Table 14. Anulytical Procedures 

Unit.sof Detection General use 

Parometer Method of a1wlysis (refer c~) measure limits standard 

TCin ~era ure /11 situ deteominarion \ISing •c 0.1• 

(Temp} Hydrolab 4041 or Hydrolab 

Surveyor II or Yellow g.s 

lnsnuments (YSI} mode 57 

di=lved oxygen mere.-

Dissolved in situ determination using mg/L02 0.1 mWL :=: 5 mgiL 

Oxyw:n {DO} Hydrolab 4041 or 8000 or YSJ 

model 57 di~lvcd oxygen 

meter 

Tr~arency Secchidisc inches I inch 

Total Filtration on ~ fiber mgiL TSS l mWL li~ded filter, detcrnnn.ation of 

solids (TSS) increase in weight;con dt).1ng at 103-105 

Volatile Loss in weight ofTSS !liter mWJ-VSS I mWJSW.'J'EO.ded upon ignition at 550"C 

sohds(YSS) 

Turbidity Nephelometric use of NTIJ O.lNTU 

(Turb) Hach model 2100A 

turbidimeter 

CondJctivily YS1 model33 S..CT jlllllnfan I jlllllnfan 

(Cool) oonducti~ity mel« or 

electrolytic ronductivity 

~set, model MCJ 

orH 4041 or 

SurVeyor II 

Alkalility Titration of 10 mL sample mgiLCaCOl I rngiL 

(Alk) 0.02 N H~O to 

bhenolph ein and 

rom cresol green-melhyl rod 

end points 

pH Sargent-Welch model PBL pH Units 0.1 units 6.5-9.0 range 

meter, calibrated in field or 

Hydrolab 4041 or H~ ab 

~oeyorll 

Nilralo- Cadmillll reduction mo:lhod tngiLN 0.01 mgiL 

Nitrite-N on Teclmicon Allt().Analyar 

(NC¥NOz-N) 

62 

YES 008000 
Table 14. (Concluded) 

Units of DeJection Genera/use 

Parameter Method of analysis (reference) measure limiz.~ standard 

Ammo11ia-N . Phenate method on TechniC<lll 

(NI-£3-N) Aull)-Analyzer mg/LN 0.01 mg'L 15 mg!L 

Total Digestion at 3 70"C follow«! mgiLN O.l 1ng/L 

Jgelclahl-N by iletennination of ammonia 

(TICN) as above 

TO!al Digestion to conven all 1ng/LP 0.001 rng!L 0.05mg'L 

phosphorus phosphorus f<nnS lb 

(fP) Orthophosphste fOllowed !lr 

delmninarion ~ascorbic acid reduction using 

T edmicon A1110-Analyz.er 

Dissolved Field filtration followed mg!LP 0.001 mg/L 

phosphorus by TP analysis as above 

(DI') 

Chemical Titrimetric, low-level tngiL I mgiL 

oxygen meiliod sample re6uxed wid1 a 

clenl3od (COD) sulfuric acid; potassiwn dicbromatic, mercuric sulfalc, 

and silver sulfutc solutioo; 

treated with standard ferrous 

ammooium 

~yU Concentration by filtralion, I llfiL 

extraction with 

delmninatioo 0= density and calca.tation of 

concentration by standard 

foonulae 

63 

VES 008001 
pH were measured at depths I foot below the surfuce and 2 feet above the bottom of 

Lakes I, 2, am 3, except "1lell they were tharnally stratified at Which time measurements 

were made only at a depOJ of I foot 

Sea:hi disc tranSpartDCies were •neaued using an &-inch dilllllder S=.hi disc, 

;wuch wa.~ lowm:d WJtil it disaJllle:lllld fiom view, mel the depth noted. The disc was 

lowered further and slowly raised unll1 it reappeared. This depth was also noted, and the 

average of the two depths was recorded. Site depth was measured using a weighted line 

calibrated in feet. 

Samples for water chemistly were collected using a 4.2-liter (L) plastic Kemmerer 

bottle. Near-surface (1 foot below surface) water samples were collected from all the sites 

. in the three lakes, and near-bottom samples (2 feel above the bottom) were collected Mien 

the lakes were thcnnally stratified, ll'lOSt oftm only a1 Lakes I aod 2. Total alkalinity and 

phenolphthalein alkalinity were measured in the field on these samples using Hach 

alkalinity kits. Sample bottles were filkxl and sent to the lEP A laboratory for additional 

analyses. Samples for dissolved phosphorus were filta-ed in the field through 0.45-

micrometa· (urn) pore size type MF-Millipore filters. AU samples d'eslined fur the 

laboratory were stored on ice during transp011 and kept refiigerated ~mtil processed. 

Vertically integrated samples fa cbkropbyll and ph}1oplanklon were collected 

using a weighted bottle sampler with a half-glllloo plastic bottle. The sampler was IOW«ed 

at a coostant rate to a depth twice the Secchi depth, or to oear the lake bottom, and raised 

at a constant rnle to the surfuce. Ollorophyll samples were transferred to a foil-v,.rapped 

quart sample bottle ax! filtered tbrough micro6bcr filters. The chlorophyll filters were 

then wrapped in alun:rin..un foil mel the Jillrale volume measured using a graduated 

cylinder. Filters were kept fraz:m in the laboratory unbl 8ll8lyzed For algal idootification 

aod enumeration, 380-milliliter (mL) WB!er snbsamples were taken, preserved wi1h 20 mL 

of formalin at the time of collection, m1d stored at room tetoperaturc 1mtil they could be 

. examined 

Also, vertically integrated 10-L samples were collected from site I at each of the 

three lakes for zoo~lankton identification and enumeration. The samples 'M're .filtered 

through a Wisconsin net, arxl the colleded zooplankton were placed in a 250-rnL bottle 

VES 008002 
with 10 mL of ethyl alcobol and 190 mL of deionized wale!:. In the labomtory, each 

sample was filtered through a 0.45-pm filter. The organisms were reruspeDded in 10 mL 

of deioni:IJod water. One mL of sample was pi!ICEd io Sedgwick Rafter Cell and examined 

using a diffe~ential contrasl microscope at I OOX magnification. Organisms in the five 

widths of the cell were COWlted and recorded. 

For alg<ll identification and enumeration, the sample was d'IOroughly mixed, atXl a 

1-mL aliquot was pipened into a Sedgwick Rafter Cell A differen1ial interference 

contra 1 microscope equipped with a lOX or 20X eyepieoe, 20X or lOOX objective, and a 

Whipple disc was used for identification and counting purposes. Five short strips were 

oounted. The alga.e species were identified and were classified into five main groups: 

blue-greens, greens, dia!oms, .flagellates, and others. For enumeration, bluo-green algae 

were coumed by trichomes. Green algae were counted by individual cells c:>«::ept for 

Actinas_ti'Um, Coelastrum. andPediastrum, which were recorded by each colony observed. 

Each cell packet of Sccnedesmus was counted. Diatoms were counted as one organism 

regardless of their grouping connections. For flagellates, a colony of Dinobryon or a 

single cell of Ceratium was reoorded as a unit. 

Ben!hic·samples b' maaoinvertebralc ccamination were colleded using a petite 

pooar dredge. The samples were washed in a 30-mesh screen bucket, and the residue was 

preserved in glass jars containing 95 percent ethyl alcohol. In the laboratory, the samples 

wel'e washed again, and the organisms were picked from the bottom detritus, identified, 

counted, and preserved in 70 percent ethyl alcohol 

Literature Rniew 

The literature is replete with publications dealing with lake and reservoir 

restoration, as a result of lhe impetus proviclod by the Congressional mandate through 'the 

Clean Lakes Program of the Clean Water Act. Noteworthy among them are: Dunst eta/. 

(1974), USEPA (1979), Q,oke arr:l Kemedy (1 981), Peter90n (1981), Wekh 

(1981), Reckhow ll'ld Chopra (1983), Chapra ll'ld Reckbow (1983), Cook-e eta/. (1986), 

Rclicld eta/. (1987), Relield eta/. (1988), Moore and Thornton (1988), Olcm and Flock 

(!990}, and Wedepobl el a/. (1990). 

65 

VES 008003 
Recently, two publications on lake management were released by USEPA Olem 

and Aock (1990) updated the .Lake and Reservoir Restoration Guidance Manual first 

prepared in 1988. This secood edition "'aS written primarily to give lake managers 

pmctical information on how to Jlrotect, restore, 1100 manage lakes and reservoirs. 

Anotha· manual, Monitoring Lake mid Reservoir Restoration, by Wedepohl eta/. ( 1990) 

is the first in a seri~ of technical supplements. This volume included information on 

de!.ign and implemeolltlion of a lake monitoring program during and after a lake 

restomtioo project. 

Lake restoration processes are broadly classiJied into those limiting nutrient and 

sediment influx and in-lake trealment and control measures. The fonner include point 

source nutrient renwval and control, nutrient diversion, and control of nonpoint sources of 

nulrients and sediment The Iauer include sud1 techniques as dredging, dilution and 

di:.-persion, nutrient inactivationlprecipitation, artificial desttatificatioo and hypolimnetic 

aeration, harvesting of nui.saoce organisms, and biological control of nuisance organisms. 

Not all the restoration techniques can be ~Y awlied to all lakes; occasionally, 

potential negative imp:lcrs do occur. 

This study, !iJase ID post-restoration monitoring of FHSP Lakes, followed phase 

II, a program of flow diversion and saliment dredging for nutrient and sediment control 

and removal Hence, this l.i1eralure survey, dealt with only the case histories of lakes 

'mere dive:sioo and dredging were the primary or JlXlia- restoration techniques employed 

to protect, preserve, and enhance the water qlllllity conditions and lake uses. The 

responses of these lakes to the ~mt techniques used are summari::red here to make 

the readers aware of the "'ide variations in results reported in the literature. 

Di11ersion 

Divasioo of nutrient-Deb inBow streams is one method of re&oring lakes by 

reducing both nitrogen mx! phosphorus sources. The diversion of treated wastewater 

efillleuts or stormwaters from eutrophic lakes and reservoirs has resulted in different 

degrees of suocess in reversing the eutrophication process and improving water quality. 

The diversion of ten tllll!licipcl wastewater treatment plant etlbms from Lake 

66 

VES 008004 
Washington, WA produced a significant improvement in lake water quality (Edmondson, 

1968, 1969, 1970). A similar diversion program for Lake Sammamish, 4 miles cast of 

Lake Washington, had little effect on trophic conditions {Emc.ry et ol., 1973). After 

nutrient diversion, by which appo'Oximately 40 percent of the Iota I phosphorus (TP) and 22 

percent of the nitrate-nitrogen input were diverted away from lsaaqunh Creek, the lake's 

lartlCSt tributary, there had been no measurable amelioration in surface water nutrient 

concentrations, algnl activity, light penetration, or hypolimnetic oxygen deficit The 

primary reason attributed was thai the amount of phosphorus (I') diverted did not result in 

the phosphorus input to the lake below the critical level. 

Significant short-term water quality improvements were obSC<Ved in Whjte, 

Muskegon, and Mona Lakes near Muskegon, Ml, for P, nitrogen (N), hypolionnctic DO, 

and chloropbyll a after the diversion ofrreated wastewater from discharging directly into 

these lakes. But the lakes did not cxperiem:e any si&nificant improvements in Secchi disc 

transparency (Freeman and Canale, 1979). Reduction in lake P concentrations were 

correlated with changes in nutrient londing. Similar correlations for N were ineonclusiye, 

but changes in ammonia and nittate levels were explained in terros of the effect of 

diversion on various limnological processes. 

Following diversion of ono-lhird of the external P loading of Lake Sammamish, 

WA, Welch et a/. (1980) neported tlJat P concentration decreased from 33 

micrograms/liter (flg/L) to 27 flg/L. Although Secchi disc and pbyloplanktoo biomass did 

not change, bluc-go'Cen algae decreased by SO percent. It was indicated that rapid 

community development of the shoreline might lead to an increase in P loading, which 

could equal ono-half of P p~eviously diverted in 1968. In contraSt, in the case of 

dilution/flushing technique, low-nutrient dilution water added to Moses Lake in 1977-

1978 produced significant improvements of lake water quality (e.g., chlorophyll a 

decreased 60 to 80 percent, TP decreased 50 to 60 percent, blue-green algae decreased 

from 96 pe«:ent in 1970 to 68 percent oftbe total phytoplankton in 1977-1978), and 

resulted in adequate control of productivity in portions ofthc lake (Welch and Patmont, 

1980; Welch, 1981). 

67 

VES 008005 
Lake Vesijarvi, Finland, "'as reponed to have shown rapid imp-ovement m 

bacteriological quality and water quality (Ke~o, 1982) after the diversion of muniopel 

wastewater that had been discharged to the lake fur 60 years. P levd decreased 60 

percent and N level decreased 30 percent. After several years, although the recovery 

pl'Ocess slowed, and blue-green algal blooms began to appear during summer months, 

subsequent changes bave indicated a continuing improvemelll. 

Garrison and Knauer (1983) evalua!ed a restoration projea with stonn sewer 

diversion, alwn treatment, and artificial circulation in Mirror and Shadow Lakes, 

WaupllCil, WI. Four years o.fler Jake restoration, there were no signs of the lakes reverting 

to the pre-restoration trophic state. 

The J"edooion in nutrient loading by diwrsion to a subatctic lake in Sweden 

produced a 75 pen:ent reduction in phytoplanl.10n biomass (Holmgren, 1985). Mean 

seasonal TP levels deaeased from 168 to 74 J.lg/L, and Secchi disc transparency increased 

fiom 1.3 to 2.1 m with a significo.nt sbift in algal species composition. 

To reduce P C)ICI.ing WJd the occunence of nuisance blooms of Osci/latoria 

agardhii, both P loading reduction (fu:m 3 to I g,lm2

) and intensified flushing with low P 

'"atm were impii:IOOlled for the restoration of Lake Velume, tho Nedlerlwxls (Hasper, 

1985). Results indicated a reduction in algal biomass and a 75 perocnt reduction in 

summer TP concentrations. 

Wclch eta/. (1986) studied the decrease in the release of sediment P ood oxygen 

deficit fufiowing wastewater diversion from Lake Sammamish, W A. The impovemenl in 

water quality bas been the result of a decrease in the 8l'laelllbic sediment P release rate 

during SUJtlJllel' and full. The rate decreastxl from 5.8 :t 2.5 milligmms per square meter 

per day (mg/m2 d) before and after wastewatec diversion (1964-1966 and 1971-1974) to 

an average of2.5 ± 2.5 rng!m2d in the early 1980s. A 50 percent decrease in hypolimnetic 

oxygen deficit rate bas bca1 associated with this decrease in the release rate. Total loading 

(including inlml81 loodiDg) decreased by 10 pcroent following the 1968 wastewater 

diven.ioo, lUI by 36 p<m:n.1 since 1975 because of the decrease in sediment release and a 

sligbt decrease in external loading. 

68 

VES 008006 
In 1971, sewage effluents were diverted from the watershed of Lake Mendota, WI 

(lathrop, 1990). P levels and rommer bluc>grwi aigru blooms m the lake did not 

decrease inunediately following the effluent dh-er..ion because of higll phosphorus loading 

&om spring ruooft' fi-om 1973 to 1976. However, begjnning in the late 1970s, P !eve~ 

began to decrease because of lower P loadings from many years of below-nonnal spring 

runoff As a result, sumn11:r alsaJ blooms became less severe and water quality impoved, 

particularly from 1986 to 1988. 

The lower P levels in Lake Mendota also caused decreased P loadings to 

doi>lnstream lakes, whidt o:xhibited a decrease in P contents and algal blooms (ibid.). 

Altl1ough improved water clarity was not dramatic in shallowe.· lakes, Waubesa and 

Kegosa oontinucd to have algal growth. The lollg4mn data indicated that all the Y ahara 

lakes were oruch more responsive to changes in external P loadings than '''a'S tbouglll 

during the 1970s before diversion. These results suggest the importance of control of 

agricultural and urban sources of nonpoinl pollution to the lakes. 

A multivariate ~1al~ focused on the hnJX!Ct of municipal wu.o.tewater diversio11 

(m early 1979) from Lake TU1Silanjarvi, Finland oo the phytoplatJkton community (Varis, 

1990). The cooc:entnllioo of total N appearod to have been strongly infhlftUSJ by the 

wastewater diver..ion. The growth factors with strongest oorrelations in the canonical 

system were the dissolved inorganic N/dissolved inorganic P mtio and temperature. 

Dredging 

Dredging of sedimcnls is in=asD1gly being used as a metOOd foc ~ring 

eutrophic lakes or reservoirs. Dredging has boc:o shown to iffiirove water quality, reduce 

inta.nal P loadings, dcaease aquatic macrophyte growth, and restore lost ~tiona! 

amenities by physically deepe>ling the lake, and removing oxygen demanding and nutrient· 

ridt organic bottom materials. The mmiber of dredging projects bas increased in recent 

years. 

The disadvanla8e5 of dredging are its cost, P release from sediment during 

dredging, reduction of benthic food supplies, potential envirorun01tal problems with 

disposal of dredged mataial, and noise (Edmondson, 1990). 

69 

VES 008007 
Heavily polluted li"OID 1930 to 1957, Lake Tnumnen, lite Netherlands, was 

restored by ~'UCiion dredging of the top layer of the bottom sediments (Gronberg, 1982). 

Nutrielll:; and biomass levels decreased signilicantly and eutrophic species of 

pl )1o~lankton disappeared as oligC){ropbic species returned to this once oligotrophic lake. 

Dunst (1982) discussed a dredging program for 12 Wi.'lCOIISin lakes, including the 

design methodology and in.funnarion requirements to select a suiulble project. Sediment 

disposal from 12 other dredging projects in W JSCOnSin was also discussed. 

Dooris eta/. (1982) strongly suggested that ~g ofbottom sediments from 

Sawgrass Lake (Pinellas County, FL) was favored over drawdowu as a lake resloratioo 

measure. They am~ at this CXJOC!usion based on laboratory tests after considering the 

problems of conlllmi.nation in the lake sediment and the tutfavomble sediment properties 

{arset~ic, chlordane, polychlroinaled biphenyls, high organic maner and water content, 

slowchying chaxacteristics, etc.). 

The Hyde Park Lake (Niagara Falls, NY) restoration project consisted of removing 

polluted lake water and the dredging oflakebottom muck. and day (Pettit er a/., 1982). · 

The clay was usid as a liner fur existing secured \a00.6JJs. Continuous fresh water wa5 

supplicxl by a nearby reservoir. ~ ard post-oonstructioo studies, along with several 

investigations undertaken during the construction period, veriticxl the improvement of 

water and enviroommlal quality during the consbuction phases. Construction of a 

siltation (settling) pond with a trash collector and an oil boom ensured the prevention of 

sih and trash from entering the lake via its tributary, Gill Creek. Also, stone riprap and 

new vegetation provided stabilization of the SUlTOIIDding soil areas to help prevent 

erosion. 

Awro.ximately 1.6 millioo cubic yards of soft sediments were drcxlged from Lake 

Lansing. ML, from May 1978 through August 1983, and 221,000 cubic yards of sand were 

redistributed wi1lrin the lake (Mikula, 1985). Sudiloe area (182 beaares or ha, 450 ac-eS) 

ax! maximum depth (11 m. 35 feet) mnaincxl the same after dredging. but the mcm depth 

increased from 2.1 m (6.9 feet) to 2.7 m (9 feet). lt is reported that the lake exhibilcxl no 

apparent change in lhe extmt of oxygoo depletion due to drcxlging. Tbete WIL'i no O)(ygen 

near the bottom Stortly after the onset of Slnllifiallion (May, June). Oxygen 

70 

VES 008008 
concentrations less than I mg!L extended upwards to the 4.0 m depllt. Comparison of 

pre- and po&t-dre:lging data indiamxl an increase in transparency and substantial 

reductions in in-lake P and dllorophyll a. It was postulated that the increased volume of 

Lake Lansing "''Ollld have had some effect on decn:a.<ing the lake TP concc:ntratioos due 

to "dilution." Changes in nitrite IWld nitrate and oxygen depletion were not eviderJt. nte 

lake improved in trophic status from a highly eutrophic condition to a mesotrophic 

condition. Heavy metals, ~y amenic Me! mercury, were not remobilized during 

dredging. 

.Bellthic macroinvertebrate oonmlUnities did not change in composition, but IJJeir 

individual numbers did inaea<;e after dre:lging. Composition of the fish community was 

poor before an:l after dredging. Phytoplank!on growths displayed a seasonal diversity of 

types, which varied in pattents typical of mesotrophic and/or eutrophic lakes. Although 

zooplankton populations did not cbange in oomposit ion, their individual nwnbers did 

increase afll>' dredging. 

Prior to dredging in 1978, Cltara and Najas \\'IO'e the dominant species in Lake 

Laming (ibid.). Dominant species oocurring after dredging (1983, 1984) were 

Myriophyllum sp. and Chara. Native milfuil (M. exalbescens) was much more abundant 

than Eurru.ian miliDil (M. spicatum). Simi1lr to ~ging, plants grew to a depth of 

3.0to 3.5 rn 

Reelfoot Lake (15,500 acres atllOI'Ill8i pool level) is reoowned for its abundance 

of fish and wildlife resoun:es, and it is a;tima!ed to bring in a recreational revenue of about 

$4 million amually. Since the I~ this Te.mc.ssee lake has beaJ degrading as a sports 

fishing resource. Only large-scale dredging, dm'Miown, or both were considered to be 

etreaive in restoring this lake (l'ennessee Wildlife Resources Agalcy, 1985). Because 

dredging was fuuOO to be prohibitively expemive ($.53.7 million), drawdown was selected 

as the restoration alternative. (t would occur from July to Decembtt when fishing activity 

was estimatfd to be at only 30 f)ei'COll of it'> total activity. Fishing trips were expected to 

inerease from 50,000 to 65,000 trips amually as a result of the lake restoration. 

It is reported that upstream development increased the sediment load entering 

North Park Lake near Pit1sburgh, PA The ruMlp of sediment within the Jake had 

71 

VES 008009 
reduced its surfuce area by approximately 5 aacs. Between April 1984 and Novc:rnb« 

1986, an estimated 35,500 wbic yards of sediment were dredged at a cost of $69,450 

(Pennsylvania Deprutment of .Environmental Resources, 1988). The water quality after 

dredging was not reported, but c!J:edging resuhed in increased lake surface area, fiShing 

places, and boating areas. The appearance of the lake is also reported to have improved. 

The dredging of Ratoooa Ulke and its sun:ounding park in Berkeley, MO, 

provided a much-needed water-based recreational OOlity for residents and vis.itors. The 

project began with the removal of a ponion of an earthen dam to release water fiom the 

lake, followed by dredging aod storage of dredged material on site for dewatering (Bhasin, 

19&8). Later, additional sediment was removed to provide a healthy environment for 

aquatic life by increasing the lake depth, and 1inally, the earthen dam was restored.' 

Approll.imaldy 20,000 cubic yards of sediment v.-ere dredged Other improvements 

included laOO.scaping di~urbcd areas, retention walls of railroad tics, roads, beach 

improvements, ruld lighting. The total cost of dredging and the other improvements was 

approximately $400,000. 

DiversionandDredging 

Stonnv.'aier divamn aod dredging of Lake Saaljav.-ea, W A, have dramalical1y 

decreased the lake's seasonal M.d yearly mean N levels (Gibbs & Olson, loc., 1985). 

Anunonia aod nitrate loadiogs were both rtduced as a result of the diversion, while 

dredging has .taiuced ammonia release fit:m the sodima1t during stratification. The Jake's 

P oootau also decreased due to dredging. Biological productivity in the lake deaeased 

because algal growth appeared to be N limited. Since 1981, Lake Saeajawea has 

experienced increasing S=hi disc transparency and decreasing chlorophyU a. Average 

summer dllorophyll a k-'Vcls indicated a shift fiom a eutrophic Jake to a mesotrapbic lake 

following lake restoration. However, Secdli disc readings are still in the eutrophic ranges 

(<80 inches). Nevertheless, 87 pen::tnt ofP was oonln'buted by the ground wruer. 

Stonnwater di\.-ersion ood inllow stream sedimeruatioo ponds reduced the total 

~ded solids (TSS) load to Lake Fenwick, WA(URS Co., 1985). The average annual 

total N ruld TP in the hlkewater were 0.489 ruld 0.043 mgiL, respectively. Wat!O'Shed 

72 

VES 008010 
management reduced T P by 6l! percent and TSS by 78 percent Ninety percent of the 

TSS reducMn was due to the stonnwater mnoff diversion, while the rernnining 10 percent 

was due to retention in the ponds. Sto ~nwa er P load wns reduced 30 to 70 percent, 

which is equivalent to an overall P reduction of 17 to 40 percent. Stonnwate•· TSS loads 

were reduced by 60-80 percent, which is equivalent to an overall TSS reduction of 54 to 

70 percent. However, in-lake nutrient concentrations have not changed siwufJC&tlly since 

1979. The lake is still reponed to be deminated by blue-green algae in the su~er. 

The multipart restoration progJam for Wapato Lake (30 acres), in Tacoma, WA, 

consisted of!) gradual dilution of the recreation basin (south~ oflhe lake with nutrientpoor municipal water during the SUDl01<:r months; 2) stormwater detention and ueatment 

in the north basin and adjacent wetlands with a bermlovertlow spillway be«ween tbe two 

Jake basins; 3) diversion· of most stonnwater around the lake; 4) limited dredging of storm 

sewer outfall areas; 5) a drastic drawdewn of lake water to consolidate borrom sediments; 

and 6) an application of alum to the recreational basin in summer 1984 (Entrance 

Engineers, Inc., 1986). Stonnwatcr diversion and· wetlands treatment reduced P loading 

to the south basin by more !han 90 percent and demonstrated a successful project. 

However, summer blue-greeo alg& blooms continued to persist due to the unavailability of 

satisfactory dilution water and major cban&es in the lake's ecological characteristics. 

A wide range of Sllldics have been perfonned before possible restoration of Libeny 

Lake, in Spokane, W A (Kennedy Consulting Engineers, !985). These SIUdjes pointed to 

high concentrations of phosphorus in cenain inflows to the lake and within the lake 

sediments causing eutrophication_ Sewering oftbe developed areas of the lake basin was 

first done to eliminate the large source ofP. Acklitional project activities were diversion 

of flood flows around the marsh at .the south eod of the Jake, alum treatment orth~ entire 

lake, dredging of the most enrichod sedinJell.ts from SO acres, water quality monitoring 

dwiug and after the in-lake works, and a smdy of storm water runoff The w11ter clarity in 

Uberty Lake during the S\llll1llCf and full of 1984 was better tban it had been for almost ten 

years. The lake revened to mcsotrophic conditions after these restoration measures, 

based on four years of monitoring. Comparison of pre- and post-restoration nutrient 

budgets indicated that P looding was reduced 34 percent. Sewering was primarily 

73 

VES 008011 
responsible for !his reduction. Even thoug)l the desired change in the phytoplankton 

conununities (from primarily blue-green to primarily green algae) was not seen, indications 

ore that long-temt algal productivity and incidence ofblue-green algal blooms !tad been 

significan~y reduced. 

The Norfolk Broadi8Jld, England, comprises about SO small, shallow eutrophic 

lakes. As an experiment in lake restoration, the Alderfen Broad was isolated by diversion 

of an inflow stream wilhout removal of its recently deposited P-rieh sediments (Moss et 

a/., 1986, 1990). In four yrors (1979- 1982) after isolation of Alderfen Broad, the 

phytoplankton crop was greatly decreased; the lakewater cleared; and net release of 

phosphate-phosphorus (PQ,-P) from !he sediment ceased. Because of reduced water-

. column nnbulence caused by plants and the organic matter supplied to the sediment 

surface in their decay, the mechanism for release of P04-P from the sediment was 

reactivated, which resu.ltod in a large phytoplankton crop in spring 1984. As a 

consequence, the aquatic plant population declined. In 1985 there were both spring and 

summer phytoplankton growths. 

In another experi:nx:DI, scdiinents were dredged from Cockshoot Broad, and dams 

were placed against the nutrient-rich River Bure, but t.be Broad continued to be fed by a 

small stream draining an agri:culturol and fen catclu:nenL A reduction in phytoplankton 

growth occurred soon after the isolation and dredging, and the water cleared. Part of the 

Broad was recolonized with a diverse species of aquatic plants. 

Gorton Pond in Warwicb, Rl, is used fur both primary and secondary contact 

~ation, _propagation of fish, and other aquatic life and wildlife. It serves as a drainage 

sink for its surrounding watershed, and as such receives the surface nmoff from 790 acres 

of urban area. There is a SUlSll enclave of homes without sewers, however (Keyes 

Associates, 1982). Stormwat·er and wastewater diversion, as well as dredging along the 

inlet lllld outlet areas, were reconunended as part of the comprehensive lak.e restoration 

project. 

Between 1978 and 1986 an estimated 276,000 ml (361,000 cubic yards) of 

sediment was removed frorn Nutting Lak:e at Billerica, MA, by hydraulic dredging 

(Baystate Enviroruncutnl Consultants, 1987). The influence of domestic wastewater on 

74 

VES 008012 
!he lake has been elimiruncd However, !he dredging was not as successful as anticipated. 

Considerable quantities of soft sediment remain in the lake. The only benefit observed was 

an increase in DO levels Bl the surface ofthe east basin and tJnoughout the west basin of 

t.he lake. Reduction of rMCropbyte nuisance m selected areas has f051ered increased lake 

use for swimming and boating. 

Economic evaluations of restored lakes in Florida showed that gravity drawdpwn 

was the least eJ<jlEIIsive method. whereas sewage effluent divetSIOn was 10,000 times 

more expensive in terms ofhecrares (Dierberg and Williams, I 989). Options for all lake 

restoration or enhancement measures can be ranketl in the following order (least expensive 

to moot expeosive): (!111'~ty drawdown < grass carp introduction < rneehanical drawdown 

< aeration < stormwmcr control (drnwdown and dredging) < effluent diversion. Within a 

particular restoration category, the cost spanned appro><imately 1-112 orders of ma8Jlihlde. 

Lily We in Kenosha County, WI, with a surface area of90 acres and a maximum 

depth of six feet, was dredged in 1978 and 1979 to eliminate dense weed growth, prevent 

6sb kills, and in general enhance recreational usage (fishing. swimming, boating, and water 

skiing). The lake was deq>ened to a maximum depth of22 feet and the storage volume 

increased from 432 acre-feet to 986 ac;re-feet (LLPRD, 1981). The lake was monitored 

from 1976 to 1981. 

Since completion of the dredging project in Lily Lake, DO conpentrations did not 

drop below 7 mg/L at any depth during winter, thus avoiding winter fish kills. Prior to 

dredging, !he lab had low orthopbosphorus levels, 4 !'giL. Little change was noted 

either during or after the dredging projcc.t. Likewise, chlorophyll a levels were low in the 

luke. However, the cootce.ntration incr-eased fi"Om about 3 !Jg/L to an avel'age value of 

18.5 )l,g/L during dredging. Chlorophyll levels dropped back to 5 jlg/L after dredging.. 

Macropbyte growth covered !he entire lakcbed prior to dredging. A diversity of 

plant species was present but PoUJmogetoll robbln.fii dominated. In 1980, the first year 

after dredging, !he Jalce was fuund to be reinvaded by vegetation, however. Growth 

covered 75 percent of !he lake bottom, with CJooro and Myriophyllum as codominant 

species. 

75 

VES 008013 
It is repru1ed that ihe overall lake usage inctl!ased greatly at Lily Lake. Water 

skiing and sail boating became common, and beach usage rose by a fac-.or of ten. Fish 

habital :Uso improvcxl. Olmmenls roccivcxl on the project we<e positive, expressing 

pleasure wilh revitalized Jake conditions and usability. 

RESULTS AND DISCUSSION 

Wntcr Quality Characteristics: Phase ill Monitoring (198&-1991) 

Physical Cluu·acteristics 

Tempenture and Dissolved Oxygen. Lakes in the tcmpente zone generally 

undergo seasonal variations in temperature through the wale~" column. These variations, 

with their accompanying phenomena, are perhaps the most influential controlling factors 

within the lakes. 

The temperarure of a deep lake in lhe temperate zooe is about 4•c during early 

spring. As the air temperatures rise, the upper layers of water wann up, and wind action 

mixes lh£m with the lower layers. By late spring, the differences in thermal resistance 

cause the mixing to cease, !IX! the lake approaches the thermal stratification of the 

summer season. Shortly after the temperature variation in water comes the physical 

phenomenon of nx.,-easing density with decreasing temperature up to a certain point 

These two interrelated forces are capable of aeating strata of WBler of vastly differing 

characteristics within the Jake. 

During them1al stratification, the upper layer (epilimnion) is isolated from lhe 

lower layer of water (hypolimnion) by a temperature grddient (thermocline}. 

T ernperallln:S in the epilimnion and hypolimnion are essaUially mifoon The thennocline 

will typically have a !harp temper:lllure drop per unit depth from the upper to the lower 

margin. When the U1ermal strtttification is established, the Jake enters the summer 

stagnation period, so namerl because the hypolinmion becomes stagnant 

With cooler air temperatures duting the mu season, !he temperature of the 

epilimniou decreases Wltil it is the same temperature as the upper margin of the 

ihennocline. Successive oooli:ng through the thermocline to the hypolimnion results in a 

76 

VES 008014 
uniform temperature through the water column. The lake men enters tbe fall circulation 

period (feU turnover) and is again sul:!jected to a complete mixing by wind. 

Declining rur temperatures m1d the tbm1ntion of an tee cover during the winter 

produce a slight inverse thennal stratification. The water column is essentially unifonn in 

temperature a t about 3 to 4°C, but slightly colder temperatures ofO to 2•c prevail just 

below the ice. With the advent of spring and gradually rising air temperatures, the ice 

begins to disaj>pear. and the temperature of the surface water rises. The lake temperarure 

again becomes unifonn, a.od the spring circulation occurs. 

The most important phase ·or the thennal regime from lhe smndpoint of 

eutrophication is the summer stagnation pe~iod. The hypolimnion, by virtue of irs 

stagnation, traps sediment materials such as decaying plant and animal matter, thus 

decreasing the availability of nutrients during the critical growing season. In a eutroj,hic 

lnke, lhe bypolinmion becomes anoxic or devoid of oxygen becaU&e of the increased 

content of highly oxidizable material and because of its isolation from the atmosphere. In 

the absence of oxygen, the conditions for chemical reduction become favo.-able, and more 

nutrients are released from the bottom sediments to the overlying waters. 

However, during the fall circulation period, the lake water becomes mixed, and the 

nutrient-rich hypolimnetic waters are redistnbu!OO. The nutrients that remained trapped 

during the .stagnation period become available during the following growing season. 

Tberetbre, a continual supply of plant nutrients from 1he chainage basin is not maitdat01y 

for sustained plant production. Fruh (1967) and Fillos and Swanson (1975) state that 

aller an initial stiiilulus, the recycling of nutrients widrin a lake might be sufficient to 

sustain highly productive conditions for several years. 

·Isothermal plots for Lake I and Lake 2 in 1990 are shown in figures 13 and 14, 

respectively. Also, the vettical temperature profiles for these two lakes at selected dates 

in 1989 are shown in figures 15 and 16, respectively. The vertical temperature profiles for 

lake 3, site I for 1989 and 1990 are sbo\\11 in figure 17. 

Figures 13 and 14 show mat !he summer stratification begins in early April and 

imensifi.es progressively during 1he summer months. Lake 2 is deeper than Lake ·I and 

exllibits a typical Sll1llifteation pattem. However, the thermal gmdient exhibited 

n 

VES 008015 
Figure 13. Jsothennal and iso-dissolvtd oxygen ploiS for Lake I 

0;0~.0~-~~--~--~---v-~~~~~----~----~~~-r~--~ 5 

10 

15 

Figure 14. Jsothenual and dissolved oxygen profiles foo· Lake 2 

78 

10 12 

VES 008016 
' 

21 

15 

0 

;;; 

.! 5 

~ ... l!l 10 

7/13/89 

15 

0 I 

5 -

10 - I 

1015189 I 15 

0 10 

TEMPERATURE, 'C 

31 11 

I 

5118189 1 

8117189 

I 

I 

- t - ~ 

1117189 

20 0 

21 

I 

I 

I 

I 

I 

I 

10 

I 

I 

I 

I 

I 

I 

I 

31 11 

8{18/89 

1-

-

t/14/89 

0 

-

-

20 

DISSOLVED OXVG£N, mgA. 

21 

i 

I 

I 

I 

I 

I 

I 

10 

Figure IS. TemperaiUre and dissolved oxygeo profiles fur Lake 1 

31 

I 

I 

I 

I 

I 

I ' 

/ 

/ 

-

-

20 

VES 008017 
.. 

TEMPERA T\JRE, •c 

0 ' ,..1 ____ 2"'T1T""T _ __ 3..,1 1,..'--.....,.....,;;,.21;.._ ___ 3:.,1 1,..'---..-..2'-----n31 

/ 

/ 

)( 

I 

I 

I Dlsoolvod 

I O><vgen 

I 

1

1-... Tampenotu,. 

~7/89 

I 

I 

I 

I 

I 

/ 

I 

I 

I 

I 

I 

I 

ti/18/89 .. ~~----~------_. 

t r------r--~-, ~ 

/ 

/ 

/ 

I 

I 

I 

I 

I 

I 

I 

) 

/' 

/ 

1!117/89 

1-

1-

1-

y 

j I 

I 

I - I 

I 

I - I 

I 

I - I 

/ 

/ - 9/14189 11(7/89 

I 25 '-----,-':o,.- --2~0 o 10 20 o~ --,..Lo----.J20 

DISSOLVED OXYGEN, mg/l 

Figure 16. Tempernturc and dissolved oxygen profiles for Lake 2 

80 

VES 008018 
Dissolved ' oxygen ,/ 

5 _--::;,.-{ 

Temperature 4/27189 10~----~------~ 

0 ,...---,.- -r-----, 

10~----~------~ 

0 r---""TT-r--- --. 

j 

% 10~----~------~ 

~ 0 

c : /I 

I 

5 1- I - / 

I ~0 

10 

0 I I 

I 

5 1-

1 

I - I 

I 10/9/90 

-

5,12'190 

I 

I 

I 

I 

8113/90 

.I II 

I 

- i-1 

I 

I 11fl/90 

100 10 20 0 10 20 

DISSOLVED OXYGEN, mg/L 

21 

. .,.1 

I 

I 

' I 

' 

I 

I 

I 

I 

I 

I 

I 

I 

I 

I 

0 10 

Figure 17. Temperalllre and dissolved oxygen profiles for Lake 3 

81 

31 

I 

I 

I 

I 

' 618189 

- 9/ 14189 

- 3/21/90 

6{7190 

9/19190 

20 

VES 008019 
throughout Lake 1 is as pronounced as that for Lalw 2. In both these lakes, the maximum 

observed water temperalllre was about 310C on July 14, 1990. The maximum 

temperamre differentials experienced by Lakes 1 and 2 during 1989, l.O'C and 13.20C, 

respectively, occuJred on d1e same date. TI1ereafter, tl1e intensity of stratification began to 

deerease. Lake 3, shallowest of the three lakes, experienced much less thermal gradient, 

excq>t for the obsep'ation on April 27, 1989, when the diffemx:e between surfuce Mel 

near-bottom ware.· temperatures was 7.2°C. The reason for the anomalous observation is 

not readily apparent. Such a magnitude of temperature gradient was observed at no other 

time in Lake 3 during this investigation. Lake 2 was fOund to become isolhamaJ by 

October 9, 1990, after .full turnovcr, whereas Lake I was isothermal by early Sql(emba 

1990. 

The aforemenlioooi general observations fer the three lakes apply to data gathered 

in 1989 (figures 15-17) and Olher po51·implernen1Btion moni!Oiing years. All the data 

' 

gathered for the FHSP Lakes • physical, chemical, and biological • have been entered into 

USEPA's STORET system and are readily accessible. 

It is oommoo knowledge that the impomdmenl of water alters its s*iysical, 

chemical, and biological characteristics. The literruure is replete with detru1ed reports on 

the effects of impoundments on various water quality parameterS. The physical changes in 

the coofiguration of the water mass after impounclrnen; reduce reacration rates to a smaD 

fraction of those of .free-flowing streams. Where the dcplb of impot.lldment is 

considerable, the thermal stratification acts as an effective barrier for the wind-induced 

mixing of the bypolimnetic zone. TI1e oxygen transfer to the deep waters is essentially 

coofined to the mokx:ular diffusioo transport mecbanism. 

During the period of SUilU1llll' stagnation and increasing water temperatures, the 

bacterial decomposition of the bottom Ol'gllllic sediments exerts a high rate of oxygen. 

demand on the overlying waters. When this rate of demarJd Cltoeeds the oxygen 

replenishment by molecular diffusioo, anaerobic cooditions begin to prevail in the Zl)nes 

acljacent to lhe lake bottom. H>JX>limnetic zones of artificial impoWldments were also 

fOOnd to be anaerobic \vilhin a year of their fOOnatioo (l<othandaraman and Evans, 1975). 

82 

VES 008020 
·n1e DO isopleths for Lakes 1 and 2 for 1990 are shown in figures 13 and 14, 

respectively. Selected verocal DO profiles for the three lakes are mcluded in figures 15-

17. The DO profiles for Lakes 1 and 2 penain to 1989, whereas tigure 17 shows the 00 

profiles for Lake 3 for botl1 1989 And 1990. 

DO depletion was more severe in Lake 2 compared to Lake I and began to occur 

during the latter pan of April. As the summer thermal stagnation mtensified, the anoxic 

zone of hypolimnctic waters in Lake 2 progressively increased, reaching a maximum 

duling early July. The extent of this anaerobic zone started diminishing Lhereaft.er, and the 

DO concenttation became unif<>nn in the water column in early October. 

During the period of peak sll"atification, Lake 2 was totally anoxic at depths 9 feet 

from the SUJfuee and below. About 49 acre-feel or approximately 14 percent oftbe lake 

volume was anoxic, somewhat resuicting habitat for desirable fish food organisms and 

fish. During summer months, adequate oxygen levels did not generally exist at depths 

below 6 feet from the surface. 

Oxygen depletion in tl1e shallow Lakes I and 3 was not as severe.. No anoxic 

conditions were observed in Lake I during 1990; bow.--er, near-OOttom anoxic conditions 

were obse•ved there dnring 1989 (figure 15) and 1991. Significant oxygen depletion 

occw·red in Lake 3 even though the water body ex eri~eed only weak tbertnal gradients 

during S\liiiiil<2" monlbs (figure 17). Oxygen demand from lake bottom sediments during 

summer months appears to be substantial in all three lakes. 

Table 15 shows tbe percent DO saturation. levels at the surf nee of the FHSP Lakes. 

The highest aod lowest percent saturation values observed for Lake I were 172.S and 

55.0; Lake 2, 201.2 aod 4J.I; and Lake 3, IS5.8 and 45.8. For inexplicable rea3ons, tbe 

DO levels were supersatumted in all three lakes for the first eigbt months of calendar year 

1991, with very few exceptions. Such supersaturated conditi<>ns did not prevail dnring 

1990. The saturation levels in lbe lakes were_ generally higbee throughout 1991 compared 

to 1990. 

Sreclti Disc 'l'ransparencies. Soocbi disc visibility is a mensw;e of tbe lake water 

transparency or its ability to allow liglrt ttansmission. Even though the Seccbi disc 

transparency is not an actual quantitative indicatJon of light transmission, it serves as an 

83 

VES 008021 
Table 15. Surface Percent Dissolved 1,>a1 ~~ Saturation Levels 

In Fl-ank Holten State ark akes 

Lake3 

Dare Lake I Lake 2 Sile I 

41.27/88 1/A 68.0 97.0 

6107 172.5 201.2 122.8 

7/12 139.9 142.7 85.6 

8/23 72.4 68.0 90.7 

9121 100.2 102.4 105.0 

4/27/89 147.6 134.9 149.9 

5/18 91.8 81.4 102.0 

6108 121.2 - 124.1 

7/13 I 12.2 114.0 67.0 

8/17 106.7 126.3 80.1 

914 62.0 45.0 45.8 

10/05 79.8 98.0 86.7 

11/07 95.6 103:9 97.9 

lfl7/90 100.5 100.0 1103 

2114 97.3 98.2 101.2 

31.21 95.0 95.6 98.9 

4123 140,6 139.3 154.4 

5116 80.9 91.5 

5124 92.9 102.9 92.8 

6/07 83.9 81.0 111.9 

7/09 11 7.9 137.6 185.8 

8113 81.0 86.8 89.9 

9119 75.9 57.6 73.4 

10/09 55.0 41.1 58.9 

ll/07 85.2 80.4 85.1 

12111 103.5 100.8 97.7 

2121/91 124.8 117.1 133.9 

3/19 104.1 103.2 113.8 

4/17 136.0 136.6 126.6 

5/14 135.4 122.4 182.1 

6/13 170.3 176.5 151.6 

7/11 94.5 119.8 93.3 

8122 143.8 158.5 147.8 

9120 99.4 52.8 72.4 

10122 94.9 98.3 87.1 

11/19 95.1 102.3 99.1 

VES 008022 
index and a me~ms of comparing simi!ru· bodies of water or the same body of water at 

different times. Since changes in woter color and turbidity in a deep lake are go1m1ly 

caused by aquatic flora and fauna, tnmspareocy is o.tlm related to this entity. 

The mean and range of values observed tor Seccbi disc readings (m inches) for 

Lakes I, 2, and 3 were, respectively, 16, 5-28; 16, 6-28; and I 8, 7-30. Table 16 provides 

these values along with a summary of obselvations for other' physical and chcmjca) \vata 

quality parameters. The mean Seochi disc values for all the lakes were comparable, as 

were the minimum and the maximum values for these lakes. No clear trend among Secdri 

disc readings, turllidity, and suspended sediment values could be discerned It is 

somewhat sw:prising that Secchi disc values were not higher in Lake 2, whicb has a 

maximum depih of about 25 feet, compared to the other two shallower lakes. llnpounded 

water bodies with maximum depChs of about 25 feet are known to have much higher mean 

and maximum Secchi disc traoSpan:neies {Kochandlnman and Evans, 1983a; 1983b). 

Tu.rbidity. High lllrllidity affects the aesthetic quality of the water. Its origins are 

gcner..U.ly consido-ed to be mll1icipal and industrial wastes; clastic moterials derived from 

the drainage basin; roil erosion resulting from 881icultural praaices and Uiban and 

highwdy developmaJts; Jake sediments stirred by mnd, waves, and high-speed boating 

activities in shallow lakes; and detrital remains of algae aod aquatic and terrestrial plants 

and animals. However, in the case of the FHSP Lakes, some of these causative agents, 

sucb as indusnjaJ wastes and higiHipeed booting activities, are absent 

The mean and range of tllrbidity values for these lakes were similar except for one 

very bigh value (11 0 NTU) of the near-botrorn sample from Lake 1 on May 6, 1990. The 

mean value foc site 3 of Lake 3, the shallowest of all the saJq>ling sites in the lake systan, 

was higher than other sites. In nearby Horseshoe Lake in Maruson Couniy, IL, an oxbow 

lake with a meon clcplh of only 3 feet, the mem and range of turbidity vah1cs were 

reponed as 40 and 22 to 66 Nr1.J (Rdlfekk eta/., 1992). Clarity in the FHSP Lakes is 

much better than thai for Horseshoe Lake. The mem and range of !ulbidity values in 

Nr1.J for >wfuoe samples were 8.5, 0.3-39.0 for Lake 1; 7.1, 0.2-15.0 for Lake 2; 7.4, 0.5-

17.0: 8.0, 12-19.0; and 11.9, 0.5-27.0 fur sites I, 2, and 3, respectively, of Lake 3. 

85 

VES 008023 
Table 16. Water Quality Characterisliell of f rJnk Bolten Stute Park L akes 

l,a.ke. l l-J!ke 2 

Slll'(gce Ntar.bocwm Sur (gee Ncar-bottom 

Parameters lt/' 1!.011 Range Mea11 Range Mean Range .ill eon Range 

Secchi readings (inches) 16 5-28 16 6-28 

Total suspended solids 24 8-76 31 8-214 22 6-62 22 8-47 

Volatile suspended solids 14 1-29 14 4-32 13 2-32 12 2-24 

Turbidity (NTV) 8.5 0.3-39.0 11.1 0.5-110.0 7.1 0.2-15.0 9.0 0.8-39.0 

Nitratelnilrite-N 0.06 0.01-0.10 0.06 0.01-0.10 0.07 0.01-0.34 0.05 0.01-0.JO 

Total ammonia-N 0.11 0.01-0.37 0.15 0.01-0.47 0.15 0.01-0.60 1.23 0.04-7.30 

Total kjebdahl-N 1.9 0.7-3.3 1.9 0.8-3.0 1.7 0.4-2.7 2.6 0.8-8.1 

Total pho."jlhnte-P 0.18 0.08-0.39 0.18 0.08-0.30 0.17 0.04-0.44 0.36 0,07-2.20 

Dissolved phospbate-P 0.05 0.00-0.28 0.06 0.00-0.17 0.05 0'.00-0.26 0.27 0.00-1.74 

Conductivity ()lnlho/cm) 373 296-450 382 282-468 381 312-456 466 238-747 

Total alkalinity 114 20-140 119 70-150 122 80·170 148 80-260 Pbeno~hthalem alkalinity 12 0-25 6 0-20 II 0-25 3 0-20 

pH (uruts) . 7.7-9.5 7.1-9.2 7.6-9.5 6.5-8.7 

Cbemieal oxygen demand 37 24-49 36 25-47 36 26-48 33 23-44 

Chlorophyll-a 91.3 33.5-158.8 90.9 42.2-161.8 

Chlorophyll-a (Corr) 91.4 32.3-173.6 91.1 38.3-155.4 

Chlorophyll-b 8.2 2.0-23.5 7.6 2.4-14.0 

Chlorophyll-c 5.0 0.9-13.5 4.8 0.1-21.5 

Plueophytin 12 0.0-8.3 13 0.0-1 1.5 

S.i~ I [,gflt. ~r:..t~ S.il6. 3. 

Parameterg Mean Range Mean Range Meu11 Rc111ge 

Secchi readiDll$ (incl~es) 18 7-30 17 6-28 13 5-25 

Total suspended sotids 22 5-50 22 4-52 30 4-61 

Volatile suspended sotids 8 2-26 8 3-23 9 2-1 9 

Turbidity {NTU) 7.4 0.5-17.0 8.0 12-19.0 11.9 0.5-27.0 

N'itratelnitrite-N 0.20 0.01-5.30 0.07 0.01-0.22 0.09 0.01-0.38 

T ota1 anunonia-N 0.11 0.01-0.60 0.09 0.01-0.38 0.10 0.02-0.39 

Total kjeldahi-N 12 0.10-2.40 1.1 0.30-2.40 1.1 0.10·2.10 

Total phospbate-P 0.14 0.01..0.31 0.14 0.03-0.28 0.!8 0.06-0.42 

Dissolved pbosplule-P 0.05 0.01-0.14 0.05 0.01-0.20 0.05 0.02-0.20 

Conductivity (!unholan) 573 433-714 5n 443-719 580 448-748 

Total alkaliDicy 164 90-220 165 90-230 169 70-240 

Phenolphlhalem alkalinity 4 0-20 4 0-15 6 0-25 

pH (units) 7.6-8.8 7.4-8.8 7.5-8.8 

Chemical oxygen demand 27 19-42 26 18-37 28 20-48 

Chlorophyll a 56.9 21.2·120.5 55.4 23.4-lll.S 60.4 14.6-172.2 

Chlorophyll a (Corr) 56.8 18.5-120.2 55.3 23.2-117.9 60.7 13.1-186.9 

Chlorophyll h 8.7 1.1-38.4 8.9 0.8-45.3 11.1 1.3-58.3 

Chlotphyll c 3.4 0.0-I 1.5 3.3 0.0-10.4 3.3 0.0-11.0 

Phneopbytin 2.0 0.0-11.7 1.6 0.0-112 1.8 0.0-15.4 

Note: All chlorophyll values are in J.tg/L; other values are in mgiL except where noted. 

VES 008024 
Chemical Characleristics 

pH and Alkalinity. It is gcrnniJy considered lbat pH values above 8.0 in natural 

waters are produced by a photosynthetic me that danands more carlx:>n dioxide than the 

quantities fumi•hOO by respiration and d'IC()mpooition (Mackenthun, 1%9). 

Photosynthesis by aquatic plantS uses carlxm dioxide remol'ed from bicarbonates when no 

free carbon dioxide exists in the water medium. Decomposition and respiration tend ro 

reduce pH and increase bicarlx:>natcs. 

The alkalinity of a water or its capacity ro accept protons is generally imparted by 

bicarbonate, carllooate, and ~xide components. The species makeup of aJ.kalinity is a 

function of pH and mineral cornpositi<:n The carbonate equilibrium, in which cwbooate 

and bicarbonate ions and carbonic ocid are in equilibrium, is the du;mical system present in 

natural waters. Delamination of the #leoolphlhalein end point provides a measure of the 

carbonate species of the toral alkalinity, \\bich is ga1et3lly taken ro be twice the amount 

indicat.ed by this end point Phenolphthalein alkalinity is then the difference between the 

toral alkalinity and cmbonate alkalinily. 

The pH and allcalinity values ohserved in the lakes are typical of Illinois lakes. The 

highCSI pH values of9.5 were obsen>ed in the s1.1rface water samples from Lakes I and 2, 

indicating algpl bloom conditions. Lake 3, generally turbid from res-uspension ofbottom 

sediments, exhibitod a maximum pH value of 8.8. The near-bottom samples of Lake 2 bad 

lower pH values than the near-bottom samples of Lake 1. Lake 2, being deeper than Lake 

1, undaweot a higher degree of anoxic conditions in the deeper strata, resulting in a 

higher degree of atJat:robic deoomposi.tion of orgllnic matter. AB expected, this ~ted in 

a lower r.mge of pH values and a higbtt r.mge of toral alkalinity in Lake 2 than in Lak-e l. 

The mean carbonate alkalinity for the 9Jffuce samples of Lakes l and 2 was about 25 

mwL and that fur Lake 3 was about 9 mg/L; however, the mean total al.kalinity for Lake 3 

was 165 mwL. much higher than the mean values fix the surface samples from Lakes 1 

and 2. Geoerally, alb1inity of surfaoe Wllkr in Lakes 1 and 2 decreased during !OUIDD!<r 

mooths, presumably due to algal photosynthesis, and simultaneously increased iu the 

bottom water samples. 

87 

VES 008025 
Conducth·ity. SpeQfic C()llduclance p-ovides a measure of a water's capaci1y to 

convey electric ctUTent and is used as an estimate of the dissolved minenl quality of water. 

This property is related 10 the total concenttation ofionized substances in water and the 

temperature at which the measurement is t11llde. While specific condu~'lwlce is ·affected by 

factors sucl1 as the nature of dissol~ substanec:s, d1eir relative concentrations, and the 

ionic sttength of the water ~lie, the geocbcmisey of the dnlinage basin is the major 

factor detemriuing the chemical collSiitueots in the waters. Practical applications of 

conductivity me3Surcments include purity of distilled or deionized water, variations in 

dissolved mineral concentrations in water samples, and estimation of dissolved ionic 

matter in water samples. 

The ocmduc:tivity values for Lake 3 wae higher than the surfuce S3111P.Ie values fur 

Lakes I .and 2, a phenomeoon similar to that ob6crved for total alkalinity. This is primarily 

because of the direct impact of Han!ing DitdJ on Lake 3. Also, the increasing trend of 

conductivity toward the lake bottom follows the same pattern as for alkalinity. The mean 

and ninge of eonductivity values (m ~em) ilr surface and near-bottom S311llles, 

respedively, were 373, 296-450 and 382, 282-468, fur Lake 1; 381, 312-456 and 466, 

238-747 f«Lake2; and 573, 433-714; 577, 443-719; and 580, 448-748 fcc Lake 3, sites 

I, 2, and 3, respectively. 

Pbospbo1.11s. Phosphorus as phosphate may occur in surface waters or ground 

waters as a result of leaching from lllinerals or ores, naiUral processes of degradation, or 

agricuiiUral drainage. Phosphaus is an essential nutrient fur planl and llllimU growth and, 

like nitrogen, it passes through cycles of decornpositioo and photosynthesis. 

Because phosphorus is essential to the plant growth process, it has become the 

focus of attention in the entire eutrophication issue. With phosphorus being singled out as 

prob;Jbly the roost limiting nutrient and the one most easily controUed by removal 

techniques, various facets of phosphorus cberUisl!y and biology have been extensively 

srodied in the rumaJ envirooment To treYelll biological troisance, the Ulioois PoUution 

Control Board (IPCB) (1990) stipula!es that "Pbo5phoxus as P stall not exceed 0.05 mgiL 

in any reservoir or ll!kc with a sw:fuce area of 8.1 hectares (20 acres) or more or in any 

stream at the point whcro it enten~ .my mJCh reservoir or lake. • 

VES 008026 
Unlike nitrate-nitrogen, pbosphorus applied as fertilizer. is held tightly to the soil. 

Most of the phosphorus carried into sneams and lakes from runoff over cropland will be in 

rhe particulate fonn. On the other hand, the major portion of phosphate-phosphorus 

emitted from municipal sewer systems is in a dissolved fom1. Tilis is also true of 

phosphorus generated fium Maerobic degradation of organic matte.· in the lake bottom. 

Consequently, the furm of phosphorus, raneiy particulate or dissolved, is indicative of its 

souxce to a cer1ain extent. 

From his experience with WJSCOOSin lakes, Sawyer ( 1952) concluded that aquatiC 

blooms are likely to develop in lakes during summer monthS when concentrations of 

inorganic nitrogf31 and inorganic phosphorus exceed 0.3 and 0.01 mg!L, respectively. 

These criricallevcls for nitrogen and pbosphorU'l <X>I!CCltrations have been accepted and 

widely quoted in scientific literature. 

A sw1li!a)' of the o~ fur total and dissolved phosphate-phosphorus in 

the lakes is given in table 16. The mean disso.lved phosphorus levels in all the lakes varied 

from 0.05 to 0.06 m!VL, and the mean total plOsphorus varied from 0.14 to 0.18 mS'L fur 

surllloe samples. Even the lowest observed total phOsphorus values in the Jakes were 

three to eigbt times bigber than the aitic:al values suggested by Smvya · (1952). The total 

and dissolved phosphorus mean values for Lake 2 bonom samples were 0.36 and 017 

mg!L, respectively, indicating that a very high proportioo of the total phosphorus is in the 

readily available dissolved fonu. These phosphorus values are mud1 higher than those for 

the surface samples. Levds of dissolved oxygen play a key role in controlling the amount 

of phosphorus released from the sedirneniS into the overlying walcr. Fillos and Swanson 

( 1975) reported a 2 I .fuJd increase in phosphorus release from scdimmts during anoxic 

conditions as opposed to aerobic cooditions. The total 300 dissolvod pllOSphorus data for 

Lake 2 near·bottom water samples dearly show this internal regeneration of phosphorus 

during periods of strnlificalion. 

Nitrogen. Nitrogm in natural waters is generally fOund in the fiml of nitrate, 

organic nitrogen, and Blllll100ia-nit Nitrntes are the md product of the aerobic 

SU!bil.ization of organic nitrogen, and as such they occur in polluted waters that have 

undergone self-purification or aerobic treatmmt processes. Nitrates also occur in 

89 

VES 008027 
percolating ground waters. Ammonia-nitrogen, being a constituent of the complex 

nitrogen cycle, results from the docomposition of nitrogenous organic matter. Ammoniamtrogen can also result from municipal and industrial waste disdlarges to streams and 

rivers, however. 

The concerns about nitrogen as a contaminrult in water bodies are twofold. First, 

because of adverse physiol.ogical elfeas on infar¥s and because the traditional water 

treatrocnt processes have no effect 011 the removal of nitrate, eoncentrations of nitrate plus 

nitrite as nitrogen are !imiied to 10 mg!L in public water supplies. Second, a 

concentration > 03 mgiL is considered sufficient to stimulate nuisance alg~~l blooms 

.(Sawyer, 1952). The IPCB stipulates that anunooia-nitrogen and nitrate plus nitrite as 

nitrogen sbould not exceed 15 and 10.0 mgi.L, respectively. 

Nitrogen is one of the principal elemental oonstituents of amino acids, peptide, 

proteins, urea, and other Ol'gi1Ilic matter. Various furms of nitrogen (for examtile, 

dissolved organic nitrogen and inorganic nitrogen sucl! as ammonium, nitrate, niLrite, and 

elemental nitrogen} caonot be used to the same extmt by c:liffi:oent groups of aquatic plants 

and'atgae.. 

Vollct~wcider (1968) reports that in laboratory tests, as a general rule, the two 

inorganic fODIIS of nitrogen, ammonia 1ald nitrate, are used by planktonic algae to roughly 

the smne extent. However, Wang et al. (1973) reported lbat during periods of maximum 

algal growth under laboratOI)' oonditions, arnmoniwn-nitroge;n was the source of nitrogen 

Jll'cferred by ·planktons. In the case of higher initial ooncentrations of ammonium salts, 

lower yields were noted than wifu equiva.len oonccntratioo.s of nitrates (Vollenweider, 

1968). This was attributed to the toxic effects of ammooium salts. The use of 

nitrogenous organic compounds has been noted by several investigators, according to. 

Hutclrlnson {1957). However, Vollcnw<."ider (1968) cautions that the direct use of organic 

nitrogen by planlctons bas not been definitely establi<;hed, citing that none of 12 amino 

acids tested with green algae and dill!oms was a sow-ce of nitrogen when bacteri&-free 

culiUI:CS were used. But the amino acids were oompletely used up after 'a few days whe2l 

the cultures were inoculated with a nlilctle of baderia i.<olated from water. He has 

opined that in view of the t8ct thai there are always bactErial mma active in narur-e, the 

VES 008028 
question of1be use of organic nitrogen sources is of more interest 10 physiology than 10 

eoology. 

The mean and range of values for ammonia, nitratelnioite, and kjeldahl nitrogen in 

the Jakes are included in lable 16. The me.m and range of values for ammonia·N (in tng/L) 

for surface and near-bottom samples were 0.1 I, 0.01-0.37 and 0. 15, 0.01-0.47, 

respectively for Lake I and 0.01-0.60 and 1.23, 0.04-7.30 for Lake 2. Corresponding 

values for Lake 3 SUiface samples at sites 1, 2, and 3 were, respectively, 0.11, 0.01-0.60; 

0.09, 0.01-0.38; and 0.10, 0.02-0.39. 

The mean and range of values for nitratelnioite-N in mg/L for surl'ace and nearbonom samples were 0.06, 0.01-0.10 and 0.06, 0.01-0.10, respectJvely, for Lake I and 

0.07, 0.01.0.34 and 0.05, 0.01-0.10 for Lake 2. Corresponding values for Lake 3 surfece 

samples at sites I, 2, and 3 were, respectively, 0.20, 0.01 -5.30; 0.07, 0.01·0.22, and 0.09, 

0.01·0.38. 

The mean and range of values for kjeldabl-N in mg/L surface and near-bottom 

samples were 1.9, 0.7-3.3 nnd 1.9, 0.8-3.0, respectively, for Lake I an.d 1.7, 0.4-2.7 and 

2.6, 0.8-8.1 for Lake 2. Corresponding values for Lake 3 surface samples at sites I, 2, 

and 3 were, respectively, 1.2, 0.10-2.40; 1.1, 0.30-2.40; and 1.1, 0.10-2.!0. 

Mean inorganic nitrogen (total ammonia-nitrogen and nitrate-nitrogen) for the 

surface water samples was generally less tban the suggested critical concentration (0.3 

mg/L) for nitrogen. In Lake 2, the mcoo values for total ammonia nitrogen increased from 

0.15 mg/L at the surface to 1.23 mg/L at the bottoiiL Kjeldabl-nitrogen me&~ values 

showed an iocrcasing trend toward tho bottom of the lake. These are clear indications of 

the significant anaerobic dccompo&ition of the organic debris occurring 011 the lake 

bottom. 

Total Suspended Solids and Vol.atllc Suspended Solids. Generally, the amount 

of snspended solids found in impounded waters is small compared wid1 the amount found 

in streams because solids tend 10 settle to the bottom of the lake. In shallower lakes, 

however, tlris aspect is greatly modified by wind and wave actioo and by the type and 

intensity of use to wiUcb these lakes rue subjected. Also, bottom-feeding fish, particularly 

carp, are known ro stir up bottom sediments and increase turbidity and sediment 

91 

VES 008029 
concentrations in the overlying waters. Volan1e suspended solids (VSS) are measures of 

the organic fraction of the tOtal suspended solids (TSS), and thus !he difference between 

these entities is taken as the inorganic ~eel particulate matter. There are no state 

watel' quality standards for the suspended sediments in the surface waters of illinois. 

Barring one vrsy high TSS value for a Lake I bottom sample, the mean and range 

of values fouod for the lhree lakes (table 16) are typical of shallow lakes in Illinois. The 

mean and range of values o~ in Horseshoe Lake, Madison County, wue 49 and 25 

to 70, respectively. Horseshoe Lake is mudl shnllower than Lake 3. Gemrally, the 

org~mic fractions of the suspended sediments in tlte lake varied from 35 to 60 percent. For 

Horseshoe Lake, it was about45 percent (Rehfeldt el aL, 1992). 

ChlorophyO. OtlorophyD a is a prirnaty photosynthetic p~t in an oxygenevolving pbotosyntbetic org;misms. Extraction and quantification of chkxuphyll a can be 

used to estimate the biorntiSS or standing crop of planktonic algae present in a body of 

water. Other alglll pigmeniS have limited distribution and are consida-ed accessory 

photosynthetic pigments; pat1icularly chlorophyll b and c can give infonnation on the type 

of algae presem. Blue-green algae (Cyanoph)'IS) contain only chlorophyll a, while both 

Lbe green algae (Clllorophyta) and the euglmoids (Eugleoopbyta) contain cbJororbyll a 

and c. ChkrophyD a and c are also present in the dialoms, yellow-green, and yellow· 

brown algae ((luysophyta), as v.-ell as the dinoflagellates (Pyrrbophyta). Therefore these 

accessory pigments can be used to identifY the types of algae present in a lake (IEP A, 

1990). 

To obtain Jiving algal bionJa5s, chkroJilyll a values are cooected f<r pbaeqilytin 

a. which is produced wher:t cblorophyll a breaks dov.n. If a large amount of pbaeophytin a 

is present, a stressed algal population or recentdie-ofris indicated (ibid.). 

Chlorophyll values for the lakes are shown in table 16. Tix: mean and range of 

<tlorqjlyll a values in flg/L we"~e 91.4 and 32.3-173.6 for Lake I; 91.1, 38.3-155.4 for 

Lake 2; and 56.8, 18.5-120.2; 55.3, 23.2-117.9; and 60.7, 13.1-186.9, ~vely, for 

sites I, 2, and 3 of Lake 3. Algal biomass f<r Lakes I Md 2 were comparable and much 

lrigher than f<r Lake 3. Based on cblorophyll a criteria for classifying the trophic state'or 

92 

VES 008030 
lakes, all three lakes oould be categ01ized as highly eutrophic. This aspect wt11 be 

subsequently deall with in more detail. 

Biological Characteristics 

Alg$C. Seasonal and spatial distnbutions of algal densities, expressed as the total 

cx>unts per milliliter (ctslmL), for each of the three lakes are depicted in figure 18. As 

shown, algal densities of the 80 water samples oollected duling tl1e three years ranged 

from a low of22S ctslmL on September 19, 1990, to a high of33,300 ctsfmL on October 

15, 1991, bod1 in Lake 3. Except for one sample (May 16, 1992, from Lake 2), all the 

other 53 samples collected from Lakes 1 and 2 showed alSiil densities > 2000 ctslmL. 

In an earlier study (Kolhandaraman aod Evans, 1983 a), alSill densities in Johnson 

Sauk. Trail Lake, IL, were between 270 ctslmL and 22,000 ctslmL during a period from 

May 1981 through September !981. In Lake L<>Aqua..Na, lL, total algal counts ranged 

from 800' ds/mL to 25,000 ds/ml. duling spring tluough fall of the three yea~'S from 1984 

through 1986 (ll?PA, 1990). For a period from April 1990 through October 1990, total 

algal densities in Horseshoe Lake, lL, runged from 180 ds/ml. 10 286,000 ds/mL 

(Rehfeldt el a/., J 992). Algal <l>"namics is a oompleJt phenomenoo, and the a!Sill counts in 

a lake ecosystem flucruate in a w:ry wide range. 

As sho'Ml in figure 18, there were e<tteme tluctua!ions in algal derlsities in each 

lake. Higbost algal drosity for each lake was observed in July for cad! year. Other algal 

density pulses occurred in APril and CX.:tober or November. In general, algal density 

decreased in May, Aul,'llSI, and Seplember oompared to the previous months. By contrast, 

bigJl algal counts in Jolmsoo Sauk Trail Lake (Kotbandaraman and Evans, 1983a) 

occurred in August and Seprember 1981. The higlle& algal density observed in Lake LeAqua·Na was io the sample ooHected on Novanber 14, 1984 (lEPA, 1990). 

Figure 18 also indicates that the seasonal and spatial distnootion of algal densities 

in Lakes I and 2 are vay sim.ila'. Lake 3 had lower algal densities than Lakes I and 2, 

especially during the summer and fall of 1989 and 1990. Howevec, in I 99 I all three lakes 

had similar algal deosity distribution patterns. 

VES 008031 
100,000 

Lake 1 I - ---- Lake 2 II 

50,000 ---Lake3 I I 

II 

I I 

I I 

I I 

I I I 

I 

I 

10,000 1\ 

I 

I -' /I ' 

~ 1 I '/ J 

c: I ::0 5000 ' ~ 0 

" 

~ I l "' I 

w I II "'\ E 

\V, (/) I II 

z I ' 

w I II 

Q I I I I 

:;J, II \ 

g ,, I I I \ I I I I 

< : \ ~ I I I I 1000 I I ' I I I 

\ I ' I I I 

" l I I \ I 

500 'I l I I 

I 1 I 

II 

u 

l 

100~----~~----~------~----~~------------~ 

1989 1990 1991 

SAMPUNG DATE 

Figure 18. Total algal densities in Franlc Holten State Parle Lakes 

VES 008032 
Algal Sprcics Richness. The number of algal species in the samples nu1gcd from 

6(February21 and March 19, 199l , inLake2,andMay 14, 199l, inLake 3)to 19(July 

II, 1991, in lake 1). 

In the 80 water samples exmnincd, 65 g~~l species were found: 9 blue-greens 

(Cyanopbytes), 19 greens (nonmotile Chlorophytes), 19 diatoms (Bacillariophytes), 15 

llagcllates (EuglenophyteS, Volvocales ofChlorophytes), and 3 desmids. These 6S algae 

species and their occurrence in the three lakes for each yea~ are listed in table 17. In this 

table, the occurrence is marked as "X" or "Y". An 11X '' indicates the occurrence of the 

orgnnism in any given year of investigation. A ·•y• indicates the organism was found in 

more than 50. percent of the samples in a given year. 

Table 17 suggests that the occurrence of green algae and diatoms in each lake was 

quite frequenL The algae occurring moot frequently in tbe tbree lakes were 

Aphanlzomcno11 jlos-oquae, CMiaJfTUm mlcropomm, Crudgenia reClllngulari.s, Oocysris 

borgel, Scenetlesnws dlmorphus, Melosira gronr1lata. E11glena gracilis. and 

Trachelomonas crebea. Most of these algae are indicators of eutrophic conditions. A 

polluted water blue-green algae, LJ1718bya diqueti, also occurred frequently and dominated 

in l akes I and 2 during summer OJtd full. ActinOJtrum hantzschii occumxl frequently in 

the three lakes in 1989 and in Lakes 2 and 3 in 1991 only, but it was never a dominant 

species. CoelasfTUm microponmo was frequently found in Lakes I and 2 in 1989 and 

1990. Euglena acus, o taste and odor flagellate, was only present in Lake 3, more 

frequently in 1990. A11abe!Ul spiraides, Pediastrum duplex, Cyclotella ocellata, and 

Phacus pleuronecres also occurred waD three lakes during each year of the study. 

A1J examination of the data shows that algal density peaks in July or during mn 

were due to high counts of bhoe-greens or green algae or a combination. of both. The 

dominant algae were either A.na/xJell/1 spiroides, Cyanarcus homiformis, Lyngbya digneti, 

OscillaJorla chlorina, Chlorella ellipsoidea, or Chlorella sp. 

A study of nearby Horseshoe Lake, 5 mHes north ofFHSP Lakes (Rehfeldt ct aL, 

1992), reported that A.plranizomenon jlos-aqulle, Crucigenia rectangularis, and Synedra 

de/Joati.ssima were the most frequently observed elgal species in the lake. 

95 

VES 008033 
Table 17. Occun·ence of Algae In F11mk Holten State Park Lakes 

~zk.e. l lak~ 2. dJ.At.~ 1 

Algal >peau 1989 1990 1991 /989 1990 1991 1989 1990 /991 

Blue-green algae 

Agmenelfwn sp. X X X 

Anabena >piroide.s X X X X X X X X X 

Anacys1is Jhermalls X X X X X X X X X 

Aphanizomi!Jron f/os-aq11ae X y y X X X X X X 

Cyanarc>ts homiformis X 

Lyngbya dlgnetl y X X X X X X 

Oscillator/a angustissima X X X 

0. chlorirra X X X 

Oscillatoria sp. X X X X X X X 

G.reenalgae 

Actinastrum hanrzsclrll y X X X X X y X X 

Ankistrodesmus convolatus X X X X 

A.. spirnli.J X X X X X X 

Chlocoarclna <'Orrsoclata X X X 

Chlorelfa ellipsoldca X 

Or/orella sl'. X X X X 

Chlorosorcma con.voclaf<J X X X 

Coelastrrmr mlcroporum X X X X X X X X X 

Crucigenia rectangularls X X X X X X X X X 

C tetrapedia X 

Micactinium pruillum X 

Oocysris bo'jei X X X X X X y X X 

P¢iastntm upla X X X X X X X X X 

P. simp/e:x X X X X X X X X 

P. tetras X X X X X 

Scenedesmru caritl4llrs X X 

S. dimorphus X X X X · X X X X X 

S. quadrictmda X X 

ScJrroeclerla sp. X 

Diatoms 

Asterionel/a formosa X X 

Calonels anrphisbal!na X 

Cyclorel/a atom11s X X X 

C memghiniana X X X X X X 

C ocelfaJa X X X X X X y X X 

Cymat(}{)leura M>lta X 

FragiltJria crotonorsls X 

Gomphoneis herculeana X 

Gyrosigma marcum X X 

Melosira ambigua X X X 

M. bindesana X 

M. gmnulata X X X X X X X X X 

\\ \Wavlc11la cryptocephalil X X X X 

N. gastrium X 

Stephanodi.Jars nlagarae X X 

96 

VES 008034 
Table 17. (Concluded) 

£,o.lu:. l lllk 2. l.ro.k. ~ 

A /gal spepi,.s 1989 1990 1991 1989 1990 199/ 1989 1990 1991 

Diatoms 

Surviclla OV<Jta X X 

Syncrlra acus X X X X X X X X 

S. tabulata X X X 

S. ulna X X 

Flagellates 

Carleria mult.ifilis X X 

Cermium hirwzdinel/a X X X X X X X 

Ch/o.nrydomonas relnhordi X X 

ChrysOC<JCcus n~escerzs X X 

Dinobryon senu aria X X X 

Euglena acus X X X 

E . . gracilis X X X X X X X X X 

E. oxyuris X X X X X X 

E. ><iridis X X X X X X X 

Glenadinium sp. X X 

Peridinitmt cinctum X 

P/uu:us p/eurtmectes y X y X X X X X X 

P.sp. X 

Platydorina candantm X X X X 

Tra<·heJomono.s crebea y X X X X X X X X 

Desmids 

C/osterium sp. X X 

Glelllxlinium barge/ X 

Glenodinium sp. X X X X X 

Notes: X = cq,anism 'VIIS foorxl in a givaJ year; ard Y = organism was fuund in more 

than 50 percent of the samples in a given yeat. 

97 

VES 008035 
Zooplankton Density. The tmu "planktoo" refers to those mia-oscopic aquatic 

forms having little or no resistance to =ts and tiving fie& floating and suspended in 

open or pelagic waters (American Public Health Association et at.. 1992). Plankton can 

be divided into planktonic plants or phytoplank1011 (microscopic algae), and planktonic 

animals, zooplankton. l11e zooplankton in fresh water comprise princip111ly protozoans, 

rotifers, cladocerans, and oopepods; a grea1cr variety of O<gaDisms occur in marine waters. 

Since Wiscoosin plankton net was used ror colleding plankton samples, protozoans w= 

not detected. In this report, protozoans are not included in zooplankton. 

Totaf obseaved 2.00]>lankton densities rnnged from 300 to 7500 Cls/L, from 200 to 

14,300 cts/l.., and from <iOO to 6,800 ClsiL for Lakes I, 2, and 3, respectively. The 

variation of zooplankton densities for each lake showed no trend with time. 

In the three lakes investig;l.led, 25 zoopl!mktor1 species were fuund. These 

included 14 rotifera, 6 cladocua, 3 copepoda, and 2 other species. All three major groups 

of zooplankton were found during the throe-year study period. Howewr, Acari and 

Cyciocyprisforbezi wa·eobserved in 1991 only at Lakes I aod 3. 

The dominant zooplanktons were fOOnd to·be ei~ rotifera or cladoceta The 

dominant species were Chromagaster ova/is. Keratellacocltlearis, K. stipitata, Bosmenia 

coregoni, Daphnia Jaevis. and Diap)omus minutus. Diaptomus minutus, Bosmenia 

corego11i, and Daphnia p11fex, species occwing most frequently, occurred more than 50 

percent of the time. 

Benthic Organi'iiDS. Benthic macroinvatcbrates are animals within the aquatic 

systan visible 10 the naked eye, and theY can be mained by a U.S. Standard No. 30 mesh 

sieve. These coounoo, easily collected organisms have limited Dl0b!1ity and are present 

throughout the growing season. An abundant and diverse community of 

macro invertebrates is important as a reliable fuod sow-ce fur fish. Mactoinvertebrates are 

sensitive to cllanges in the aquatic environment, C<Vrially 00. 

In terms of population density, samples from site I of Lake 2 had the lowest and 

highest populatioos, mngjng from 28 indivW!ls per square meter (July 13, 1989) to 

II ,481 (November 7, 1989). In tenns of sample dry weight, the sample at the same 

location on July 13, 1989, was the lowest, with 0.019 g. Again, samples from this site 

9S 

VES 008036 
showed the widesl v-.uiation in population lev~ls due to fluctuation in Cha.oborus levels. 

Numerous factors influence the 'veiglll of a sample, sucb as population density, species 

composition, and growth stage. The sample with the highest dry weight, 3.921 g was 

icund on March 21 , 1990, at the sampling site in Lake 2 established durina the period 

when the dredging restoration program was irnplemenlfrl (historic site). 

'The mean values of the samples eoUected at each station are presented in table 18. 

Lake 2, had the highest two stations in mean population and sample weight. Perhaps 

trient and phytoplankton abtmdancc intlueoced the benthic productivity of tl1is lake. 

The 100111 benthic DO is inversely rola!ed to the depth of the station. The deepest 

station, site I of Lake 2, had tbe lowest mm DO levels !l1d were usuaUy < 1 ppm during 

the summer. The shallow stations (historical sites of Lakes I and 2, wei site 1 of Lake 3) 

all bad a mtm benthic DO > 5 ppm. 

The eommlD'lity composition of the sampling station means, show.> that the 

shaUower stations are mainly dominated by 0/igochaeta and Chlronomidae, while the 

deeper stations are dominated by Chacborus. 

Benthic maaoim'12tebrales, an importlln1 source of fish food org<wisms, are 

chidly needed during the growing SC$011. Low DO conditions make the benthos in the 

deeptr areas of the lake unava:ilable during the critical wanner months. The produQjve 

volume of the lake, in terms of fish habitat and food, is theref01e reduced. 

Tropltlc Stare. Eutrophication is n natural proce.5S th.at 'affects every body of 

watel' from the time of its formation. As the lake ages, the degree of enrichment by 

!Ultrient mmmals increases. In general, the Jake traps a Jl0<1ion of the nutrients originating 

in the swrounding <h'ainage basin. In addition, precipitation, dry fallout, and ground-water 

inflow are the other eootnbuting sources. 

The literature has suggested a wide variety of indices of trophic conditions. 

Indices have boon based oo Secchi disc ~. cllbophyU 4. hypolimnetic oxygen 

depletion, nutrient concentrations, !WI biological pru:ametCI'S, including species abundance 

and diversity. The USEPA (1980) suggests in its Glean Lakes Program Guidance 

_Manual (table 3: 10-4) the use of fuur panuueters as trophic indicators: Secchi disc 

99 

VES 008037 
Table 18. Mean Benthic Macroinvertebrates Va lues 

in Frauk Holten State P3rk Lakes 

(ind.ivlduals per squo.o-e meter) 

St4tions 

Lake No. I Lake No. 2 LalleNo. 3 

HisL Site Site I HisL Site Sill! I Site I 

Chirorzomus (bloodwonn) 50 294 212 235 2 

Chironomidae (non-Chironomus) 586 182 158 31 323 

Chaoborus (phantom midge) 194 1,321 715 4,769 273 

Cerato~gooidae (biting midge) 18 1 48 57 110 72 

Oligoc aeta (aquatic worm) 876 475 1,835 464 820 

Total numbers 1,887 2,320 2,977 5,609 1,490 

Total dry weight, grams 0.789 0.815 1.182 0.901 0.488 

Dissolved oxygen, parts per million 8.0 3.9 7.8 2.8 5.7 

Approximate deplh, feet 6 18 6 25 7 

(Sample$ were collected on 813/89, Lln/89, 3/21/90, 7/9/90, 4/17/91, and 8/22/91) 

100 

VES 008038 
transparency, and concentrations of carllon, phosphorus, and chlorophyll a. Those aiteria 

are reproduced in table 19. 

In addition, the lake trophic state index (TSI) system developed by Carlson (1977) 

on the basis of Secchi disc transparencies, chlorophyll a, and total phosphatc-P values can 

be used to evaluate a lake's trophic state. The index munber can be calculated from Secchi 

disc transparency (SD) in meterS. chlorophyll a (CHL) in micrograms per liter (Jlg/L), and 

total phosphorus (TP) in llt¥L as follows: 

TSI(SD)=60 - 14.411n(SD) 

TSI (CHL) = 9.81ln (CHL) + 30.6 

TSI (TP) = 14.42 In (TP) + 4. 15 

The !lU!Ilerical index rnngcs frorn 0 to 100. Lakes wifh TS! values <40 are 

classified as oligotrophic (nutrient-poor or relatively unproductive, biologically speaking), 

and those with TSI values >SO are classifitld llS eutropliic (highly productive). Each major 

division (10, 20, 30, etc.) represents a probability of a doubling biomass. 

Table 20 gives the mean and range of values ofTSI b the Jake stations, using tbe 

observed SD, TP, and CHL values. The~~ TSI values tor the lakes, based on all three 

parameters, are high and in the 70s except f<x Lake 3, 'Which bas a TSI mean based on 

dlloroJ:hyU a values of 69. Lake 3 ~bited the lo-st chlOI'OfhyU a values of all d1r00 

lakes. However, the TSI mean value was li:AIId to be almost 70. Based on the USEP A 

aitaia and the TSJ values for lbe lakes, it is ooocludetl lhat Iiley are CUtTelllly 

bypereutropbic oc highly nutrient cnridled. This is not entirdy surprising because most 

illinois lakes .and impoundments were rotWI to be nutrient enricbed and even exhibited 

symptoms of eutrophy right frorn their llllSCenCy (Kodmdaraman arxl Evans, 1983a, 

1983b) ~use of their org.nie, rich bottom soils. Internal regeneration of nutrients 

under anoxic conditions during the SUinmer stratification period was determined to be 

adexjuate to cause algal blooms (ibid). Bodamer (1992) reported for Lake Springfield, IL, 

"ilicll mldelwml sign.iiicm dredging in the upper reaches of the tributary arms of the 

lake, that dre;!ging alone was not the solution to reducing nlllricnt levels in. the water 

colwm. 

101 

VES 008039 
Table 19. Quautitative Definitions of Lake Trophic State 

(USEI'A, 1980) 

Oligo<rophy Eutrophy 

Total phosphorus (winter), Jig/L ()..1 5 2:20-30 

Chlorpbyll-a (summer), ftg/L <2-4 >6-10 

Seccbi disc depth (summer), m 2:3-5 9.5-2 

Primarv productivity 

Carbon (mg!m21yr) 30-100 300-3000 

Crubon (ug!m2/day) 7-25 75-700 

Table 20. Carlson Trophic Stale h•dex Values for Lake Stations 

£aka l lakt!Z l.akf. ~ Site. l 

Parameter Mean Ra11ge Mean Range Mean Range 

Seccbi disc n 65-78 71 65-77 71 6b-80 

Tolai p~!Jate.P 78 67-90 76 67-92 74 65-87 

Ch!oroph_ a 74 65-81 74 66-80 69 59-76 

l<U 

VES 008040 
Macro1>hytes. As indicated in table 13, macrophyte surveys were conducted on 

seven dill'crcnt occasions during this inve;tigation. During the first two nips, (JWle and 

July 1990) the lak:ebed was examined 81 15 to 20 feet (more than twice the SeodD disc 

rrnnsparency) from tbe ~ all around each lake by walking, searching fur aquatic 

rooted vegctatioo. It became appEU"Cflt thai the lakes are totally devoid of any rooted 

submerged aquatic plants. This is true not only for the dredged portions of the lakes, but 

also for the two undredged areas, one each in Lake I and Lake 2. Even relatively shallow 

Lake 3 did not harbor any vegetation. TI>is total absence of aqoatjc vegetation is quite 

puzzling. Transparmcies in the lakes are low (average Sea:hi disc readings are $8 

iodles), which is one of the faaors ooo1nbuting to the lack of vegetation. A second factor 

cxml be the loose, ftufiY lake bottom sedUnoJIS (which is true for the southern portion of 

Lake 3, more so than for Lakes I and 2) from which Ill3a'ophytes oould easily get 

uprooted by wind and wave action. Also, grazing pressures from wildlife populations 

could easily decimate the standing cmp as experienced in Peoria Lak.e (Roseboom eta/., 

1989). As is weU known, rooted aquatic vegetation is an essential 00111pOill"llt of a wellbalancOO ecosystem Jroviding fuod and shelter for desirable sports fisheries. Ibis aspect 

is :all the more importanl and relevant, considering the met that the lakes are heavily used 

fir fishing. The remaining five macrophyte surveys w'el'e made from a boat by probing tbe 

lakebed with an oar at frequent intervals. 

Sediment Characteristics. The s~ of sediments in the aquatic 

ecosystem is not only .(tysical in nature, but also dle!llical and biological. In addition to 

the dircd. loss of storage capacity resulting from sediment deposition, lake sedimro.ts play 

an important role in intrc:dlcing substancx:s sud> as phosphorus, nitrogen, adsorbed trace 

metals, aod organic oompounds to the overlying waters J:Micularly llllder anoxic 

conditions during periods of thermal stratificalion. Also, the beolhic ~ are known 

to bioaccumulate toxic substances from the aquatic medium and pass them up the fuod 

chain to potentially dangerous levels for birds, animals, and lnunans. 

The r~ults of analyses of sediment samples collected from the lakes on June 7, 

1988, are given in lllble 21. Alsi:l, included fur refeceuoe are the Jlli9l values fur 

phosphorus, kjeldahl nitrogen; and a few of the heavy metals reported by Kclly aod Hite 

103 

VES 008041 
Table 21. Frank Rolteu Stare Park Lakes Sediment Cbamcrcristics 

Mean Value 

L.aB.c l lals.e.l Ml~f 1. far 63 Illinois 

Parameter Historical Site Historical Site Site I Site 2 Lake.•• 

Percent residue by weight 27.7 29.5 21.5 24.5 

Percent residue by volume 10.3 8.9 4.8 8.8 

Pbo~rus 72 691 870 985 666 

Kje1 nitrogen-N 3530 2740 1660 1730 5530 

Cadmium · 3.4 2.2 3.9 5.0 1.0 

Copper 38 24 27 28 41 

Lead 91 29 47 52 50 

Mercury 0.37 0.04 0.05 0.06 0.09 

Arsenic 9 6 8 12 11 

Chromium 17 IJ 17 22 23 

Iron 16000 15000 22000 28000 28631 

Manganese 4400 630 11000 1000 13 13 

Zinc 180 83 108 120 II I 

PCB's 75.0 10.0 10.0 10.0 

Aldrin 1.0 1.0 1.0 1.0 

Dieldrin 1.6 1.0 1.0 1.5 

DDT Analog,s 10.0 10.0 10.0 10.0 

O'P'·DDE 1.0 1.0 1.0 1.0 

l"P'-DDE 1.0 1.0 1.2 3.0 

O'P'-DDD 1.0 1.0 1.0 1.0 

l"P'-DDD 1.0 1.0 1.0 2.0 

0'1"-DDT 1.0 1.0 1.0 1.0 

P'P'·DDT 1.0 1.0 1.0 1.0 

Chlordane tech. & met 5.2 5.0 5.0 7.9 

Chlordane C isomer 2.1 2.0 2.0 3.7 

Chlordane T isomei 3.1 2.0 2.0 4.2 

Endrin 1.0 1.0 1.0 1.0 

Methoxychlor 5.0 5.0 5.0 5.0 

Alpba-BHC 1.0 1.0 1.0 1.0 

Gamma-BHC 1.0 1.0 1.0 1.0 

HCB 1.0 1.0 1.0 1.0 

Heptachlor 1.0 ).0 1.0 1.0 

Heptachlor epoxide l.O 1.0 1.0 1.0 

Note: Nutrients and metals are expressed as mglkg of sample, and all the orSJllliCs are expressed liS ~lglkg 

of sample. 

• J<eUy and Hire (1981). 

104 

VES 008042 
(1981) for sediments ooUected from 63 lllinois lakes during summer 1979. Phosphorus 

concentrations in the FHSP Lakes are componble r.o the values reported for other Dlinois 

lakes, and kjeldahi-N values are mud1 less than tbe mean val\le for other lakes. The 

e<ldmium level is three to five times higha· in FHSP Lakes. The sampling site in Lake I 

exhibited much higher levels oflead, mercury, and zinc than the olher two FHSP Lakes 

and the mean values for the 63 Dlinois lakes. There has been no fish advisory in the recent 

past fur the fish caught m these lakes. The IPCB has not set standanls for sediment 

quality cbarJcteristics. 1he org;uric constituents reported in table 21 are in parts per 

billion. The polychlorinated biphenyls (PCBs) values measured for Lake I were 7-1/2 

times higher than the values rneaswal fur the other lakes in the 6-ysteln. However, all 

other reported org~Ulic constituents fur the three lakes were the same or comparable. 

Compariwns of Water Quality O.aractcrlstics for tl\e Restoration and Postes o~ation Periods 

Limnological data on the pre-restoration conditions of the lakes arc extremely 

spaxse. Hemy, Meisenheimt;r, &Ge:ocJe.lnc. (1975) reported on the lake conditions based 

on one sample ooUected from each lake on October 27, 1975. They concluded thai Lakes 

I 8lld 2 were relmively clear, but Lake 3 was murky. Lakes 2 and 3 exhibited high 

concentrations of nitrates. Ammonia levels were below detection limits in Lakes I and 3 

and 0.2 mgiL in Lake 2. They also reported vey high counts of fecal oolifonn in Lake 1 

(2400 cts/1 00 mL), probably due to sewage or oooCamina1ion by waterlowl. These 

o•g1111isms were not detected in the other two lakes. 

Table 22 shows the mean and range of values observed in the lakes during the 

restoration period (1977 to 1984) for. oertain water quality parameters, 'Nbich were also 

monitored during the post-restoration monitOting period (I 988 to I 991 ). Barring the very 

low pH valueof2.4 reported fur Lake 3 by Brigham (1984), which is aoomalous, all otber 

mean and raoges of values sbown ·in O~e table are typical of Dlinois lakes. Brigham 

indicated in tbe report that the cblorophyll a values are expessed as mWL It is preromed 

these values are fllYL. which will be cootmenSUnlle with the observations fur otba- lllinois 

lakes. 

lOS 

VES 008043 
Table 22. Surfill't! W11ter Quality.Characteristics 

Frank Bohen State Park Lakes during Restoration Period 

(1977-1984) 

Lake No.1 LakeNo . .2 Lake No.3 

Parwneters Mean Ra11ge Mean Range Mean Rlluge 

Dissolved oxygen 9.0 3.4-18.6 8.8 3.8-18.4 8.2 l.Q-18.0 

pH, units 6.3-9.4 7.2-9.3 2.4-9.6 

Total alkaliniry 95 9-160 118 76-166 155 6o-320 

Dissolved pbospbare-P 0.05 0.01.0.17 0.04 0.01.0.13 0.08 O.ot-0.42 

Total phosphate-P 0.17 0.04-0.35 0.13 0.03.0.23 0.26 0.04.0.71 

Total ammonia-N 0.45 0.45-1.77 0.29 0.03.0.70 0.50 0.03-2.60 

Nitrate-N 0.07 0.01.0.85 0.06 O.oJ-0.72 0.07 0.00.0.79 

Particulate residue (18o•c) 26 Q-198 22 1-206 47 1-389 

Chlorophyll a 84.5 0.1-329 35.7 0.6-259.0 94.0 0.2-429.0 

Note: Values in mg/L unless otherwise indlcated. 

Source: Brigham (1984). 

106 

VES 008044 
Table 23 shows the mean value.~ of these parameters for both the restoration and 

post-restoration peiods. I be su:face mean DO concentrations in 311 the lakes during 

these rwo periods are high !r1d are oom)lW'&ble. Brigham (1984) report.ed that only 8 

percen1 of all t!te surfuce DO CJbservatioffl for the lakes wtte ~ 5 mg/L, and 20 _percent 

more were ~ 6 mWL The oou espollding values for the current investigation are 5 and 6 

percent based on 282 !r1d 106 obselvations. respectively. Brigham (1984) opined in her 

report that ''removal of 3 teet of accumtllntoo sediment from each of the lakes, however, 

sbould improve DO concentrations by limiting the amo\lllt of potential oxygen-demanding 

material in the sediment" Hol.'.eVer, as discussed earlier, oxygen danand from the Jake 

bot!Om sediments caused oxygen depiction in the bottom waters of the Jake during the 

wann summer periods. 

Toea I alkalinity was correspondingly higher in the Jakes during the post-restoration 

period, dissolved phoophate-P was similar, 11' was lower in Lake 3, total ammonia was 

significantly less, and nitrate was much higher and particulate residue (suspended 

sediments) much lower in lake 3 during the post-restoration period. A statistical 

evaluation of the parameters oommou to both the peiods fuHows. 

Table 24 presents the fiequency of ()('.CUlMJCe of total and di=lved pbosphat~ , 

31llJll0nia.-N, and nitrale-N for all three lakes dtxing the restoration !lld post-restoration 

periods. For 11' in Lake I, 95 percent of the observed values were S 0.3 mg/L, 75 

percent were ~.2 mgiL, 50 p«eent were~ 0.15 m!VL, and 25 Percent were S 0.11 mgJL 

during the restoration period. The = ·ponding values for the post-restoration period in 

Lake 1 were 0.38, 0.22, 0.17, and 0.13 m!VL, respectively. In Lake I, a higher rWJge of 

CO!la!ll.trations of total and <msotvOO pho..<;phorus were found fur fue top quartile of values 

during the post-restoration period. There was a ~ redpction in ammouia-N values 

tluoughout the post-restoration period. For. nitrate-N in Lake I, the middle two quartile 

values were double or more during the post-restoration peiod than the value; finxl for 

the restoration periOd. 

Total and dissolved phosphorus levels were higher in Lake 2 during postrestoration monitoring. They were o~ in lake 3, however, due to tl1e diversion of 

Harding Ditch, resulting in decreased scdilllCill inflow into the lake. Ammonia·N levels in 

107 

VES 008045 
Table 23. Mean ·water Ootalily Cha.:actcl'istics of Frank Holten State I' ark Lal<cs 

for Restoration (19"77-1984) and Post-Restoration (1988-1991) Periods 

Rr::s..w.caf-iQa &:.t.iad. Pau.Refloratjon Perigd 

Porame1ers LakeJ .Lake2 Lake 3 Lalu!/ Lake 2 We 3 

01ssolved oxygen 9.o• s.s• st s.s• 9.68 9.68 

Total aJkaJjnil)l 958 llsB 155. ,c 1143 1223 •b J64c 

o.os• 0.048 0.088 o.os• 

a 

Dissolved phosphaoe-P 0.05 o.os• 3 

0.17

8 0.133 0.263 a 0.143 Total phosphllte-P 0. 18b 0.17 

Total ammonia-N 0.453 0.29a,b o.soa 0 . II o.J5b O.Jib 

Nitra.te-N 0,078 0.063 0.078 o.o63 O.o?a 0.20 

Particulate residue 263 228 478 248 n• 223 

Oll.orophyU a 84.5a 55.18 94.78 91.33 90.9" 

56.9

3 

Notes: Cblorophyll a ex~ as Jlg/L; and all othu-measurements are mgl[. 

Mean values with similar superscripts are not significantly differmt by Duncan's multiple 

range tests at O.OS significance level. · 

lOS 

VES 008046 
Table 24. Frequeney of OccmTence of Ccrtnin Water Quality Parameters 

in Frank Holten State Pnrk Lakes 

Total Dlssollwl 

Percent :S ll.hosehonu e.h .t;rz.h fJ.r ~~ d,mmonia, .. A f:i.itrnte-JV 

indicated value A B A B A JJ A B 

95 0.30 0.38 0.15 0.20 0.98 0.36 0.20 0.10 

75 0.21 0.22 0.08 0.08 0.62 0.1 0 0.04 0.10 

50 0.1 5 0.17 0.04 0.03 0.38 0.10 0.30 0.10 

25 0.11 0.13 0.02 0.02 0.21 0.06 o:o1 0.01 

Total Dissol»ed 

Perl'blf S e,hOE/!.MTU$ e.h~se.h ru · AmmoniD-d Nitrote-N 

in4iclzted value A B A B .-4 B A B 

95 0.20 0.42 0.08 0.24 0.60 0.54 0.14 0.18 

75 0.16 0.22 0.04 0.06 0.38 0.1 6 0.05 0.10 

50 0.12 0.15 0.03 om 0.29 0.10 0.03 0.10 

25 0.08 0.11 0,02 0.02 0.1 5 0.09 0.01 0.01 

ake3 

Total Dlsso/V<td 

Percl'nt S e.hrzmhorus e.hoseh!!.!J£'+ An1monio~A ~!itr e-l!f. 

indiarkd \'alue A B A B A B A B 

95 0.65 0.24 0.17 0.10 1.00 0.42 0.30 0.39 

75 0.35 0.17 0.10 0.06 0.66 0.10 0.06 0.10 

50 021 0.13 0.06 0.04 0.34 0.10 0,03 0.10 

25 0.11 0.11 0.02 0,03 0.25 0.05 0.01 0.01 

Notes: A p data fa restoration period (1977-1984); B = data for post-restoration period (I 988, 1991); and all values are~ a~ mg!Luoless indicated otherwise. 

109 

VES 008047 
each quartile were lower in Lakes 2 and 3 during the post-restoration monitoring period. 

However, the trend was reversed in tbe case of nitrate in both lakes. 

Duncan's multiple range test (Walpole and Meyers, 198S) ':"11S used to delineate 

the differeooes in the mean values of the water quality charocteristics in Lakes 1, 2, and 3, 

grouping tb.e data for these lakes individually for the periods covering the restoration 

(19n to 1984) and post-restoration (1988 to 1991). The tests were carried out at the 5 

percent significance level, ond the results are included in table 23. 

The statistical tests indicate that for several of the water quality characteristics in 

the three lakes, no statistical dilfurenoe was observed between the data during the 

restoration and the post-restomtioo periods. TI1e Slllface DO, total and dissolved 

pho5phale-P, particulate residue, and cl!lorqDyll a all full under this categoty. Total 

alkalinity in Lake 3 was lllUd! higher compared to the other two lakes for both types of 

data sets considered here. Total ammonia levels were higher in all lakes fur the restoration 

period compared to the post -restoratioo peliod. Observed data funned two distinct sets 

of data with respect to amm.ooia-N. Signi.ficanlly high nitrate levels were measured in 

Lake 3 during the post-restoration period compared to the other two lakes and the 

restoration period data fur all three Jakes. Mean values of nitiates in Lakes I and 2 fur the 

post-restoration period mel the values for aU three lakes during the restoration period 

were statistically similar. Nitrato-N values for Lake 3 were significarwly higher during the 

post-restoration petiod. 

CrcdSurvey 

A a-eel survey was conducted oo FHSP Lakes .fiom March 15 to November 15, 

1991, by the INHS under Fooeral Aid Project F-09--R The data for the creel survey are 

includoo in the appeodix as tables AI and A2. For the most part, the results of the creel 

survey were about \Waf would be expectoo from an Uiban lake. But exceptions were 

fomd in 8llg!ing presrure and boat fishing versus shore fishing. The total of 248 

hoursfuae (hWac) fishing pressure measured is low oompa1ed to 666 hrslac at Beaver 

Darn and 850 brslac at Si.IO<J.n Springs. Further, shore fishing accounted for 80 per0011 of 

the fiShing effint and boats accounted fur only 20 percent. Normally, one would expect a 

110 

VES 008048 
60-40 split the other way. Tite angler using FHSP l.akes traveled an average 4.6 miles to 

fish, and tl1e oVI!raU rating of the lake by the anglo'S on a scale of I - 10 was 2. 7, 

indicating much dissatisfaction with the fishing. 

Angler catch results are presented separately for fish caught (includes both fish 

harvested and those released) w1d for fish harvested. The results of the survey showed 

that anglers caug}!t and/or harvested nine species of fish including black and white crappie, 

largemouth bass, channel catfish, bluegill, drum, rainbow trout, redear smfish. and yellow 

bass. A misoellaneous categOrY fur fish caught in too low a quantity to be included in the 

SWililll'l)' statistics includes yellow and black bullhead, carp, bigmouth buffalo, bowfin, 

gizzanl shad, green Sllllfim, and shonnose gar. In all cases, the catch statistics are below 

wbat would be expected or targeted for these lakes. As an exmnple, largemOU!h bass, the 

main predator stocked in these lakes, were caught at ooly 4.8 pounds/ac, but one would 

expect the catdJ rate to be about 20 poUlldslac. Further, it appears that the anglers are 

keep.ing most of what they catch, ns the dilferenoe between catch and harvest is not great 

The average size of fish harvested was small. Yellow bass, for instance, were less than 0.1 

pound on the average. It is difficult to envision anyone being able to catch a fish that 

small 

In &l!IliDafY, the catCh results rellea the angler rating of the lake. Anglers were 

catching low numbers of fish !hat, b' the most part, were smaller than expecttd or 

desired This is probably due to lack of maaopbytes, significant reduction in fish habitat 

during the Slll'llm' sbnlificalioo period, poor quality ax! quantity of benthos, ovcrbarvesl, 

and/or J?05S'bly because most of the fishing was from the bank, limiting anglers to a 

relatively small proportion of the lake. 'The lack of a trout stocking program, which was 

disoontiuued after 1990, might also acoount for diminished fishing pressure. 

Park Attendance and User Survey 

Ever sinoe lalre restoration and the upgtade of the State Park facilities, park 

attendance bas steadily increased. Table 25 shows the estimated mnnber of visitors to the 

Stale Park from 1981 through 1991 ba9ed on the murber of vehicles entmng through the 

main entrance, counted using an automatic oounte£, ax! as;uming an average of three 

Ill 

VES 008049 
Table 25. Estimated Visitors Rcconl for Frank Holten State Park 

Month 198/ 1982 1984 /985 1989 1990 1991 

llforrthly 

avt!rage 

lapuary 3,031 1,389 3.0'16 3,806 10,747 '17,334 3,574 6,138 

February 2,Q62 2,640 3,001 5,828 5,412 19,625 12,704 7,325 

March 2,266 3,627 6,545 7,916 14,143 22,530 25,227 11,751 

April 2,295 5,734 2,488 37,686 38,949 36,31 s 37,175 22,949 

May 14,524 18,456 17,897 27,706 43,898 45,691 60,165 32,620 

June 14,322 15,882 22,424 29,100 43,831 44,359 49,283 31,314 

July 18,176 20,598 27,010 25,294 46,905 45,458 70,959 36,343 

August 19,415 16,839 20,864 29,453 34,033 39,335 88,149 35,441 

September 8,502 13,685 . 14,807 25,975 53,058 39,043 48,794 29,123 

·October 7,396 11,789 8,030 7,655 23,038 28,251 22,840 15,571 

November 5,173 11,469 10,182 9,320 19,094 22,644 14,002 13,126 

December 2,234 6,232 2,935 3.289 5,780 11,604 13,177 6,464 

Totals 99,396 128,340 139,279 213,028 338,888 372,189 446,049 

ll2 

VES 008050 
persons per vehicle. The nwnber of vehicles entEring the park was estimated upwards to 

account for the vehicles entering through another entrance for Lake 3. As indicated 

earlier, the park provides excellent recreational facilities such as picnicking, hiking, 

jogging, baseball, basketball, tishing, Wld boating. Figure 19 shows views of the attractive 

entrance to the park, baseball diamond, baskeiOO!l court, part of the golf course adjoining 

Lake l , and a picnic sbeltel". 

Park attendance inaeased sigoi6ca11ly in -1985 after completion of the lake 

restoration project 200 the upgrade of !he park fucilities by 1984. The park shows a 

steadily increasing number of vi~itors ~ince 1985. This is due in large measure to !he 

e1Ccellent upkeep and rnanagemc:n1 of the park facilities and control and elimination of once 

rampant crime, trilsh, and dEbris problems. The authors have seen lllaJ and women 

walking, jogging, and exerci.'<ing during early momillg and late evening hours. ·nus would 

not have been the case prior to 1984. Table 25 indicates heavy use of the park fdcilities 

from April through September. The site superintEndent indicated that several thousand 

people use the park's picnic fucilities during holiday weekends such as Memorial Day, 

Fourth of July, and Labor Day. 

To elicit infunnalion about tl1c pc:a:ptions of park fucility usa:s, a questionnaire 

was prepared and distributed during the SUJJJIIlfJ" of 1991 from the on-site OOllcession · 

stand and by FHSP personnel. A copy of the questianoaire is pr=tcd as table 26. A 

5UI1llll3ly of the results of the 17 JeSpOnSeS received is gi\'llll in table 27. 

Of the 17 respondents, 12 were male axl51k-ere female. Most were in the41-50 

age group, and no one under 20 ~ed. The survey indicales that picnicking is the 

most common activity, fuDowecl by fishing. The park facilities are used heavily during 

weekends, and 4Q percent of the respondents used the park throughout the wock. Almost 

all of them had visited the park prior to the restoration program. The m!Yority arc very 

frequent users of the fucility and rate it higbJy as a recreational resource. Warer quality 

and fishing in the lakes are peroeived as having in:p"o''td It wns unanimous that the 

parl<grounds have imj:roved a lot and are IIIlXh sa1tt 10 use. Nearly e\~e had positive 

f~ about the fucility and iJVlicaled dlat they used this valuable resource more 

frequently afif2" the restoration and cnlmament of the quality of the lakes and the park. 

lll 

VES 008051 
Attractive enHance io 1he park 

Figure I 9. Frank Holten State Park 

114 

VES 008052 
Picnic sheiter . 

Basketball court 

Figure 19. Concluded 

I 15 

VES 008053 
Table 26. Fronk Hollen State Park User Survey 

I. l am a: Male _ _ Female_ 

I am be()!leeo the ages of <20 years old _ _ 

20·30 years old __ 31-40 years old _ _ 41·50yearsold _ _ SJ-60 years old __ 60+ years old __ 

2. I usually go to FHSP to go: 

fishing bixd watching 

JOgginglwalking boali!W=>oeing 

P.icnicking on a timilly outing 

biking boy scouting 

other 

other 

3. When I visit FHSP, it is usually: 

during the week 

on the weekend 

any day during the week 

4. The first time I ever visited FRSP was: 

before 1975 

between 1976·1980 

between 1981-1985 

between 1986-1990 

after 1990 

5. I go to FHSP: 

0·5 times per year because it's the only 

6-10 times per year park around 

11-20 times per year 

21-50 times per year because irs the best 

5 H times per year park atound 

6. Onascaleoflto 10(1 istheworst, IOistbebest), howwouldyourate 

FHSP as a recreation resource? 

(circle one) 2 3 4 s 6 7 8 9 I 0 

116 

VES 008054 
rF YOU HA V£ BEEN VISTITNG I'HSP SINCE BEFORE 1985, PLEASE ANSWER 

11-IE FOUO\\'ING QUESTIONS: 

7. Has the quality of the water in the d1r7C FHSP lakes improved since. 1985? 

yes, a lot 

8. Hasthefishingimprove1 since 1985? 

yes, a little 

no, not at all 

yes, a lot 

yes, a little 

no, not a1 all 

9. Has the quality of the park grounds iln!Juwdsince before 1985 (i.e., trash is picked up, 

grass is regularly mowed, restrooms are clean)? 

yes, a lot 

yes, a linle 

no, not at all 

10. Is FHSP a safer place to reacute (i.e., fish, jog, walk, picnic) now than it was before 1985? 

yes, a lot 

yes, a linle 

DO, not at all 

II. Do you use the park llld its liloilities mae row than you did before 1985? 

yes, a lot 

yes, a little 

no, not at all 

~why do you use the park more? (dleck all that apply) 

The fishing is better now than it was 

The water is cleaner aro more attractive 

The park is a lllllCh safer place to go 

There is more to do at the park 

Other --- ------ Other - ----------

l17 

Majoc Minor 

Reason Reason 

VES 008055 
12. Please provid~ any commeniS you have regarding FHSP. 

TIIANK YOU 1br llll.'>Willing this questionnaire. Please return your oompleted questiormaire to 

the concession stand. the paik offiCe, or by mailing it using the self-addressed, suunped oovelope 

to: 

118 

VES 008056 
Table 27. Sunu!W)' of User Survey Responses 

Percent of M1mb•r of responses to 

responses the questiotl 

Response Numbel' 123 4 56789 10 II 12 13 14 15 16 17 

Que$ion I 

a. mule 1 1111 1 1 1 I 1 I I 12 70.6 

b. foOUlle I I I I I 5 29.4 

to1Jl1 17 100 

age<20 0 0.0 

21 -30 I 5.9 

31-40 I I I I . I s 29.4 

41-50 1 I I I I I 7 41.2 

51~0 3 17.6 

60 + I 5.9 

total 17 100.0 

Question 2 

•. fish 1 I I 1 I 1 I 1 10 58.8 

b. jog/walk I I I I I s 29.4 

c. ~cnic I 1 I I I I I 1 I I I 13 76.5 

d. ike I I I I 4 23.5 

e. bird watch I I 5.9 

( boallcaooe 0 0.0 

g. ~mily outing I 2 11.8 

h. boy scouting 0 0.0 

i. other I I 3 17.6 

Question 3 

a. ckuing the week 0 0.0 

b. on the weekend I 1 I 1 I 1 I I I I 10 58.8 

c. my day I I 1 I I 1 7 41.2 

total 17 100.0 

Question4 

a. before 1975 I I 1 1 1 I l I I 1 1 1 1 I I I 16 94.1 

b. 1976-1980 0 0.0 

c. 1981-1985 0 0.0 

d. 1986- 1990 I 5.9 

c. afior 1991 0 0.0 

total 17 100.0 

Quostioo 5 

a. G-5 times I I I 3 17.6 

b. 6-10 times 0 0.0 

c. ll-20 times 11 1 3 17.6 

d. 21-50 times I I I 4 23.5 

e. 51+ times 1 I I I I I I 7 41.2 

total 17 100.0 

Question 6 

a. FHSP Ranking 9l010101010 810 5 7 7 9 10 10 10 810 total 153 100.0 

(G-10) average 9 

ll9 

VES 008057 
Table 27. Concluded 

Percem of 

Numbor of responses to 

respon.res the que.ttlon 

Question 7 

Water quality improve? 

n. lots I 1 I I I II I I 1 I I 14 82.4 

b. little I 5.9 

c. no 0 0.0 

total 15 88.2 

Question 8 

Fishing improve? 

a. lots I I I 1 I I 1 I I I I 1 13 16.5 

b. little 2 11.8 

c. no 0 0.0 

total 15 88.2 

Question 9 

Park grounds improve? 

n. lots I 1 11 111 1 1 I I I I 17 100.0 

b. litde 0 0.0 

c. no 0 0.0 

total 17 100.0 

Question 10 

Safer to recreate? 

a. lots 11111 1 11 I I 1 1 I 1 I 17 100.0 

b. little 0 0.0 

c. no 0 0.0 

total 17 100.0 

Ques1ion II 

Use park more? 

a. lots I 1 I I I I I I I I I I 14 82.4 

b. little I I I 3 17.6 

e. no 0 0.0 

total 17 100.0 

If yes, 

a. I O'lo more 2 ll.8 

b. 25% rnore I 5.9 

e. 50% more I 2 11.8 

d. 75%Wof0 I I 5 29.4 

c. 100%more I I 5 29.4 

total IS 88.2 

If yes (1 major, 2 minor) 

a. fishing is better I I J I I 1 I I I 10 58.8 

b. water is cleaner I I I 1 I I 2 I 1 I I 13 76.5 

c. parltis sar ... I 2 I II I I I I I I I IS 88.2 

d. more to do 1 11 111 I I I I 1 I 14 82.4 

c. other I 2 11.8 

Question 12 

other comments I I I I I .J I I 14 82.4 

(I positive, 2 negative) 2 I 5.9 

120 total 15 88.2 

VES 008058 
T11e overall impact . on the park of the change in park · management, the 

implemen!lltion of the USEPA-assisted Clean Lakes Program, and the lake restoration 

work done to mitigate routing ofl-255 tb.rougb the park has been very significant. Gone 

are the criminals and the landsc.ape strewn wilb garbage and urb.ao trash and choked with 

uncut grass. Gone also are the weed·lilled, shallow lakes overrun by r~ugh fish (Roberts 

et al., 1988). 

Frank Holten State Park is now safe to visit and displays a landscape and lakes that 

are aesthetically attractive. This ·setting regularly attracts large numbers of picnickers. 

The expanse of open water is extensive enough to invite the use of small recreational 

boats. Day visits to the park b.ave increased significantly. For example, on Memorial Day 

1979, approximately 1000 people visited the park; on Memorial Day 1991, that number 

increased to nearly 17,000. Use of the golf course has increased as well; women now use 

the course, and tournaments are regularly held there. Park officials have observed many 

more families visiting in recent years than during the late I9?0s. Family reunions and 

church picnics occur regularly at the park, and groups now need to reserve park space one 

year in advance. 

Tlte early morning hours find walkers and joggers at FHSP, including groups of 

women who would not have driven, let alone walked, through the park in the late 1970s 

and early 1980s. Boy Scout troops use FHSP fucilities each year to enhance their slcills 

during organized scouting events. Area junior high schools also reserve the park each 

year for special events, and high schools hold cross-country meets there each fall (ibid.). 

Fishing bas also increased noticeably after !DOC completed dredging the FHSP 

Lakes. Anglers are numerous enough to support a bait shop, which opened in 1988. A 

boat rental concession also opened that same year. The extent of these positive changes at 

FHSP considerably exceeded the expectations of most of the professionals involved with 

the park and lake restoration projec~ when project planning began in the mid-1970s 

(ibid.). 

Currently, the area near the inlet of the stoun drain at Lake I is blighted with urban 

debris such as tires, cans, and shopping carts. It also reeks of a fuul stench even during 

winter months. This storm drain serves a very low-density, light nonresidential land use 

121 

VES 008059 
for the Bistate Development Agency Station Garage and a school with a large paved 

playground. A stom1water detention basin serves the station ga:rage before rainwater 

flows into tlle w·ainage sy-stem. Figure 5 sOO\VS viem of the detention basin, the inlet to 

the undergroutld stmm drain for crossing the Lake Drive enst of the lake, and the outlet of 

the drain discharging into the lake. These three pipe drains always have standing, stagnant 

water, which is invariably septic atd emits a foul odor. The bay area into wbidl the stonu 

drain discharges has soft, black, septic bottom sediments resembling sewage sludge. 

Aesthetic conditions in and around the storm drain and bay area could be and should be 

improved by increasing the water circulalionfmovement pattems, and by eliminating 

anoxic conditions of the lake bottom sediments in and around this bay area Park visitors 

use this area e.xtensively for bank fishing. 

Figure 20 shows '<iews of Harding Ditch and the dredged spoil disposal site. As 

indicated earlier, Harding Ditcl! was relocated along the western edge of Lake 3. 

However, the hydraulic oonditions of llie drainage sys1em are such that heavy rainfall 

events, and fiows from the Ditdl back up into the Jake through the outlet in the lake. This 

problem is further oompotmded by logjams in the Ditcl! botb upstream and downstream of 

the lake's outlet. These logjams also cause uncontrollable backup of water into Lake 3, 

resulting in the inundation of timberland between Lake 3 and Lake 2 Since the 

completion of dredging operations in 1984, the disposal sites have been overgrown with 

volunteer native timber and vegetation. 

122 

VES 008060 
Harding Dit'Ch laden with 

Figure 20. Harding Ditch and dredged spoil deposal site 

123 

VES 008061 
- i"iigh w ater !evels in Lake 3 

inundating timber 

Dredged spoil disposal site 

wilh native bushes and trees 

Figure 20. Concluded 

124 

VES 008062 
CONCLUSIONS AND RECOMlliiENDATIONS 

Conclusions 

The overall impact on U1e parl<. of the· cbange m park management, tbe 

implCllltntation oftl1e USEI'A-assisted CLean lakes Program, and the completed 

lake restoration work bas been very significant Frank Holten State Park is now safe 

to visit and displays a landscape and lal<.es that are aesthetically attractive. 

A geoernl user smvey carried out clwing the summer of 1991 reveakxl thai the park 

fucllities are ronsidered safe mel higbly 1'll1ed as a recreational resource. Gone are the 

vandals and criminal elements ltld the lllldscape SlreWll with grubage and urban trash 

and choked wiib uncut grass - and this OCQIJTed soon after the implementation of the 

restoration of d1e lakes and 1nanagemcrt of the parkgrounds in lhe late 1970s. Ail;o 

gone are the weed-filled, shallow lakes ovemm by roUgh fish. 

A creel survey conducted in the laJres from March 15 to November 15, 1991, reveals 

lhat the fisb and fishing opportunities are of very poor quality. TI1e respondents, 

specifically anglers, indicaled lhat they rate the fishing opportunity at 2.7 on a scale 

of 1-10. The poor quality of fisheries in the lakes can partly be attributed to the total 

absence of my aquatic maaopbyte beds in the lakes. Even the undred&OO areas of 

Lakes I and 2 are delloid of rooted vegetation. The lakebeds are devoid of sny 

aquatic habitat stroc1ures md resemble an aquatic desert. Additionally, these lakes 

have not hem restocked with game fish periodically. in recent years. 

• The oxygen cooditioos in the lal..-e are very similar to conditions at Jakes in other parts 

of the state. The surface DO conoentratioos in these Jakes were not statistically 

different between the poSt-restoration and restoration periods. Lake 2, the deepest of 

tlle three lakes, exhibits typical summer b1rutification, and the two shallow lakes 

exhibit temperature gradients during summer months. The oxygen conditions at 

depths below 8 to 10 feet from the suffilre are also below SUmdard during S\lltlll1(2' 

months. 

• AD the Jakes continue 10 be hi~ eulropltic, exhibiting high nutrient concentrations, 

low Sea:bi disc visibility, higb ClX)'I!I:D deplEtion during SUII1ll1tY, high chlorophyU a 

VES 008063 
concentrations, etc. Dredging did not significantly euhance the physical, chemical, 

and biological water quality characteristics in tbe lakes, bul the Jake volume in eaeh 

lake has increased and excessive weed growtb has been brought under control. 

• There was no statistical difference between the data observed during the restoration 

and post-restoration periods for the fullowiug parameters: surfuce dissolved oxygen, 

total and disoolved phosphat.e-P, total suspended solids, and chlorophyll a. 

Significantly high levels of nitrate were measured in Lake 3 compared to the other 

two lakes dming the post-restoration and restoration periods. 

Bathymetric conditions in the lakes have been very stable since the completion of the 

dredging projects. Sedimen~n bas been very light, ranging f:ium 0.5 to I foot. 

Some of this may have resuhed trom sloughing of bed material during the dredging 

period. The limited sediment inputs to the lakes further support the effectiveness of 

rerouting Hal'ding Diteh in reducing sediment inputs to the lakes. 

• Sediment inputs trom the storm drains into Lakes 1 and 2 were miDimal for the two 

full years of study (less than 50 tons eaeh year). Based on the average to above 

average precipilatioo fur the period, these !lUlnbers can be considered representative 

of "nonnal" couditions. 

• The Harding Ditch sedimeot inputs of 1279 tons fur Water ~ear 1991 and 823 tons 

for Water Year 1992 indicate that sediment input to Lake 3 is likely to be more 

variable. These sedimeol inputs represent in-lake sediment accumulation of 0.015 

feet and 0.01 feet, respectively. Anticipating an annual loss near the bigha- of these 

values, sediment accumulation rates will be 0.015 feet pcr year or I foot every 67 

years.. 

• Because of the concentration of sediment input from: Harding Ditch, this . 

aocumulation sbc>uld not be expected to be eveoly distn'buted. Instead, it should be 

expected to· concentrate near the Ditch connection. Thi<> process may already be 

indicated in the lake by a slight distortion oflake depth distribution as shown in figure 

12. 

• Hydrologic conditions fur tbe two-year evaluation period iOOicate that in general, an 

inflow rurplus exists fur all of the lakes during the winter and spring. For these 

126 

VES 008064 
seasons, evaporation rates ore low and the ground-water table is higll, resulting in 

stable and generally high lalre levels. 

In the summer and faU, evaporation and ground-water infiltration rates are higher, 

and lake levels for Lakes J and 2 "decline steadily except following heavy rainfall 

periods. Levels in Lake 3 appear tO be maintained by the makeup flow provided by 

Harding Ditch. Clearing of Harding Ditch tO maximize flow capacity would catainly 

lower Lake 3 water levels by I 5 tO 2 feet. 

Overall, the restOration program had a vt'1)' positive, aesthetically pleasing. and 

beneficial impact on the SUllOUilding urbm area The lakes and park system draw 

significantly more visitors tO this recreatiooaJ area compared to the pro-restoration 

ptriod. 

Recommendations 

• Alleviate anoxic conditions in tl1e da.-per waters of the lakes. The dissolved oxygen 

oonditioos in the lake deteriorate during the summer months, thus limiting the extent 

of fish babitaL 

• Carty out a detailed investigation to idemi1Y and alleviate the causes of a tOtal lack of 

submugtrl vegeuttion in the lalres, \\bicb severely restricts the habitai fur 6sb and 

fish 8xxl organisms. This may also be the ¢marY reason for the poor quality of 

fisheries in the lakes as revealed by aeel census. 

IMal1 artificial fish cribs, brush, md other 6sb habitat struciUres at str.Uegic locations 

tO improve fisheries. f\wly techniques fer restoring aquatic vegetation fourd 

sucocssful by Roseboom el al. (1989) in Pooria Lake. 

Remove bottom sedimcniS in and around the stomJ drain bay area of Lake I tO 

alleviate anoxic conditions. As an alternative, this area being shallower th,'\n 4 feet, a 

horizontal flow mechanical mixing and aeration device sboold be considered. This 

would alhance the oxic conditions ill the water and the sediments, and thus mitigate 

the pe.-vasive fOul smell. 

127 

VES 008065 
Control stagnant conditions in the storm drainpipe culverts in Lake I by unproving 

the hydraulic circulation patterns in the culverts using a strategically placed 

circulating pump. 

Remove tl1e logjam in Harding Ditch, which causes flow to back up into Lake 3, 

causing inundation problems. Maintain the Ditch for maximum hydraulic flow. 

Complete construction of the Harding Ditch levee across outlet from Lake 3 to 

provide protection of lake >)'Stan from pollution by stonnwate.-. Omside.-

construcrion of new outlet works 10.. tile lake system to limit bacldlow of water fit>m 

tbe Ditch and at the sainc time aflow Ol&flows from Lake 3. Stoun event impoct of 

the ditch on the lakes would be reduced, but makeup water to maintain summer lake 

levels shwld still be able to enter the lake. Omtrol water level in Harding Ditch to 

back up water through Lake 3 to Lakes l and 2 to maintain all three lnkes at a 

common level. This may necessitate ci£ocing of the "siphon" and lowering the bEd of 

the interconnecting channel between Lakes 2 and 3. 

128 

VES 008066 
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VES 008067 
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URS Co. 1985. Lake Fenwick restoration project. URS Co., Seattle, WA. 

Varis, 0 . 1990. "Development of phytoplankton community in restored eutrophic lake · 

A multivariale analysis." lntemationale Vereinigung ji1er Theoretische und 

Angewandte Limnologle 24(1}: 693-697. 

Vollenweider, R.A. 1968. Scient!fic fundamentals of lakes flowing waters, with 

particular reference to nitrogen. and phosphorus as factors in eutrophication. 

DASJCSl/68.27, Organization tor Economic Cooperation and Development, Paris, 

France. 

Walpole, llE., and R.H. Myers. 1985. Probability and statistics for engineers and 

scientists. Third edition, Macmillan Publishing Company, New York, NY. 

Wang, W.C., W.T. Sullivan, and R.L. Evans. 1973. A teclmiquejor evaluating algal 

growth potential in Illinois swface waters. ISWS Report of Investigation 72, 

Champa.igl), IL. 

Wedepohl, R.E., D.R. Knauer, G.B. Wolbert, H. Olem, P.J. Garrison, and K. Kepford. 

1990. Monitoring lake a11d reservoir restoration. EPA 440/4-90-007, USEPA, 

Washington, DC. 

Welch, E. B. 1981. The dilution/flushing teclulique in lake restoration EPA-{)00/3-81· 

016, USEPA, Con>allis, OR. 

Welch, E.B., and C.R. Patrnont 1980. "Lake restoration by dilution: Moses Lake, 

Washington." Water Research (G.B.) 14(9): 1317-1325. 

Welch, E.B., C.A. Rock, R.C. Howe, and M.A. Peddns. 1980. "Lake Salllllllllllish 

response to wastewater diversion and increasing mbao runoff" Water Research 

(G.B.) 14(7): 821-828. 

134 

VES 008072 
Welch, E.B., D.E. Spyridakis. J.l. Sinister, 8nd RR Homer. 1986. "Declining lake 

sediment phosphorus release end OJC)Igel deficit foJJoY.ing wastewater diversioo." 

Journal ofWmer Pollution Comrol Federation 58(!): 92-96. 

135 

VES 008073 
APPENDIX 

)36 

VES 008074 
Table AI. Fish Caught by A.ngJers at Frank Holten State Park Lakes from 

.March 15 to November 15, 1992 

Ntmt.be•· 

Species Number/hour caught Number/acre 

Black crappie .036 2391 15.14 

Bluegill .328 23568 149.17 

Olannel catfish .064 . 2846 24.34 

Drum .001 102 .65 

Largemouth bass .032 1520 9.62 

Rainbow trout .013 1144 7.24 

Redear sunfish .004 194 1.23 

White crappie .151 6069 38.41 

Yellow bass .061 · 3683 23.31 

Miscellaneous .029 1642 10.39 

Total .719 44159 279.49 

Pounds Average 

weight 

Species Pounds/hour caught Pounds/acre (pounds) 

Black crappie .005 348 2.202 .1455 

Bluegill .036 2476 15.668 .1050 

Channel catfish .043 1966 12.446 .5113 

Dnnn .001 99 .630 .9789 

Largemouth bass .014 764 4.832 .5022 

Rainbow trout .009 769 4.868 .6752 

Redear sunfish .001 39 .245 .1992 

White crappie .029 999 6:321 .1646 

Yellow Bass .002 146 .927 .0398 

Miscellaneous .025 1607 10.!70 9766 

Total .165 9213 58.309 .2086 

Notes: Information provided above pertains to the total num.ber am weight of fish 

caught. 

.Miscellaneous category: FL<;b caught in too low a quantity to be included in the 

summaty - yellow and black bullhead, carp, giz;z.ard, shad, etc. · 

137 

VES 008075 
Tablt A2. Flsh Harvested at Frank Holten State Park Lakes 

from March 15 to November 15, 1992 

Numbec 

Species Number/hour harvested Number/acre 

Black crappie .009 828 5.24 

Bluegill .214 14706 93.08 

Cbarutel catli~ .047 2738 17.33 

Drum .000 86 .55 

Largemouth bass .003 2?-4 ' 1.41 

Rainbow trout .012 1041 6.59 

Redeared sunfish .004 133 . . 84 

White crappie .076 2663 . 16.86 

Yellow bass .011 619 3.92 

Miscellaneous .021 1269 8.04 

Total · .397 24305 153.84 

Pmmds Average 

weight 

Species Pmotdslhour harvested Pounds/acre {pounds} 

Black crappie .002 215 1359 .2594 

Bluegill .032 2205 13.957 .1499 

Channel catfish .041 1856 )1.749 .6779 

Drum .001 99 .628 1.1527 

Largemouth bass .005 322 2.039 \.4504 

Rainbow trout .009 720 4.556 .6912 

Redeared sunfish .000 36 .226 .2691 

White crappie .023 731 4.629 .2747 

Yellow bass .000 42 .263 .0670 

Miscellaneous .023 1507 9.538 1.1872 

Total .136 7733 48.944 .3182 

Notes: Fish harvested represent the tOOll ownber and weight of fish kept (total fish 

caught minus the fish released back). 

Miscellaneous categocy: Fish caugbt in too low a quantity to be included in the 

swmnary - yellow and black bullhead, carp, gizwd, shad, etc. 

138 

VES 008076 
' 

A TI ACHMENT 7 

Exterual Email correspondence from Dan Stephenson 

VES 008077 
Message-----

From: Stephenson, D•n (mailto:Oan.Stephenson@Illinois.gov] 

Sent: Tuesday, October 04, 2011 8:05 ~l 

To : NcBride, Jane e. 

Cc: Knuppel, Shelly l.; Cohen, Mi tchell; Cronin, Fred; Bruce, Debbi e 

Subject: Re: Fish stocked i n Frank Holton St at e Park l akes 

The info you ment i oned be ., and a much ntOre has been sent to t he attorneys 

handling t he case against t he i nci nerator nearl y annuall y for years t hrough si~ply contacting t he district biologist and occasiona l ly through t he FOIA. They 

have copi es of absolutel y everything i n our fil es (whi ch is considerable) and 

have discussed wi th t he biologist on numerous occasions . This has t aken up a 

great deal of t~e . That being said, does t he biologist reall y need to go through 

al l t his again? If so, Fr ed Cronin i s in the Horseshoe Lake State Park offi ce. 

I am at home now and don't have a nu~ber . He is schedul ed i n the fiel d, as are 

nearly all the bi ol ogists; every day i n Oct. That creates a prob e~ as does the 

f act t hat he has been invol ved wi t h this from t he get-go and has already put a 

lot of time and effort in. He wi l l no doubt be hesit ant to go thr ough it again. There really is a lot of info. How far back do you want it? we have fil es on 

Frank Holton dating back into t he 60's probably. 

p.s. Your question was regarding stocking . Most species are native and 

reproduce naturally, t hey don' t need to be stocked. As a matter of f act I 

believe only the channel catfi sh have been routinely stocked. Jn addition, and I 

don't know if this is· pert inent, but t he lakes at Frank Holton are connected via 

ditches to the Mississi ppi River all~• ng a constant exchange of multi ple species 

between l ake and river. Thi s is not a static syst em. There coul d be a claim 

that the fish tested originally came from the river and pi ck up the methyl 

mercury elsewhere. Just a thought. Anyway, I have copi ed Fred and you may get 

in touch with him f or further info. I just di dn ' t want this to De a grea ter 

burden than i t al ready has been. Thanks. 

Fr001: ~lcBride, Jane e. [JMcBri de@atg.state. il.us] 

Sent: Tuesday, Oct ober 04, 2011 3:09 PM 

To: Stephenson, Oan 

Cc: Knuppel, Shelly L.; Cohen, Mitchel l 

Subject: FW: Fish stocked in Frank Holton State Park l akes 

Dan 

How a re you. I trust you are aware, but maybe not, veolia (Haz Wast e Incinerator 

near above ment ioned state park), has been granted a DHR permit t o conduct a fish 

study 'relevant t o their RCRA perntit . Issue i s 11ethyl mercury i n the water and 

mercury bioacc ... ulat ion i n the fish . Risk assessments ·ar e dri ving permit limits 

on mercury feed rate and emissions . 

\~e met ><ith Veoli a to discuss t he first draft of t heir proposed methodology 

today. veolia is hopi ng to get the field work done asap. The original effort 

wa s to get i t done by Oct. 1. Obviously, t hat is not happening. 

VES 008078 
It would be helpfu l to have t he information equested bel ow, but also any and all 

fish dat a avai lable for t he state park l akes - creel cen$us, all stocki ng info 

(what species are stocked when ) as •rell as f ish biol ogist/llanager ~<i om on t he 

l akes. It would be very helpfu l f o r" the consultants t:o hear f rom someone ";ho 

knows where t he best oca o~s might be to get t he species they are after - white 

crappie , l argemouth bass, channel cat, carp. 

The consultants indicat e t hey will try to get the revised work pl an back to I EPA 

and USEPA i n two weeks. It wou ld be very helpful for us and the11 to have any 

and all avail able fish i nfo as t hey put this next it eration of t he work plan 

toget her. 

Could you call me. 217 782 9633 

Jane McB 

CONFIDENTIALITY NOTE: Th is message and any attach~ents are f rom a law fir~ . They 

are sole l y for the use of t he i ntended r eci pi ent and may contai n privileged, 

confidential or other legally protected nfor~a ion. If you are not t he i ntended 

recipient , pl eas e destroy al l copies without reading or disclosing their contents 

and notify t he sender of t he error by reply e-mai l 

TAX DISCLOSURE: The IRS requires t hat we i nf orm you t hat any u.s. federal t ax 

advice in this message (including any attachments) is not i ntended or writt en t o 

be used, and cannot be used, to (i ) avoid any penal ti es unde~ the Inter nal 

Revenue Code or (11) pr01110te, 11arket or recOfllllend to another party any 

t ransaction, _ arrangement or other matter. 

VES 008079 
ATTACHMENTS 

Management Status Report: l<rank.Holten State Park Main Lnl<e 

VES 008080 
Lka e .M anaj?emen t St a t us e R ort ~ 

Date of Report: 04/03/03 Fisheries District: 16 

Manager: 

Fred A. Cronin 

Lake Name: Frank Holten Main County: St. Water II: 198 

Lake Clair 

Ow11ersbip (STATE, PUBC, Acreage: 97.0 

PUBO): STATE 

LM STATUS REPOnTS WILL INCLUDE THE FOLLOWING 

SECTIONS: 

I. Listing of the Sport Fish Regulations in Effect 

2. Listing of Fisheries Management Activities Completed 

with Evaluation of Success · 

3. Lake Management Plan Progress Table 

4. Recommendations for Observed Problem Trends 

I. Listing of the Snort Fish Regulations in Effect 

A. All Fish . Two Pole and Line Fishing Daily. 

B. Channel Catfish • 6 Fish Daily Creel. 

c. Large or Sroalhnouth Bass· 14-inch Minimum 

Length Limit. 

D. Large or Smallmouth Bass • 6 Fish Daily 

Creel. 

E. TroU£ • Fall Season Closed. 

F. Trout · Spring Season Closed. 

2. Listing of the Fisheries Management Activities 

Complete<! with Evaluation of Success 

A. 04/04/02 . Stocked 3,638 ten-inch rainbow 

trout. 

B. 06/26/02 Stocked 5,481 eight-inch CCF. 

c. 09/03/02 • Stocked 4,850 four-inch LMB. 

D. 10/17/02 · Population survey · 2 x 30-minute 

EF run • Successful. 

E. 10/ 17/02. Stocked 3,686 ten-inch rainbow 

trout 

3. L~ke Management Plan Prof!reS.< Table 

Largemouth Bass · 

t.MP Q!.!i!l~ J..2ll.Z 1m 

CPUE (#lhr). 60 68 

PSD 40:70 59 47 

VES 008081 
I 

RSD" 

Wr 

YAR 

20-30 

90-110 

1-5 

37 

105 

0.3 

32 

106 

0.1 

SIGNATURES: 

DRtrlc1 Fb.IH:ritll t\bua(r 

'Rtg'o•a.l fisllc:ries Admln.l"'rtlfOr Dlllt. 

FM 43.0 

( cootinued) Lake Manae;ement s tatus Report Page2 

13. Lake Manaaement Plan p 'Table (continued) 

I 

The largemouth bass population appears to have changed little ove>" the past three years. 

Numbers remain low with a CPUE (#/hf) of 29 in 2002. Size distribution appears somewhat 

improved with PSD and RSD14 both increasing in the 2002 survey. Average relative weight 

(Wr) of the bass collected in the 2002 survey was 103. 

Bluel!ill 

lr .MP l1MI< 1997 1998 1999 2000 2001 2002 

CPUE(#Ihr) 120-240 218 880 648 56 166 113 

PSD 20-40 0 1.6 1.6 0 2.1 5 

RSD7 10-20 0 0 0 0 0 0 

Wr 90- 110 92 95 100 95 102 98 

The bluegill da!a presented in this Lake Management Plan Progress Table speaks for itself. 

The CPUE has varied but quality is consistently poor. PSD is very low and we have yet to 

collect a single bluegill over 7 inches in length. The poor bluegill quality is the result of 

several factors. Poor water quality, low numbers of predator species, and high numbers of 

competing species (buffalo, carp, gizzard shad, yellow bass, and bullheads) are likely the 

predominant negative impacts .. 

I Channel Catfish 

ILMP Goals 1997 1998 1999 2000 2001 2002 

CPUE (#lhr) 4.5-7.5 6 4 6 0 5 3 

PSD 40-70 50 100 50 - 50 0 

Wr 90-110 89 101 90 - 97 85 

Ouly three channel catfish were collected in 2002. They were between 12.5 and 15.5 inches 

in length. 

IWbite Crappie 

I LMPGoals 1221. !..29~ 1999 2000 2001 2002 

VES 008082 
CPUE(#Ihr) None 86 140 86 10 95 106 

PSD 98 70 33 44 19 15 

RSD9 2 1 57 30 44 2 12 

RSD10 7 46 26 11 I 8 

Wr 100 92 98 96 93 

99 

· ·-continuedFM 43.0 

Lake Status 

The crappie populations have not changed dramatically-over the past three years. White 

crappie is the dominant species. Numbers remain about the same and size strucrure appears 

improved wiUt an increase in RSD9 and RSD1o.lt is encouraging to see some of these fish 

reaching quality siu. 

3 

Maintaining a decent sport fishery in this lake is challenging. Tho physical habitat of the 

lake is quite poor. The lake is sbaUow and tutbid with no aquatic plants and little structure. 

The lake also floods through ditches connected to the Mississippi River. This cormection intrOduces 

undesirable species including common carp, buffalo, grass carp, bighead carp, gizzard shad, yellow 

and buUheads. These species compete directly and indirectly for the available space and 

lresom-ces of !he lake. Tbe water quatity of the lake is also impacted by urban and golf course run-off. 

IHe:avy fishing and harvest pressure is also present. All of !hese factors combine to make 

e~::~~:::~=t~ofbalanced and sustainable sport fishing populations unlikely. However the 

lc stoelcing of rainbow trout, channel catfish, and largemouth bass can provide some quality 

an ~lin~opportunities at this lake. A Christmas tree habitat improvement project will be completed in 

of this year (2003) and should benefit the fishery and increase angling success. 

VES 008083 
I 

FM 43.0 

VES 008084 
ATIACHMENT9 

Curriculum Vitae for DgJgna Owen, Franklin Engineering Group. Inc. 

VES 008085 
EDUCATION 

M.S. Envlronmenlal MCJ W?Aer Resources Engineering· 

VM<Jertll Univor91y. 1994 

BA!liOOgy 

Bndgewater Colege, 1987 

EXPERIENCE 

f!ESUME 

Ms. Owen has m~ proja<i a:ti'lilies, sche<llles, and budgels lor regulaiOry driven projeds sucll as MACT corrPance 

evallations. RCRA !ria bums alld cofll>liance ~. ell dispersion modelilg, ci'ea i¥ld mJii.palhway human he<lllh and ~ 

risk aasessml!flts for hazardous was1e combUstion faciiies, alld RCRA Pa:l A and 8 p.rmit ~ens. She has managed the 

development of HWC C~relle slve Petlofmance Tests and Reports, as II as the modilicalion ol taciiiy Tille V permls to 

incapotale llle results ol si/Cb lesli>g. She serves as lhe primary reg<bory CO!lSlotant on a variety of penrating i¥ld engineenng 

projects under different slate and US EPA region aut!IO!Ity. 

Ms. CH.ml has ex1efiSI'Ie expenence In Human Hea&h ood EcoiogO:al Risk Assessment for 1\aurdous msle coot<Js!lon ·facfiies. 

She managed the ~ of J\.house risk assessment me<k>ls 1W:h provide more llexilily than COfmleoi:Eiy-avalable 

packages. She alld her team per1ormed tile Hum<11 Heallh and Ecdogical Risl< Assessments lor the waste propellanllndneralors 

a11he Radford Amr( Ammuniion Plant using in-house models basad on the mosl current guidance avalable allhe line i¥ld v.llich 

were subject to intense rego..Oatory agency sau1iny. The "'"'*' of the rislt assessmems mel all 8IJillicallle elCj)OSI.fe goidelines, 

resulting in no ad<ilional risk-based perm~ lmils under RCRA. MOre recen\!y. Ms. <Moo prep;!fed the Screening-Level Humoo 

Heallll i¥ld Ecologic31 RiSll Assessments for the BGAO iSCWO project. That project was COO'(IIetad on M aggressive adhed.-

using prolocols negoliaed IWil llle regula!ory agency. She and her leBn1 have prepared rislt assessment protocols and Wltk p!a1s 

and executed rislt assessments for complex. conwnercial waS(e incinerai'oo facil~ies w.th oru~ combustlcn ooils, as well as fO< 

capli'l8 combustors llU'ni1g a vaO&ty of cherrd was1es. AI of these projects in\OO!ved nt of assessment protoco4s, 

sele<ii:ln i¥ld iJstilicalion o1 Chemicals o1 Potential Concern (COPes), meteorological dala processirlg, and estabishitg 1<11\d uee 

ctassif!Calbl Md reoepfo< grief maps. 

Ms. Owen served as the tasl<manager for the trial bum repOOilg tasks compleled a1 TOCOf lor the vx Agent canpaign. She was 

reSPOnsible fO< meeting ~ and budgets for developing the !ria bum repO<ts. This included de'181oping v.al< plans lor sialf eng ~ ass9lment of tast.s, quality review of the worl< product Md ullinale respoosibility for lhe mat deiverables. 

Ms. 01\en successfuiy ~M~oped Md negollaled CAA pennl applications Md amen<menls, including primary reporting and testing 

dorumentalion for t.llscellaneous Organic NESHAP (MON) MACT compliance. She has d8\l!!loped Md managed llle de.efopmenl 

of rusiO<n dalabaoo systems kl< management of raw ma1eflal usage MCJ hazardous missions~ necessary tor conlilllng 

MON MACT compliance and other repo!fng requremenls. She has overseen MON MACT prelminary Md perbmMce testing and 

rep011ing for~~ requireme~ She "'.ihO<ad Class 3·RCRA fadlty pennll modffications, Md !ria bum and rislt bum plans 

and reports with various state reg~Ao;~ory ~enoies Md US EPA regilnel personnel. She developed relaive aoo.~racy lest 

assessment (RATA) waver requests i¥ld diMIIoped"' le\ised all sections ol runerous RCRA Part 8 perm~ awlicalions. She has 

de..,loped SPCC plans, SWPPP plans, and t.OAR plans for lacililies 'Aih varying regula!ory issues Md chellenges 

Ms. Owen pariicipat.d in llle ~nl of 51<11\dard eperallng procedures lor sevenal RCRA facilies. She has dewloped 

COJl1lliance checkfisls lor in<iJSiria boiler and incinerliol facilities and pM'o:ipaled in on-site Internal regulatory aulits for SIF and 

incineralor facil~s. 1.15. Owen par1ki>afed in llle englneenng calcUalioos and aulhor&ip of several Tcle V air pemits Md permit 

arnerxkrents. She deYeloped IIUmeiOOS sampling and analysis plans, compliance testing pro1Dcols Md 0Jality Assurance f'nlject 

Plans and has suocessUy managed al necessary subcontractors to execute air tasting plans i¥ld demonstr.e ~. 

Previcusly, Ms. Owen served as all engineEfilg cons<toot respcoSi>le for fing SARA Tille Ill Form R and Tille V VOC and HAP 

reports to lhe US EPA Md stale agencies and dem>pmenl ol dala rna'dermce systems. She assisted in ~ing and ""'illlli19 

ol remediation Sites usllg biJreme<il!ion, "*Wing and other ecooo~minalion techniques. She pali~.in UST removal 

projects incb!lng prelmlnary co~ wllh slale Md local olli::ials, on-s~ supeMsion of conlracl persomel, feld analyll:al 

work, and trealmeol of excava1ad materials. Ms. Owen pnwided technical support i:Jr lnduslrial hygiene, salety, Md ergonomic 

VES 008086 
RESUME 

Delana W. Owen (CQ<lt) 

projects fa-a \lllriety of indUSIJies inclldlg printing, leaihef frlishing, and marufactumg. She parlicipated in ...,ry reliew of US 

EPA and OSHA de-"'lcj)ing issues. 

As a sroio<' researdl associate, Ms. Owen was responsille for the perlomnance of labOilltory resea!dl toward the removal of 

hazardous oontarnilaots in soil, gromdwater, and wastewa~er through biostirrulalioo arnd bioaugmentalioo procedures. She 

de~ speciai2ed baclerial cullures fa degro:Jation of specific O.gani:s and maintailed trea!allily records., aa:otllis, and 

datallase system. She pedormed analyll:altechniques sum as gas dvomatography, mass spearosoopy, resprometry, surtac!Mt 

testing, TOC and COO delermilations, lefl1lentalion. and microscopy. Ms. ()"""' desii"Gd and constructed bench-top arnd pllol 

scale t ea!ment un1is and deslgned, Implemented, and wtele final repor1S on tea~atclily studies for smnis.sion to customEKS. 

As a quality oontrol\'esearch associate, Ms. Owen was responsille lor I!OaOOiologlcal inoculum preparation for large-scale 

p<Odoction and qually assurance procedures iwolvi-q enzyme assa)'S, lola! and selective bacisrial enumera!ion. moisture testing, 

gam stain analyses, and salrnonela screerilg. She m~d en!le stocl< Cllture and labora!C<y lrwentory arnd illenaced Vlith 

production per:oonnel and management in deletminillg pcoduclion sclledule and g problem ....-as. 

CERTIACA TIONS AND TRAINING 

Hazardous Waste Sile Operalioos (OSHA 29 CFR 1910.120(e)2) 

Confined Spaoe Entry (OSHA 29 CFR 1910.146) 

EMPLOYMENT HISTORY 

1998 • Present ftriln ~ Gro141, Inc. 

1994-1998 

1994 · 1994 

1992-1993 

1989· 1992 

1988 · 1989 

ORE T edlnoiogies,lnc. 

Serlo< Engineer 

Mosely & Associates, Inc. 

Erwironmenlal EngileerirQ Consulant 

Vandelbllt University 

Rasearm Assistant 

Novozymes Billogicals,lnc. (formerly Sybron Chemicals, Inc.) 

Senio< Researdl Associare 

Novozymes Bi®gicals, Inc. (formerly Sybron Chemicas, Inc.) 

Quality Control/Research Assodate 

VES 008087 
VES 008088.pdf 
Notification of Compliance (NOC) Report 

Veolla ES Technical Solutions, L.LC. hereby submits the Notification of 

Compliance (NOC) Report in compDance with · 

40 CFR 63.1210(b) and 40 CFR 63.12070) 

AppliCable Rule: 40 CFR Part 63.1200, Subpart EEE - National Emission S!andards for 

Hazardous Air PoUutants for Hazardous Waste Combustor'3. This NOC 

is being made in accordance with §63.9(h). 

SECTION I 

GENERAL INFORMATION 

A.. If you have been issued a Title V penni!, do not complete this form. Submit your NOC In 

accordance with your Tide V pennft. [§63.9{h)(3)) · 

B. If you have not been issued a Title V permit, complete the remaining portions of this. section 

and also complete Sections 11-V<. [§63.9(h)(2)(i)] 

C. Print 01 type the following information for each facility for which you are making notification of 

compliance status: · 

She! Address I #7 Mobile Ave. 

l Sauget j iL 

ZIP Code 

162201-1069 

Veolia ES Technical Solutions, LL.C. 

Faci!y Street Addrass [!! different than Responsible Offic:iars Street Acl<lress) 

Phone OPTIONAl 

General Mana er 618-271-2804 

I Sauget I lL 162201"1069 

D. Indicate the relevant standard or other requirement that is the basis for this notification and 

the source's compliance date: (§63.9(b)(2)(lil)) ' 

. Basis for this noli!icalion relevant slandanl or other 

40 CFR 63.1200 

1 

' v 

. ~ I 

. .. -.. , 

. ·-. . .: 

VES 008088 
SECTlON II 

CERTIFICATION (Note: you may et1J the text In this $OCI/on a.s deemed approplfaltl) 

Based upon Information and belief formed after al'easonable inquiry, I, as a respoosible official of 

the above-mentioned facUlty, certify the Information contained in this report is accur.ite and true to 

the best of my knowledge. The above-mentioned facility has complied with the releVant Slandard 

or and other applicable requirements referenced in the relevant standard. [§63.9(h)(~)( )(G)) 

Trtle 

General Manager 

SECTION Ill 

Describe the methods you used to determine compliance. [§63.9(h)(2)(i)(A)) 

RCRA Trial Bum Data from EPA approved testing as required by the RCRA Part B Rermit and using ~II ··: 

approved EPA methods were used to demonstrate compliance with all applicable emission standanls : 

defined in 40 CFR 63.1219. In addition, Comprehensive Performance Testing apprOved by USEPA, Regloil 

5 on August 8, 2008 and conducted in August and September of 2008 and Comprel)ensive Performance 

Testing approved by USEPA, Region 5 on November 25, 2009 and conducted in Oepember, 2009. See tile 

attached Operating Plllll!lleters Tables and HWC MACT Emission Standards table for Units 213 and Uillt ; 

that define the operating parametars estabtished dUring testing that ensures cornpiance with the · · 

oelformance Slandanls. 

SECTION IV 

Describe the results of any performance tests, opacity or visible emiSsion obse~s. 

continuous monilqring system (CMS) performance evaluations, and/or other monitoring 

procedures or methods that were conducted. (§63.9(h)(2)(i)(B)] · 

See attached test results that were used to develop the limits defined in the Operating Parameter Tab~ . 

referenced in Section Ill of this report These results also include CMS Performance evaluations and · 

monitorina methods. · · • 

SECTlONV 

Descobe the methods you will use to detemnine continuous compfiance, Including a description of 

monitoring and reporting requirements and test methods. (§63.9(h)(2)(i){C)) 

Continuous compfoance is based on the opera1ing parameter limits estabUShed from connpfiance testing, ',. 

defined in the attached Operating Parametars Table referenced In Section Ill of this report. These 

incinerator operating parameters are monitored continuously to verify compliance by. a process . 

monitoring and control system. The details of these systems are defined in detail in SectiOn 2.0, 

Incinerator Process description refetenced in Sedlon VIII of 1his report and attached: 

2 

VES 008089 
Descrlbe the type and quantity of hazardous air poAulants (HAP) emitted by the source (or 

surrogate poftu1ants if specified in the relevant standard), reported in units and avet'l!Qing times 

and In accordance with the lest methods specified In the relevant standard. [§63.9(h}(2)(1)(0)) 

See attached test results from compliance testing that was conducted to demonstrate compliance with ·: •. 

the HAP's and other llutants defined in Sub art EEE. · 

SECTION VII 

If the relevant standard applies to both major and area sources, present an analysis 

demonstrating whether the a11'ected soutce Is a major source (using the eml$sions dllta 

generated for this notifiCation. [§63.9(h)(2)(Q(E)) 

This facility is a major source due to its applicabiBty to the NESHAP regulations, speclficaHy Subpart Ef;& 

and Subpart 00. Regardless of the lacility's emission concentrations, this facillty is a major source by definition. • 

SECTION VIII 

Oesaibe the air pollution control equipment (or method) for each emission poln~ incfuding each 

control device (or method) for eaCh hazardous air pollutant and the control efficienCy (percent) for 

each control device (or method). [§63.9(hX2)(i)(F)] · 

See attached Saction 2.0, Incinerator Process Description from 2009 Petfonnance Test Plans for 

Incinerators 2, 3 and 4 that describes the air pollution control equipment for each en:tission point. Also,. 

see attached the compliance testing data defined in Section IV of this report that details the control 

efficiency for each control device. · 

SECTION IX 

A Did you submit an application for construction or reconstruction under §63.5(d) that contained 

prefiminary or estimated data? [§63.9(h)(5)} · 

Yes 0 . .. No 0 ... Not appUcable o . (did not submhn appHcation for construction or 

reconstruction). 

B. If you answered yes, provide aclual emission data or other conected informatio~ below. 

END OF FORM. A Responsible Dmc/11/ mm alan rtJis fonn - See Section fl. 

3 

VES 008090 
Dioxin/Furan (D/F) 

Mercury (Hg) 

Semivolatile Metals (SVM) 

Cadmium, Lead 

Low Volatile Metals (L VM) 

Arsenic, Beryllium, Chromium 

Carbon Monoxide (CO) 

HWC MACT Emission Standards 

~ Standard (@o/o 02) 

ngldscm TEQ 0.20 (>400 deg F) 

0.40 (5400 deg F) 

ugldscm 130 

ug/dsem 230 

ugldsem 92 

ppmv 100 

ppmv 32 

gr/dscf 0.013 

M.!!thod Qf Comnljm~ . ' 

Qperating P~e~r 

L~ " 

Opcrating Param~ Limits •.. , . 

Qperating p~ 

Limits . .. 

Qperating P~r 

Limits 

Oontinuous ~~P.IlS 

Monitor 

Operating P~~f~!M~ter 

' Limits -

Operating p~~ Limits' .. 

VES 008091 
UNII~ 213 OPERA TIN~ rARAMETER LIMITS 1 

I'·, <.:,i 

Ooc:JatiQa fmmeter Units Llmi.t1 Test Date 

Perfunnance 

Stapdl[ib 

·. 

Maximum Total Pumpablc Whr 3107 1m, 1993 ORE, (!IF 

Wutc (Hoarly Rollin& Total) 

Maximum Total Hazardous Lbibr 

Waste (Hourly Rollin& Toull) 

4017 Jan, 1993 OR.E,Il/1' 

Maximum Stack Gas Flow Aefm 15,147 Jan, 1993 DRE,QIF, 

R.ole {Hourly llolliAg AVOI'li&C) Port.,SYM, 

LVM 

Minimum Primary Combustion DegF 1686 Dee,2009 ORE, O(F 

Chamber Iaopenbl!e (Hourly 

llolllllg A v=ge) 

Minimum Secoodory Combustion De&F 1817 Dee..2009 ORE, O!f 

Chamber Tempe<a~me (Hourly 

Rolling AVC"'&C) 

Maximum Baghouse Inlet DegF 420 Dee,2009 DIP, SVM, 

Temperature (Hourly R.oOing L~ 

€a..A VC"'&•> 

~ Nlox.l'tunp. Low Volatile Metals Lbibr 46 Sq;,200t LVM 

Feedratc (12 HOlD' R.ollmg TotaQ 

Max. Total Low Volarile Metals Whr 

F~te (12 H<Mr Rollin& Total) 

47 Scp,2008 LVM 

Maximum Semi Volatile Metals lblhr 63 Sep, 2008 SvM 

Fcecntc (12 Hour R.olllns Total) 

Maximum Mercury Feedralc Lblhr 

(12 Hour Rolli~Jg TotaO 

0.0019 Aug,2008 Rg 

Maximum CbJorine Fcecnm Lblhr 218 Aug. 2008 SVM,LVM 

(12 Hour RolllDg Total) H~ 

Maximum Asb F«drate (12 617 Dec:, 2009 Plrt. 

Hour Rollin& Total) 

Mlnim.um SO<talt Foedlllle Lbllb a. 1.$7 Dee, 2009 HCVql2 

{Hourly Rolling Avenlge) 

M"lllilllum Carrier Fluid Flowratc Oalllb CI, 1.46 Dec,2009 HatCI2 

{Hourly RoOing Aven~ge) 

1 Opc:mill& panmeter limlt$111 table re6cet more cooservaiM value betwea~ Uni12 and Ullll3 test dlla. 

..... 

VES 008092 
UNIT 4 Q~ERATIN~ PARAMETER LIMITS 

•· :,. 

~?$;:" 

Perfonnaou 

Opcrarjng Panpns::tq .!.!11m ldmiJl Tcstf>Atc Standards 

Maximum Total Pumpablc LM!r PCC-3291 Dec, 2009 DRE,DIF 

Wute (Hourly Rolling Toul) SCC- 1176 

Maxlnwm Totall:lazardous LM!r PCC-12.897 Dec, 2009 DRE,DIF 

Wute (Hourly RoUin& TOilll) SCC- 1176 

Maximum Stack OU Plow Actin 37,432 Dcc,2009 DRE,DIF, 

Rate (Howty Rolliog Average) Part, SVM, 

LVM 

Minimum Primtry Combustion DegP 1499 Dec, 2009 DRE,D/P 

Chamber Tempera!Ure (Howty 

Rolling Avenge) 

Minimwn Sccoodll)' Combustion DegF 1886 Dec, 2009 ORE, DIP 

CbiUJibct Tempemute (Hourly 

Rollin& A v'era&e) 

MaxJmum Bag!louse lolet DegF 400 Dec, 2009 DIF,SVM, 

TemperaiW'o (Hourly Rolling LVM 

Avenge) 

Max. Pump. Low Vol>tile Metals Lblbr 47 Aug.,2008 LVM 

$~ll:ecdndo (12 Hour Rollin& Total) ~~® 

·~i.t.x. Total Low Volarile Metals Lblbr so Aug.,2008 LVM 

Fcedrate (12 Hour I!DIIing Total) 

Maxlnwm Semi VoWileM.W. Lblbr 

Feedrale (12 Hour RollingTo!al) 

64 ~.2008 SVM 

Maximum Mercwy Feed me Lblbr 

(12 Hour Rollin& Total) 

0.026 Aug.,2008 Hg 

MaxJmum Ollorine Feed rile Lblbr 229 Dcc,2009 SVM.LVM. 

(12 Hour Rolling Total) HCVCI2 

Maximum A.sb Feed Rale (12 LM!r 6444 Dec, 2009 Part 

Hour Rollin1 Total) 

Carboo lojccdon Fecdndo · 

(Howty Rolling Awn&e) 

Lblbr 6.2 Dcc,2009 DIF,Hs 

Minimum SorbentFecdndo LbllbCJ, 2.2S Dec, 2009 BCl/Cl2 

(Hourly Rollin& A"""'3c) 

Minimum Cerrier Fluid Flowr8le Galllb Cl, 3.10 Dec, 2009 HCIIC12 

(Hourly Rolling Awn&e) 

VES 008093 
·.· 

. ' ' . ... 

. • : 

.... ·. , . 

.· . : } . ' •, 

. , . ·· . . 

c· 

····· ... . " 

•, .. · · .. 

.• · .. ,: 

: .. 

' . 

·, 

· .... . " 

• ' 

. " 

··' ' 

'• 

. . 

... ···. · : · 

, •, 

UNIT2 

EMISSION RESUl-TS 

. . ' 

· .... 

.• 

,, •. : .. , .v· . .. .. : ···, 

•' 

.· ... ··. 

.· .. 

, .. 

.. ··. " . 

-. : 

• ' 

' ' 

' • 

. '· 

. : .... ~ .· . .. ·. ., . 

..... .. ~ ~-: 

_ ;' (, · . 

•, . . .. :. ·.: 

.. ., 

.' ., 

•"· 

., " 

" 

•' : ' 

·.' . .. : 

.. ·<·· ' •' 

. · . ,· 

" · " 

... .. ,. . 

'. ·: :· 

·, 

. ,. ,·' ' ·. ·:··· ..... 

.. · ·. I: ." • 

.· / ':.:· . ': . 

: . ~-

, 

·. 

. · ; 

,• 

VES 008094 
ENSR 

Table 3-3 RM 29 Sampling Parameters and Emission R<tsulls-w .. k of AugU$111, 2008 

~N<)+ -·---·-·+·· -1-·1..-., l..oa·-- -1 --'~ i~ ·- ~ o8" -·- ...... l>S~Iarr"=:Tin:-:- ~·--·-·· I.Hts =-1 1;.40 '11:05 i!i'j ···- -

ln. Hg 

·-

I o/SeC ., ... .., .... , . 5Va4 

!6:50 H:te 1:!;_4 AVG$ 

63.5 

58.0 

~ 

78.15 

SU18 

1.99 

1.38 

89A 

582 

75.66 

.4928_ 

2.06 

1.34 

87.9 87.0 

__§7 ~ 57.9 

lDl~·=-

13. 15 75.85 

47.76 50.57 

@[ 

l.86 f.97 . 

1.21 1.31 . 

llll 329.5 3692 

·Slaclt ,-~ :_No 0, lllllln> - 228.1 !~1.5 

f7JX1 

11.80 

11..6~ 

1?,;391 '-03 ~>04 . 

10.011. 

~ti: -1-+-':'0= -Hf--? 0. . 0.211 

~ 0.13 ~ Q.13 

I 1~ I· '.ffi ~ll&

--

VES 008095 
·. 

Tobie 3-4 SUmmaty of HWC MACT Mmls- August 11, 2008 

Low Vola!:lla Metals Emissions - ~o~glm> @ 7% 0 2 

Metals Run Ibm: Run3 

1e 

~. 

Total VM 58.1 

Semi-Volatile Meal Enmslons - pglm"@ 7% 0. 

llla1alo 

P! 

.· . 

.. ·· : 

.. 

... . . .. . . 

Run 1 

1.38 

:23) 

SVMn 

Run2 

240 

1.34 

2C2 

Runl 

241 

121 

242 

Standard = 240 pg(m" 

Memny Emissions iJg/m"@ 7% 0, 

·.· 

·' . .. . ·. 

. ·,. 

. . 

Zl8 

51.9 

· . 

ENSR 

"· .... . 

VES 008096 
ENSR 

Table 3-5 RM 29 Sampfing Paramat, rs and Emission Results - Week of September 8, 2008 

Run Nu. 1 2 3 

Dole 'oe Sep.OB as.s~B 't o~ 

Start Time Units '14:36 • 12:2l • !RM 

S!oo Time • 16 ~ • 1-4:31 • 11:S3 AIIGS 

Barometric Pressure in. Hg • 29.60 • 29.75 • 29.72 29.71 

Volume Met8fed dd , n:382 • 79.269 • 78.905 n .ll5!l 

Sample Volume dsef 75.296 78..407 78.654 n.4SJ. 

Moisturo %vh 41.4 41.2 41.6 . • 41.5 

0, at Stack %dry • 11.21 • 10.91 . , 11.35 11.16 

jA>og. Stack Temp. 'F , 385 • 381 , :Jl-4 •:m 

Stack Flowrata ds<Vn 4,600 s.ms 5.2-48 5,()15 

lsokinelies % 107 11l3 •100 104 

Tahll ·,,..., LVM 

Ouantily Colecttd 119 12.16 2.79 9.18 8.04 

• Slack Cone. @ 7% 0.. ~glm' 8.16 1.74 5.98 5.29 

.· Slack Emission Rate lblhr ~ 2..40E.Q5. B. 10E-05 6.85E.Q5 

Qlsee 1.266-ai 3.02E-06 1.02E-ai a63E-OS 

I (Cl\- SVM 

Qualltiiy Colleded V9 2.73 274 2.20 2.55 ... 

Stacl< Cone. @ 7% 0, pglm' 1.~ 1.71 .1.-43 1.66 

siack Em111oion Ra1e lblht 2.25E.Q5 2.J5E.Q5 1.94E.Q5 2.18E-05 

glsee 2.1J3E.C6 2.96E.(6 2.44E.Qi 2.7SE-ai 

- SVM 

0uaa1.ay ""locted V9 45.1! 13.9 39.0 32.84 

Stack Cone. @ 7% 0, ~giro' 31.6 8.7 25.4 21 .6 

Stack Emission Rata lblhr 3.76E-Q4 1.20E-04 3.45E-04 2.80E-04 

· Qlsec 4.74E..OS 1.51E.Q5 4.34E.{J5 3.53E-05 

A>seliit:(AI)-

· Quanlhy Collected 119 2.130 2.10 2..10 2.33 

Stack Cone. @ 7.% .0, 'IJ9frrt: l.BB 1.31 '1.37 1.52 

Sl1ick Er!Jlitbn 'Rate lhlhr . u1'e.f6 .1.81E-ai 1.BSEai 1.99&65 

olsee . . 2.9tf.m :z.2llE.(E 2.34E.Qi 2.51E-ai . 

·' 

. m....:,;, 

Cl'ualliy Coliictad 119 . 0.20 . 0.3l · .. 021 0.3) 

Stad 'Cone.·@ 7% 0, 119"m"' 0..1;i . 0.12 ·a. t3 0.13 

Stack.Eriliuibn Rita· b'hr ·1.65E.(6 1:72E-11l 1.ne.a; 1.7fE.(6 

•· 

. .Qisec 2.08e.o7 2.17E'{J7 2.22E:W 2.166-07 

LVIII. Total ~ ualm" 10.2 32 7.5 &.9 

SYUTotal • ualm" 32..4 . 10.4 26.9 23.2 

VES 008097 
Table 3-6 Summar.y of HWC MACT Metals-September 8, 2008 

l ow Volatile Metals Emissions -pglm•@ 7•.4 0 2 

Metals Run 1 · R11n 2 Run 3 Average 

As . 1.88 1.31 1.37 

Bo 0.13 0.12 0.13 

.cr 82 1.7 6.0 

Total LVM 10.2 3.2 7.5 6.! 

LVM Raaulatorv Standard= 92 pglln" 

Se.IIII-Vola!lle Metal Emissions -pgtm•@ 7% ~ 

Melli Is Run 1 Ran 2 Run3 Averaae 

P.b ::0.6 8.7 25...4 

Cd 1.83 1.71 U3 

Total SVlo1 32.4 10.4 26.9 23.2 

SVlo1 ReQulatory Standard= 23l ~ 

' . . . . 

. . . . . . .<.. ... .. ~ . . . •' . . . 

•. 

: . \ 

·. .. 

3-7 

ENSR 

. . ~ 

: : 

. ' 

.·. 

VES 008098 
Aa'COM !. '~ I Table3·2 RM 5/26A Sampling Patllmotera and Ernlsslon Results - TDtaJ ChlotldeiPM 

Run ld entificati~ Run1 Run 2 Run3 Average 

Roo Date 12.()8109 12109109 12110109 

Start Time ' 10:05 9:46 11:00 

StopTrne 11:11 10:49 12:03 

Elchau~ !.211~ r;go!lli!l!lli 

Temperatlse (deg. F} 378 383 380 374 

. Moisture (volume%) 44.4 42.9 43.2 43.5 

·Oxygen (dry vcilume %) 10.3 10.4 9.3 10.0 

Carbon Oioxi:le (dry volume%) 8.6 8.2 8.1 8.3 

Volume!r!c Aow Rate 

acrm 15,453 16,634 16,661 16,250 

dscfm 5,352 5,963 5,921 5,745 

Total Chlorine _, ppmv, dry @ 7% 0 2 13.4 16.0 23.5 17.7 / .. l I % of standard • 42.0% 50.2% 73.5% 55.2% t~ 

Imill Ell ttiruate Mat1er 

gr/dscf@ 7% 0 2 0.0013 0.0017 0.0008 0.0013 

% of Standard • 9.7% 13.2% 6.2% 9.7Y. 

' HC_q. Stanctord • 32 ~~~"""· cll)'0 '1% 0, 

• -· Mall« Emissi<>"l S.ndlrd. 0.013 gJidsd@ '1% 0, 

_ .... 

VES 008099