL 4.8 393.3
388.5
2/23/06
7
13.1
2.2 4,1 362
249
5.81
DL
DL 12.8
4/20/06
7 28.1
18.4
10,4 603
243
0.54
0.16
0.03 14.0 441.3
5/9106
7 9.0
18.4 8,3
547
190
8.70
0,21
DL 39.0 381.3 342.3
6/6:06
7 7,5 23_6
7.9
523
210
6.82
0,29
0.27
0.00 42.0 380.0 338.0
6 /29/06
7 6.5
24,5 8.2 525
223
0,41 0.15
0,28
0.00
22.0 346.7 324,7
8/9/06
7 6.5 24,5
8.2 525
171
1.21 0.46
0.40
0.27 70.0 306.7 236.7
9115106
7 8.7
21.8 8.2 552
144
7.88
0.33
0.38
0.20 14.0 197.3 183.3
1 0.`13/06
7
14.1
9.7 8.2 736
289
0,23 0,08
0.17
0.00 66.0 522.7 456.7
11/16/06
7
6.8
7.9 9.0
_
_686
263
3.19 0.11
0.11
DL 20.0
360.0
340.0
2006 Average
7 11.0
18.6 7.6
612
224
3.53
7.72
0.20
0.03 30.5 372.3 341.8
Table 2. (cont.)
t otal
2123106
8 14.0
2.1 3.8 362
158
4/20/06
8 27.4 18.4 10.4 603
223
5/9/06
8 8.9 18.4 8.2 547
197
6/6/06
8 7.2 23.5 8,0 522
210
61129/06
8 6.6 24.6 8.3 531
223
8 19/06
8 7,7 26.1 7,6
375
197
9;15106
8 9,3 21,5 8.2 559
289
10/13/06
8 10.1
10.4 8.0 694
289
11116/06
8 7.0
7.8
_9.1
696
289
2006 Average
8 10.7 18.9 7.5 681
234
2/2106
9 8,3
4.2 3.6
9
12.8
4.3 4.1
4%20106
9
27.3
18.4
10.4
5 /9106
9 8.7
18.7
616/06
9 7.2 23,6
6%29106
9 6.8
8/9/06
9 8.0
9 115106
9 9.2
10;13106
9 11.0
11116/06
9 6.1
2 006
A
verage
9 10.5
8 .1
8 .2
2 11 8.1
9.0 8.9
NN3 P04-TP P04-SRP
TSS TS TDS
0.53
0.06
DL 5,6 386.7 381.1
5.72
0.00
DL 12.0 398.7 386.7
0.53
0.16
0.03 8.0 422.7 414.7
8.46
0.16
DL 43.0
406.7 363.7
6.91 0.29
0.26
0.00 47,0 392.0 345.0
0.40
0.14
0.23
0,00 16.0 332,0 316.0
1.36 0.33
0.34
0.24 11.0
232.0
221.0
7.91 0.31
0.37
0.20 13.0 205.3 192.3
0.21 0.06
0.14
0.03 31.0 433.3 402.3
3.52 0.11
0.11
DL 23.0 376.0 353.0
3.56 7.28
0.18
0.03 21.0
358.5
337.6
1 288
236
0.51
0.67
0.53 6.8 508.0 501.2
485
354
6.17
0.81
0.81 11.6
518.7 507.1
632
236
0.53
0.22
0,17 13.0
440.0 427.0
741
210
8.49
0.85
0.62 41.0
489.3 448.3
817
249
6.56 0.27
1.23
1.02
44.0
532.0 488.0
1 815
236
0.43 0.17
2.53
3.08 14.0 1122.7 1108.7
1 455
249
3.90 0.29
2.04
3.02 35.0
780.0
2526
407
5.92 0.18
3.62
4.43
8.0
1133.3 1125.3
3981
420
0.78 0,13
2.27
2.51 15,0
2064.0 2049.0
1005
302
3.76 0.01
1.23
1.12 18.0
496.0 478.0
20.9 7.5 1475
2 90
3.70 4.23
1.55
1.73 20.6 808.4 787,8
Table 2. (coat.)
total
/06
519106
6(6106
6129/06
819/06
9115106
1 0/13 !06
11/16106
2006 Average
2 '23/06
4120/06
5(9%06
6/6/06
6129/06
8 /9/06
9115/06
10113106
11/16,06
2 006 Average
11 13.4
4.3
4.0 470
354
11 27.4
18.4 10.4 645
236
1
1
8.6
18.7 8.2 740
210
11 7.2 23.6 7.9 778
249
11 6.9 25,7 8.2 1851
381
11 7.3 27,0 7.8 1523
302
11 9.5 23.8 7.3 2395
381
19.7 8.3 4035
407
1 1 6.1
8.5 9,0 871
_
315
11 10.7 20.7 7.5 1447
311
1
2 16.0
2.7 2.8 145
289
12 13.9
3.8 3,9 463
354
1 8.1
10.4
655
263
12 8.4 18.3 8.2
751
236
12 6,9 22.5 8.0 741
236
12
5.9 23.7
8.1 1676
394
12 7.7 26.2 7.9 1418
302
12
8.6 22.1 8.2 2252
407
12 9.4 15.3 8.0 3229
433
12 6,5
8.3 8.9 810
289
12 11.0 19.3
7.4
1214
320
N H3 P©4 -
TI
0 .47
0.53
1.21
0 ,50
0.4 0
8.52
0.92
6.56 0.23
1.26
0.21
2.45
4 .10 0.42
2.00
0.15
3.44
DL
6.30
2 .25
0.83
1.53
0.48
0.52
1.36
0.51
0.36
0 .21
0 .23
0 .55
6 .13 0.14
0.80
0 .82
0 .98
2 .27
1 .79
3 ,08
2 .14
_
3.61 DL
0.62
3.88 11.00
1.39
0 .34 6.8
1.33 8.4
0.22
13.0
0.73 42.0
0.97 47.0
3.08 15.0
1 .0
T S TDS
458.7
451.9
653.3 644.9
458.7
445,7
514.7 472,7
524.0
477,0
1 106.7 1091.7
782.7 761.7
1109.3 1104.3
2229.3 2140.3
446.7 427,7
828.4
801.8
4.47 5.0
2.68 89.0
0.66 19.0
1.76 26.6
0.32
0.23
0.65
0.77
2.75
2.51
7.6 484.0
8.0 642.7
22.0 465.3
39.0 508.0
43.0
500.0
20.0 1018.7
36.0 737.3
4 76.4
634,7
443.3
469.0
457.0
998.7
701.3
0 .47 25.0
416.0 391.0
1.49 24.6 752.3
727.7
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 2. {coat.}
Date
total
T DS
2/2106
2'
`23106
4120/06
5
%9106
616106
6/29106
8/9106
9/15%06
1 0/13/06
1 4 18.5
14 26.1
14 8.0
14
7.0
14
6.3
14 7.7
14 8.9
14 10.6
14 6.3
e rage
14 11,6
4 ,2 3,8 734
18.3 10.4 655
18.2 8.2 761
22.6 8.0 775
8.1 1437
8.3
1830
21.2 8.3 2100
8 .6 3829
8.8 896
18.8 7.5 1420
20.0 497.3 477.3
341
6.50
1.33
1.33 12.8 705.3 692.5
236
0.53
0.36
0.23 27.0 469.3 442.3
246
8.61
0.85
0.60 46,0 549.3 503.3
263
7,48
0.20
1.09
0.80 75.0 542.7 467.7
433
0.56 0.38
2.08
2.16 24.0 872.0 848.0
302
4,78 0.59
1.83
328 41.0 976.0 935.0
381
5.58 0.19
2.77
3.89 12.0 965.3 953.3
551
0.76
0.13
2.29
2.27 6.0 2040.0 2034.0
368
3.79 0.02
0.93
0.71 36.0 472.0 436.0
342
3,91 7.86
1.41
1.56 30.0 808.9 779.0
Table 3.
Macro
Invertebrate data collected In 2006 from the 8 Sangamon
River
sample sites associated
with the
Decatur Sanitation
District
Total
Number
749
1301
926
959
832
# of families
6
10
7
6
10
MBI
6.898531
326
442
13
687
2 93
9
11
8281
5.935154
Table 4. Mean MBI Scores
for Sangamon River
sites upstream and doenstream of the
main discharge from
the Sanitary District
of Decatur Treatment Plant
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table S. Fish data collected
at 11 sites in the Sangamon River
tar the Sanitary Dist
P
rT
I cta
n V
r ht
rtrxneos
Leoornrs cr
nell
Ettieastcxna n
i n" n
L etxxnis hurnrhs
Lepornis
9r
C
6
u r.
44
1
22
7
6
L
P
l us jai
1 1
-These
wee ti-a Indmduals Found
T otal Nun,be: o
f
indrvvcluals
6 8
88
2 12
7'?
96
-72
120
304
8 89
133
256
T otal Taxa
11
12
10
8
11
6
9
2
13
14
11
index of 6")c Irnegnty 1!131) Score
3¬3
40
3 6
36
28
28
36
36
42
4
d
4 0
R4ean
161 Upstmant
34.57
Mean 161 Doxn7sweant
40.50
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 6. Meab
IBI scores far Sangamon River
sites upstream and downstream of the
hsrge
from the Sanitary District of Deactur
Treatment Plant
Year
9
e am K e
1
0 01
2 00
z
oo
20
0
0
34
a ll mean
1
31
1
34
Biotic Assessment of Water Quality in
a
Reach of the Sangamon River Receiving Effluent
From the Sanitary District of Decatur
Eastern linois University Report
July 2008
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Biotic assessment
of
water- quality in a reach of the San
rom the Sanitar-v
District
of Decatur
Charles L. Pederson Ph.D. and Robert U. Fischer. Ph.D.
Department of Biological Sciences
Eastem Illinois Universit-V
61920
Submitted
to:
per Lane
Decatur. Illinoi
Introduction
d ment of rivers
to create resen-oirs used for
irrigation purposes. as
urban water
supplies. and recreation.
is commonplace.
However. impoundments
may impact
do,wnstream
aquatic systems and their
surrounding terrestrial
habitats. Diminished
water
qualit-- and availability. closures
of fisheries. extirpation
of species. groundwater
depletion. and more
frequent and intense
flooding
are
increasingly distinguished
as
consequences
of current river management
associated with impoundments
(Abram
1996.
Collier ei al 1996. Naiman ei al
1990. Specifically. dams
can affect riven
systems
by altering flow reggime.
changing nutrient and
sediment loads. and
moditving,
enera-v flow (Ligon
et al 1995). As a result.
river reaches downstream from
a dam may
no longer
able to support native species.
which will be reflected
by reduced integritA-
of
biotic
communities.
(Naiman et al 1995. NRC 1992).
critical for sustaining ecosystem
integrity and
native biodiversitýl
in rivers
(Pots'. qtr al. 1997). Dams
can have v
habitats
depending on the purpose
fects on downstream
aquatic
poundments
used for
urban water
supplies reduce flow rates
below.- the dam throughout the
entire year
(F inlayson et al. 199-1) as ý% ell as increased
daily and seasonal
varia
(Finlayson et al. 1994.
McMahon &. Fiitlayson 2000.
In addition. abiotic
perature. dissolved
oxygen. turbidity. pH. conduct)N-itA and
solids
d in the
downstream river system (e.`g.. (Finlayson
et al. 1994),
1 export high concentrations
of nutrients into rivers. Carpenter and
'vVaite
pollution
may include agriculture. livestock
LTrazin(_,. and urbanization while
sanitary
discharýre
and industrial waste are examples
of p(
s ource pollution.
the
Water
Quality .-pct of 1972
to upgrade
their systems and. as a result.
many communities were forced
to build
advanced tertiarv water
treatment facilities (Karr et al
1985).
Yet
these treatment
documented that concentrations
of phosphorus were hiyghest
in streams draining
on-point source pollution
can have
ffects on the
ecological intetgritA- of river systems.
Non-p
auncultural
basins and at sites influenced
by wastewater dischar<2es. while Twichell
et al
(2002) reported that sewage effluent
inputs had elevated nitrate levels.
These enhanced
peered to increase productivity
within a river because primar%.
productivity and detrital processing
usual]\- are limited by low ambient
strewn nutrient
concentrations
(Stockier and Shortreed 1978. Flwood
et ýal 1981
habitat
(e.g.. flo\ý regime. bottom substrate
composition. instream cover.
etc.)
nical water quality must
be suitable for support of individual
species in
aquatic
communities. The San,-,amon
River
opportunity to
study these relationships in a stream
influenced by I
pint source discharges. i rte
Santaamon River Basin is a 1-1.000 km'
watershed
or portions of eiuditeen
counties in central Illinois.
More than 3 740 Lm of
ms within
the basin course throu!7h glacial and
alluvial deposits creating ty-nically
with sand and gravel substrates. Strearris within
the basin have been
m pacted
for most of the past centun _ receiving inputs from
both point and non-point
sources.
Current land use is 80°,6 agricultural of which 85°,i} is corn
or soybeans. The
great expanses of prairie that once existed in Illinois
have been reduced to isolated hill
and sand prairies coupled
with remnants along highway and railroad right-of-ways
and
ive deciduous woodlands
now are limited to stream niparian areas.
Major metropolitan
areas
associated with the Sangamon River are Bloomington.
Decatur. and SpnnCgfield
representing a combined population
of
more than
500.000 residents. Impoundments
associated with urbanization
include Lake Tavlorville. Lake Sangchris.
and Lake
ringfield on the South Fork of the San-amon: Clinton
Lake on Salt Creek: as well as
ecatur.
Dam and extending
downstream to incorporate discharges
tided to characterize stream habitat
q
Project
History
ongoing- municipal and reservoir manat ernent by
in 1998 during an assessment o
Lies from combined sevva<,,,e overfový (CS
potential impacts of
yell as the rnain
treatment plant. .ill sites were located in the cnainstem
of the Sangamon River extending
t play. the status of the biotic integrity
of the Sangamon
t1v in flux. In 1998-99 and continuing from `_'001-?006. an
ling, prog=ram was initiated to document temporal and
spatial heterogeneity
urban reach of the Sangamon River be,-,Iinin`g
just below the Lake Decatur~
i
m int-tit lanlmnrk:,; vtithin the City. r)t'T7erntxir
s tream of the dam. which impounds Lake Decatur to the Wyckles Road
the west edge of Decatur. Sites 1. 14. J. 6. 7. and
8
are within
the
UPSTREAM reach extending from the dam to the discharge o
located in the DOWNSTREAM reach
vv
hich exten
main treatment plant discharge to the Wvckles Road
Bridyge. Throughout thi
hic levels in the context
of
2003. samples also
were
collected from the
n additional DOS :ýISTREAM site (=14) located
I
km
north of
the
of CR 600E and CR 800N. near the Lincoln Trai
_' (an open channel entennL the SanLamon River from the Lincoln Park
CSO)
and
10 (located in
Stevens
Creek
in
Fain-ievv Park)
are
distinct
from other sites larg
due to their location outside of the mainstern of the SanLamon River. Because these Si
isolated from reservoir or sartitan discharges, they are not included in
sample protocol after 2'003.
Y
The ....
trearn
Habitat
assessment
P
rnrerilirt-
( tiI4,-%P)
w h,ý,-h
._";ý.lrlcýzteý lots- 1:W'.
usinL,, features
considered important to
biotic integrity. was
performed by us during-,
the
month
of July in 1998. 2001. and
2007 through 2006. At each
stream site. two
independent]\ assigned
metrics related to substrate
and instrearn cover.
channel
morpholo;av and
hydrologV. and riparian and
bank features to
one of four habitat
quality types usimt
guidelines established by the
Illinois Environmental
Protection
A4aency (199-1).
The mean total score of the
15 metrics forms the
basis of an overal
habitat qualitAý
rating for the stream
reach
under consideration.
Habitat
qua
U PSTREAM and DOWNSTREAM
reaches tyere care<aorized
on the basis
of its SNAP
score
as follows:
<59=
Very
Poor: 59 - 100 =
Fair: 100 - 1-12 =
Good:
>
1-12 = Excellent.
AP scores for
UPSTREAM and DOWNSTREAM
sites were 8-I and 95.
s superimposed
on substrate characteristics.
channel morphology
and bank
o f all
mainstern s i
p li-. sical
structure of the stream I
s
can
aid in understandim.,_ the functioning
of stream systems.
Given that
This overall
physical structure provides
a backdrop for the abilit- of the
study reach to
port
a diverse flora and fauna.
Routine assessment
of characteristic water quality
organs
charact
understanding the
pate
natural
systems. As a result.
chemical
features of
ithin often-narrow
ranges of tolerance
for certain pht sical and
chemical
their environment. analysis
of these variables is imperative
for
at structure based
on SNAP still results
in
"fair" qualit,,
stream reaches indicating
that the
m ogeneous.
po-genic
impacts to decrease
biotic irate
we incorporated routine analyses
of various
River sites studied since
2002
al components
aria
giant
Q
ualitative judgements
Good vs. bad) based
on established Nocriteria usin,
data from
1998.
2000
-2007
«.ere consistent.
The Macroinvertebrate Biotic Index
clas
reaches
as GOOD/FAIR.
ho,. ever. the MBI dovvrtstream was
the upstream
MBI. indicating conditions
significantly improved DOWNSTRE.,Vvl
of the
discharge
from the SDD main treatment.
And the Fish Index
of Biotic Inte_T1 ty
calculated
from 1998.
2001 throutrh 2007 classified
both reaches as FAIR. but
was able to
detect a
significant difference bet-,ýeeen
stream reaches ýýith improved habitat
;TREA.NI
of
the
discharge from the SDD main
treatment. Also, since 2002
we
h ave c
ontinued to refine our
s
ampling
p rotocol for d evelopment
o f b enthic a
monitoring stream
habitat quality. Indices of diatom
community, structure did
not
differ
between UPSTREAM and DOS'
periods. However, q
s ed
on analr-sis of
a fire comparisons
of shifts in
ible
and clearl-v icatcd promise
for utility of
for biomonitorin2
stream conditions.
Methods
t Ion a :
r
V4'ater
quality
data tkere collected
on six occasions from Nlav to
December. 2007.
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Sampling
,as
initiated at the
Lake Decatur dam and preceded downstream.
While
in
the
field. additional abiotic variables
(dissolved oxygen. pH. conductivity.
and temperature
were determined) Using
Eureka Amphibian and ?Manta
multiprobe. Surface
water
samples tivere collected
at 0.3 m below the surface; arid returned
to the laboratory
on ice
and arialvzed within
<-enerally accepted time limits.
.1.11 samplin
conducted
accordin-7 to Standard Methods for
Examination of Water
and Wastewater
1990. In the laboratorti-. suspended
and total solids determinations
-were made
bv
drt-in, residue collected
on
standard
-lass fiber filters as
well as unfiltered samples
placed
t ared porcelain crucibles
at 10;-105 "C. Total dissolved
solids v.ere calculated
b\
difference. Total phosphorus
(folio,.wing persulfate digestion)
and soluble
reactive
phosphorus
(utilizing., filtered. undi`-ested.
sample aliquots) were
determined usiMx the
ascorbic acid method.
The phenate method was used for determination
of ammonia
nitrogen_ and total
oxidized nitrogen (NQ,-N -Y-
NC)_-N) was determined
via the cadmium
reduction method. Colorimetrv
of all nutrient analyses ýkas determined
usint,, a Beckman
DL' 5;0 Life Science UV'Vis
Spectrophotometer. YAlkalinity and
hardness were
measured by titration
to colorimetric endpoint methods.
For all chemical analyses.
due
consideration
was given to qualiry control
and quality assurance procedures.
including but
not
limited to parallel analyses of laborator<
standards.
.'6.1acrain vertebrates
ed from 9
of the: I 1 sites usin<_
modified
multiplate samplers (I-lester
and DendN- 1962). Substrates
were placed on the stream
iods of six weeks. beginning July 9.
2'007 to allow colonization.
Samplers
order to avoid loss of invertebrates.
and placed in
,garlisms were p reserved
in the field k ith W h,
e thanol c ontaini
I
(1'/IBI) accorc
acrointi
ertebrates were
data were used to calculate a
Macroin
axon is
p ollution tolerance
value ranging, from zero to
eleven based on available
l
iterature and previous field experience.
Based on present assessment methods.
MBI
v alues reflect water quality as follows
( IEP., 1988):
- 7,5 -
Good/Fair: 7.6 - 10.0 - Poor:
>
110.0
- Ven Poor, Macro invertebrate
for 2'007 were compared
to those data.~ý hich ýýere pooled
from 1998.
1001 throu:ý,h
2006.
Fish
Fish
.k ere sampled on 9-11 of JuIN 2007 b<- hand
seinin-.
with
attempts to standardize
sampling? effort at each site. Fish were identified
to species. counted and returned
to the
stream
alive when possible. although voucher specimens
were preserved and retained.
When field identifications were not practical.
specimens were preserv
formal in and returned to
the laboratory, Species richness and evenness
(Pielotl. 1977)
were used as fundamental measures
of
diversitx.
Fish eommunM data also tsere
used to
determine the communit---based Index
of Biotic rote-rity (11311). Vdlich uses m
elr
e
me
in three categories.
t o
a ppraise
fist? communities
( K
a .rr et
al..
19 86). ý,'alues o
a re assl
for each metric. and the values for the
individual metrics axe then summed
to
rate a
score from 12 to 60. Calculation
of IBI values ,vas aided by
an interactive
program
ýMtten in Basic for use on an
IBM-PC (Bickers et al.,
1988). The utility
of IBI
c qualitative
characterization of
streams. as follows: _51-60
excellent:
comparable to best situations
without human disturbance.
41-50.9 --
ý_ood: wod
bullheads. sunfish.
and carp predominate: diversity
arid intolerants reduced,
21-30.9
--
poor: fish dominated
by omnivores and tolerant
forms. diversity notably
reduced. <"] -
vend poor:
few fish of any species present.
no sport fishers exists.
Fish IBI scores
for
20 07 «ere compared to those data_
which were
ere pooled from
1998. 2001 and 2002 through
Renthic algal
(diatom)
samples
.krtificial substrates
were continuously exposed at
1 I sites in the main
channel of the
San,,-xamon River from 10 July
- 31 Julv during 2007.
Substrates kvere I x 3 inch clean
4gla.ss microscope
slides suspended at the surface of the
stream in commercially
available
ytometers (ýý ildeo. Ire.).
Unfortunately. all but 2
substrates were lost due ei
natural occurrence
(i.e.. hi,-,Ii discharLxe events) or due
to
vandalism.
.As such.
torn assemblages wereýnot
pursued as results would
have been
uninformative or inconclusive.
Results
Water
chemistry
L evels of 13 separate water q
p ined
for eleven mainstenn
sites
in 2006 (Table 2 ). P rinciple
Components .- nalvsis confirmed
multivariate dif:
t rend
established in prior sarnplinýa
years continued throughout
period. with
levels for each of the variables
locations.
Most notably,
ed along
with a general
`varnefish: species
richness may be below expectations.
31--40.9
- fair:
conductivity.
presumably resulting
the main treatment plant
of the Sanitary District
of Decatur.
Water
continued to
be relatively
homogeneous over the entire study reach dunnt_=
f high discharge from the dam
which impounds Lake Decatur.
:' total
of' I I Hester-Dendy Multiplate samplers
were placed along the main
stern of the
ver associated with
the Sanity District of Decatur
for determination of
unities. For the eleven
sampling locations %ýe sere only able
to
collected
data for nine sites aloný,ý the stretch
of the SanLamon River
associated Vvith the
Sanitary District
of Decatur. a total of 67-13 organisms
representing
taxa were collected (Table 3). The MBI values
ran.L ed from :i.7 to 6.9 for the nine
sites
in the order Diptera.
N M I s cores for the 9 main c
hannel s ite s a ssessed In 2 007 t
vere lion
v alues
obtained during 1998 and 2001 2006.
NIB! scores aver
S'I'REAN1 sites were 7.04
.aver the
seven
\
ear
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
these overall scores
warrant
a "aoodlfair ratirt(-." However.
rwo-factor ANQVA
r
evealed the difference in
IvIBI values to be significant (p<0.05)
between upstream
and
downstream
sites. indicatimr that stream habitat quality
is better at the
DOWNSTREAM
Fish
.A total
of.--' 180 fish of 19 species from 10
families were collected at
1 I sites dunnu} July
`'007 (Table -I). :-s in the previous
sample periods the fish community
in 1007 again
was
dominated by the
family Cvpnnidae (minnows and carp).
Sid-nificantydifl-erences 4vere
not observed
(p>0.0_-5) in community-based
measures of diversity
between
and DOWNSTREA
N1 reaches. Stream quality in the
Sangamon Foyer
basin as evaluated
opulation samples and the Index
of Biotic Integrity ranged from 19 (Sites
3 and
to -II (Site 14). indicating
overall stream quality of poor
to good. Overall mean
IBIs
for
data pooled from 1998.1001-1007
were 31 and 3_5 for the UPSTREAM
and
STREAM
reaches. respectively. Two-factor
ANOVA confirmed this
difference
sting
that overall habitat quality-
based on the
community. is improved
in the DOW
Diatom
communitt`
structure
Because only two of the I 1 samplers
placed in the stream were recovered.
further analvsis
,,amon
I n,,,-os were priman
upon such factors as substrate stability. pool
variability and quafr% due to stream
flo'.
and loss or reduction ofriparian
zone vegetation that had occurred at each
specific site.
ches 1
Iv to metrics related to flow. The DOWNSTREAM
reach
continuous flock from SDD.
whereas UPSTREAM flow varies greatly due to
h alterations have
lead to simplification of stream
habitat with
concomitant reduction in spec
decline in qualitA
of the aquatic resource.
Based
on physical
uality aquatic
system with minimal
ariation in physi
y and an o-erall
at structure as measured by
SHAD.
the
reaches of the Sangamon
.
Which
we stu
indistin,Tuishable.
Hotiýever. PCA confirms that
.I'
istinct
on the basis of their physical
and chemical characteristics.
Discharge from Lake
Decatur is the primary
input to the
ch. resultin ,., in our obsen-ation
of relatively hiLoher
variability.
in floN\
Conversely, stable and predictable instream
e
N
-11 of
m
b iotic
r m
v work-
v
9
i n th
reach DOW ýSTRE. 'ýý the SDD facilitate den elop
ertt of more diverse
communities
as confi ed b
conducted
in other ri erine systems (Sanders 19f_i ;
Fisher
1983: Peckarskv 1983: Re lee
1985: Ross ei al. 1985: %Valde
1986: Resh el al.
1988). Difference in the
overall nature of the UPSTREAM and
DOS"NSTREAINT
reaches becomes
less
distinct
during periods of high reservoir
dischargge.
Vw'e also
believe that drastic reduction of instream
flow resulting by routine
elimination o
reservoir
discharge is detrimental
to habitat quality in the UPSTREAM
reach. Overall.
results suLTrgest that a threshold
exists with respect to flotk. i.e. periods
"hen discharge is
less than
400 cfs. When flow is below this
threshold. the UPSTREAM
and
DOWNSTR
discharge exceeds
-100 cfs.
of the
San`gamo
discrete while they appear to behave
as a continuum when
This suggests
wý
that water quality-
is compromised in the reach
from the dam to the discharge
of
the main
treatment
plant of the Sanitan District
of Decatur as a result ofmanat`ement to
maintain
e ls by eliminatinti
outflow. In contrast. effective management
of Samtamon
River may
require maintenance of instream flow above
the proposed threshold (400 cf:s)
ontinuous dis
of PC.A Factor analysis pro
caches. Sites DOWNSTREAM
of SDD may
productivity as a result of nutrient loading
as
xed b% hi<gher levels
of dissolved solids. conductivity. total alkalinity.
oxidized
nitrogen- and
phosphorus.
e'v'e
believe that suspended
organic material including
phtitoplankton algae derived from the reservoir
may be supporting heterotrophs in
the
UPSTREAM
sites. In contrast.
ilitatint, a shift from a
stream s,,-stem that relies on allochthonous input
of algae
to one that
relies on autochthonous instrearn primart prod ucti-,-I tv.
o f stream
mo
a m reaches
are reflected by hip==her
made
v
t have become
vvidek used for
sites %,. ere characterized during
1998. 200
d hiyaher
1131 values. indicative of improved habitat
diverse
biota and a variet%
ted with the
main treatment plant outtall from the SDD
increased inte;_rrity due to
predictable instream flows and increased
pus pnmar-, production due in part to nutrient
loading.
'ations made durinlg the 2007 sampling period with data
P A report). 1998
(Sanitarti- District of Decatur) and 2001-2 006
1 values for DOWNSTREAM
sites
were generally similar or sliwgl
during all previous sampling
periods.
l
in
1990 and the Lincoln CSO in 1992 b% the
sanitation district have
lead direct to improvement
of
the
water quality
of
the
Sangarnon
River which
has been maintained over the past
seven years. .Additionally.
them: has been
no reduction
in the quality of the Sangamon
River section located near the
Sanitary
ict of Decatur
in the last
Additional fish and
invertebrate specimens had been collected for
determination of tissue
levels of zinc and
nickel. but analyses were not conducted
upon request by the
Sanitary
istnct
of Decatur. Samples have been retained
in the event those analyses
arc requested
at a
future date. Instead. eve conducted a comprehensive
literature review
of the effects of
these
rwo metals on aquatic ecosystems
(Appendix: A).
xt contract year. special projects
are intended to determine
the effects of
sanitary effluent
on benthic al,2al assemblage structure and productivitN
using a
bioassay
approach.
This is intended to allay difficulties
eye have had with loss of
artificial
+
substrates.
In addition-
we are planning to initiate an investigation
of nutrient loading to
and export
from Lake Decatur.
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table
1. List of the 13 sites utilized
by the Department of Biological
Sciences far
studies
conducted on reaches
of the Sangamon River associated
with the
San
S ite
-1 - Lincoln Park - above out
Site
'-2
- Lincoln Park - outfall canal
Park - below
outfall
Site
"4
- Oakland (Lincoln
Park Drive) - above
outfall
(Lincoln Park Drive) - belo-w
out
Site
"6 - 7°'
ward
- upstream of outfall
Site '-7 - 7`'' 'A.'ard -
downstream o
S ite 48 - SDD Main
Treatment
Plant - upstream of main
outfall
M ain treatment Plant - downstream
of main outfall
Site
#
10 - Stec ens Creek in Fainiew Part:
- Samamon
River - downstream of
Stevens Creek
s Road
near the Lincoln Trail Homestead
State Park. l km north
of
CR
600E and CR 80ON
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table
2. Measured water quality
variables for 11 mainstem sites in the Sangamon
River
associated
with the SDD.
T otal
Date
Site DO Temp pH
Cond Hardness Alkalinity TON
NH4 PO,.TTr POr-SRP TSS TS TDS
6126/07
1
253.1
2094 0.91 0.12
0.24
0
14 14.5
2347
220.2
8/23/07
1 6.9 270 92 5,62.0
271.4
251.3
0.17 0.05
0.11
0,11 24.0
425.3 401.3
9x27107
1 4.4 20.9 8.3 516.0
236.7
223.4
0 15 0.19
0,15
0.07 26.2
384.0 357.8
10/25/07
1 7.1 11,6
7.8
501.0
261.2
1954 , 0.37 0.00
0.19
0.04 30.0
340.0 310.0
11/29/07
1
8.3
4.9
7
.4
474.0
212.2
167.5 0.27 0.10
0.11
0.04 6.9 321.3
314.5
1
2/13/07
1 12.7
6.0
7.8 677.0
253.1
209.4 0.25 0.03
0 1 1
0.01
19.0
4147 395.7
6 126/07
3
253.1
223.4 0.84 &11
0.22
0.12 22.5 226.7 204.2
8/23/07
3
4.5
261
8 .7 6 34.0
281.6
258.3 0.49 0,15
0.12
0.09 15.0 4573
442.3
9127/07
3
4
.4 2 0.6
7.9
625.0
257
1
230.3 0.39 0.12
0.15
0.06
29.2
4587 4294
10/25/07
3 4,6 11.8
7.6
526.0
228.6
237,3
0.64 0.12
015
0.03
12.0
345.3 333.3
11/29/07
3 6.6
4 5 7.6 574.0
271, 4
209.4 0.49 0.05
011
0, 04 6.4
382.7 376.3
12/13/07
3 9.3
5.8
7.7 649.0
255.1
209.4 0.68 0.09
0,13
0.02
15.0
444.0 429.0
6/26/07
4
249.0
209.4 1,16 0.09
0.24
0.13 24.5 2493
224_8
8/23/07
4 5.5 270 8 .8 5 59.0
263.3
230.3 0.16 0.03
0.15
0.11 33.0
425.3 392.3
9/27107
4 4.4 204
7.8
653.0
281.6
258.3 0.17 0.05
0,14
0.09
16.0
460.0
444.0
1 0/25/07
4
5.8 10.7
7.6
503.0
293.9
223.4
0.44 0.29
0.17
0.04
11.7
328.0 316.3
11
1"29107
4
8.6
2.7
7.6 627.0
287.8
265.2 0,38 0.66
0,12
0.05 3.6
382.7 379,1
1 2/13107
4 10.8
4.0 7.9 774,0
283.7
2373
072
0.33
0 10
0.01 12.8 525,3 512.5
6126107
5
249.0
2094
1 16 0.10
0.23
0 13 22.0 270.7 24$.7
8/23107
5 6.4 27.1 9.0 583.0
261.2
258,3 0.70 0.05
0
13
0.09 33.0 4200 387.0
9127107
5 3.9 20.5
7.8
648.0
293.9
237.3
017
0.05
0.16
0.09 18.5
466 7
448.2
10125/07
5 5.7
11,3 7.6
485.0
273.5
195.4 0.37
0.28
0.17
0.02 18.5
316.0 297 5
11129/07
5
7.3
3 .0 7.8 6 22.0
283.7
265.2 0.41 0.60
0.13
0.05 6,2
386.7 380.5
1 2/13107
5 10.4
4.0 7.9 767.0
285.7
237_3
0.72
0.31
0.10
0.02
12.9
508.0
495.1
6/26107
6
289.8
223.4 1.11 0.09
0.23
0.12 35.0 293.3
258.3
8123/07
6 5
4
2 70 8.2 656.0
265.3
258.3 0.36 0.05
0,11
0.09 20.0
425,3 405.3
9 127/07
6 6.6 22.4 7.6 746.0
326.5
286.2
0.11 0.05
015
0.05
14.2
530.7 516.4
10/25/07
6 6.0 12.4 7.6
465.0
302.0
2234
0.34 0.40
0.14
0.04
107
2880
277.3
11129/07
6 6.3
3.9 7.5
482.0
224.5
223.4 0.30 0.36
0,26
011 6 0 3173 311,3
12,13/07
6 9.9
4.2 7.9
735.0
279.6
216.4 0.67 023
0 10
0.03 13.7
492.3 478
7
6/26/07
7
244 9
223.4 1.20 0
12
0.23
0.13 42.0 306.7 264 7
8
/23/07
7 4.7 26.8 8 .0
671 0
0 0
2 79-2 0
43
0.07
008
0.06 28.0 4-147 4467
9
/27/07
7 5.7
18.8 7.6
595.0
273.5
258.3
0.05 0.02
015
0.05
32.5
410.7 378.2
10/25/07
7 71 11,6 7.8 470.0
228,6
2094 0.15 0.41
013
0.04
15.5
310-7 295.2
11/29/07
7 8 4
4.0 7.3 516.0
222.4
230.3
0.35 0.48
025
0.08
26.0 292.0 266.0
1
2/13/07
7 9.9
4.2
7 .9 7 39.0
2694
230.3 0.67 0,22
0.11
0.03 14.5 4947 480.2
6
/26/07
8
249.0
223.4 1.02 0.11
0.24
0.12
43.0 330.7 287.7
8/23/07
8 4.0 27.5 8.0
697.0
324.5
286.2 0.21 0.05
0,19
0.14 15-5
474.7 459.2
9/27/07
8
4 .7
2
1 1 7.6 582.0
253.1
272.2 0.04 0.05
0
18
008 16>.9 386.7 369.8
1 0/25/07
8 6.3
11.3
7 .6 4 82.0
244.9
195.4 0.18 0.30
015
0.01 17.0 304.0 287.0
1 1/29/07
8 8.6
3.8
7 4
405.0
195.9
188.5 0.32 0.41
0.25
0.13 12.3
2560 24'x.7
1
2/13/07
8 9.2
3
7 7.8
733.0
244.9
1954 0.58 0.33
0
15
0.07 15.3
470.7 455.3
6/26/07
9
2571
223.4 1 42 0.11
0.59
0.52 25.0
404.0 379.0
8/23/07
9 6.4 30.3 8.4
4031.0
504
1
6840
5.32 0.15
1.62
042 7.6 26440 26364
9/27/07
9 6.0 27.5 8.0 4283.0
465.3
718.9 5.38 0.05
2.00
2.53
7.0 2741.3 2734 3
10/25/07
9 7.3 22.2 8.0 4279.0
449.0
5444
5.67 0.05
1.94
2.86
10.7
2658.7 2648.0
1 1/29/07
9 9.4 184 7.9 3987.0
477.5
474,6 6.46 0.12
1.86
2.39
16.6
24747 2458.1
12113/07
9 7 7 170 7.8 3134.0
440.8
307
1 6 44 0.05
1 45
2.52
7 3 1966,7 1959.3
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 2. continued
9/27/07
10125/07
11/29107
12113/07
1 6.3 30 4 8.4 3941.0
11 5.9
27.0 8.0 4181.0
11 7.3
21,3 8.0 4234.0
11 8.7
16.8 7.9 3890.0
11
8.2
15-1
7.8
3080.0
6 /26/07
12
8/23/07
12
7.0
9/27/07
12 7.2
10125/07
12 8.1
11/29/07
12 9.0
12/13/07
12 11.0
8123107
9/27107
10125/07
11
/29107
1 3/07
2 9.8 8.2 3900.0
2.4.3 8.1 4300.0
171 8,1 3934.0
11.5 8 1 3681.0
9 .0 7,9 2043.0
1 4 10.4
29.2 8.1 3-438,0
14 8.9 22.3 8.3
4007.0
14
10,0
13.2 8,3 3694.0
14
13.3
6.9 8.2 2968.0
14 11
0
7
6 8 6
2202.0
471
4
698 0 4 89 0.05
1.93
510.2
670.1 5.06 0,05
1.99
473.5
488.6
6.08 011
2.14
8
2234
2.
2 .14 9.8
1 77
13.6
1
3.8
7.9
13,0 7.9
13.2 8.0
140 7.8
131 77
13.5 7,7
23 1 8,0
22.1 8.0
1 83 8
1 5.8 8.3
variable
DO
mg L-1
Temp,
0C
pH
Cond
us
Hardness mg I-1
Alkalinity mg L-1
TON
mg L-1
NH4
mg L-1
P04 - TP mg
L-1
P04-SRP mg
L-1
TSS
mg L-1
TS
mg L-1
TDS
mg L-1
601, 6
623.2
621 0
616.8
598.2
579.8
3942.8
3865.2
3571
3261
2 28.9 0.54
242.9
0.37
2 38,
7 0.47
2 41.5 0.36
2694
237.3
1.76 0.17
0.
2.55 8.2 2685.3 2677.2
2.62 13.6 2668,0 2654
4
2.88
217 24613 2439.6
6 13.7
6387
5 32.6
698.0 6.03 0,11
1.88
467.3
732.9
5,36 0.07
1,73
424.5
725.9 6.02 0.05
2.29
477.5
4677 6.46 0.13
1.80
357.1
279.2 5.95 0.12
135
2 6.37 0.06
1 78
4837
663.1 7.51 0.05
412.2
390.9
0.72 0.04
1.93
428.6
467.7
5.26 0.05
341
353
1
202
4
5.75 0
15
1 43
2 58.8
282.0
279.6
2
79,
6
1 98.8
2 52.7
4 67,3
462.0
451 8
4298
6
8
6.37 0.05
1.73
0 27
5 45.8 5,85
548.6 489
580,7 5.96
0
0 , 11
0 .27
0 .26
0 .22
0 .24
0 .23
0 .08
0 06
0 10
0 .13
0
14
0 .14
0.15
0.14
0.18
1.77
1 66
1.81
2.02
1.77 12.9 1294 7
TDS
0
.42
19.0
2604.0
2585.0
223 12,0 2729.3 2717.3
2.67 19.2 2486 7 2467,5
3 ,07 18.9 2300 0 2281.1
9 3.5
470.
2.60 37.9
2625.3 2587
4
2.72 19.3
2373.3 2354.1
176 24.0
1858.7
18347
1.82
277
1402.7 1375.0
0 2250.7 2230.7
2 ,03 16
87
417.6 402.1
4 243 408,8
419.5 401.6
410.7 397,8
396.5 373.2
378.4 363.0
2497 1 2487.2
2203
7
4 2 282.9 2266,5
2 5.8 2102
1
20764
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
`ýc3ýýitzýrý,
its
A nalysis o f w ater cliclilistry III a t I I I llaiEZstctla sitcs ill the S angamon (ti=er associated with t he
- 2-
-6
-4
-2
0
2
4
PG1
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table 3.
Macroinvsrtebrate data collected in 2007 from the 9 Sangamon River sample sites associated with the Decatur
Sanitation
District
Trtchoptere
HyýIsychidae
Coleoptera
nn
e
--
r
"0""8'
Furbel
ýýe
a
11ý
UP
=
6.84
Dawn =
5.87
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* * * * * PCB 2009-125 * * * * *
Table 4, Fish
data collected in 2007 from the Sangamon
River sample sites associated with the Decatur Sanitation District
G enus
phales
fctalurus
nphales
L ?orosonia
Moxostoma
Etheostorr7a
Gambusia
C arpoides
Notropis
Micropterus
Micropterus
rinella
notatus
macrochirus
n
otatus
1 24 1 168
27
38
purIctatcrs
p romelas
e thrurum
p unctulatus
0 1 0
2 39
4 1
0 1 0
S ite4
_44
7
17
0
69
20
0 1 0
1
0
SIte5
10
10
2
8
22
34
31
0
1 2
Slte6
13
40
57
42
5
27
Site? SIte6
1 10
19
4
47f-1 1
1 4
1 4
0
11
43
0
Siteg
54
4
1 8
12
0
10
54
65
97
0
0
1 2
43
23
0
_
10
3
1 3
0
0
0
0
27
2
Slte14
_
112
1
0
26
1 8
_
rside_
_
minnow
iii
cat
h ead minnow
liniouth bass
d bass
eelcolored shiner
keimouth
m
innow
low bullhead
T otal
61
Richness
6
1131
32
54
9
29
1 167
9
34
1
29
U p= 31.43
Down =
39.25
1 02
9
35
92
9
290 147 221
13
9
13
30
31
37
215
63
181
11
7
9
39
40
41
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
APPENDIX .A. Poten
ature.
constituting
2'0-?0C) ppm (by
weight) of the Caz-th's crust
(Goodwin
Introducti
Both
zinc and nickel are naturally occurrinv7 elements
(AI-SDR 2005). Zinc
and
as elemental zinc in nature (Llo-,d and
Showak 198-I). Nickel
r der
of
abundance
in the earth's crust. with an average
concentration of
0 .0086°ýo:
the concentration of nickel increases towards the center
of the earth. It is
comprise 0.`'`'°lo of the mantel and
5.8% of the core- thus making it the fifth
most abundant element on earth
(L'SDFIHS 2'005: Duke 1980).
Both elements are naturally
occurring. and both are considered micronutrients
and have
hate variable
solubilitA in aqueous solutions
bio!teochernical cycles that form the chemical
buildin-a blocks of life. They are divided
into tuo categories:
rnacronutrients and rnicronutrients. Macronutrients
are required by
in large quantities and include: water. carbon.
hydrogen, oxyLyen. nitro4>en.
phosphorus. sulfur. and calcium, klicronutrients.
like zinc are only required in trace
quantities (Audesirk
1996). The
National
Academy of Science estimates
the
Recommended
Dietary .Allowance (RDA)
I-'(-)r
zinc' is I 1 mL,d
for men mid 8
women (ATSDR 200:3).
sites and rucke
naturally
occurring element. but due to its reactivity (amphoteric: capable
o
chemically
either as an acid or as a base) it is not y
e and Nickel on
Stream Ecosvste s
(EPA)
has identified zinc at 985
of the 1.6
of the sites (ATSDR 2005). Zinc
release
from
both natural and anthropog==epic sources: hoEVever. releases
zinc chloride(ZnCl,). zinc sulfate(
acetate(Zn(C,
H ;O+ ). zinc cvanide(Zn(Citif ), ),
chromate(ZnCr0a ). and zinc ýh% droxide(
phosph
ent in nature.
i
c ommon
r
opogenic
anthropogenic
zinc
4 )
(Goodwin 1998: W"hIO 2'0(.)1 ).
ounds are naturally occurring. however the
EPA
has
de
toxic pollutant under the
Federal
(hater
Pollution Control Act and the Nati
etNiS(J4). nicks
The most commonly used and released
forms of nickel
chloride(:' ICl, ). nickel by droxide(N i(OH ), ). nickel
( '.Vi
(N1-l4):(SO4),). nickel
ride(?
Ni(-NO;),).
nickel acetate(N1(CH=CO)r). nickel oxi e(NO). and nickel
carbonate(NiCO,) (ATSDR
1005: Eisler 1998).
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* * * * * PCB 2009-125 * * * * *
Zinc and Nickel in the Env
ne and nickel are naturally occurring elements.
Zinc
is a bluish-white metal that
%vhite metal. and is insoluble in water (EPA 2003). Like
zinc. in nature nickel
is
o xide. and carbonate (Eisler.
1993). In typical riverine environments 90% of
zinc
is
present
as
aquo
ions (Zn(H,O)(,)-- (Spear. 1981 ). Elemental nickel is a hard.
lustrous.
found in multiple compounds: chloride. sulfate,
nitrate. hydroxide- and carbonate (Eisler
1998). Both elemental compounds have varying degrees
of solubility in tivater,
d nickel are characterized as hea`-%metals. -vvhich is a
loose term that
encompasses any of the high atomic weight metals (Nebel et al.
2000). .A major problem
with heavy metals
is that unlike organic pollutants. they are not broken do"hn by bacteria.
Since they are not de,raded they can bioaccumulate in the tikater column and
sediment.
leadmta toybiocnaLnification in the food chain (O«en
et al. 1995). HeavA metals are
extremely toxic because. as ions or certain compounds. they are soluble in water
and
eadily in strong acids. In nature. zinc
occurs
as
three compounds: sul
orbed into the body. Once in the bod% they tend to combine
with and
bit the functions of vital enz-,-mes. Even very minute concentrations
can have severe
oloý,ical and neurological consequences (Nebel et al. 2000: Oven et al. 1995).
In nature both elements
are regulated by biogeochemical cycles. Chemical and physical
dc2radation of rocks and soil release nutrients that arc available for biotic uptake, As
those orýýanism die they re-release their nutrients into the
soil or atmosphere. Zinc and
ash, and forest fires (Eider 199
precipitate back to
earth,
an
orunent as soil dust. from volcam
released into the atmosphere where
they
al, 2000), This c%c
drastically thrown out of equilibrium due to anthropogenic stressors. Hum
el include: minim(,. smeltint-. cornbustiori o
d industrial
setikaue.
road
surface
runoff.
Eisler 1998: EPA 2003 ). Normal backa-round
c and nickel vary vastly depending on the ecosystem and other
1e 2).
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Zinc
Z inc is a ubiquitous micronutrient that
is essential for normal trTowth_ reproduction.
and
«ound healing,
of biotic org>anisrns (Audesirk 1996; Eisler 1993).
Zinc is a cofactor for
more than
200 enzymes that are fundamental for maximum
catalytic actiyitti. cellular
respiration. chemical detoxification. metabolism.
and neurotransmitter synthesis
(Vesela
CT al. 2006: Eisler 1993: Rai et
al. 198: u'ri;ght et al. 2007). Its primary
metabolic effect
zinc-dependent
enzymes that regulate the biosynthesis and
catabolic rates c>
and DNA (EPA
2003: Eisler 19933).
Acute
and chronic toxicities
of zinc are variable b%
or,-a.nism
(Cable A-1).
nd antagonism with other
variables
The environment and
interactions Evlth other chemicals produce radically
altered patterns
ulation. metabolism. and toxicity: some
of which are beneficial to on=anisms
whereas others are
harmful (Eisler. 1993). Zinc bioavailabilin and toxicity
to aquatic
or4ganisrns are
hM,_hest under conditions of low pH. low alkalinity.
losv dissolved oxygen.
and elevated temperatures (ýVeathereley
et al. 1980).
R
Copper:
The toxicity of zinc is believed to be due to its interactions
ýý ith copper
xtures
of zinc and copper are general acknowledged to be more than
of aquatic organisms. including marine:
fish (Eisler.
Cadmium:
Zinc has been shown to dirnim
1990: Herkoyits &
n g zinc concentrations
al
s orption of
depresses
t al..
P re-eynncitrr r)f Omafn/T fnr ti, -n u-,-f,A:}cý: ir,
murus pules) protected
agt
I
Clurius la_eru) (Hicnly
et
al.. 1987).
xic effects o
sho«-z to
protect embryos
for 96h (Howell. 1985).
Aqueous solutions of Zinc-Cadmiurn mixtures are usua
additive in toxic1r% to aquatic organisms. including
lah et al.. 1988:
Verriopoulos and Dimas. 1988: Eisler and Gardner.
are less toxic to Duphniu muglw
than tyre
individual elements (Eider. 1993).
Zinc
exhibits
antaiomstic effects on uptake of
cadmium by -Tills and tissues of the freshwater clam (.4noderriu
ctif,,,eu) and other
:l1tacdowu. but accelerated cadmium transport
from the gills to internal organs (Hemelraad
). Exposure to cadmium maN cause chamaes in
the distribution of zinc since
th compete for a common transport carrier svstern in renal proximal calls. This
can cause zinc ace ttmulation in the l i% er and kidney. particularly
if dietary intake of zinc
deNelopmental maiform
is marginal (ATSDR
2
005:
Leant:
Line
is believed to
increase the toxicity of lead,
but
data are conflicting
(.
_'00'ý).
Lead-zinc mixtures
were more than additive
in toxicity to marine
copepods. and
fish accumulate
lead tip to 10 times
faster in sewvater with elevated
zinc
( Verriopoulos
and Limas 1988:
Eisler 1981). In terrestrial
animals zinc
[.ends to protect
against lead toxicosis
(Eisler 1993).
Zinc Bioaccumulation
and Biotic Affects
L ine does not
volatize from soil or water. but is
deposited primarily in
sediments throut'h
absorption and
precipitation. Zinc complexes
with
various
organic
and inorganic
'mops
to affect
its biolotTical activitA
and mobility in aquatic environments.
The level of ý
+
s aciditl- increases (ATSDR
-'M). The
relationship
between biota and
sediment concentrations
is not proportional_- the
biota
contains relatively
little zinc compared to the sediment.
Zinc bioaccumulates
moderately
in aquatic
organisms. bioconcentration
is higher in crustaceans
and bivalve species than F
in
fish. In some fish.
it has been observed that the
level of zinc found in their bodies
did
not directly relate to the
exposure concentrations.
It has been shorn that
bioaccurmilation
of zinc in fish is inversely
related to the aqueous exposure
(McGeer et
al.
2003). This
suggests
that
fish placed in en
hi--her
in urban
areas. eggs.
i
s p ositiV
(A SDR 2'005).
lover zinc concentrations
zinc concentrations tend
to be
he
liver. and lowest in muscle tissue.
Accumula
ein concentrations. and
is lower in all tissues
981:
Eisler &ý LaRoche 1972;
Grade et al. 1989).
the v,ater column-
unto and
e sult of
sediment
zinc on the food base of the
sucker. that is invertebrate
unkirtrick
acid Dixon 1989).
Miller et al.
(1991 ) conducted a stud%- to determine
the relationship
concentrations
of copper and
zinc in ,vater. sediment. benthic
invertebrates. and tissues of
White
Sucker K'uroslomus comnxersoni)
from six contaminated Ontario lakes. The
de.,aree
of metal contamination
in the lakes varied progressively and eýere
compared to
The% discovered
a direct correlation bet-veen
Zri concentrations in
invertebrates and
sediment- but not with water concentrations.
Concentrations of Zn and
Cu in fish
tissue were strongly correlated
with waterborne metal levels
rather than those
in sediments. The
concentrations of Zn in the liver. kidney. {gill.
bone arid stomach were
ificantly
correlated to waterborne concentrations.
Concentrations in the kidney.
o a less extent correlated with sediment.
Zn levels. The\ did not
discover a relationship
between fish tissue metal concentrations
and invertebrate metal
rile there were no
4gender differences in concentrations in liver.
kidney.
h er
e
w ere
s ianiticrnt d i f ferences t o ugonadal tissue.
LinC:
concentrations Stere
h igh er i n o varies t han to testes.
Nickel
importance. It is
trace element in animals.
althougrh little is know about
its
red a micronutrient based on studies of
nickel deficienc% in
1
several
animal species (e.ý7. rats. chickens, cows. 47oats), Nickel
deficiency primarily
affects
the liver and cal cause abnormal cellular morphology.
oxidative metabolism- and
fluctuating lipid levels. It has also
been shown that decreased
arotivth
and
hemoglobin
concentrations as well
as
impaired glucose
metabolism can be linked to nickel
deficiencies
(USDHFIS ?005; Zaroogain et al. 198-1). .cute and
chronic toxicities of zinc
are variable
by or-anism (Table A5). y
Svne
n tagonism with other variables
AmonL7 animals. plants, and microorganisms.
nickel interacts with at least 13 essential
elements:
calcium. chromium. cobalt. copper. iodine. iron. magnesium.
manganese.
molybdenum. phosphorus- potassium. sodium, and
zinc (Nielsen 1980).
At
the cellular
level. nickel
interferes with en7vrnatic functions of calcium. iron. ma-7nesium.
ese, and zinc (Kasprzak 1987). Mixtures of metals
(arsenic- cadmium- copper-
curv. lead.
zinc) containinu, nickel salts are more toxic to daphnids and
fishes
than the individual compounds (Enserink et al. 1991 ).
-additive in toxicity to aquatic al -aae in combination with
zinc
(WHO
:1 in binding, to
D
of D
knov,n as "finger loop domains.
cular targets
vitamins,
and polycycli
carbons (PAI-Is) (Eider 1998). Chelatinýi-, agents mitigate the toxicity of
nickel by stimulatint7 nickel excretion
(USPHS1993:
USDHFIS 2'005).
Chelators reduced
t he toxicity
of nickel to aquatic plants. presumable be lowering nickel bioax
(
WHO 1991). Lipophilic chelating agents. such as triefvlenetetramine
(1 _4X I 1-tetraazac% clotetradecane)
are more effective in abating nickel toxicltv than
hydrophilic ag'entsýlike EDT.. cNclohexanediamine tetraacetic acid, and
h-droxtiethvIenediamine triacetic
acid. Lipophilic agents are believed to be more
effective due to their abilit,, to bind to nickel both iratracellularly and extracellularlv.
rophilic agents cats only bind extracellularly (USPHSý1993:
USDHH F
Nickel Bioaccumulation and Biotic
affects
ncentrate t
o
aquatic o rganisms
o r small
terrestrial
mamma
l ,oý:'e'* er.
studies have shown that plants can tans: up arid accumulatc nlckzl
( ý
0
nll s
2'(:)03 ). Nickel concentrations in carnivorous fish (e.ýa, Lake Trout) did not increase
s lani
' ificantiv with
aure. and had a mean bioconcentration factor (BCF)
of
c oncentration
of
nickel in mussels ( Crussvstreu riijo,,inicu) a nd
o vsters Ofh-tilis e didis)
and I OpiAý-seaxvater for 12 vt eeks averaged 9.26
-- 3.56 and 12.96
e ight for C . virginicu. and 10.04 = 2 .66 and 1 6.43 W
3A
9p«iu
dry w eight
o r _t1. edtdis. There was a sianificant linear relationship
found bettikeen nickel uptake
by
nickel concentrations. There was an inverse
relationshi
nickel
concentrations and dry weight for both species.
However, after a
ration period in which the treated species
wvere returned to ambient flow
tltrations in
(."
rir(inicu
were reduced 73 and 89%
and
.1l edulis were
r educed 48 and 68°o respectively (Zaroo«ian
et al. 1984).
McGeer et al (2003) examined BCF's of various aquatic
organisms (e.g. algae.
arthropods. mollusks.
and fish) as a group based on whole bode metal
arid exposure
concentrations. For exposure concentrations within
the raniae of 3-5Op.,/L nickel in %tiater
a mean BCF value
of 106--56 .vas obtained. The results indicate an inverse
correlation
'alues and exposure concentration. There
vs-as no evidence that nickel
aquatic organisms
S urti eti N ational W
ater- Quali
d
zinc are naturally occurrin4u elements. T
c orrelations
bet\%een nickel
sediment concentrations and nickel concentrations
in IINer and tissue
samples of fish (USGS
2'000).
Toxic heavy metals, including
Ni
and Zn introduced into aquati
tend
to accumulate in
sediment. It is belietied that metals reactinL E%ith sulfides control
the
toxi
-ollinv- poreuater
(the
water tilling the spaces between g
W S). a component of iron sulfide can create
S ummary
and even indicated
that nickel concentrations in
increasing t rophic level. Likewise. the
U
.S.
Geological
sment
INAW'QA)
Program found no
statistical l\ slCan1ficant
1 accurnulation
are
etals (
h's biogeography and anthropogenic sources.
There I
i.
elements e:
. while the researchers and
and
anta.onistic reactions with other metals and
chemicals, however. the data is limited.
""r with the bioaccumulation
is incomplete when considerin.t all ofyearth-s
organisms in proportion to the amount
of
orýý,_arrisrrts studied. It is hard to conclude the affects of zinc and nickel
on
rorlment when there
are so mane confoundim factors that can alter their behavior.
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table Al. Solub
1998).
i nc and Nickel
Compounds
in "v'ater.(Eislerl993;
Eisler
Index
Solubility L,11-
Zinc Chloride
61.-1
Z inc
Sulfate (rrionoh%drate)
3.38
N ickel Chloride (hexah%drate)
2.-100-2'.300
Nickel Sulfate (hexahvdrate)
2.-10()-`'.4
Nickel Nitrate
-17
Nickel I1,,droxide
.13
l Carbonate
.09
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
( aci 'd"t 1 -\-;,alkal'n*
I it)
El,(oxidation-reduction potential)
ration status
(aerobic.
microaerobie.
anaerobic)
capacity
InorLani
composition
composition
I
Water content
Clay mineraloLn
H-,,drous metal oxides
tier
ý Cation exchanýLle c apacity,
anion e xchange capacit-
I
Temperature
i Solar radiation
drostatic pressure
i
cater hardness
Turbi
altitude
Electronic Filing - Received, Clerk's Office, June 15, 2009
* * * * * PCB 2009-125 * * * * *
Table A.3.
Background Concentrations of Zinc and Nickel.(Eisler
1993;
Eider 1998;
03;
Barcelout 1999; ATSDR ?00-+) (Concentrations
are subjecte
geographical
differences)
Z n
Brackish/Estuaries
er% Oirs
;streams
water
7
0mL,-%
l Opta/L
<7. I
pgIL
> 10pg%L
< 40pa/L
0.1-1 apa/L
< 40jg/L
0 . 1-1 0ýqý-2
/L
<1U . ,2
ý E 1-fects
100% ýnowth inhibition 7d
18
.Selenusirum
S. cupricorrn7tum
40-69ppb
95%
_ro«-th inhibition 1-Id
18
S. c upricornutum
I OOppb
& v77ec1'estruin
300m-o,
Lethal
-17
quudriccuda
.
ýcenedesirum
I00pta/ýc,
1 00% u rowth inhibition
-I-
cupricoinutuni
7 days
.'arthropods
Duphnia 7na`,na
1 -', 40mk-?
%k7hole bod\
?690m2.lkt7
Mortalitz
'A-hole bod-,
D Up1777iU P2717X
i s Toxicitti, of Zinc
2
ý " t""4
l C.v7
Hella U flecu
( "Q
L C50
LC50 24h
disiaidis a71n-`
LC50IOdass
Diatom
.1 ii-schiU
clOsieri
centrum micuns
'71- OO11u
7
2
18
18
41;9
11
-1;_47
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* * * * * PCB 2009-125 * * * * *
_Table
A4. continued
__
Species
Cane.
i lodc
nu
ucutilbrmus 5ftq:,g
.annelid
Cupitella cupitutu
(Adult)
Fish
Pintephales promeles
Re
4
8h ýi 25ýC
0
L C50 1'8 davs
47
Larvae
6004%
I t
8 00palg
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* * * * * PCB 2009-125 * * * * *
Algae
.-1 nuhuenu inc'q uu
l i s
I OM<U'L
.4nucvstis niduluns
1 60pw_>/L
( Blue-Green)
r 7edeSinCIS
uc'utilorinis
'L
p ellic1110su
100
M ollusks
Ju-u plicileru
?371
(Freshwater
snail)
Luinellidens MUrýZiriuli.s
(Freshwater
rnttssel )
Arthropods
Copepods
E udiuptornu.;
puduntis
3.6m-.'L
Preulpinus
''L.
eric?duphniu
dUhiu
1 3.0ftg!L
( 96h)
40
I 'L
LC50(48h) d pl-16.0-6ý - 5
38
D uphnia h.valine
1. 9m u L
Duphniu mugnu
days)
9
100Pg/1_.
Growth inhibited in 9 days
-42
A nnelids
Lumhr'iCUILIS
iwricuutes
Fishes
Ca
prinus
curpio
(Common Carp)
II
ctulurus p unclums
LCIO
tt)is_h_)
710
U T
t C'ýO
T oxicitv o ¬ Nickel
C Ot1Cý
s
G rowth inhibited
Photos
nthesis 1
Growth inhibited
No ;-uro-,vth in 1-1 d
R eference
e d
;0
ýO
0
- 19
29
G
rowth reduced -47°'0
50
Groýkrth reduced 8'0f0
50
d
50% In 14davs
.0-8. fl,
-118
-6.5
38
0 .0ma-%I. LC50(96h)
-1--'.p4
t o
Ilicropterus suimoicies
61-185P`I LC10
10
(LarL,emouth Bass)
1.-18-2.84mý7/L LCýO
10
Pimephules promelus
3,1m-./L
LC30(96hyd PH8.0-8.5
38
(Fathead mmncnO
>4.0ma/L
LC50(96h),d
pl-16.0-
:,
8
Amphibians
.-1 mhYstvmu Opucum
410u(,!L
LC
50
(Marbled Salamander)
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* * * * * PCB 2009-125 * * * * *
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* * * * * PCB 2009-125 * * * * *
-19
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* * * * * PCB 2009-125 * * * * *