ORIGINAL

APPENDIX L through APPENDIX M

H30132

The pond itself supports very few animal species (turtles, surfaceTnsects, some tolerant fishes) though emergent vegetation is able toflourish tn the shallow reaches of the waterway. Many species notfound associated with Army Creek waters per se feed in or near severalof the gravel pit ponds since these nearby bodies of water are notpolluted and support a wide variety of clean-water forms.

The pond survey revealed: benthic invertebrates (none), water-borneinsects (4), reptiles (3), amphibians (l), rooted aquatic vegetation (6major types), birds (29), mammals (none in the pond); see Appendix fordetailed list and clarification.

The creek survey, from the outfljow of the pond to the t i d a l gateat the Delaware River, produced the following list: benthic inverte-brates (5), water-borne insects (5), reptiles (4), amphibians (4), rootedaquatic vegetation (6 major types), birds (32), mammals (l); see Appendixfor detailed list and clarification.

The biological data, correlated with field observations, stronglyindicate that Army pond is suffering under severe pollution/organic en-richment stresses. However, the waterway is able to recover moderatelywell by-the time the creek enters the marsh beyond point B (Map 1). Thespecies diversity is very low in the pond, with those organisms presentknown to be tolerant of eutrophic waters; the species diversity of thecreek and marsh fauna is much greater, including organisms more commonly

found in cleaner waters.

One apparent, obstacle to the continued improvement of downstream water* "

quality is the inflow of process water from the Amoco Chemical Corpora-tion's Polymer plant at point E (Map 2). The Amoco outfall area Is characterizedvast algal mats on the submerged vegetation and on the water surface andby a white precipitate covering much of the bottom of the creek. Benthicsampling near this seep showed no macroinvertebrates although turtlesand schools of minnows near the site seemed unaffected by the milky ef-fluent, especially near point D.

HB301322

APPENDIX L

R30

(Red)

Biological Baseline Survey of Army Creek,New Castle County,.Delaware

I Summary: Army Creek is a slowly flowing, fresh water stream prim-

a r i l y consisting of a large pond adjacent to the Llangollen l a n d f i l lI and a two-mile long creek flowing through an extensive reed marsh (Phragmi tes)

to the Delaware River.I A biological assessment of the creek and surrounding area was con-" ducted on September 12, 13 and 20, 21. Data was gathered via direct

observation, faerslhic sampling (two methods), fish seining and personal

I communication with local residents.

I ' Results of the survey indicate that the pond is highly eutroohic,the major discernable causes being: a) seepage of nutrient-rich leachate

• from the landfill, b) natural siltation and nutrient enrichment fromsurface-water runoff, c) accumulation of orqanic detritus due to very• .litt l e water movement through the pond, d) influx of above-normal

* levels of phosphates and total nitrogen via Army Creek,

The major source of pollution and enrichment seems to come from1 the leachate from the Llangollen l a n d f i l l , where the^ following water

chemistry values have been recorded (Delaware Water and Air ResourcesI * Commission, 5/5/72 and RFW, 9/73): chloride - 1300 mg/1, iron - 6k mg/1,

total kjeldahl nitrogen - 530 mg/1, organic nitrogen - 60 m§/l, ammoniaI nitrogen - 470 mg/1, total phosphate - 2.1 mg/I, BOD - 150 mg/1, and

1 COD - 1400 mg/1. Several seepage areas are devoid of plant life (Point| C, Map l)t the exact reason being as yet undetermined although the high

chloride i^vel is suspect.ar -

g • Some nutrient enrichment may be attributed to inflowing Army Creek

* waters, where phosphate and total nitrogen values of approximately 2.0_ rog/1 have been recorded. These values are 10X to 1OOX above those in

I a "clean" stream (Reid, 1961) and are most likely the cause for abundantalgal growths in the creek. Aquatic fauna in the incoming portion of

[ j^ Army Creek Is rather "normal", many benthic invertebrates, insfrogs, tadpoles and water-borne insects being recorded.

1AR30I32U

-3-

No species of economic importance are presently taken from the pondor the creek even though yellow perch and large-mouth bass were known

to exist there several years ago (DeIlAversano-persona1 communication).The carp and suckers presently reported in these waters are not sought

by fishermen; also, the Army Creek reach near Route 9 (Map 2) is postedwith No Fishing or Swimming signs. The marsh does, however, serve as

a resting/feeding area for ducks and these are reportedly taken in smallnumbers during the hunting season. The marsh most likely does not serveas a breeding area for estuarfne or marine organisms due to the tidalgate which l i m i t s or prevents entrance of such biota into Army Creekfrom the Delaware River.

Materials and Methods:

The survey of Army Creek was conducted by direct observation along

its entire length from the origin northwest of Delaware Route 13 to theconfluence with the Delaware River. Secondly, a benthic survey using arowboat and a 0.1 m^ Peterson dredge was conducted from the DelawareRiver to the power-1 ine (Map 2), comprising eight sampling stations.The pond was also sampled by the same method, being a total of twelvestations,. Thirdly, a walking benthic survey was conducted from point B(Map 1) to the power 1ine using a 6" by 6" brass Eckman grab, all inverte-brates collected being sieved through a #30 mesh sieve in the field andpreserved in a 10% formalin solution.

A fish survey was attempted in both the creek and the pond usinga one-man ^ine. Though some minnows were collected in the shallow reach-es of the marsh, this method was deemed inadequate, thus the relianceof fish data upon personal communications and direct observation. Futurestudies w i l l be conducted with a 35', 1A" mesh two-man seine to more

quantitatively describe the fish population.

3*1 IU I

/ -6-

REFERENCES

1. Abbe,-G.R. 1967. An Evaluation of the Distribution of FishPopulations of the Delaware River Estuary, M.S. thesis, U. ofDC Iawa re.

2. Amos, W.H. 1955. A Guide to the Aquatic Animals of Delaware andto the Waters in Which They Live. M.S. thesis, U, of Delaware.

1 3- A.P.H.A. 1965. Standard Methods for the Examination of Waterg and Wastev^aler (12th Ed.), Am. Public Health Assoc., N.Y.

if. Borror, D.J. and R.E. White. 1970. A Field Guide to the Insects,— Houghton Mifflin Co., Boston.

5. CaTrns, J. and K.L. Dlckson (Eds.). 1973. Biological Methods forthe Assessment of Water Quality. ASTM, • Phi ladel phi a, Pennsy Ivarvi a.

I-1 6. Chamberlain, E.B. 195L A Survey of the Marshes of Delaware,

Delaware Board of Game and Fish Commissioners.

I ^^ 7. Conant, R. 1958. A Field Guide to Reptiles and Amphibians,^^ Houghton M i f f l i n Co., Boston.

§ 8. Delmarva Ornithologist, 1972, 1973. Box 213, Unionvi?le, Pa.

9. Ingram, W.M., MacKenthun, K.M., and A.F. Bortsch. 1966. BiologicalI Field Investigative Data for Water Pollution Surveys, FWPCA,

Washington, D.C.

| 10. Odum, E.P. 1959. Fundamentals of Ecology, W.B. Saunders Co.,* Philadelph?a, Pa.

I II. Pennak, R.W, 1953. Freshwater Invertebrates of the United States,| Ronald Press Co., N.Y.

12. Petsrson, R.T. 19 7. A Field Guide to the Birds. Houghton Miff 1 inI , Co^, Boston.

13. Reld, "J6.-K. 1961. Ecology of Inland Waters and Estuaries. Rheinhold• Publishing Corp., N.Y.

14. Robblns, C.S., Bruun, 8. and H.S. Zim. 1966. Birds of North America,I , Golden Press, N.Y.

-7-

* Appendix i3 "List of Species Recorded at Army Creek

Symbols for relative abundance indicate: a ~- 'abundant, c - common,

u - uncommon, r - rare; sp. indicates identification to genus only;

? indicates identification not certain; o indicates not found.

Aquatic Forms - found in the creek or marsh.

I. ArthropodsA. Insects In Pond In Creek

1. Water strider Fam. Gerridae a a2. W h i r l i g i g beetle Fam. Gyrinidae a a3. Mosquito larvae Fam. Culicidae a c4. Midge larvae Fam. Chironomidae u c5- Water boatman Mesperocorixa sp. r c

6. Dragonfly larvae Fam. L i b e l l u l i d a e o c

7. Damsel fly larvae Fam. Coenagrionidae o uB. Crustaceans (crayfish, shrimp, amphipods, isopods, crabs)

None found; small planktonic forms may exist, such asDaphnia sp.

V

II. Molluscs (snails, clams)1. Pulmonate snai1

MI. Annelids (segmented worms)-- 1. Tubi fex worms o u

2. Aquatic oligochaete (sp?) o u^^««r -

IV. Vertebrates1. Snapping turtle Chelydra/serpentina c c2. E. Mud trutle Kinosternon subrubrum a c3. American toad Bufo americanus o u4. Bull frog Rana catesbeiana u u5- N. Leopard frog Rana -pipieus o

.8- $ ORIGINALH (Ked)

In Pond In Creek6. Green frog Rana clami tans o u

7. Water sn/ake (!£•?) u u8. Eastern garter snake Thamnophi s sirta1 is o u9- Fat head minnow ? o c

TO. Carp, Suckers- (reported) u r

V. Plant communities (emergent vegetation)1 . Common reed Phraqmi tes comrnunis c a2. -Cattail Typha sp. o c

3. Mallow Hibiscus sp. u u

J " **- Coontail Ceratophyllum sp. c c5. Arrowhead Sag!ttaria sp. c c

I 6. Willow tree SaHx sp. c u

7. Water l i l y Nvmphaea sp. c c

* V!. Mammals1. Muscrat o u

— Terrestrial Forms - those associated with the creek but not l i v i n g inI ™ the water. Most are common forms.

I. Birds- Near Pond Near Creek| • Wood duck AJx spousa x

Black duck Anas vubripes x xj Mallard duck Anas platyrhynches x" x

Snowy egret (?) Leucophoyx thula x x| Green heron Butor ides vi rescens x

Turkey vulture Cathartes aura x xI -- Duck hawk Falco peregrinus x x* • Osprey Pandion halJotus , x

FUng-necked pheasant Phasianus colchicus x xI ——————————————j Spotted sandpiper Actitis macularia . x

Herring gull Larus arqentutus x xRock dove Columba 1 i v i a x xMourning dove Zenaidura macroura x xNight hawk Chordeiles minor x

I* Chimney swi ft Chaetura pelaqlca m D O fl XOOC

(Red)Near Pond Near Creek

Belted kingfisher Megacoryle alcyon xI

Flicker ^ * Colaptes auratus x . xDowny woodpecker " Dendrocopos pubescens x xAcadian flycatcher (?) Empidonax virescens xCrested flycatcher Myiarchus crini tus . x xTree swallow Tridoprocne bicolor x . x

Bluejay Cyanocitta cristate x xCrow Corvus brachyrhynchos x xLong-billed Marsh wren Tel ma tody tes pa 1 ustri s x x

Mockt ngbi rd Mimus pol yq lot tus x x

Catbird Dumetel la carol Jnensi s x xBrown thrasher Toxostotna rufum x xRobin Turdus mi grator i us x xS tar 1 i ng . Sturmus vul gar i s x xHouse sparrow Passer domes ticus x x

Purple grackle Quiscalus quiscalus x xCa rd i na 1 R i chmoudena card J na 1 is x xCh-tpping sparrow Spizel la passerina xSong sparrow Melospiza melodia x

Red-winged blackbird Agelaius phoeniceus x xBrown-headed cowbird Molothrus ater x

Note: It is possible that the species lists may be lengthened if futurefield work warrants same. Bird species which may be expected to winterover may be determined by referring to one of the stated references.

I 1 . Maiwna 1 s* The only mammals living in the creek are muscrats, seen near point

D (Map 2) > -However, sightings, tracks and local reports comprise thefollowing list of mammals found in the vicinity: white-tailed deer,Norway rats, field mice, ground hogs, grey squirrels, cottontail rabbits,moles, foxes, striped skunks, oppossums and raccoons.

s; p.*'•'• — *'***«-

*•—""••*• "**- -*—

DATE: i£ October 1973

TO: Henry Haley

CC: Terry HetserWalt Nlessen

FROM: Dave Bruderly

SUBJECT: New Castle W.O. No. 1^_I2

GENERAL

The Delaware Estuary extends from the capes to Trenton, New Jersey,a total length of about 13^ miles. The width of the estuary variesfrom TOO ft. at Trenton, to 2200 ft, at Philadelphia, to 7 00 ft. atNew Castle, to 27 miles at'' the widest portion of Delaware Bay, at to12 miles at the capes. The estuary has a total drainage area of about13»5*J-0 square miles, of which about 6800 square miles lie above thehead of the tide at Trenton.

The mean fresh-water discharge Into the estuary Is about 11,650 cfsat Trenton, about 16,U75 cfs immediately below the mouth of theSchuykil1 River, and about 20,000 cfs at the capes. The tidal prism(exclusive of fresh water) at the capes is about 93 b i l l i o n cu. ft. •decreasing steadily to about 2.35 billion cu. ft. at Philadelphia.Mean maximum current velocities in the navigation channel betweenPhiladelphia and the sea are on the order of 5-0 to 5.0 ft. per sec-ond. The maximum velocities and durations of ebb currents are gen-erally greater than those of flood currents with the predominanceof ebb currents Increasing with distance upstream. The mean rangeof tide at the capes is about ^.3 ft. and the range increases grad-ually'through Delaware Bay to about 5.9 ft. at St. John Light, then

• gradualfy decreases to about 5-^ ft. at Reedy Point, then increasesstead? l *-to about 6.7 ft. at Trenton for conditions of mean freshwater discharge.

Salinity intrusion In the Delaware Estuary generally does not occuras a well-defined salt-water wedge. In most portions of the estuarywithin the limits of salinity intrusion, salinities from surface'tobottom are essentially the same and there is little difference inthe phasing of the current from surface to bottom. However, in thatreach of the estuary between St. John Light and Artificial Islandthere is a tendency toward formation of a weak salt-water wedgeduring the turn of the current from ebb to flood.' In this reach

7 0 - 7 B 7 ftRSO 1 332

'Memorandum to Henry Haley v._ j.i. 16 October 1973'; '.11 u vi i

the turn of the current at the bottom normally Teads the turn at the surfaceby about 1.0 hr and at such times bottom salinity may exceed, surface salinityby as much as 50 percent. The water in the" slower reaches of the Delaware Bayhas a saline content almost as great as that of the sea for normal conditionsof fresh water discharge. Salinities throughout the estuary decrease steadilywith distance upstream as shown in -Attachments 4, 5, and 6.

The Delaware Estuary is generally considered to be well-mixed since the tidalmovements are very large compared to incoming fresh water. The small differencein observed salinity between surface and bottom waters (Attachments 4, 5, and 6)lend support to this statement. It is also apparent that salinity at a givenstetion is a function of the stage and phase of-the tide. Salinity is highestduring neap tides at high water slack and lowest suring spring tides at lowwater slack. Flow volume data for the station at the Delaware Memorial Bridgeis given in.Attachment 1.

The temperature in the estuary will generally decrease slightly with increasingdepth. Solar heating during the summer is the primary cause of higher surfacewater temperatures. In the winter, however, solar insolation will be relativelylow and the estuary waters w i l l be essentially isothermal.

DIFFUSION AND MIXING PROCESSES

Water density is a direct function of both the temperature and salinity. Sincethis estuary is very nearly isothermal and 'isosaline for a given seasonal andtidal condition, there is very lit t l e vertical density stratification in thewater column. By Assuming a typical summer water temperature of 15° C. (59°F)and a typical winter water temperature of 4°C (3S°F) and converting chlorinityto salinity by the relationship

Salinity ppm = 1.805 (chlorinity ppm)Attachments ht 5, 6, and 7 can be used to compute approximate estuary waterdensity for neap, mean, and spring tidal slack waters, summer and winter.(Attachment 8) The computed density ranges from 0.999 to 1.0030.

The leachate wi l l be discharged at a temperature of 15° C (60° p) ancj shouldhave a density at that temperature of about 0.9990. Diffusion and mixing ofthe leachate will be caused by a cojnplex interaction between the buoyancyforces, the dispersion of the plume momentum, and the ticfal current forces.Lateral mixing due to currents w i l l dominate the mixing process at the pro-posed outfall sjte. Vertical mixing will also be_ prevalent due to the lackof vertical density stratification.

The dominance of lateral and vertical mixing due to tidal currents makes thequantitative detefnii nation of mixing and diffusion a very involved and com-plicated procedure that is-beyond the intended scope of this phase of the pro-ject. A hydraulic model of the estuary is located at the Vlcksburg District,US Army Corps of Engineers. Several attempts at mathematical modeling of out-fall and dispersion processes have been made and have utilized the capabilitiesof-the hydraulic model. DuPqnt - Deep Water Works and New Jersey Zinc Corp.have each studied dispersion processes by field dye studies and math models.INCODEL (ORSC) has also conducted studies on the estuary mixing presesses.Access to such work would be essential to modeling the leschate ciisp&rsjpru . oif this becomes necessary. A ft u U \ J J

-2-

Memorandum to Henry Haley Q ]£ October 1973(Red)

A qualitative analysis of the hydraulics in this reach indicated that theleachate w i l l be of slightly lower density than the receiving waters. Theplume w i l l rise to the surface and spread laterally at varying rates de-pending on the" tidal, seasonal, fresh water run-.off, and meteorologicalfactors. The plume w i l l be distributed upstream and downstream of the out-fall by tidal currents. It is possible that concentrations of leachate coulddevelop in eddys along the western shore. However, this <s highly unlikely.In any event, the leachate would most likely be highly diluted. The flowdiversion dike w i l l keep most of the leachate in the western channel and w i l lthus reduce the effective mixing volume available. Attachment 9 sketches thelimits and probable-pattern of horizontal plume dispersion over one tidalcycly of an ebb current, followed by a flood current.

OUTFALL SITE DESCRIPTION

The proposed location for the outfall is at the foot of Gr'antham Lane. ThisIs Channel Station No. 205 by the US Army, Corps of Engineers -survey systenuThis reach of the estuary is characterized by tidal flats on both the eastand west shores. The tidal flats along the west shore at the proposed out-fall site extend approximately 1200 feet into the estuary. The depth thenincreases to about 20 feet at approximately 2000 feet from the shore.

No detailed data has been obtained on the soils and sediments in the river.

Pilings from several old finger piers extend out into the estuary both northand south of the proposed outfall route. . These piers are not in use nor cap-able of being used. There are not marine terminals or marine facilities inthe vicinity of the proposed outfall. Amoco Chemical has no plans to developsuch a terminal.

The US Army Corps of Engineers has constructed a flow diversion structure inthe middle of the estuary, near the proposed outfall location. This dike isan attempt to slow siltation of the 40 foot navigation channel and to mini-mize shore erosion. The hydraulic characteristics of the river have thusbeen altered significantly. As shown in Attachment 2, the estuary is dividedInto two channels for significant depth by this barrier (Pea Patch Island Dike),The west channel is approximately 20 feet In depth, while the east channelIs maintained at ^2 feet by VSCOE dredges. The west channel is not dredged.

Normal spring tidal mrrents for the west channel at New Castle Channel Station200 range from 2.^ kts on the ebfcj tide to 2.3 kts on the flood tide and forthe east channel rlnge from 2.8 kts on the ebb'tide, to 2-3 kts on the floodtide. The total <fess section area of the estuary at Channel Station 205 isestimated to be 160,000 square feet, with the west channel section having58,500 square feet. There is little mixing between the two channels alongthe length of the dike.

Attachment 10 lists In tabular form the mean current velocities, cross sec-tional areas, and flow volume for the west and east channels created by thePea Patch Island Dike. Dilution ratios have been guesstlmated assuming theleachate Is completely mixed with the tidal prism over the ebb and floodperiods. ftR3QI33M

-3-

Memorandum to Henry Haley n^V f-L '^ October ?973

PRELIMINARY OUTFALL DESIGN

Preliminary investigations indicate that the ^ecetvincj waters at the proposedoutfall site at Channel Station 205 are so wel1 mixed that a diffusion struc-ture is not needed on the end of the outfall. A detailed study of mixing anddiffusion in the estuary using the Vicksburg hydraulic model,'mathematicalmodels, and/or field diffusion studies would be necessary to resolve thisquestion. Modeling would also be required to optimize1 diffusion design.

It is therefore proposed that a 18 inch diameter outfall pipe be installedat the head of Grantharn Lane, that it extend 2000 feet into the estuary toa termination point in about 20 feet of water, t'hat the outfall not be equippedwith a diffuser,"that the pipe be entirely buried in a trench out to the dis-charge point, and that the pipe be made out of a suitable synthetic material.It is anticipated that installation costs and maintanance costs w i l l be mini-mal and that time constraints can be met if this type outfall is designedand installed. The outfall angle of discharge should be horizontally.

Detailed engineering design of the outfall should investigate what means,if any, are needed to prevent river sediments from plugging the outfall duringperiods of low flow. Methods of preventing fouling of small boat anchorsshould be investigated with manufacturers.

The pipe trench can be excavated by a dipper dredge or clamshell dredge.Dredged spoil should be loaded on a barge and retained for trench backfill,if possible. This step is contingent on a favorable spoil analysis thatdetermines the sediments to be non-polluted. This method is recommended tominimize material f i l l costs and to eliminate the need to locate a spoil dis-posal site. The pipe.should be installed with a minimum of 4 foot over-burden to adequately protect it from freezing, exposure by scouring, anddamage from commercial and recreational marine traffic. Sheet pile may beused to support trench walls, however, single backfill with gravel, sand,and spoil should be adequate. Assuming a slope of repose of 3:1 for thetrench walls (unsupported) it w i l l be necessary to remove about hOOO cu. yds.of dredge spoi1.

RECOMMENDATIONS

l) Determine soils and marine sediments composition so that pipe trenchdiameter and prpe foundation can be established. Analyze marine sedimentsto establish if tbey are polluted.

2) Develop"asap'khe information package needed to support the permit appli-cation to the US Army Corps of Engineers, Philadelphia District, includingwater quality certificate, dredge spoil analysis, preliminary engineeringdrawings, and methods of construction.

3) Develop minimum cost outfall design as described earlier.

R30I335

Memorandum to Henry Haley 16 October 1973

10 Determine availability of existing diffusion, mixing studies, and modelsdeveloped by 1NCODEL (DRBC), DuPont, and New Jersey Zinc in the event de-tailed diffusion modeling must be conducted.

5) Develop detailed design for simple submerged pipe outfall with a hori-zontal discharge. No diffuser is recommended.

6) Use Weston's Southwest Regional Office to assist in preparation of Corps-of Engineers permit application.

REFERENCES

1) Hydraulic and Salinity Verfication, Report No. 1, Technical Memorandum No.2-337 Delaware River Model Study, by Corps of Engineers, US Army, WaterwaysExperiment Station, Vicksburg, Mississippi for the District Engineer, Phila-delphia District, Corps of Engineers, US Army, Philadelphia, Pa. May '56,

2) Salinity Tests of Existing Channel, Report No. 2, Ibid. June '5 -

3) Wiegel, Robert L., Oceanographlcsl- Engineering, PrenticerHal1, hnc.,Englewood Cliffs, New Jersey, 1"9<&.

If) Tidal Current Charts - Delaware Bay and Rrver, Second Edition I960, U.S;Department of Commerce, Rockville, Maryland 20852.

5) Dispersion Studies in Delaware River, 1NCODEL, "Estuary Model and PotentialApplications towards Stream Purification Evaluations", June, 1961.

6) Surface Water Records - Part 1 - New Jersey,. U.S. Geological Survey, 1971.

7) Chamberlin, Stanly G., and Cook, David D., "Evaluation of Waste DispersionIn Estuaries using Fluouescent Dye Tracer, Proceedings Annual Marine TechnologySociety Conference, September 71, pp. 639-6 6.

8) Frankel, Richard J. and Gumming, James D., "Turbulent Mixing Phenomana ofOcean Outfalls" Journal of the Sanitary Engineering Division, ASCE,'pp. 33-59*April 1965. .

9) Monney, N.T.,."Measurements of the Engineering Properties of Marine Sed-iments", pp. 21-ja MTS Journal, V. 5, March-Apr!1 1971.

jr - _ '10) Myers, Holm, and McAllister, Handbook of Ocean and Underwater Engineering,McGraw-Hill.

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»W f..j\ •1-14 \U<tf(iJ BASIC OCEANOGRAPHY

used up, and a reducing "nvironnimt nf hydruscn sullidr exists. Kor rxninjilt1, in theBlack Srn below a depth of a fow hundn-it nu-ti'rs, UaS has rcplai-t-'I llir dis,<«lvr<i ()«Rnd thus tliat inland st-u conlatns an onorinoua volume of reducing rnviromii'i«t.

20 30 40. Soiimty, %.

Fig.l-t Density of acawnlcr as a function oft empernture-aml salinity iu parts" per thousandby weight. (After Dirtnch,'*)

* - — - .Figure I-Gr is a vertical section tlironi;li the Atlantic Ocean showing the distributionof dissolved "Os.

CURRENTS AND THE SEA FLOOR*Importance of CurrantsCurrents as a subject of physical oerannpra-phy arc of special importance to the

ocean ehpinrcr. Surface currents nitVct tin* drill of ships, buoys, debris, and waste.Subsurface and sea-floor currcnU affoct ground inrklo, dnip sulnucrstliles, pmountctl strtK'lurrs, and they often affect visihiUly near the sr-a floor. Inxvsof sea-floor currrnty arc becoming very important in considerations of largo scalemininR-at-soa operations.Currents cause the following effects: (I } as rt hydrodynainic imi>cdinient they cause

a drag force that is proportional to the square of the velocity; C-) as a transportmechanism they cause a drift effect «n floating fquipnient or debris proportiaruil to tlicfirst power of the velocity; and ('J) as a source of vertical and Uoriz"ntnl5hc»r they canscHously interfere with cables or subsurface operations, particularly if the shear isnot exp<«tcfi.

A very intcrcstinE case of shear occurs in thctftraits of Gibralter. At the surfaceAtlantic water is onterine the M«litt*rranoan at a spred of niorp than I knot, wlulo atthe Mine lime below a depth of about IOU m, salty Mediterranean water is llnwing outat a speed of about I knot. This 2-knot-or-prcattr shear at the inter face is distributed"Vertically over only a frw tuns of meters. Tliis interface is alfco the iniU<Uc of theIhcrtnocline, where the shear sets up iarpc internal waves, many of which have beenmeasured as over 20 m hiRli. To a lesycr degree-such differential currcats and eiTcctsare prvbout in str&iU that join other water TORSOS of different density.

* *Bee also Sea Motion in this section*Cei

R3013U1*

-

Attachment 8

Estuary Density at Station No. 205 (Winter and Summer) ^ '-•"•.} ).

Ch'lorinity (ppm/ SalInTty (ppm) CW CSiFc i5°c

Neap Tide

High Water Slack .. 2100 5780 1.0030 1,0020

Low Water Slack 390 702 1.0005 .9998

Mean Tide

High Water Slack 1900 : 3 20 1.0025 1.0016

Low Water Slack 300 5^0 ' 1.0002 .9995

Spring Tide

High Water Slack 1800 32 0 1.0022 l.OOlU

Low Water Slack 250 . 450 1.0001

3Y _________________ DATE

RO'Y . . .,cW«TCHI3»..,ENNSYIV*N,A

<D BY _____ DATE ________ W.O. NO..OJ5CT ————————————————————————————————————————— _UBJECT__ ____________ I ————— i ———————————————— : —— • ,

Attachment 10 r";>3T v(Red) ' •'

West Channel East Channel Comb i nedkts fps kts fps

nal Ebb Current (spring) Velocity ' " 2.4 4.0 2-.8. 4.7mal Flood Current (spring) .Velocity 2.8 4.7 2.3 3.8

.hannel Cross Sectional Area (sf) 58,500 101,500 160,000Normal Flow Volume - Ebb (cfs) 234,000 477,050 711,050

Flood (cfs) 274,950 385,700 660/650Ebb (gpm) 105,019 X lo£ 214,100 X 1(£ 319,119 XFlood (gpm) 123,397 X ]& 173,102 X ICT 296,499 X

Net Seaward Flow (gpm) 9 X 10°

ueachate Outfall 3&00 (gpm)5.2 (mgd)

- i l u t i o n of Leachate OutfallEbb 29,000:1 88,644:1Flood 3 ,277:1 82,J60:1

Net Seaward Transport 2,500:1

rresh Water in flow (cfs) . . -—' 20,000

Maximum transport on flood tide -^ 11 miles upstreamean transport on ebb tide /—' 9 miles downstream

QuaHty Oata froffl

-'*

Attach. 4 . . I! 00 gpmach. 2 ^^

.Compos i fg<Ca]

TOS 742'C 16°° 378

,/ ' t>.6 . 5552'9 6'2 59 « <:' 47 42 5g| ,6-6 6.0

,!?N 72 87.5' R| ^ 101I'fcMnity ' 4.2 , 5! 'Aci'dity 1743y • 60•> *, ^

a'L 2I 21P b 2 8 ^, 'S 5.1 4.8j .06

Cd '' ' 2.2"3 2.05

2.05Total Kjcldahl N 530 ' ' 2'°5

1n?c N 60..on i a M 470

•otal Phosphate N 2.1

«OV P. W«»TI3N, INC.

iMTER-OFFICE MEMORANDUM

DATE: 12 Oct. 1973•»"'f i -' ' *-•

File

FROM: P« Kl°Se

SUBJECT: Toxicity Study on Pumped Leachate from w ° No ^3 -10Llangollen Landfill Area, New CasHe County, Del.

In accordance with RFW objectives' in the Llangollen landfill (Delaware)leachate control effort, a static bioassay toxicity test was conductedfrom Oct. 4 through Oct. 8, 1973. This test, designed to measure apossible toxic effect of the pumped leachate on a given fish species,was carried out by Roy F. Weston at the Weston Laboratory facilitieslocated in West Chester, Pa., in accordance to the procedures outHnedin Standard Methods, 13th Edition.

Methods and Materials:

The pumped leachate from RFW wells number 27, 28, 29 and 31 is ultimatelyreceived by the Delaware River via Army Creek. For this reason riverwater taken at low tide at Newcastle, Delaware was used as the diluentof choice. The test organisms used were Bluegill Sunfish, Lepomi smasochirus, obtained from the Kuntz Fish Hatchery in Elverson, Pa. Thisspecies was chosen in consideration of prevailing Army Creek conditions:salinity up to one percent, high turbidity, high COD and other parameterswhich make the water inimical to such test species as rainbow trout.Consul tat ion_ with Delaware River Basin Water Quality Division personnelsubstantiated our choice of test organism.

The fish were%cc1 imated to Delaware River water for ten days prior tothe bioassay sfudies. The bluegills averaged 7.0 centimeters in lengthand weighed an average of 5.9 grams. Fish were not fed during the 96hour test.

The test containers used were five (5) gallon rectangular glass aquaria.Original leachate dilutions were not changed during the test cycle, butre-aeration of the aquaria was necessary three times with oxygen at arate of 15-20 bubles per minute in order to maintain a D.O. above 4.0mg/1. A total of six (6) dilutions plus a control (river water)set up and a total of ten (10) fish were used for each di lut ion,

(fod)The bioassay study was conducted at 20 C 4- 1 C wi th the pH of thetest solutions ranging between 7.0" and 7.5, while D. 0. valuesranged from an original high of 8.9 to 4.0. Additional water qualityvalues of the composite leachate and of the dilution water are givenin Table 1 .

Table 1

River Water Leachate Composite(RFW #4893) (RFW

COD (mg/1) 58 39

SS (mg/1) 48 55TDS (mg/1) 2369 378pH 7.4 8.0

ALK (mg/1) 40 • 240Cl- (mg/1) • 1040 108

Total 'Hardness (mg/1) • 444 140

Fc (mg/1) 0.79 23.9Mn (mg/1) 0.10 0.12

Results and Conclusions

The test results indicating the leachate dilutio-- used and the responcesof the fish at the conslusion of the 96-hr, test are presented in Table 2,Readings (in hours) were taken at 0, 2, 24, 48, 72, and 96, the data ofwhich are on file at the RFW Laboratory.

Table 2Results of 96-Hr. Bioassay

___Results after 96 hoursCone, of No. Fish

Tank Number Leachate* pH Temp (°C) D.O. (ppm) Killed1-(Control) " 0% 7.0 19*5 6.1 02 ' "35 7.3 19.5 ' 4.5 03 V-50 7.4 19.5 4.7 04 60 7.5 19.5 4.0 05 70 7.5 19.5 4.6 06 85 7.5 19.5 4.3 07 100 7.5 19.5 4.3 0

Dilutant: Delaware River Water

R301350

Since the TLm corresponds to the median lethal dose (or concentration)at which 50/o survival is observed, this value cannot be calculated inthis instance as all fish survived' the duration of the test even in1 00/£ pumped leachate.

During the last forty eight hours, one fish in Tank No.7 (100% leachate)lost its sence of equilibrium. The static bioassay test as set forthin Standard Methods, as performed by RFW personnel and as agreed uponby the DRBC shows that the pumped leachate is not "toxic" over the testperiod to the organism chosen. The leachate may thus be presumed tohave limited or no adverse effects upon the1 existing biological communityof Army Creek or of the Delaware River.

Peter N. KloseAss't. Project Scientist

PNKrbja

si n oS H iH it u

ROY F. WESTON, INC.ENVIRONMENTAL SCIENTISTS AND ENGINEERS

November 29, 1973•OV F AlillHl INCir*-< :»•<(rtt',1 C"» JfM

, , tju« s<,v«*a -<i sjj-Mr. Albert Madora «m «««» »(*,M.New Castle Co.Engineering Building . W. 0. 463-10-222701 Capital Trai 1Newark, Delaware 1971 1

Dear Mr. Madora:

A follow-up biological assessment of Army Creek and its adjacent marshwas conducted on November 20 and 21. The methods utilized were similarto those described in the Biological Baseline Survey submitted to NewCastle County on September 28, 1973. Benthic samples were taken In ArmyCreek adjacent to the l a n d f i l l , with emphasis placed on the region betweenthe outflow of the pond and the culvert at the power line berm. The sampleswere collected with a 6" x 6" Ekman grab and sieved through a standard#30 mesh sieve.

Recent Increases in the pumping of leachate by the recovery well systemhas caused a dramatic change in the appearance of the Army Creek pond.The dissolved iron (ferrous iron) in the leachate undergoes oxidation inthe pond to form hydrated ferric hydroxide, a rust-colored floe, which hasbeen settling over the bottom of the water way. Concern over the toxiceffects of the floe (precipitate) was ameliorated upon discovery of largepopulations of water insects and small schools of minnows in the stretchfrom the pond outfall to the power line. The insects included severalspecies of water boatmen, diving beetles, mayfly larvae and midge larvae.Midge larvae, chironomids (bloodworms), were collected in great numbersat the p6nd outfall and in somewhat diminished quantity at down-streamlocations. Bloodworm larvae are one of the most tolerant organisms in regardto low dissolved oxygen and are commonly regarded as being reliable indi-cators of severe pollution of fresh water areas when present in suchabundance, as Is the case in Army Creek.

•The c6nc1us^ns that can be drawn from my observations are that a substantialamount of fey*jc hydroxide is being precipitated In Army Creek, but that noclear toxic response has yet been shown downstream of the pond. It may be,however, that the, floe is not yet present in sufficient quantity to adverselyaffect the biological life in the downstream area. The Army Creek pond isheavily impacted with the floe.

Mr. Albert Madora , ,:, -2- i i ' November ?

Upon consultation with Drs. Basil Parker and George Potera of the BiologyDepartment of Lehigh University. Bethlehem, Pennsylvania, it has beenlearned that in similar past cases the continued precipitation of ferrichydroxide forms an inert layer over the bottom of the receiving water andalso deposits on the surface of vegetation to the point of preventingphotosynthes is. The obv ious consequences of the above phenomenon wouId beto eliminate most, if not all biological l i f e . In the case of the downstreamportions of Army Creek some slight deposition of the rust-colored precipitatecan be seen on aquatic vegetation and in slow-flowing downstream areas. Thepond itself now shows heavy deposits. Therefore, though present damage isminor so far, continuation of this situation would almost inevitably lead toloss of the biological life existing .in.Army Creek.

Very truly yours,

Peter N. KloseProject Scientist

PKvrcrkcc: Mr. Warren 0'Sullivan

. R. Niessen, M. Apgar, J. A. Weaver, A. Metry, H' nry Haley

R30I353

MOV F. wttarON, INC. 0^

INTER-OFFICE MEMORANOUM

DATE. 29 January 1974

TO, File

cc: A1 MadoraWarren O'Sul1?van

FROM: P.N. Klose (Staff Biologist)

SUBJECT: Biological Assessment of Army Creek w O No 463-10

The third in a continuing series of biological assessments of Army Creekand its adjacent marsh was conducted on January 23, 1974. The methodsutilized were similar to those described in the Biological BaselineSurvey submitted to New Castle County on September 28, 1973 although thelatest study also made use of plankton sampling. Benthic samples were "taken just downstream from the pond outfall, at the weir, at the rail-road bridge and In the marsh near the power line berm using a 6" x 6(tEkman grab while plankton samples were collected at the weir and atthe tidal gate.

The previously described problem of extensive deposits of hydrated fer-ric hydorxtde settling on surfaces within the waterway has continuedsince the last report (November 29, 1973). This rust-colored floe hascovered the creek bed and all emergent or rooted aquatic vegetation.As was found in earlier studies, the toxic effect of this precipitateseems to be minimal or, at best, below a level readily discernible bybiological assessment methods.

Insects collected with the benthic grab included the same groups as be-fore, water boatment, diving beetles, mayfly larvae, dragonfly larvaeand madge lacvae (bloodworms), although the total numbers were somewhatreduced. Thj . reduction may be associated with winter population shffts,however, rattier than with leachate effects. Planktonic forms collectedat the weJr overflow included several species of fresh-water copepods,dilates and rotifers as well as many forms of green and blue-greenalgae. The presence of these species is significant since, were thepumped leachate of a toxic nature, these forms (composing the firststep of the local aquatic food chain) would probably not be present.However, due to lack of previous sampling of the plankton and due to

Memo - File -2- ' 29 January 1974

the cold winter weather, no assumptions as to changes In species diver-sity or population density brought on by the pumped leachate can beproposed.

The conclusions which can be drawn from this latest survey are that con-tinued precipitation of ferric hydroxide has covered the entire creekbed and banks and has heavily coated all aquatic vegetation In the creekand downstream marsh but that, as before, no clear toxic response hasyet been shown. A further reasonable conclusion is that most photosyn-thetic activity in the creek has been brought to a standstill; the onlyarea of primary productivity possibly remaining being the nearrsurfacephytoplankton.

The continued deposition of this inert layer in Army Creek w i l l undoubt-edly lead to loss of the presently established, though highly stresses,biological community. Long term effects w i l l be felt even if pumpingof the leachate were to cease. Therefore, a decision should be made assoon as possible if the marsh should be saved as such or if Army Creekis to become an open conduit used to convey leachate wastes to theDelaware River at the expense of most, if not a l l , biological lifewithin the marsh boundary.

The adverse biological impact of the leachate emphasizes the desirabili-ty of discharging waters from the recovery well operation directly intothe Delaware River. Thus, from an environmental impact standpoint,the installation and use of the discharge pipeline to the Delaware Rivershould be given high priority.

PNKrjep

W30I355

HOY F. WB«TOfM, INC.

- OFFICE MEMORANDUM

DATE; 16 July

TO: Filecc: Al Madora

Warren O1Sullivan*• Walt Niessen

PROMt F. N. Klose (biologist)

SUBJECT: Biological Assessment of Army Creek W.O. No. 463-10

The fourth in a continuing series of biological assessments of ArmyCreek and Its adjacent marsh was conducted on June 27-28 and July 16,197*+. The survey methods used included: a walking tour of the creek'and marsh from the tidal gate to the upper end of the pond; benthicsampling via Eckman dredge at several points in the pond, at the weir,railroad bridge and near the tidal gate; seining for fish and turtlesin the upper pond and for minnows in the lower stream reaches; planktonsampling at the tidal gate and weir.

The appearance of the waterway st i l l suggests a continuing process ofhydrated ferric hydroxide deposition. However, the covering of this•precipitate on the banks, creek bed and rooted .aquatic vegetation seemsto be less dense than during the previous studies of November 29. 1973and January 29, 197**-. This change may have been brought about by heavyspring rains and the subsequent flushing action. Although the depositmay have been less thick than previously noted, the turbidity of therust-colored water was as severe as during the previous surveys. Aswas found In earlier studies and by the bioassay conducted in September,1973, the toxic effect of this precipitate seems to be minimal or belowa level readily discernible by the biological assessment methods used.

A quali tatlv^descrtption of the effects of the pumped leachate mustInclude the apparent reduction in the numbers and species diversity ofdiatoms, algae, rotifers, Insects, and some crustaceans and the apparentmaintenance of the minnow, frog, turtle, fish and water insect populations.

Plankton and benthic sampling showed a marked decrease or total absence ofthe algae, diatoms, rotifers, mayfly larvae, dragonfly larvae, ciliatesand copepods present during earlier periods. This reduction In the lowerstages of the food web may very well be a result of the decreased photo-synthetic activity caused by the extreme turbidity of the rust-coloredwater. Even so, many species discovered earlier In the pond or creekwere found in significant numbers during this latest survey* among them

flR3QI356

biological MjjtijjiifeiiL ui Hi-iny tict:K

being: fresh-water crustaceans (Oaphnia, Cyclops, Macrothrix) ,. mosquitolarvae, water boatmen, water striders,~sa few damsel fly larvae, Chi ronomouslarvae, whirlygig beetles and snails (Physa) . Larger fauna not seenduring the winter surveysffau^: present*during this latest survey included:turtles (snapping, eastern painted), frogs (bull and green) , shiners(minnows), carp (Cyprinus) and a few ducks. Emergent aquatic vegetationseems to be thriving as well as last year with only those plants directlyimpacted by spray from the pumping well discharge pipes showing any signsof serious damage. it Is believed that even though the diatom and algaepopulations may be drastically reduced and thus produce a void in thefood web for small organisms dependent upon them, the major energy inputstems from the growth and decay of aquatic plants present and possiblyfrom insects and other small forms being washed into the creek during rains;By utilizing the larger plant forms as a food source, many of the lowertrophic levels are able to exist despite the ferric hydroxide floe andresultant turbidity.

Early visual examination of the upper pond revealed the possibility thatthe resident turtle population was far lower than last year. However,further wanderings produced a large baited turtle trap holding nine easternpainted turtles and two snapping turtles, all of medium to small size.This development and the obvious lack of turtles in the pond suggests thatthe population Is being drastically reduced by local meat hunters, petenthusiasts or researchers. Whatever the reason, the reduction in turtlenumbers should most likely not be attributed to the pumped leachate.

The conclusions which can be drawn from this latest survey are that thepond and marsh are suffering from the continued deposition of the hydratedferric hydroxide, affecting the primary producers and many of the lowerfood web components. However, since the precipitate is not toxic, thehigher trophic levels (rooted aquatic plants, turtles, frogs and carp)are able to continue to exist in the pond, at least in limited numbers.

R30I357

-2-

ROY r WESTON, INC.WESTON WAVWIST CH£STfR. M, 1KNO

inter-office memorandumTO: - File ' DATE: }k October

Al MadoraWarren O1SullivanWalt Niessen

FROM: Peter Klose (biologist)

SUBJECT: Biological Assessment of Army Creek W. O. No.: 463-010-22

The fifth In a continuing series of qualitative biological assessments ofArmy Creek and its adjacent marsh was conducted on October 10-11, 197**.

The methods of study utilized included plankton sampling in Army Pond, in thecreek at the weir and in the marsh near the tidal gate. Benthic invertebrateswere sampled with a 6" x 6" Ekman dredge and sieved through a 1 mm mesh net inthe field. Birds, turtles, snakes and small mammals were noted along the entirelength of the creek and marsh via a reconnaisance and use of field binoculars.Fish were Sampled with a dip net and noted visually while they were swimming inshallow reaches of the creek.

It must be remembered that the overall purpose of these short-term studies isnot to precisely delineate each species change or minor quantitative alterationof each community. Rather, the interest here Is in recording any readilydiscernible large-scale changes in the receiving water body which may be attribu-table to the pumped leachate.

In that vein, the overall condition of Army Creek has not deteriorated sub-stantially. Larger fauna and flora are seemingly as abundant as previously; *turtles are present, carp and minnows have been seen In their usual habitats, birdsare as numerous as ever, snakes and amphibians are also still quite common inthe area, as are rabbits, racoons, mice, rats, groundhogs, grey squirrels andother mammals. ,,Previous surveys (July 197*0 indicated that the turtle populationhad been reduced by trapping and their lowered numbers were still in evidence atthis most recent survey, although they were quite easily and commonly observedbasking on logs iff the pond.

Emergent aquatic vegetation seems to be reduced somewhat In distribution andvigor of mature plants. Those plants directly impacted by spray from the dis-charge pipes have suffered severe necrotic damage even though large willowsgrowing on the shoreline near discharge areas seem to be doing quite well.Another area suffering some reduction is the lack of ducks making use of thearea for feeding and resting. Though the true cause of the ducks' absence maynot be directly linked to the pumped leachate, there is a good chance that thelack of algae, sub-surface vegetation and benthic invertebrates isfor them to seek food elsewhere.

7/tAR30I35

-2-/*>'V*

As was the case during the July, 1974 survey, there is an apparent markedreduction in the numbers and species diversity of organisms in the lower stagesof the food web. Planktonic and faenthic sampling In Army Creek and the marshleading to the Delaware River showed an evident decrease of algae, diatoms, rotifers,insect larvae, ciHates, copepods and water insects present during earlier studies.This decrease most likely is not solely due to fall-winter population shifts,since invertebrate populations should not decline appreciably during coldermonths and since these populations were much "healthier" a year ago.

Biological vitality of this small waterway continues to exist at a reduced leveldue to the effects of the pumped leachate directed into the pond. Deposits ofhydrated ferric hydroxide continue to cover the banks, creek bed, and rootedaquatic vegetation and turbidity of the water is s t i l l very high. Apparentlythis turbidity serves to reduce or eliminate photosynthetic potential of algae,diatoms and sub-surface rooted aquatic plants.

Conclusions to this point of pumping operations are:

1. No major negative impacts have been suffered by Army Creek due topumped leachate operations,

2. Major floral and faunal populations seem relatively unchanged overthe past 14. months;

3- Minor changes include:Some spray damage to vegetation,Reduction in water transparency,Reduction in invertebrate populations,Reduction in algae populations,Increased sedimentation of ferric hydroxide

Long term effects of continued pumping operations will most likely be eliminationof most photosynthetic activity within the creek and subsequent further damageto existing invertebrate populations.

PNK:m!s

MOYF WfSTON.MC.WfSTON WAYWEST CHCSTffl. M, 1*MD

inter-office memorandumTO: Al Madora DATE: 6 May 1975Warren O1Sullivan

Walt NiessenFile

FROM: Peter Klose & Edward Simek (Biologists)

SUBJECT: Biological Assessment of Army Creek y^ Q No . 463-010-22

Introduction:

A sixth in a continuing series of qualitative biological assessments of ArmyCreek and its adjacent marsh was conducted on 23 and 30 April, 1975. The surveymethods used included: a walking tour of the creek and marsh from the upperend of the pond to just below the railroad bridge; faenthic sampling via theEckman dredge at several points in the pond and at the weir;.seining for fishat the weir and just below the railroad bridge; plankton sampling at the weirand at the tidal gate; water quality analyses by boat along the length of thepond and in the lower creek area.

The general appearance of the waterway still suggests continuing hydrated ferrichydroxide deposition, though the rate of deposition has decreased by as much as50% over last year's level. The covering of this precipitate on the pond andcreek banks and on the rooted vegetation Is slightly less dense than in previousstudies. The overall turbidity of the rust-colored water also appears slightlyless severe than In previous studies, likely due to a decrease in pumping ratefrom the wells.

Water Quality:

Several water quality parameters were measured on 30 April to determine if anyreadily discernible large-scale differences existed in water quality withinthe area. Measurements were made from a small pram using a Martek Mark V DigitalWater Quality Analyzer. Res.ults are given in Table #1. Water quality parametersmeasured were temperature, dissolved oxygen, conductivity, and pH.Few important differences were observed in water quality with regard to the variousparameters and points sampled. Temperature varied less than 2 C throughoutthe pond and was only slightly higher in the lower creek areas. pH values werealso quite uniform In all places. Dissolved oxygen values were quite similarexcept at stations #1 and #2 in the upper pond area, which showed slightly lower *values. Oxygen saturation in this area was between 50 and 60 percent whereas theother points sampled were all above 80 percent saturation. This is to be expectedsince the upper pond area possesses considerable accumulations of anaerobic mud,being in a much more advanced stage of eutrophication than other areas of the .pond.

*- Q Q n i c rvHit UU I ODU

Conductivity readings were quite uniform in the pond area but rose substantiallynear the mouth of the creek. This conductivity rise Is probably due to the in-fluence of slightly saline river water which is entering the creek through theImproperly functioning tide gate.

These water quality determinations suggest no real upstream-downstream differencesin the system. All parameters are quite normal for a highly eutrophic pondsystem, where nutrient rich waters which are high in detritus w i l l cause a slightD.O. depression but have no real effect on the other parameters measured.

Biota:

Benthic grab samples yielded no organisms In the pond area, as has been the caseIn past studies. The bottom generally consisted of muddy sand, thick organicsediments, and was, In places covered with leaf-litter and twigs. At the weir(Benthic Station #4), several beetle larvae of the family Dystiscidae were collected,The water depth was very shallow and the bottom more sandy than in any of thepond areas. A few midges, water striders, and whirligig bettles were also ob-served, but generally, the benthic biota in this downstream section of the ponddischarge was far less abundant and less diverse than that found during previousstudies.

Plankton tows were made at the weir (Map #1) and at the tide gate on a fallingtide (Map 12). Although the sampling was not designed to be quantitative, theamount of water volume sampled at each location was approximately equal. A fewcopepods and dlptera larvae were observed in sample #1 at the weir but the num-bers of organisms were generally quite low. Samples #2 and #3 from the tidal gateshowed a slightly higher diversity of organisms (Table #3) and considerably higherspecies numbers. All three samples were very high in detritus, illustrating animportant net export of detrital material from the marsh and creek into theDelaware River.

Fish were sampled with a two-man seine net (35' X 3/8" mesh) just above the weirand below the railroad bridge (see Map #1). Shiners, killifish, and juvenilesunfish were sampled at both locations but were more abundant below the railroad _bridge.

Although carp were not sampled, they were visually observed in the pond and In thecreek, and appeared to be quite abundant, especially in the creek section betweenthe power] ine b'erm and Route 9.

A list of specle^sbserved In the survey is included (Table #4). The residentturtle populatjon/appeared to be in high numbers, especially In the lowercreek areas. Reptile populations seen In the pond included a large (41) commonwater snake. Many bird species were observed in the area, especially ducks andother birds which feed in the marsh and pond. Among such species were: commonegret, great blue heron, American bittern, kingfisher , and several types ofshore birds. Emergent aquatic vegetation appears to be thriving with only thoseplants directly impacted by spray from the pumping well discharge pipes showingany signs of necrosis (tissue damage). *

Other Pollution Sources ; . '~

Other pollution sources may in fact be more detrimental to the system than thepumped leachate, in light of their higher contaminant concentrations. A newseepage area along the eastern borders of the landfill is oozing leachate frombeneath the landfill into the Phragmltes stand just above the.weir. The leachatehas a very pungent odor and appears to be highly toxic to the vegetation in theImmediate area. It undoubtedly contributes much to the lowering of the waterquality and reduction of aquatic invertebrates in the creek area above the weir.The low number of planktonic organisms found at the weir also reflect this poorwater quali ty.

North of the Route 9 bridge, a white precipitate was observed along the banks ofthe "Clean Tributary" (Map #2) and along the main creek banks. The source of thismaterial was not traced, but it too is influencing water quality in the system.

Conclusions:

The overall purpose of these short-term studies is not to delineate minor quantitativealternations in each blotic community but rather to record readily discerniblesignificant changes in the receiving water body.

This study concludes therefore that the overall conditions of Army Creek andArmy Pond have not deteriorated substantially since an original slight depressionin biotic diversity and abundance was observed in the fall of 1973» after pumpedleachate operations began. More significant biological degredatlon of this systemhas' occurred due to direct seepage from the landfill into the waterway. Thenew leachate Inflow along the eastern border of the landfill is an example ofsuch a source and is causing severe localized biological degredation. When con-sidering the entire waterway, however, the biological vitality over the last twoyears has been approximately constant.

k Rf^ f*t s O C. O30 ! 3b<£

Table 1

Water Quality Analysis

Com(Micromhos/cm)

Station ff Depth (Feet) Temp. (°C) Conductivity D.O. (mg/1) pH

1 2.0 13.50 222 4,6 6.942 2.5 13-60 219 3.8 6.933 3.0 15*04 234 6.6 6.934 3-0 14.90 234 7.8 6.945 3.5 15.32 236 6.1 6.926 3-0 14.34 -229 6.1 6.887 5-0 14.05 226 5-6 6.898 3-0 17.32 512 _ 6.9 6.949 3-0 17.94 472 6.6 7.0110 3-0 18.32 ' 363 5.8 7.26U 2.0 18.91 282 7.5 7-1112 1.0 18.56 283 8.5 7.0413 5-0 16.68 554 7-5 6.91

Table 2

Benthic Grabs

Grab # Sediment Description Macrobiota

1 Fine Sand No Organisms2 Orange Mud No Organisms3 Dark Mud No Organisms4 Fine Sand Coleoptera larvae

Fam. Dystiscidae

Table 3Plankton Samples

Animal LocationSpecies Found

Cyclopoid copepods WeirDiptera larvae

Gammarid amphipods Tidal GateCyclopoid copepodsCalanoid copepodsDiptera larvae Tidal GateCalanoid copepodsCyclopoid copepods

Table 4

Species Observed in and Adjacent to Army Creek and Army Pond

Plant Communities (emergent aquatic vegetation):

1 - Common reed Phrogmi tes communIs2. Cattail Typha sp.3. Arrowhead SagIttaria sp.4. Water l i l y Nymphaea sp.

I I. Invertebrates:

1. Coleoptera larvae Fam: Dystlscidae2- - --- - Hydrometra sp.3. Diptera larvae4. Cyelopoid Copepods5. Calanoid copepods6. Gammarid amphipods7- Pulmonate snail , Physa sp.8. midges Fam. Chironomldae9. water striders Fam. Genidae10. whirligig beetles Fam. Gyrinidae

I I I . Vertebrates:

1. Eastern Painted turtle Chrysemys picta picta2. Eastern Mud Turtle Kinpsternon subrubrum sufarubrum3. Northern Water snake Natrix sipedon sipedon4. Carp Cyprinus carpio5. Shiner Notropus sp.6. Ki11 ifish Fundulus sp.7. Juvenile sunflsh Lepomis sp.8. Wood duck Aix sporusa9. Black duck .Anas rubrlpes10. Mallard duck Anas platyrhynches11„ Rock dove Col umbra 1 J v i a12. Belted kingfisher Megacoryle alcoyon13- Crow Corvus brachyshynchos14. Mockingblrd Mlmus polyglottus15- Purple grackle Tuiscalus quiscalus16. Starl ing'" Sturnus vulgaris17- Cardinal » Rlchmoudena cardinalis18. Red-wlnged»fcjackbtrd Agelaius phoeniceus19- American Brttern Botaurus lentiginosus20. Great blue heron . Ardea herodias21. Great white heron Ardea occidentalis22. Tree swa11ow Tridoprocne b J co1o r23. Carolina chickadee Parus carolinensis24* Marsh sparrows Ammospiza sp.25. American goldfinch Spinus tristls26. Common Egret Casmerodius albus

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(Red) •ov f WCSTOW weWESTON WA*WEST CHESTER Wl 03*3

inter-office memorandumTO: ,Al Madora

Warren O'Sullivan " DATE: " 3 December 1975Walt NlessenFile

FROM: P-N. Klose, E.M. Simek, T.D. Johnson and K.R. P h i l i p p (Project Ecologlsts)

SUBJECT: Biological Assessment of Army Creek - W O W - 0463-17

Introduction

The seventh in a continuing series"of qualitative biological assessments ofArmy Creek and its adjacent marsh was conducted on 14 November 1975. Theoverall purpose of these short-term studies has been to record readily dis-cernible significant changes in the receiving water body, rather than todelineate minor quantitative alternations in each biotic community.This survey was the third undertaken during late autumn conditions.

Methods

The survey was limited to sampling stations accessible by foot, as the boatutilized In previous visits had recently been stolen from Vince Dellaversano'sproperty.

Water quality and aquatic organisms were sampled at stations A,B, and C(Figure 1). Station A was In Army Creek approximately 100 meters upstreamfrom Army Pond. Station B was at and beiow the weir at the base of Army Pond.Station C was approximately 400 meters upstream from Station A. Temperature,pH, conductivity, and D.O. were measured at stations B and C by means of aMartek Hark V Water Quality Analyzer. At stations A and B biological sampleswere taken,.

Benthic samples were obtained by means of a 6" X 6" hand operated Ekman grab.Due to the rocky bottom conditions prevailing in Army Creek,- samples were con-siderably smaller than would be the case with optimum grab performance.

Plankton samples were collected with a 0.5m diameter, #10 mesh (273/*sperture)net. At station A the net was towed along the bank in shallow water. Atstation B the net was streamed for approximately 5 minutes in the currentimmediately below the weir at the base of the pond.

W-alt Niessen -2- n&iflftAL 8 December

'* (Red)A 35 foot, 3/8" mesh two-person seine was utilized in shallow, stagnantstream backwaters near stations A and B to sample for ft.sh and macroirivertebrates,A reconnaissance of the entire l a n d f i l l along Army Creek and pond was under-taken to describe the terrestrial vegetation and wildlife of the area. Avegetation map is shown in Figure 1.

Resu!cs: . . . . - -

Water Qua!i ty

Water quality data are presented in Table 1. Water from Army Pond was approxi-mately 1.5 C warmer than Army Creek-water above the pond, presumably due tosolar warming. Dissolved oxygen was at 65~70% saturation everywhere but atthe surface near the weir, where 100% saturation occurred. Conductivity wassomewhat higher in the pond water than in Army Creek water and pH was somewhatlower. This may reflect the addltion'of dissolved salts via the leachate.

Aquatic Biota

Plankton data (Table 2) show that Army Creek above the pond contained a rathersparse and monotonous plankton assemblage. At station A, oligochaetes (aquaticannelid worms), presumably swept up from the bottom, dominated the animalcommunity, and blue-green algae dominated the phytoplankton. The turbidwater and anaerobic bottom mud were indicative of highly eutrophic conditions.

In contrast, a diverse, abundant plankton commvnity was present at station B(Table 2) This community evidently-originated in Army Pond and Its presencesuggests that overall water quality In Army Pond was fairly good. Larval andjuvenile stages of Cyclopoid copepods were present. Filamentous blue-greenalgae and the green alga, Spirogyra both of which may at times be Indicativeof eutrophic conditions, were moderately abundant in the samples.

The zooplankto.n community is dependent for its existence on the presence ofabundant and- diverse phytoplankton. Phytoplankton is in turn sensitive towater quality. The nature of the zooplankton community at station B impliedthe presence of a fairly abundant and diverse phytoplankton assemblage. Inaddition, the presence of young copepods, which are more sensitive to pollutionthan adults, suggests that water quality was moderately good. The presence ofcladocerans (small crustaceans) reinforces this conclusion.

Zooplankton is "an important food source for macroinvertebrates and small fish.The plankton origfnating from Army Pond may support a larger fish populationthan can exist u ?t>ream of the pond.

A series of benthic grabs at station B yielded no organisms due to the substratum,past leaching in the area, and the season. The substratum was generally com-posed of pebbles, but a fine, rust-colored sediment was also present in largequantities. This sediment appears to be composed primarily of iron hydroxideand Is evidence of the large export of iron compounds from Army Pond.

ftR30i3

Walt Niessen -2- OKIuUM. 3 December 1375

In shallow areas an abundant riffle fauna inhabited the undersides of rocks-01tgochaetes, flatworms and large numbers of one species of insect larva werefound In a riffle area immediately below the weir.

Only one fish (Fundulus sp.) was caught in the seine near station A. Althoughthis small sample was in part the result of seining over such a difficult streambottom, populations were undoubtedly quite small. No schools of fish were notedin the area.

A seine haul in Army Creek just below the weir (Station B) yielded 5 fish andone crayfish (Table 4). The sampling conditions there were similar to thoseat station A. Therefore, the larger catch probably reflects the presence ofa larger fish population below the pond. Again, no schools of fish were seen.Freshwater fish often pass the winter in a torpid or dormant state. The lowwater temperature may have forced many fish into the overwintering state,accounting for the fact that fewer fish were noted during this visit than duringprevious visits.

Terrestrial Vegetation

The vegetation of the Army pond area is represented•in Figure 1. Due tothe season several species were absent or unidentifiable. However, themajority of trees and shrubs were identified as well as some herbacous species(Table 5).

A mature stand of native hardwoods was located on the southern bank of theravine where Army Creek enters the pond. The stand contained most species oftrees native to northern Delaware. Zonation of species associations occurredfrom the crest of the ravine to the creek. White, black and chestnut oaks werefound on the highest ground, hickory, beech and tulip on the slopes, thensweetgum, cherry and red maple on the floodplain and lower slopes, and finallywillow along the stream banks. This is the typical zonation of the forestassociations of northern Delaware. The oaks, hickory and beech were quite matureOne oak from which an annual growth ring increment core was taken was over 150years old,

The association of sweetgum and tulip-beech, which are characteristic of a wethabitat, were found along the creek from Route 13 to the south bank of thepond. These species were common on both banks of the creek draining Army Pond,and were found sparsely scattered or in small pockets along both banks ofthe pond. Sycamore, silver maple, black locust and willow oak were also foundmixed with sweetgum and tulip-beech.

Cattail (Typha latffo.l la) was found along the water's edge In low bank areas,and in shallow pools on the landfill. Phragmi tcs common i s, the common reed,was associated with Typha In wet areas and occurred along in dryer areas onthe banks and top of the landfill. Both species were more abundant on thelower marshy reaches of the pond and creek.

R30I369

Walt NIessen. -3 ' ' Oa!&{»AL 8 December T975

Japanese honeysuckle (Lonicera Japonica) and Phragmi tes dominated the steepsouthern bank of the l a n d f i l l . They were also found on the south bank of thepond and provided dense ground cover throughout the area. The top of thelandfill was dominated by dense stands of bunch grass and broomsedge(And ro'pogon v i rg I n I cus ) with occasional admixtures of rabbitfoot grass (Pol ypogonmonspl iensisjand pan i cum grasses.

There were cherry and white pine saplings, some exceeding ten years of age,scattered about: the periphery of the landfill's upper surface. A clump ofcherry trees near the center of the l a n d f i l l adjacent to the railroad trackswas probably the seed source for the cherry saplings.

Where leachate was oozing from the landfill along its southwestern edge, therewas usually a supression*, sometimes dramatic, of the plant cover. In someplaces, however, bunch grass and cattail were found growing near, and occa-sionally in, the leachate drainage. Sporatic tissue damage was found in thebunch grass. The leachate seems to have killed a number of cherry and redmaple trees and caused sizable areas of bare mud. Seepage reported near theweir in April 1975 appears to have ceased.

Leachate pumped from wells appeared to be less toxic than the seepage fromthe base of the landfill. Willows growing directly in the spray runoffseemed healthy. Annual growth ring increment cores taken from these treesshowed l i t t l e growth repression in recent years, as might be expected if theleachate were toxic or detrimental to the trees' growth.

Terrestrial Wi 1 dl Ife:

The list of animal species observed In the Army Creek area (Table 6) is somewhatsmaller than those of previous surveys, but comparisons must be made with caution,Previous surveys Included observations by boat and coverage of the marsh areadownstream of the weir and railroad trestle. The advent of winter also accountedfor the fact that few terrestrial animals~~were observed.

Quite a few common field and open shrub bird species such as white-throatedsparrows, song sparrows, catbirds, chickadees and juncos were observed. Thesecomprised the majority of individuals seen. Of the larger birds, one greatblue heron, one sparrow hawk, and one red-tail hawk were seen. The owners ofthe landfill report successful duck hunting in the area. No migratory water-fowl were observed by the field team,

»No mammals or reptiles were sighted in the area although there was evidence oftheir presence. Beneath the bunch grass on the surface of the landfill therewere active runways and nests indicating large populations of small mammalssuch as the meadow vole (Mfcrotus pennsyl vanicus) . The presence of the red-tailhawk and sparrow hawk and observations of their hunting patterns supports thisindication. Rabbit pellets, were common on the landfill and hunting was In pro-gress during the survey. ' Burrows, probably of woodchucks , were found oftenalong the slopes of the landfill. Other evidence Indicated the presence ofsquirrel, mole, and raccoon.

a r* o t\ * o "? n&R30 f 3/0

Walt Niessen '4- VA.:<*U*riL 8 December 1975/;> . -* •\tw*g . ^

Cone Ius tons:

The overall environmental status of the study area has changed l i t t l e sinceApril, 1975- However, as in the April survey, few benthic organisms werefound. This may be an Indication of changing conditions in the benthicenvironment. This possibility should be explored In future surveys. Planktonand water quality parameters were not greatly changed from the April survey.Leachate has had a localized effect on terrestrial vegetation, but has notaffected terrestrial animals to any noticeable degree. Pumped leachate hashad l i t t l e effect on nearby vegetation.

Seepage from the southwestern portion of the l a n d f i l l (Figure l) has increasedmarkedly since April,. 1975- However, seepage from the eastern portion hasvi rtually ceased.

&R30I37

CRfGIBAl(Hvd)

Table 1

Water Qua!ity Data

Station Temperature Conductivity D.O.% of pH(milliohms.) ml/L Saturation

C' 9'1 0.07 5.2 65

Bat weir: surface ' 10.7 n i o ,,„.? S;! f:j >«• • 7.,o

rlffle:

7-50

1372

Table 2

Plankton at Stations A and B

Station A Plants: OscT1latoria - very abundant

Anabaena - very abundant

Pennate diatom - rare

Animals: Ollgochaete spp.- very abundant

Nematodes - presentCyclopoid copepods^rare

Station B Plants: Spirogyra sp - abundantunidentlfled filamentous

green algae spp- presentOsci1latoria sp.- abundant

Animals Brachionus sp - rareAsplanch'na sp - very abundantNematodes r abundantOllgocnaete spp - abundantDlpteran larvae - rareOstraced - rareIlyocryptus sp - presentChydoridae spp - rareCyclopoid copepods- presentHarpacticoid copepods-rare

AR3Q1373

Table 3

Benthic Organisms in Army Creek

\Station Sediment Description Organisms

Black mud Dipteran (midge) larvae - rare

.01igochaetes (worms) - rare

Orange mud .and No organisms notedg ra ve 1

Table A

Results of Fish Seining

Station Organisms Approx. Length

A 1 minnow (Fundulus sp) 3-5 cm

B 3 minnows (Fundulus sp) 3"5 cm

2 shiners (Notropls sp) 4-6 cm

1 crayfish *t cm

HR3QI375

Table 5

Vegetation

Common Name ScientlfIc Name

Woody Plants:

White pine Pinus strobusMockernut hickory Hlcora aIbaPignut hickory Hi cora g1abraBlack willow , Sali x nigraBeech Fagus grand J folI aWhite oak Quercus albaBlack oak Quercus velutlnaRed oak Quercus rubraChestnut oak Quercus montanaWi11ow oak . - Quercus phellosT u l i p poplar ' 'Li riodendron t u 1 i pi feraSycamore Platanus occi dentali sFire cherry Prunur Pennsylvania *Black locust Robtnia pseudoacaci-aStaghorn sumach ^ Rhus hi rtaRed maple Acer rubrumSilver maple Acer saccharinumDogwood . Cornus florldaSweet gum Liquidambar styraci fIuaSpice bush LIndera benzoinViburnum Viburnum denfcatumJapanese honeysuckle Lonicera japonicaGreenbriar 5milax sp.Wild rose Rosa multiflora

Herbaceous Plants:

Cattal Typha latifollaReed Phragmites communisRabbltfoot grass Polypogon monspeliensisBunchgrass unidentifiedMud plantalo Heteranthera reniformlsArrowhead «» Sag!ttaria sp.

O "7J /

Table 6 {i.t :J

Bi rds and MammalsBi rds:

Common Name Sclent!fie Name

Great blue heron Ardea herodiasTurkey vulture Cathartes auraRed-tailed hawk Buteo jamaJcensisSparrow hawk Falco sparveriasBobwhi te - Colinus vi rgi nianusMourning Dove Zenai dura macrouraRock dove Col u mba^ 1 i v ? aF1icker Colaptes auratusBlue j ay CaanocItta crlstataCommon crow Corvus coraxCarolina chickadee ._ Parus carol uiensi sCarolina wren Thryothorus "1 udovicianusHock i ngb i rd H i mus poiyglottosCatbi rd Dumetella carolInens i sScarl ing . Sturnus vulgari sBay-breasted warbler Dendroica cas'taneaEastern meadowlark Sturnella magnaRed-v/inged blackbird Agelaius phoen i ceusCommon grackle . Quiscalus quisculaCardinal R i chmandena ca rd i na1 IsJunco Junco hyemali 5Field sparrow . Spizella pusiI laWhite-throated sparrow Zonotrichia a l b i c o l l i sSong sparrow Melospiza melodia

.Mammals:

Meadow vole * Microtus pennsylvanni cusEastern cottontail rabbit Sylvllagus floridanusWoodchuck Marmota flaviventri sRaccoon Procyon lotorStarnose mole" Condylura cristataEastern gray squirrel Sciurus carolinensis

ftR'301377

ocrn

inter-off ice memorandumTO: Richard J. Grzywlnski DATE: 2? September 1977

cc: Walter M. LelsThomas D. Myers

FROM: p. N. Klose, K.R. Phlllpp, J.A. Williams, Jr.(Life Systems)

SUBJECT; Fall-1977-Biologlcal Assessment of Army Creek W. O. No.: 63-020

Introduction:

The eighth biological assessment of Army Creek and Army Pond was conducted on1 September 1977 by the field team of P.N. Klose, K. R. Philipp and J.A. Williams, Jr.The purpose of this study was to assess the general biological health of theArmy Creek aquatic system and its immediately bordering terrestrial components.Survey methods used Included: a visual reconalssance of the creek and pondRoute 13 to the railroad bridge below the pond outlet; fish shocking In thevia a battery operated Smith-Root series VII Instrument; water quality analysisIn the pond via various portable Instruments; seining fish In the outlet stream;and collection of benthic stream Insects below the pond outlet.

The survey of terrestrial vegetation and wildlife was restricted to the top ofthe landfill, the southern bank of the landfill on Army Creek and the woodlandlining the reed-cattail marsh above the'weir location. The mature woodland andthe quarry bank of Army pond were not covered.

The general appearance of the aquatic system is good, taking into considerationthat Army Pond Is a very shallow, heavily sedimented, and highly eutrophlc waterbody. Areas near actively pumping wells still show depositions of the rust-coloredhydrated ferric hydroxide, though the rate of deposition has decreased over theyears as the volume of pumped leachate has decreased.

* -Results of Field Study:

Water Quality-Several common water quality parameters were sampled using portablemeters: dissolved oxygen(D.O.)-YSI model 5^ meter, conductivity and pH—LaMottemeters, temperature-glass thermometer. Results are as follows, and correspond tostations on the map (Figure 1):

Fall-1977-Biological Assessment of Army Creek -2- 27 September 1977

Station #

InIet-Rt.I3123*45

Outlet

Temp. C

• 25.524.323.223.024.825.127.1

^•Measurements taken

Conduct! vi ty(umhos/cm)

225310305365310315305

close to a wel 1

D.O.mg/1

8.37.27.06.26.66.78.0

di scharge

% 02 Saturation

100%85%80%71%79%80%98%

along south shore of

PH

7.56.77.06.6•6.96.97.1

the pond.

The water quality results indicate no major changes in the aquatic system due tothe pumped leachate. Temperature In the outlet stream Is higher due to the warmingeffect of sunshine on the pond's water surface. This phenomenon, along withoxidation of mud and organic debris in the pond, also-causes a drop In dissolvedoxygen. Percent oxygen saturation increases at the outlet due to turbulence ofthe water and photosynthetic release of oxygen from algae. Conductivity increasessomewhat In the pond, possibly due to small leachate seepages (of which none werenoticed) and from the pumped leachate. Similarly, pH dropped somewhat In the pond,possibly due to the slightly acid leachate, even though the variations from 7.5 to6.6 are not very significant.

These water quality determinations suggest no readily seen upstream (above theleachate pumping)/downstream effects. Although turbidity was not measured, It wasthe opinion of one of us (P. Klose-who has taken part In all past field surveys atLlagollen) that turbidity was less than In previous years.

Aquatic Blota-FTsh collections were made via an electro-shocker In which the fishare stunned, collected, and then returned to the water. Such efforts at variouslocations throughout the lake produced numerous carp, Cyprfnus carpIo, bluegillsunfish, Lepoml's macrochirus, and pumpklnseed sunfish, Lepomis gibbosus. Noattempt at quantifying the fish populations was made.

Sefning In the outlet stream produced numerous fish, including several types whichhad not previous^ been found In that section. Species collected at the outlet were:

ir -Carp Cyprinus carpioPumpkinseed sunfish Lepomis gibbosusGizzard shad Dorosoma cepedlanumCommon shfner Notropis cornutusSmallmouth bass Micropterus dolomieuiStriped bass Roccus saxati1 isKi11 ifIsh Fundulus heteroclItus

Fall-1977-BIological Assessment of Army Creek -3-' 27 September 1977

Carp were sighted In almost all shallow areas of the pond and were apparentlymore numerous than during previous years. Turtles were observed along the shoreand on logs. As none were captured, we assume that the same species are presentnow as in the past, i.e., the eastern painted turtle, Chrysemys picta and theeastern mud "turtle, Ktnosternon subrubrum.

Benthic macro!nvertebrates were sampled via a kick-net in the outlet canal. Itwas found on previous surveys that benthic sampling in the pond produced a verylimited list of Invertebrates. Commonly, heavily silted, organic mud bottoms, asoccur In Army Pond, harbor only ollgochaete worms and a few other tolerant species,However, by sampling Tn the outlet stream, one may get a clearer idea of whateffects the existing water quality has on the indigenous fauna. Two separatesamples produced the following types of aquatic Insects:

Coleoptera - beetlesDiptera - fliesEphemeroptera - mayfliesOdonata - damselflies and dragonfliesTrichoptera - caddisfliesOligochaeta - segmented wormsHol.lusca - snailsMalacostraca - amphipodsAlgae-Oedogoniurn, Spi rogyra, Osc?llatoria, Diatoms

The above list, along with that of the fish collected, indicates a diverse, healbiological community in the outlet stream. If water quality were significantlyImpaired by the leachate pumping program, one would not expect to find such speciesas mayflies or smallmouth bass in abundance. This Is not to say that the depositedferric hydroxide In the pond is not causing any smothering of the benthic substratenear the well outfalls, just that, overall, the water quality is- sufficiently goodto allow what Is a normal biological community in that area to exist, tt is suspectedthat the aquatic system has benefited substantially from the decreased leachatepumping rates, lack of direct leachate flows from the landfill into the pond, andcessation of operations at the nearby sand and gravel firm. It .Is also noteworthythat the water flow from the wells Is probably the only saving grace for the system.The inflow at Route 13 Is very minor and can probably be measured as only severalgallons per minute. Thus, the pumped volume establishes the flow out of the pondInto the-marsh and maintains favorable conditions for the existing aquatic community.

Terrestrial Vegetatlon-The vegetation map prepared In the seventh survey of ArmyCreek, November 1975, Is still applicable since there have been no major changesIn land use or vegetation development* Table 1 presents plant species Identifiedin this current survey that are additional to the plant species list of the pre-ceding 1975 survey*

AR30138

Fall~1977-Biological Assessment of Army Creek -4-('UClJ 27 September 1977

Although no major changes have occured, there has been an Increase in the numberand type of seedlings growing on the surface of the landfill. In addition tocherry and white pine, there are black locust, sassafrass, black willow and sumacseedlings extending into the landfill grassland from the remaining lines and clumps oftrees along the southern bank of the landfill and the rail line. Given time, thisencroachment should lead to colonization of the grass area to woodland.

One observer(Kurt Philipp) present on the preceding survey noted that the grasscover on the landfill seemed much denser than during the 1975 survey. The grass-land on the landfill consisted of a wide variety of grasses and other herbaceousplants. The most common of these, such as, purple lovegrass, goldenrod, ragweed,and many asters are given in Table 1.

Common reed and cattail continue to grow in dense thickets in wet areas on thesurface of the landfill. Both these*species are more abundant along the watersedge In low bank areas and lower marshy reaches of the pond and creek. The steepsouthern bank of the landfill remains alternately dominated by Japanese honeysuckle,common reed and clump woodland (sweetgum, black willow, sycamore and silver maple).

Arrowhead and arrow arum remain the dominant aquatic vegetation of open shallowwater with mud plantain, cattail and common reed prevalent along the shorelineand marshy lower reach.

Only one leachate seep identified in the 1975 survey was found. This seep on thesoutheastern most edge of the landfill, once the worst in appearance, did notappear active. Nodding foxtail, tickseed sunflower, and common reed were growingin the wash of the previous leachate. There was no visual evidence of tissue orgrowth damage on these plants and they appeared to be advancing on the barrenground surrounding the seep.

Terrestrial WildlIfe-Although the current survey covered a smaller area than theprevious survey a greater number of bird species (Table 2) were observed since the1975 survey was much later in the fall season. Evidence of mammals on the siteremained about the same*

A good number of the birds observed may be considered residents such as crows,catbirds, blue.jays, cardinals and mourning doves and are common to field and shrubhabitats. A few migratory birds such as yellowthroat, overbird, purple finch,pine warbler and*killdeer were also observed in the vegetation along the pond.The pond i t self Appeared to supply sufficient resources for a great blueheron, a little blue heron, four blackcrowned night herons, a least bittern, aspotted sandpiper and six or seven wood ducks.

A marsh hawk and four American kestrel (sparrow hawk) were also observed alongthe banks of the pond. The number of raptors together with active runways beneath

-. -.-

Fall-1977-BIologfcal Assessment of Army Creek -5- 27 September 1977

the grass on the landfill and its banks continue to Indicate healthy populationsof mice and voles. Game trails covered the landfill areas and several rabbitswere flushed during the survey. One muskrat was seen crossing the pond. Activeborrows, likely made by woodchucks, were occasionally encountered along the land-fill banks. " Raccoon tracks and mole tunnels were also noted.

Table 1Vegetation

Common Name

Woody Plants:

White pine Pinus strobusMdckernut hickory Hicora albaPignut hickory H i co ra glabraBlack willow SalIx nigraBeech • Fagus grand!follaWhite oak • Quercus albaBlack oak Quereus velutinaRed oak Quercus rubraChestnut oak Quercus montanaWi1 low oak Quercus phellosTulip poplar Llriodendron tuliplferaSycamore Platanus occidental IsFire cherry Prunus PennsylvaniaBlack locust Robin Ia pseudoacaciaStaghorn sumach . Rhus hi rtaRed maple Acer rub rumSilver maple Acer saccharinumDogwood Cornus floridaSweet gum Liguidambar styracifluaSpice bush LIndera benzoinViburnum Viburnum dentatumJapanese honeysuckle Lonlcera 1aponicaGreenbriar Smllax sp.Wild rose Rosa multlflora

Herbaceous Plants:

Cattal Typha latifoliaReed Phragmites communisRabbitfoot grass Polypoqon monspeliensisBunchgrass - unidentifiedMud plantain Heteranthera renlformlsArrowhead Sagittaria sp.

Plants (supplement)*

Common ragweed Ambrosia artemisiIfollaGoldenrod SoII dago sp.Asters Aster sp.Tickseed sunflower Bidens polylepisPartridge Pea Cassia fasciculataClover Lespedza sp.Crabgrass Digitaria sangutnalIsNodding foxtail Setaria faberiPurple lovegrass Eragrostis spectabillsNeedlegrass Arlstida sp. flR/Ull 3RU"•••"^ "•^ P-J j j - \j j \ji t "f

Table 2

Birds and Mammals

Birds

Wood Duck AIx. sponsaMarsh* Hawk CI r.cus cyaneusAmerican Kestrel Falco sparveriusBobwhlte • Collnus virginianusCattle egret Bubulcus IblsGreat Blue Heron Ardea. herodiasLittle Blue Heron Florida caeruleaBlack-crowned Night Heron Nycticorax nycticoraxLeast Bittern Ixobrychus exl1i sKill deer Charadrius voclferusSpotted Sandpiper Actitis maculariaMourning Dove Zenaldura macrouraRock Dove (Pigeon) Co1umba 1iviaChimney Swift " ' Chaetura pelagicaBelted Kingfisher Megaceryle alcvonYellow-shafted Flicker Colaptes auratusDowny Woodpecker " Dendrocopos pubescensEastern Kingbird Tyrannus tyrannusTree Swallow Iridoprocne bicolorBlue Jay Cyanocltta cristataCommon Crow Corvus brachyrhynchosMockingbird Mimus polyglottosCatbird- Dumetella carolinenslsRobin - Turdus migratprlusSol Itary rreo Vireo sol itariusPine Warbler Dendrolca pinusOvenbird • Seiurus aurocapillusYellowthroat Geothlypis trlchasCommon Grackle Quiscalus qulsculaCardinal Richmondena cardinal is

AR301385

Table 2 continued

Purple Finch Carpodacus purpureusAmerican Goldfinch Spinus tristisSharp-tailed Sparrow Ammospiza caudacutaSong Sparrow Melosptza me1odI a

Mamma1s

Meadow Vole Microtus pennsylvanicusStarnose Mole Condylura crijstataMuskrat Ondatra zibethicaRabbit Sylvilagns floridanusWoodchuck Marmota monaxRacoon , Procvon lotor

R30I386

-' • •;- c > •.< V 'i . , i <ci

(, 'i) _"*'- UJ^ O^-7 / 27 / s.- '.-. - Ar f' r*- \ \

^^ <~ 'N. UJ>*. o

'--•'- ^7 / 2^:. • , / / S' ^"- • •»_ /

:-3 ^ -— J X',v <- s- i ?. g 5"- UJ< -IX .*<:-: 4 : **i. '.' v r '• * *t* *• Ir /

Al

tc5O

8R3Q1387

ORIGINAL(Red)

inter-office memorandumTO: -/Walt Leis, Sr. Geologist DATE: ] August

Don Phoenix, Manager, Life Systems Department

FROM: Peter KloseEdward SimekKurt Phillpp (Life Systems Department)

SUBJECT: June-1978-BIological Assessment of Army Creek W. O. No.: 463-20-01

Introduction:

The ninth biological assessment of Army Creek and Army Pond was conducted during theweek of June 19-23, 1978 by the field team of P.N. Klose, Ph.D., E.M. Slmek, andK.R. Phillpp, The purpose of this study was to assess the general biological healthof the Army Creek aguatlc system and its immediately bordering terrestrial components.Survey methods used included: a visual reconeissance of the creek and pond fromRoute 13 to the railroad bridge below the pond outlet; water quality analysis in thepond via various portable Instruments; seining fish in the outlet stream at the weir,in the pond, and in the Inlet stream; and collection of benthic stream insects belowthe pond outlet.

The survey of terrestrial vegetation and wildlife included the top of the landfill,the southern bank of the landfill on Army Creek, the woodland lining the reed-cattailmarsh above the weir location, and the woodland surrounding the inlet stream.

The overall visual status of the aquatic system is about the same as that foundduring previous studies with the exception of greater amounts of red precipitate nearwell outfalls and a 6 to 811 lower water level In the pond. It Is important to notethat Army Pond is a shallow, heavily sedimented, and highly eutrophic body of water.Major improvements in its biological condition should not be expected.

However, the most notable feature of the pond was the lower water level this year.During the 1977 stu y, the sampling boat was launched at Station 2 in about 8" ofwater, whereas thls^year that area was a mud flat. The lower water levels are dueto the low elevation of the discharge stream which was put in two years ago.

Results of Field Study:

Water Quality - The common water quality parameters of dissolved oxygen, conductivity,pH, and temperature were taken from samples collected during the field sampling.Conductivity and pH were read Immediately after returning to the Weston labs, the D.O.samples were fixed ?n the field and a WInkler titratfon performed in the lab; temperaturewas taken in the field with a mercury thermometer.

R3QI3

RFW: 2-74-39

(Red)June-1978-BlologIcal Assessment of Army Creek -2- 1 August 1978

Water quality results are as follows and correspond to the stations on the locationmap (Figure 1):

Station # Temp. C

1 18.13 19.24 19.75 19.96 19.6

pH Conductivity(umhos/cm)

7.06.86.97.06.8

220285 '245290290

D.O.mg/1

8.27.56.36.44.6

Total-Pmg/1

.18

.10

.09-09.20

Total -Femg/1

. 2.056.033.253.524.73

In addition to the usual water quality .determinations, total-phosphates and totalIron were analyzed at all five stations. Iron was analyzed due to the high Inputfrom the wells while phosphate might give indications of nutrient loadings.

Results of the water quality studies indicate no major changes In pH, D.O., andconductivity as compared to past surveys. Conductivity increases somewhat In thepond, most likely due to the pumped leachate, which has increased during the pastyear due to various well-cleaning activities. Total phosphate was relatively highin the Inlet stream (.18 mg/1). The levels in the pond decrease to .09 mg/1 butincrease again in the vicinity of the outlet stream to 0..20 mg/1. These levelsare not unusually high for a very "rich11 system such as Army Pond (McKee and Wolf,1963)*, but do help to contribute to algal productivity and, thus, water turbidity•and eutrophlcation of the pond.

Iron levels are relatively high in the pond and increase about two-fold from theinlet to the outlet. These higher levels are undoubtedly associated with the puroedleachate and the fact^that not all of the iron is precipitated as ferrous hydroxide.McKee and Wolf (1963) report that levels of 1.0 mg/1 Impart an off-taste to drinkingwater but levels 2 to 6 mg/1, such as those found, have no adverse effects on aquaticbiota other than the formation of precipitates which could cover benthic habitats.

Two readings of turbidity were taken (Stations 3 and 4), with resultant values of21 and 2$ JTU. T-hese levels are somewhat higher than would be expected for a smallpond and are caused^by suspended sediments, algae, and possibly, iron floes.

June 23 - Fish ^*.

Aquatic Biota - Fish collections were made on 23 June at Stations 3, 4, 5, and 6(see Figure 1 for Station locations). Collections were made using a 25 foot,3/8" mesh seine. All fish were Identified and returned to the water. No attemptat quantifying the fish populations was made.

McKee, J.E. and H.W. Wolf, 1963.- Water Quality Criteria. The Resources Agencyof California, State Water Resources Control Board, Sacramento, CA. 5^8pp.

R30I389

ORIGINAL /(Red)

R30I390

June-1978-BIoloqlcal Assessment of Army Creek -4- ' M » i ] August 1978———— ———————————————————————————

The list of species found and the Stations where they occurred Is presented asTable 1. In general, fish populations In and just downstream of Army Creek wereas abundant or diverse as during previous collections. Carp, blueglll, and catfishwere by.far the most Important species.

Seining at Station 6 near the flood gate to the river produced numerous fish ofseveral species. Two of these, the sucker and killlflsh, were not collected atany other stations. At Station 5, fewer individuals were collected, belonging tofive (5) species. At Stations 3 and 4, both the numbers and types of individualswere quite low. Although several juvenile carp and catfish were observed, whichwould Indicate conditions suitable for reproduction of at least some species, someof the large adult crapptes and carp that were collected had open red sores ontheir dorsal and lateral surfaces. The occurrence of these sores may be related toa water quality problem, but no direct link can be made because of the limited amountof data available. Further observations of these conditions would warrant an inten-sive water quality and microbiological Investigation followed possibly with a limitednumber of bloassays.

Benthic macroinvertebrates were sampled via a kick-net In the outlet canal (Station 5)as was done In September 1977- The following types of aquatic insects were collectedIn two separate samples:

Ollgochaeta - segmented wormsTrichoptera - caddisf1lesChtronomidae - midges

In addition to the low number of species found, the number of Individuals was smallalso. This fact, In addition to the low numbers and diversity observed in the fishpopulations, indicate possible water quality problems associated with the pond.Turtles were observed along the shore and on logs. As none were captured, we assumethat the same species are present now as in the past, I.e., the eastern paintedturtle, Chrysemys picta and the eastern mud turtle, Kinosternon subrubrum.

Summary - It is clear in comparing the Fall, 1977 biological study with the abovedata that biological conditions have changed somewhat for the worse. Severalphenomena are revealed: (a) fewer fish and less diversity, (b) fewer aquaticInvertebrates and less diversity, (c) lower water levels and Increased coverageof former water "surface by emergent vegetation, (d) numerous fish appearing withsores on their dorsal and lateral surfaces.

The cause for the fio'ted changes may be two-fold: (1) the concentrations of certainsubstances associated with the leachate (organtcs, metals, toxics) may have Increasedto damaging levels; (2) naturally-occurring population changes, such as lowinvertebrate and fish numbers due to the summer season. Spring and Fall populationsare commonly larger.

Whether either or both of these factors are operating should be investigated by aFall survey of this year. If a substantially larger benthic Invertebrate population^revealing greater diversity, Is found In the Fall, this would help allay thethat water quality Is rapidly deteriorating. It is also possible that a greater

R D n i Q iU i v o u i w -- *

ORDINALTable 1 (£gc|)

Fishes Collected

Total number of species

Station CollectedCommon Name Scientific Name 3

Blueglll Lepomis macrochirus X X X X

Pumpkinseed Lepomls qlbbosus X X

White crappie Pomox i s annularls X X X

Kl 11 ifIsh Fundulus heteroclItus X

Shiner Notropls sp. X

White sucker Catostomus commersoni X

Brown bullhead Ictalurus nebulosus X X X X

Carp Cyprinus carpJo X X X

AR301392

OftiG/KALJune-1978-BlologIcal Assessment of Army Creek -6- (Red) 1 August 1978

diversity of fish will be found as immigrants from the Delaware River in theFall. The problem of infective sores on fish would have to be addressed by aseparate, detailed study, If such Is warranted by the county.

Terrestrial Vegetation - Major vegetation patterns are as shown in Figure 1,with the exception that recent stream bed channelization disturbed vegetationalong each stream. Channelization has been performed on small tributaries at thewest end of the landfill and on Army Creek from the pond to the old location ofthe weir. Table 2 presents plant species identified on two previous surveys withthose-addltlonal species found as dominant cover on the current survey.

On the surface of the landfill the most marked change in vegetation is thesuccessive spread of woody plants from wooded edges toward the center of thelandfill. White pine, fire cherry, black locust and sumac remain the most dominantcolonizers of the grass area. White pines along the southern edge continue to showvery good growth, now reaching 4 to 8 feet In height. Dwarf huckleberry, sassafrass,sycamore, black willow and multiflora rose are less common colonizing species.

At this time In early July ryegrass, by far Is themost prevalent ground cover overthe entire landfill. Dense patches of rabbit foot clover, bracted plantain andragwood also occur throughout the surface of the fill. In "some areas along thesouthern bank of the landfill, Virginia creeper appears to be replacing Japanesehoneysuckle. Wet surface water lens areas continue to support dense thickets ofreed and cattail, with rushes and sedges occurlng here and there In shallow water

Arrowhead and arrowarum remain common submergent plants In shallow areas of ArmyCreek. However, Towering of the pond water level has resulted In extension ofshoreline cattails, mud plantain, rushes and sedges onto previous open water areas.

Only one leachate seep area at the west end of the landfill was visually active.Reed, cattails and goldenrod seemed to be having difficulty growing where newleachate had spread. Leachate odors detected along the southern edge of the land-fill seemed to Indicate more active seeps although none were located.

Terrestrial Wildlife - Birds and mammals (or their signs) observed during thecurrent survey are shown In Table 3- Observations were made during early morninghours on two nonconsecutlve days.

Many conxnon yea-r-round resident birds of the area such as mourning dove, songsparrowfcrpw and fclue jay were evident. Migratory summer residents Includingyellowthroat, In o bunting, cattle egret and rough-winged swallow were alsoabundant. Both pheasant and quail were observed in grass and reed areas of thelandf.111. Observations of great blue heron, little blue heron, great egret andkingfisher feeding all along the pond suggest that abundant forage fish In thepond provide good feeding habitat for these birds. The early morning hours of thesurvey may be the reason why only one raptor, a Kestrel, was seen. Such raptorsmost often utilize convective currents that develop latter in the day.

AR30I393

OltfGlSAL2

Vegetation

Common Name

Woody Plants:

White pine - Ptnus strobusMockernut hickory Hicora aibaPignut hickory Hicorai gla_brjiBlack wi1 low Salix nigraBeech Famous grand!foil aWM te oak Quercus alba:Black oak Quercus velutlnaRed oak Quercus rjbraChestnut oak Ouercus montanaWI 1 low oak Quercus oheljosTulip poplar Liriodendron tullpiferaiSycamore • Platanus occijentalisFt re cherry Prunus pennsyIvanTaBlack locust Rob i n t a pseucoacaciaStaghorn sumach Rhus hi rtaRed maple Ac_eg rub rumSt Tver maple Acer sacenarTnutnDogwood Comus f_1_Qrvqa_Sweet gum Liouidambar styraef^fluaTSptce bush L J nde ra senzo inViburnum Viburnum sentajcumJapanese honeysuckle Lonjcera JAQQn i caGreenbriar Smllax so.Wild rose Rosa multiflora

Herbaceous Plants:Reed Phraomttes epmmuriLSCattail Tyoha latifoMaCommon ragweed Amorqsla arremisi ifoliaGolden rod Sol idaco so.Asters Aster sp.TIckseed sunflower Sidens oolvlcoisPartridge Pea Cag sjaii fascicujata^Clover , Lssoedza sp.Crafagrasi Dloitaria saneuinalisJiodding foxtail Setaria faberiRabbits foot"grass Polvoogon monsoelienslsPurple lovegrais Eragrostis speetataillsNeedlegrass Aristida sp.Mud plantain Heteranthera reniforrntsArrowhead Saaittaria sp.

Supplement - July 1978Dwarf huckleberry Gavlussacia dumosaYellow sweet clover Melilotus officinalisRabbit-foot clover Trifolium arvenseDaisy fleafaan* Ericeron annuusBracted plantain Plantaoo aristataTimothy Phleum pratenseBroomsedge Androoogon vi rginieusBulrush Scirpus acrovirensYardrush Juncus tenuisSedge • Carex stioataVirginia creeper Parthenoefssus aulnouefoliOrchard grass DactvMs c 1 cWrataRye grass Lolturn perenne

Table 3 f.i

Birds and Karma Is

Birds

Black duck Anas rubrToesAmerican kestrel Fajcp soaryerijjsBobwh I te CoMnus. vi rgtn L.i.anus,Ring-necked pheasant Phas i.anus colchicusCattie egret Bufau 1 cus. 'bisGreat blue heron Ardea he rod i asGreen heron Sutorides vi fescens,tittle blue heron Florida caeruleaGreat egret CjSfnerpdius albusBlack-crowned night heron Nyct ico_rax_ nycticoraxGlossy ibis Plegadjs falcinel lu_$KTlldeer Charaorius vocrferjsSpotted sandpiper Actitjj maculariaMourning dove ZsnaHgura nacrouraRock dove (pigeon) Columba 11v_j_*Chimney swift Chaetura selaotcaBelted kingfisher M.egace"r'/1e ajc*/ojiYellow-shafted flicker C_g_la.p_tgs aura tus.Downy woodpecker Oendrpcooos a u be scansEastern icingbird Tyrannus^ tvrannusBank swallow Rioaria rjjjarjRough-winged swallow Stelgj.ijootervx pjf icol 1 isBlue jay CvanoeTtta cHstataCommon crow Corvus brae hyrti vne : ho sMockingbird Mimus .DO I vg lottosCatfalrd Dumete ] 1 a carol inensisBrown thrasher toxojjbma rufumRobin _ tu rduT fnrgrator[usStarl ing Stumus vulaarfsYe 1 low warbler DendrQJcaYellowthroat Geothlyois trichasRed-winged blackbird Aae 1 a jus phoen i ecusCommon grackle Qu i s ca 1 us aujscu laCardinal Rlchmondena cardinal IsIndigo bunting Passerina cygnearAmerican goldfinch Soinus tristisField sparrow Seize 11 a ousi 11 aSong sparrow Heiospiza rrelodla

Meadow vole MlcrojCus oennsy l van i eusMusk rat Ond_a_tra zibethicaRabbit SylytJagus fJo/iganys^Woodehuck Mamota .-ronaxRacoon Procygn lotor

Reotiles

Fowlers toad 8ufor woodhgusei^ fawlerLEastern painted turtle CHrysemvs pjctaEastern mud turtle Kinosternon sub rubrum

ar%Oif*iii i f) r\ P*AR30 i 395

ORIGINALJune-1978-Bioloq?cal Assessment of Army Creek -9- {Red} * August 1978

Investigation of bunchgrass areas uncovered.act Ive runways and nests of smallmammals most likely meadow vole. Numerous rabbits were flushed during the surveyand their signs were abundant. Active muskrat and woodchuck burrows were foundalong banks of the pond particularly at the eastern end. Raccoon tracks were foundalong channelized stream banks at the western end of the landfill. Fowlers toadswere seen on the landfill surface and turtles were seen on logs and banks of thepond. The most common turtles appeared to be eastern painted and eastern mud.

R30I396

ORIGINAL(fttd)

BIOLOGICAL ASSESSMENTOF ARMY CREEK

NEW CASTLE COUNTY, DELAWARE

Emil C* ZtefserProject Biologist

Kenneth J Salamon, Ph.DProject Ecologist

Michael v". Mel linger fProject Ecologist

March 1981

* " Prepared byROY F. WESTON, INC.

Weston WayWest Chester/ Pennsylvania 19380

B301397(

TABLE OF CONTENTS

(Rsd)

INTRODUCTION 1

AQUATIC COMPONENT . 1

Methods 1Results 3

TERRESTRIAL COMPONENT 9

Methods 9Results and Discussion 9Wildlife 14

R301398

(Red)

BIOLOGICAL ASSESSMENTOF ARMY CREEK

INTRODUCTION

The tenth biological survey of Army Creek and Pond wasconducted on 16 October 1980. The purpose of these on-going studies is to assess the status of the aquaticand terrestrial components of the Army Creek ecosystem.No attempt was made to quantitatively analyze alterationsin the biotic communities. Qualitative evaluation isbased on species richness and water quality analysis.

AQUATIC COMPONENT

MethodsA 14-foot boat was used to survey Army Pond. Waterquality parameters were measured at five sampling sites(Figure 1} using portable field instruments* Temperature,pH, conductivity and dissolved oxygen were measured usinga Martek Mark V Water Quality Analyzer. Dissolved oxygenbottles were filled at the survey sites and cooled. Laboratory analysis for dissolved oxygen was performed and themeasurements compared with instrument controls.

The fish population was sampled fay electrofishing witha Smith-Root series VII backpack electroshocker, operatedfrom the boat* Stunned fish were netted, identified andimmediately returned to the water.

Plankton samples were collected throughout the pond usinga one-half" meter plankton net pulled behind the boat.Organisms wore rinsed from the collection apparatus andpreserved i»»jsample bottles with formaldehyde.

ir -Plankton samples were centrifuged to concentrate theorganisms* Organisms were identified to the lowestpractical taxa using a compound microscope.

Bottom sediment was sampled at the five water qualitystations with a messenger-operated ponar grab. The pondmud was sieved through a 500 mm mesh bucket. Samples weretransferred to collection bottles and preserved with for-maldehyde.

AR301399

-2-

n't* ,*%»}>;

Rose bengal was added to the sediment samples/ stainingthe living organisms. Samples were washed through 500jim and 63 ym mesh sieves to eliminate the finer clayfraction, Benthic invertebrates were sorted from thesediment and identified to the lowest practical taxa.

Results

Table 1 presents the results of the water qualityanalyses .

Little variation in the parameters measured was observedbetween the sampling stations. Water temperature variedslightly with depth. A decrease in pH was observed atStation No. 5. Conductivity measurements increased inthe east corner of the pond and at the outlet. Dis-solved oxygen values were similar/ with the exceptionof the inlet.

The fish in Army Creek move freely throughout the pondand site specific enumeration is unnecessary. The speciesidentified are presented in Table 2. Primary fishingeffort was made along the periphery of the pond sincefish are known to congregate in warm sheltered areas.

Bluegill and pumpkinseed sunfish were the most abundantof the fish species identified. Black crappie, Americaneels/ yellow bullhead and largemouth bass followed indecreasing order of abundance.

Plankton samples exhibited •• poor species richness. Thephytoplankton community was dominated by filamentous greenalgae and secondary by the blue-greens.

Two members of the zooplankton community were also col-lected - common invertebrate copepods and cladocerans,both members of the class Crustacea. Plankton speciesare presented in Table 3.

The upper lasers of the substrate of the pond was composedprimarily of Tight silt and clays. Few benthic inverte-brates were observed. Olegochaetes (segmented roundworms)dominated the few species found in the bottom sediment.Other organisms organisms included fly and midge larvae/nematodes {roundworms) and snails. The sandy sediment atthe outlet station also contained a fauna poor in speciesrichness. Several clams were found in addition to thedominant worms. The benthic invertebrates observed inArmy Pond are presented in Table 4.

-3- .

Table 1

WATER QUALITY ANALYSES

DissolvedTemperature Conductivity Oxygen

Station (°C) pH (ymhos/cm) (mg/1)

1 (inlet) * — — — 8.92 20.0 7.2 260 7.93 17.5 . 7.2 250 7.94 18.6 7.2 320 8.15 (outlet) 19.1 6.6 330 8.0

•AInsufficient water

R3-OU02

-4-

~

Table 2

FISH SPECIESARMY POND

Common Name • Scientific Name

Bluegill Sunfish Lepomis macrochirusPumpkinseed Sunfish Lepomis gibbosusHybrid Sunfish Lepomis sp.Carp Cyprinus carpioAmerican Eel Anguilla rostrataBlack Crappie Ppmoxis nigromaculatusYellow Bullhead Tetalurus natalisLargemouth Bass Micropterus salmoides

R3QIUO

-5-

Table 3

PLANKTON

Phytoplankton: Chlorophyta - Oedogonium sp. V. Filamentous- Spirogyra sg. >Aigae

Cyanophyta - Oscillatoria sp S

Zooplankton: Daphnia sp. - Water FleaCyclopoiT"Copepod

-6-

Table 4

BENTHIC 3JNVERTEBRATES

Tax a Common Name

Oligochaeta Segmented roundwormsDiptera larvae - Flies/ mosquitoes & midges

Chironomidae Midges .Nematoda Unsegmented roundwormsGastropoda SnailPelecypoda Clams

RSOf^OS

-7-

Results of the Army Creek water quality study show littlevariation within the pond. Differences in temperature area function of solar warming relative to sampling time/ depthand related degree of shade'or overhanging trees. The pHvalues are relatively neutral, with the exception of theoutlet sample. Retention time in the eastern end of thepond with associated buildup of organics may be responsiblefor the acidic trend in pH. Conductivity-values show abimodal relationship between western and eastern sectionsof the pond. The slight increase in conductivity observedfrom inlet to outlet is most likely due to the addition ofiron oxides and dissolved salts from landfill seepage andpumped leachate. Dissolved oxygen concentration was nearsaturation at each of the sample locations. The higherinlet value may have resulted from the aerating movementof the stream. The relatively high pond values are mostlikely the result of photosnythetic activity by algae.

Sunfish were found to be the most abundant fish species.This is a common condition of most small ponds due to theirlimited ecological requirements and high rate of reproduc-tion. In addition, few natural predators (e.g. largemouthbass) are present. Carp/ also/ are relatively ubiquitous,feed at any trophic level and adapt well to poor conditions.Although second in relative abundance, the carp representthe greatest pond biomass.

Two new species were found during the survey as compared toprevious surveys: the american eel, Anguilla rostrata; andthe largemouth bass, Micropterus salmoictes. Bass are gener-ally acknowledged as being intolerant olr polluted waters.Their presence in the Army Pond community and presumedspawning in this water body, is*a notably positive aspectof the pond water quality, as is the migration of eels intothe pond system. The other fish species observed in ArmyPond were found during previous surveys, and their con-tinued presence and reproduction is noteworthy.

The filamentous green algaes - Oedogonium sp. and Spirogyra sp.are commonly»found in colonies on the surface of the ponds.In eutrophic waters such as Army Creek, dominance by a blue-green algae auch as Oscillatoria is indicative of poor waterquality.

Copepods and cladocerans are ubiquitous among zooplankton,and provide a source of food for small vertebrates.

flR30IU06— 0—

The heavily silted bottom mud contained few invertebrates;low diversity is expected in such sediments; particularlyif occasional deoxygenation occurs. Oligochaetes are avery pollution tolerant species and commonly dominate suchhabitats.

Comparison of the present survey with the previous study inAugust 1978, shows little change in biological conditions.Water quality measurements indicate no significant changesduring the intervening years. Fish populations are quali-tatively similar; however, the previous survey observed soreson numerous fish. All individuals collected during this studyappeared to be healthy and no sores were observed.

Based on the above findings, little or no change appears tobe occurring in either the physico-chemical or biologicalaspects of Army Pond. Water pH, dissolved oxygen, and conduc-tivity, are well within the standard range for small ponds.In addition, the apparently successful fish reproduction andfairly diverse community are indicative of relatively goodwater quality. Potentially toxic components such as ironoxides and. certain dissolved salts were not measured, buttheir occurrence is presumed to be below threshold levels.The dominance of blue-green algae is indicative of grosseutrophication; however, this condition would be expected insuch a small, shallow system with high nutrient imput.

Methods

The Llangollen Landfill area was divided into two basiccomponents: (1) the banks and edge of the Army Pond/ and(2) the landfill proper. The smapling survey consisted ofa walking tour of each area* Vegetation and wildlife specieswere recorded by name and location. The successional trendon the landfill was evaluated. It was assumed that the majortrees were -yje same as recorded in previous studies; therefore,the major effort was centered on shrubs and herbaceousspecies.

Results and Discussion

The site can be divided into two general areas (Figure 1):(1) the Army Pond area including the pond and stream banks,and (2) the landfill. Both areas are susceptible to distur-bance by human activities, but no major disturbance has s pon I 1*0 7

HttUw I *T V /

-9-

occurred since the 1978 survey. Therefore, the majorityof the tree species that inhabit the more mature woodedareas near the landfill are still present (Table 5).

The vegetative changes that have occurred are of two types;(1) changes in herbaceous and early successional woodyspecies along the pond banks/ and (2) the continued changesin successional series on the landfill. The southern bankcontains a lesser number of individuals and species as com-pared to the northern bank. Several herbs are currentlypresent that were not there before, or only in small amounts.Silver maple, tulip poplar, black willow, sycamore, firecherry, black locust, smooth alder, and sumac, dominate theoverstory; while daisy fleabane, wild!, grape, pokewood,goldenrod, wild rose, yarrow, arrow-wood, and Japanese honey-suckle, constitute the understory.

The northern bank contains a greater amount of woody species.It is a wider area than the southern bank. Species observedhere included fire cherry, silver maple, quaking aspen, bitter-nut hickory, white oak, black oak, willow oak, sycamore,sweet gum, black locust, tulip poplar, and black willow. Theunderstory was mainly arrow-wood, wild rose/ and Japanesehoneysuckle. There were less herbs present due to the moreclosed canopy and less open space. The understory speciesalso overlap into the open landfill area, more so along theborder between the bank and field, but also occasionally onthe field, - -

The pond borders contain populations of common reed, cattailsmartweed, arrowhead, and algal species. The western end ofthe pond is an open wetland with cattails on the southernside and reed on the northern. These two species generallyoccur as isolated clumps with little intermixing. The sectionof Army Creek, east of Army Pond, is a narrow, rock-bottomstream surrounded by fire cherry, silver maple, arrow-wood,and other riparian species.

The landfill epresents the area of greatest vegetativechange. The*area is going through the successional processfrom an open field to a woods. Currently, the area is betweenthe old field-shrub sere.

-10-

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The herbaceous species of the old field sere still dominate thearea. Several grasses, such as purple lovegrass, foxtail andcrab grass, and wildflowers, such as daisy feabane, goldenrod,and ragweed compose the majority of the species (Table 1) andcause seasonal shifts in species dominance. Woody species suchas sumac and black locust are continuing to colonize larger andlarger areas. An occasional black willow occurs in any slightlylow areas while fire cherry has established small populations.White pines appear only as isolated individuals near the northernbank except in one locale where several individuals are grouped.A new species to colonize the landfill is red cedar as a fewisolated individuals about 4 - 61 tall were observed. If leftundisturbed, the landfill presents a good opportunity to studyand record the successional development of a piece of landtypical to northern Delaware.

*Wildlife

Although the weather during the sampling period was hot andsunny, few wildlife species were observed (Table 6). Crowswere the most common birds observed. A small flock of chimneyswifts, an American kestrel and several cardinals were the onlyother species recorded. No herons or egrets were observed usingthe pond area. Summer residents have left by the sampling date(16 October) and fall migratory species possibly have not beguntheir southern migration. Rabbits were common on the landfill.Small mammal runs were abundant under the herbaceous cover onthe landfill. A local hunter indicated that deer are presenteast of Army Pond along Army Creek. Several small Easternpainted turtles were observed along the pond bank.

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BIOLOGICAL ASSESSMENT

OF ARMY CREEK

LLANGOLLEN LANDFILL

CONDUCTED

30 DECEMBER 1982

PREPARED BY

- ROY F. WESTON, INC.

WESTON WAYWEST CHESTER, PENNSYLVANIA

V Jv I U f f v f. 1_

TABLE OF CONTENTS

SECTION PAGE NO.

INTRODUCTION 1

Aquatic Ecosystem 1

Methods

Results and Discussion 3

Water Quality " . .. 3

Acjuatic Biota 6

Summary • 6

Terrestrial Ecosystem 8

Methods 8"

Results and Discussion 8

Landfill Area 8

Quarry Area 11

Wildlife 11

Summary 18

R*"i f*k I f i "730141 /*qr \& t * • *

LIST OF TABLES

TABLE NO. . TITLE PAGE NO.

1 Llangollen Landfill Water Quality 4Analyses 30 December 1982

2 Benthic Invertebrates Collected 5From Army Creek 30 December 1982(in order of observed abundance)

3 Fish Species Collected From Army 7Creek 30 December 1982(in order of observed abundance)

4 Woody Plants 9

5 Herbaceous Plants 12

6 Reptiles and Mammals 14

7 ' Birds 15

FIGURE

FIGURE NO* TITLE PAGE NO.

1 Vegetation Map - Llangollen Landfill 230 December 1982

11.18

BIOLOGICAL ASSESSMENT

OF ARMY CREEK

INTRODUCTION

The eleventh biological survey of the Llangollen Landfillwas conducted on 30 December 1982. The purpose of thissurvey was to monitor the aquatic and terrestrial com-ponents of the landfill ecosystems. No quantitative analysiswas attempted, but rather included a qualitative assess-ment of the biotic communities present. A comparison ofthe present survey data with that of previous studies musttake into account the seasonal variability within theecosystems.

AQUATIC ECOSYSTEM

Methods

Water quality parameters were measured at five sites inthe landfill pond (Figure 1). Temperature, pH, conductivityand dissolved oxygen were obtained using precalifarated fieldinstruments, 500 ml polyethylene sample bottles preparedwith preservative acids were filled, cooled, and returnedto the laboratory for total iron and phosphorus analyses.

The fish population was sampled by electrofishing. Electro-fishing was conducted from a 14f boat using a Smith-RootSeries VII backpack electroshocker. Fish were collected,identified, and returned to the water unharmed.

Benthic samples were randomly collected using an Eckmanbottom grab. Sediment was transferred to sample bags,diluted with pond water, stained with rose bengal and pre-served with formalin. Laboratory analysis included sievingthrough 500 fhid 63 micron mesh screens. Remaining organismswere sorted fed identified by major taxa.

-i-

RESULTS AND DISCUSSION

Water Quality

Table 1 presents the results of the water quality analyses.Water temperatures ranged from 5.0° - 8.4°C. Surface"skim" ice extended approximately 20' from the shoreline.The pH ranged from 7.6 to 6,9 with the lower values recordedat the downstream stations. These values are well withinthe normal range for a small impoundment of this type.

The specific conductance values are also typical. Valuesranged from 80 - 270 ymhos. Dissolved oxygen levels rangedfrom 8.9 to 14.4 ppm generally saturated by the cold watertemperatures.

Laboratory analysis for total phosphorus in Army Creek rangedfrom 0.024 to 0.066 mg/Jl, increasing the nutrient load to thepond. Excessive growth of algae was observed, and is knownto develop in lakes where the average concentration of phosphorusexceeds 0.01 mg/£ (Sawyer, 1948).

Total iron concentrations ranged from 1.75 - 3.45 ppm, con-siderably lower than values recorded for the Llangollenmonitoring wells. Leachate possibilities include ferricoxide precipitated beneath the recirculation pumps alongthe pond periphery/ and surface seepage from the slopesbetween stations 3 and 4. Settled iron precipitate athigh concentrations may impact fish eggs and benthic organ-isms utilized by fish. In addition, the deposition of ironhydroxides on the gills of fish may cause irritation andpossibly block respiratory channels. Although 1.0 mg/ihas been established as the limiting criteria for managementof freshwater aquatic life. (EPA, 1976), no impact from thissource was observed. Ellis (1973) found that in 69 to 75study sites with good fish fauna, the iron concentration wasas high as 10 mg/£,

Benthic invertebrates showed little species diversity orevenness. Table 2 presents organisms sampled from the ArmyCreek survey sites, listed in order of observed abundance.Only pollution-tolerant forms, dominated by oligochaetes,were found, * nthic organisms were found in associationwith specif ic stibstrate types, with gastropods and pelecypodsmore prevalent near the inlet and outlet (pebbles and sand),and other taxa prevalent at' sites 2, 3 and 4 (silt detritus).Sawyer, C,N.i 1948. Fertilization of Lakes by Agricultural

and Urban Drainage. Water Pollution Abs. 21.E.P.A, 1976. Quality Criteria for Water. U.S. Environmental

Protection Agency. Washington, D.C.Ellis, M.M. 1937. Detection and Measurement of Stream Pollution.

Bulletin, U.S. Bureau of Fisheries 48:365.

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Table 2

Benthic Invertebrates Collected

From Army Creek, 30 December 1982

(in order of observed abundance)

Common Name Taxa

segmented roundworms Oligochaeta

snails Gastropoda

clams Pelecypoda

roundworms Nematoda

midges Diptera

leeches - Hirudinea

AR30IU23

-5-

AQUATIC BIOTA

Fishing effort was concentrated along the periphery of thepond where fish collection was most efficient. Site specificenumeration is unnecessary since fish move freely throughoutthe pond. Table 3 presents fish species collected duringthe survey, listed in order of observed abundance.

The pond supports a relatively diverse fish fauna. Five ofthe eight species observed are classified as sport fish.Most of the fish collected were juveniles or early adult(< 3 years). Stunting, although not quantitated, is mostlikely occurring. Based on the number of young-of-yearobserved, spawning, particularly among sunfish, is prevalent.No indication of disease, parasitism, or excessively poorcondition among the fish species was noted.

SUMMARY

Based on this data, the aquatic ecosystem of the Llangollenlandfill site appears to have undergone some change sincethe previous surveys. Most obvious was the increasein algal growth (possibly a function of season), showingincreased eutrophication. The ranges of water qualityparameters examined were similar, except for the seasonaltemperature differences. Comparison of the total phosphorusconcentrations with water quality samples from 1979 weresimilar. Total phosphorus ranged from 0.02 mg/Jl - 0.09 mg/Jlin 1979, while current samples ranged from 0.02 mg/Jl0.07 mg/£ . Total iron samples, on the other hand, showeda small decrease ranging from 2.05 - 6.03 mg/£ in 1979,to 1.73 mg/i - 3.45 mg/£ in the present survey.

Fish species occurrence is also similar to that of theprevious survey (October 1980). Sunfish, the dominant speciesof both surveys are represented primarily by young-of-year.Other species noted were also observed in both surveys, andin relatively similar size ranges. The habitat is generallyconducive--to centrarchid (bas.s, sunfishes) spawning, andalthough not ideal growth/maintenance habitat, can be expectedto provide equate food and protection for a populationlimited in feoth individual size and abundance.

f - **;

Table 3

Fish Species Collected

From Army Creek, 30 December 1982

(in order of observed abundance)

Common Name Species Name

bluegill sunfish Lepomis macrochirus

pumpkinseed sunfish Lepomis gibbosus

American eel Anguilla rostrata

carP Cyprinus carpio

black crappie Pomoxis nigromaculatus

white sucker Catostomus commersoni

smallmouth bass Micropterus dolomieu

largemouth bass Micropterus salmoides

AR3QU25

-7-

TERRESTRIAL ECOSYSTEM •'. -;

Methods

Qualitative observation of the Llangollen landfill began witha preliminary drive-through of all passable roadways tonote vegetative zones and to identify representative areasfor closer observation. This resulted in observation ofseven north-south transects in the northern portion of thelandfill, as well as along the entire length of the roadwayin the southern portion (Figure 1).

The primary goal of these observations was to characterizevegetative patterns near the landfill, to record wildlifeobservations, and to observe any disturbances/disruptionsin the landfill ecosystem. Indirect observations, such asthe presence of animal tracks, scatrdens or nests; and leaflitter, and-seeds were recorded.

RESULTS AND DISCUSSION

Landfill Area

The only noticeable recent disturbance was refuse dumping(roofing shingles, bottles, metal scrap, and brush cuttings)in a few isolated areas. Vegetative cover wasvvirtuallycomplete over the entire landfill area (Figure 1). Therewas only one small area, roughly in the center of the site,that had some bare spots. This was in an area dominatedby low-growing grasses.

Vegetative changes since the last survey appear to be due tonatural succession. There is an increase in woody plantgrowth-in the open areas, with no noticeable mortality amongthese individuals. Topography and associated soil-moistureconditions are the primary influences on the pattern ofplant colonization. Low areas with standing or near-surfacewater were predominantly covered with reed grass and somecattails. Several woody plants (Table 4) tolerant of wetconditions (sumac, black willow, locust, maple), were alsofound in these areas. The mid-region of the landfill supportsadditional shjrubs and trees such as: cherry, oak, sycamore,sassafrass, gweet gum, dogwood, redbud, red cedar, and whiteand pitch pine's (Table 4). These are most likely a resultof seed dispersion from the trees along the pond bank.

The steep-banked pond areas support woody growth thatincreases in variety and age in the westward direction(Figure 1). . In addition to those species found in thelandfill area, the banks also contain hickories, poplars,and beech (Table 4).

-8-

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-10-

1 C d)The ground cover/understory species composition appears tohave changed little since the previous survey (Table 5).The same species continue to inhabit the landfill, with.some inward encroachment of brush (multiflora rose, raspberry,grape and honeysuckle) from the pond bank.

Quarry Area

As shown in Figure 1, the region south of Army Creek Pondcontains several different zones:

• a bare quarried area

• dense stands of reed grass along portions of the• pond bank and in some of the quarried area

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• mature and near-mature woody growth along thepond bank

• mature forest at the western-most propertyboundary

The reed grass was the dominant feature of the old quarried-area. Young trees such as beech, cherry, locust, oaks, hickories,poplars, maples and sassafrass were also found in the area*The bank area, although narrow in width, supported a varietyof woody growth. Most trees were near maturity, with somereaching heights of 40 to 50 feet. The trees in this areainclude: syc4amore / sassafras s, poplars, beech, cherry, sumac,locust, hickories, maples and oaks. Certain bank areas alsocontained stands of reed grass. Understory growth alongthe bank included: honeysuckle, Virginia creeper, raspberryand multiflora rose. The western-most portion of this areacontinued to support the mature oak-beech-sweet gum standas described in the earlier surveys.

Wildlife

There were niroerous signs throughout the site indicating thatthe Llangolltfh" landfill supports a varied wildlife population(Tables 6 and 7), The quarried area, especially along thepond bank contained an abundance of deer tracks and scat. Thelandfill area was heavily traversed by small mammal runways,and burrow and den openings were evident in areas of topo-graphic variability. The entire site was strewn with shot-gunshells, suggesting some hunting activity.

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-17-

The following bird species were observed at the landfill r^r-^during this survey: pigeon, crown, red-tailed hawk,cardinal, blue jay, chickadee, mocking bird, starling, andsong sparrow (Table 7). Nests were also observed throughoutthe site, both in trees and in reed grass st«ands. Specieswere similar to the previous survey, despite seasonal differ-ences. There was no evidence of recent disruption of thesite's wildlife habitats.

SUMMARY

The terrestrial ecosystem of the Llangollen landfill sitehas changed very little since the October 1980 survey. Therewas no evidence of habitat loss, or of floral or faunal mortality.The only difference since the October 1980 survey was due tonatural successional processes. Several young colonizing treeswere found in areas that previously had only herbaceous groundcover. In addition, bare areas in the southern site area havebeen reduced by the influx of herbaceous growth. Based onindirect observations, site wildlife also has not changed sincethe October 1980 survey. There is no evidence of recent dis-ruption of the site's wildlife habitats. Overall, the Llangollenlandfill site continues to support an "old field." terrestrialecosystem typical for this geographical area.

-18-

APPENDIX M

AB30IW7

xSeptember 27,

REHABILITATION OF CONTAMINANT RECOVERY

WELLS BY CHEMICAL TREATMENT

ORIGINAL(Red)

;BLEMSeveral contaminant recovery wells near the Llangollen Landfill have lestpumping eff ici ency s i nee their installation. The reduct ion in pu.r.pingrates has been as much as 50 percent of the original capacity. Continueddecline in pumping rates w i l l affect the hydrogeological isolation of thel a n d f i l l by causing the gradual rise of the peizometric surface in theupper Potomac aquifer and hindering the efficient removal of contaminantsfrom the aquifor.

CAUSES

Some of the causes of declines in well production include the following:

(1) Continuous pumping of an Artesian aquifer may result in theconfining bed, resulting in water table conditions and sub-sequent loss of yield.

(2) cowering of the water level below the top of the well screenthereby causing cavitation at the pump intake and air entrap-ment about the screen.

(y, inefficient pump operation resulting from corroded, worn, orplugged parts,

£4) Incrustation along the well screen, in the gravel pack, andin the surrounding formation due to chemical precipitationfrom pressure changes and biological activity.

(5)"Failing of the well screen by mud and silt from adjoiningformations in the tlangollen area the chemical quality ofthe groundwater is poor and in a continuous state of change,alscf overpumping has resulted in dewatering the upper 'Potomacoqu1!F«r. All the above listed causes could conceivably in-'tcra£t to result in loss of well yields.' However, since thepumping rates have declined in tfie order of 50% in some cases,it can be-assumed that clogging at the well scjze'en due toincrustation is the primary cause*

flB30IU38

-2- September 27,

REHABILITATION OF PRODUCTION WELLS ,————————————— "' p.*)Treatment and rehabilitation of wells affected by incrustation may beapproached in tvio ways.' (1) Pulling the pump and (2) Treating the screenand pump in place. With the expense involved tn pump removal .and forinvestigation purposes, only treatment with the pump in place w i l l beconsidered here. For wells located in unconsol idated formations likethose in the Llangollen area, three methods of treatment are suggested:

(1) Treatment with polyphosphate salts and chlorine.

(2) Treatment with muriatic acid,

\y. A combination of the above.

A combination of mechanical surging and backwashing along with theapplication of chemicals is used to rehabilitate a well, by providingthe necessary agitation. The chemical composition of the encrustingmaterial determines the chemicals that should be used for well treat-ment. -Although the exact chemical composition of the encrusted materialis not known, the Llangollen wells are expected to be affected by irondeposits due to its high concentration in natural ground water and inJeschate from the landfill. Moreover at such high concentrations theiron, probably in a ferrous state, exists in colloidal form and metalorganic complexes. In such cases, treatment by use of polyphosphatesalts and muriatic acid is advised. Polyphosphate salts, such as Calgon,arc deff locculants and emulsifying agents that act as detergents whensurged in the well. They serve to break up and disperse soft iron de-posits such as iron complexes. Muriatic acid w i l l dissolve iron andmanganese oxides, hydroxides and carbonates.

PROCEDURES

In view* of the prices, proposed by Delmarva Drilling Company for treatmentof two wells, it is proposed that an experimental treatment of a selectedwell should be performed by New Castle County and Roy F. Weston, Inc.Recovery well KW-*» could be utilized for treatment. In addition to ex-pected rehabilitation of well RW-4, the experimental treatment shoulddet e rm i n«T 'whether : *

(3. Such treatment can be safely performed on a'"regular maintenance basis by County personnel.

(b) The nature of the encrusting* material wouldallow treatment with the well pump in place.

in order to evaluate the effectiveness of the treatment, controlled specificcapacity tests- should be conducted before and after treating the well. --RoyF. Weston personnel should run the pumping tests and supervise the treatment.The following procedure is recommended for the treatment of recovery wellRW-A-. •

AR30U39

-3- September 27,

(1) At a selected Friday morning, well RW-4 should be shut downand allowed to recover until the following Monday. Recoverydol= should be collected periodically by Roy F. Westonpersonnel,

(2) On Monday morning, a short duration pump test should beconducted by Roy F. Weston personnel.

(3) After the pump test, the pump should be shut down and restartedwith the discharge valve closed in an attempt to duplicate theoriginal pump curve. This w i l l aid in determining wear on thepump. The pump should then be shut off.

(4) Introduce into the well screen fay means of a plastic hose, a- premixed water solution composed of 30 Lbs. of polyphosphate

salt to every 100 gallons* of water in the well casing. An 8inch diameter vie 11 will hold approximately 2.55 gallons of«cter per foot. Thus, 30 pounds of polyphosphate w i l l benecessary per .40 lineal feet of water in the well. Mixingof the polyphosphate sa.lt should be done in small batches ina barrel. In addition, about 2 Lb. of a select bactericlde(Calcium Hypochlorite) -should be added to the well for eachtreatment.

(5) The well .should be surged and faackwashed for about k hours.This is accomplished by turning the pump on for 3 or kseconds every few minutes. No discharge of water shouldbe allowed during surging.

(6) The polyphosphate should be allowed to remain in the wellovernight and pumped out the next morning.

(£) Specific capacity should be compared to that prior to treat-ment. If sufficient recovery has not been realized acidtreatment should 'follow.

(8) A commercial grade (15%) inhibited Muriatic acid is used forfurther .treatment. «Added to the acid is a stabilizing agentand »<antifoam agent. The stabilizing agent prevents Vepre- »cipi-tirHon of gelatinous ferric hydroxide in the gravel pack \arid the ant f foam agent prevents overflowing of acid at thewell head. The acid should be introduced slowly to thescreen by means of a -plastic hose in an amount about 1.5 timesthe volume of water in the screen or about 25 gallons for aten foot screen in an 8 inch diameter well.

AR30IH9

RELOCATION OF LEACHATE RECOVERY WELLSArmy Creek Landfill

New Castle County, Delaware

INTRODUCTION

Obj ectlve- *

The objective of this report is to present the rationale levelopedin evaluating the concept of relocating the recovery wells such-thatleachate and contaminated ground water could be recovered moreefficiently,. The rationale is based on the analysis of the selectedhydrologic data and includes discussions on the following aspectsof the leachate recovery program:

o Backgroundo Leachate volumeo Ground water quantity and flow conditionso Ground water qualityo Incrustation and well rehabilitationo Relocation of recovery wellso Conclusions and recommendations

Although not included in the report, the present analysis hasdrawn heavily upon the experience gained by review and analysis ofthe extensive data base gathered during the last four years.Analysis of the data would indicate that the distant recovery wellscontinue to pull the contaminants to their present locations. Toprotect the aquifer from continued contamination, it will be necessaryto contain leachate as close to the landfill a_£ possible and controlits further dispersion. This could be achieved by relocating therecovery wells as indicated by the discussions presented on differentaspects of the leachare recovery program.

Background

The Army Creek Landfill is situated in-New Castle County, Delaware(See Figure 1) .* The landfill was constructed in a worked-out sandand gravel pit riiich received approximately three million cubicyears of municipal and industrial wastes from 1960 to 1968. In _1972, it was discovered that leachate from the landfill had "the underlying confined aquifer in the Potomac Formation «tndcontaminated a nearby domestic well. Roy F. 'Weston, Inc. (Weston)was then retained by New Castle County to define the problem andpropose potential solution(s).

AR30UU

Preliminary hydrogeologic investigations conducted by Weston indicatedthat the leachate had contaminated a substantial volume of thePotoiaac aquifer and it was moving in the direction of the ArtesianWater Company's wellfield both in reponse to natural ground watergradient and due to pumping effects of the Artesian wellfield. Thenearest Artesian Water Company well was located about 1600 feet fromthe edge of the plume of contaminants*

Based on preliminary hydrogeologic investigations, a contaminantrecovery and monitoring program Was designed and implemented as aninitial step towards ev tual solution of the problem, tte recoveryprogram was designed to achieve the following objectives"

D To control the migration of contaminants towards ArtesianWater Company's wells and to contain them in an area closerto the landfill.

o To create a ground water divide between the Artesian well-field and the contaminanted zone such that the ground waterflow in the contaminated zone is reversed and the contaminatedground water moves towards the Army Creek Landfill.

c To recover contaminated water and restore the aquifer waterquality.

o To monitor the water quality and water levels in the area andevaluate the effectiveness of the recovery program.

o To develop feasible leachate treatment and disposal methodsuntil some type of permanent solution to the problem isdetermined.

As a result, a large number of observation and recovery wells wereconstructed* While the observation wells were constructed in boththe shallow Pleistocene sediments and the underlying Potomac aquifer,the recovery wells were constructed only in the contaminated zone ofthe Potomac aquifer, the recovery wells were constructed only in thecontaminated zone of the Potomac aquifer, which is the win source ofwater supply"." Pumping tests were conducted on the recovery wells.Data collected vere analyzed to determine the hydrologic propertiesof the aquif erf* interference between the wells, production rates ofthe recovery w Lls, potential for recycling the contaminants pumpedif discharged into Army Creek and the quality of the ground waterin the area..

The basic concept in selecting locations of the recovery wells wasto locate them such that the contaminant plume would shrink northtowards the landfill; then utilize only those recovery wellslocated closer to the landfill, when the ground water quality hasbeen improved and eventually restored in areas or at locations distantfrom the landfill. It was recognized at the outset that:

o The volume of leachate will be minimized if itcould be intercepted within and immediately beneath the landfill;

- jro The area covered by the landfill is small comparef to the

areal extent of the cone of depression formed in "response toArtesian wells pumping;

o The volume of water (rainfall falling directly on the landfilland laterally entering the landfill) that will potentiallybecome leachate, would also be small compared to the totalvolume of water that is available in the aquifer in this drain-age basin and» which is used by Artesian Water Company;

o Leachate will be highly concentrated within and beneath thelandfill and, therefore, its treatment -and disposal could potentiallypose problems if intercepted within the landfill;

o The distant wells will continue to pull the'contaminants fromthe landfill to their present location or beyond, as long asthey are in operation;

o It will be necessary to locate recovery wells within the refuseand as close to the landfill as possible, to control andlocalize the migration of contaminants away from the landfill;

o Leachate collection and disposal will be .required to avoidground water contamination, as leachate production continueuntil, the refuse becomes inert or it is isolated from ground.. Jor surface water; • :

*•o The' recovery wells will experience periodic problems due- to * v

incrustation and mechanical breakdowns and will requireproper maintenance.

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The recovery program has been in operation for about four years.It has been effective in removing the contaminants at locationsdistant from the landfill and reversing the gradient of the con-taminant plume towards the landfill. Operation and monitoring ofthe recovery program has generated a substantial volume of hydrologicdata. The quality of ground water in an area south of the recoverywells RW-1, RW-3 and RW-5 has been improved. However, under theexisting conditions, the recovery wells will continue to pullcontaminants to them at their present locations. Since themain purpose of the recovery program has been to both re*ove con-taminants and control their migration, it is now appropriate toconsider discontinuing the use of the distant recovery wells &JL(RW-1, RW-2, RW-3, RW-A, and RW-5) and relocate them within-«fce closeto the landfill so that leachate recovery can be optimized.

LE&CHATE VOLUME

Based on previous investigations by Weston, it was estimated thaton an average daily basis, approximately 200,000 gallons of waterwould enter the landfill. This volume included approximately 50,000gpd of rainfall water falling directly on the landfill and about150,000 gpd entering the landfill as lateral'flow from north of thelandfill.

This volume of water would become leachate after passing throughthe refuse and would contaminate the ground water beneath and downgradient from the landfill. Depending upon the concentrations ofvarious chemical constituents, this volume of leachate couldpotentially contaminate a substantial volume of ground water whenallowed to mix with it. However, if this highly concentratedl&achate could be intercepted before it reaches the ground water,the volume of leachate to be recovered will be in the order of200,000 gpd. The volume of water to be recovered would alsobe in the same order if the leachate would be intercepted before ithas traveled too far from the landfill.

The present "recovery wells pump at approximately 1.5 million gallonsper day* This .volume is approximately seven and one-half timesmore than the«»Qlume of leachate production. Considering this ,volumetric relationship, there is a need to modify the presentrecovery -system such that leachate is recovered more efficientlyand contamination of ground water is more effectively controlledand localized.

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GROUND WATER QUANTITY AKD FLOW CONDITIONS

Ground water in the vicinity of the Army Creek Landfill occurs underwater table conditions in the Pleistocene deposits and under confinedconditions in the Potomac Formation. The existing recovery wellspump contaminated water from the Upper Potomac aquifer. Prior toinstallation of the recovery wells, ground water in the UpperPotomac aquifer was flowing to the south of the landfill -under anatural hydraulic gradient and in response to pumping of ArtesimnWater Comapny's wells. Figure 2 is a map showing configuration ofthe piezometric surface in May, 1973.

When recovery wells started pumping, the water levels in the recoveryand observation wells were lowered and the configuration of thepiezometric surface started to change and adjust accordingly. Therecovery wells have been pumping almost continuously, except forseveral accidental and intentional interruptions, since late 1973..The daily and total volume of water pumped from the recovery wellshas been significantly greater than the daily rate and total volumeof leachate produced. The combined pumping rate of the recovery wellshas changed from about 4.0 million gallons per day (mgd) in earlystages to about 1.5 mgd at the present time. Similarly, the combinationof the pumped wells and the total pumping rate of the Artesian watercompany Ts wells have varied significantly during the last four years.Consequently, the configuration of the piezometric surface haschanged and adjusted accordingly to the changes in pumping ratesand combination of the pumped wells. In general, the water levelsin the recovery and the observation wells respond rather rapidlyto any changes in the pumping rates or pumping locations. When awell starts pumping, the water level is lowered rather rapidly in thebeginning and then the rate is slowed. Similarly, when a wellstops pumping, the water level recovers rapidly in the beginningand then its recovery slows down.

Figure 3 is a map showing the configuration of the piezometric surfaceon 8 February 1977. In comparing Figures 2 and 3, it is evidentthat the configuration of the piezometric surface has changedsignificantly between 1973 and 1977. When all the recovery wellsare in pperatlon, a large cone of depression is formed in the vicinityof the wells Stt- 1, RW-3 and RW-5 and small cones are developedaround, other recovery wells* The ground water f lows _ toward thesecones of depression as shown by arrows in Figure 3.

Figure 4 is a map showing a net decline in piezometric head that hasoccurred between 1973 and 1977. A large trough has developed in thearea south of the landfill. The piezometric head has declined fromless than 5 feet to more than 15 feet. Extrapolation of the contourlines in Figure 4 would indicate that the outer boundary of the zone

ARSOIHS

1 1

of influence of the recovery wells lies within 800 to 1000 feet northof the landfill. The piezometric head in the area south of theobservation wells 22, 49 and 52 is affected predominantly by theArtesian Water Company's wells.

Figure 5 is a cross-section through Amoco" observation well OW-5 and ArtesianWater Company's well AWC-2 and selected wells in between. The cross-section snows the following:

o The cop of the Potomac aquifer as interpreted from thedriller's logs; ' . f* ^

o The piezometric surface in 1973 prior to initiation of •leachate recovery;

o The piezometric surface based on data collected in 1974and 1976 when all the recovery wells were pumping;

o The piezometric surface based on data collected on 3 March1977 when all the recovery wells were off for several days.

It is evident from Figure 5, that the piezometric head has beenlowered belov the top of the aquifer in a substantial area southof the landfill and in some cases the water level was lowered veryclose to the top of the screen. This would accelerate incrustationand the wells would require frequent rehabilitation. When the wellsstop pumping, the water levels in the wells initially recover ratherrapidly but would take a long time to recover to an elevation abovethe top of the aquifer.

It should be noted that about 15 to 30 feet of drawdown inthe pumped wells (including RW-4, not shown in Figure 5) appears tobe due to well losses and indicates low efficiency of the wells.In other words, the' difference between the water levels measured in-side and immediately outside of the pumped wells will be about 15to 30 feet. In addition to aquifer hydraulic characteristics andwell construction practices, the magnitude of this difference is afunction of the pumping rate of the well and varies as the squareof the pumping rate. This difference in water levels causes significantenergy loss," increased incrustation and increased operation cost whichcould accumulate to a significant amount if the wells are in operationfor an extendefT -period. To control well losses and improveefficiency of &e veils, they should be .redeveloped and rehabilitatedat appropriate* times and should not be overpumped.

Analysis of the water quality data would indicate that the contaminants •which could by-pass the recovery wells 28 and 29 are being recoveredby the recovery wells RW-1, EW 3 and RW-5. Based on the analysis o£the available data, there is no evidence that the contaminants areby-passing the recovery wells RW-1, RW-3 and RW-5. If they are or havedone in the past, dilution and other physical and chemical processes haveattenuated them to such a level that they were not detectable in the

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Artesian Water Company's water supply. It should be recognizedthat, considering a unit thickness of the aquifer, the ArtesianComapny's wells withdraw water from a surficial area 6 to 7 timesgreater than the area that could potentially be contaminated by thelandfill leachate when it was allowed to migrate in response topumping of Artesian Company's wells.

However, to assure that leachate does not migrate south towardsthe Artesian wellfield, it will be necessary to install additionalwells within the landfill and along Army Creek prior to* toppingrecovery -wells RW-1, RW-3 and RW-5. It is very likely that mostof the leachate will be intercepted by the recovery wells within thelandfill. If so, additional wells along Army Creek would not beneeded and even recovery wells 27, 28, 29 and 31 could be phasedout of operation in due course of time. The time necessary tocomplete this phase-out can not be estimated at this rime* Itcould be estimated only after- the recovery wells In the landfillhave been in operation for several months.

GROUND WATER QUALITY

To evaluate the changes in water quality concentrations of chlorideand total dissolved solids (IDS) were used. These two parametersare considered reliable indicators of the presence of pollution inground water. Although chloride concentration is only one of themany chemical constituents that are present in the ground water ofthe Army Creek area, the concentration of the total dissolved solidsis an indicator of the composite chemical water quality, whilethe chloride concentration is attenuated by dilution only, thetotal dissolved solids are affected by a number of physical andchemical processes.

Figures 6 and 7. are maps showing the distribution of chloride andTDS in different recovery and observation wells. The maps are basedon the information obtained during the period of 1973 and 1977. Ananalysis of the data presented on the two maps would indicate that:

o The concentrations of chloride and TDS in the veils 27, 28,29, 31 «nd RW-6 are higher than those in the wells 44, 51,IE, RW«4. and In other recovery and observation wells vest of28; *" '"

o The concentrations of chloride and TDS have decreased overthe period since leachate recovery started;.this decrease isalso evident in the wells located within the landfill;

o The chloride and TDS concentrations decrease away from thelandfill in almost every well except well 42;

-7-* o on MI h 7HUOo i T^ *

o The concentrations of chloride and TDS in well 42 have increasedand the quality of water has continuously deteriorated;

o Although the chloride and TDS concentrations in wells 27, 28,29, 31 and RW-6 have decreased over the period between 1973through 1977 they are still fairly high;

o Leachate appears to be entering the aquifer beneath the land-fill in an area north of the wells 27, 28, 29 .and 31 and inthe southwest corner of the landfill; "-^

•o Leachate entering the aquifer in the southwest corner df the

landfill is by-passing the cone of influence Imposeff by therecovery wells and is moving under a natural hydraulicgradient and In response to pumping of Artesian Water Company'swells 2, 6 and 7;

•o The slow but steady deterioration of water quality in Well

42 perhaps reflects low permeability of the subsurface 0material in that direction; most of the area surroundingWell 42 is underlain by clay and silty material which retardthe movement of ground water;

o The attenuation of contaminants and improvement of water.quality in an area south of the wells 27, 28, 29, and 31appears to be largely due to dilution in response to recovery efforts,

o The recovery wells are not only removing the contaminantspresent in their vicinity but they are also effective inpulling additional contaminants to their present' locations.With specific regard to this last observation, if one or morerecovery wells were installed in the landfill north of the wells27, 28, 29 and 31, and closer to or within the landfill,leachate could be Intercepted before contaminating substantialvolume of the aquifer.

It should be recognized that, at least In the early stages,it will >e necessary to operate the recovery vell(s) inthe lan££ill in conjunction with the existing recovery veilswhich wc*ald be phased out of operation in. stages. Further-more, i£ will be necessary to monitor water quality in thewells south of 27, 26, 29 and 31 even after most of the existingrecovery wells have been phased out of operation. The frequencyof sampling and the number of parameters to be analyzedwill be modified in accordance with the changes in water quality .subsequent to replacement of existing recovery wells.

AR30llfl*8

It should also be recognized that the concentrations of thecontaminants to be recovered from the wells within thelandfill will be significantly elevated; therefore, treatmentand proper disposal of the water pumped from these wells couldpose significant problems. The exact nature and significanceof the treatment and disposal problems could not be determineduntil the wells are Installed and operated. However, theproblem could be alleviated by properly discharging theleachate pumped into Army Creek Pond such that its retentiontime is increased and by diluting it with water- from otherrecovery wells. If dilution is required, it wil>*be necessaryto continue pumping selected existing wells south* of the*landfill. It is conceivable that the treatment of leachatemay be accomplished only by a wastewater treatment

INCRUSTATION AND REHABILITATION

In the early stages of the leachate recovery progr«sm, some of therecovery wells were discharging contaminated water at 50 to 100percent higher than the present rates. Table 1 summarizes thepumping rates measured on 31 July 1977. Although pumping at highrates was effective in removing contaminated ground water, it alsocaused significant increstation problems. Consequently, the pumpingrates were continuously decreasing and rehabilitation of the wellsbecame Imminent. First rehabilitation of the wells was completedin May through June, 1976. It was necessary to rehabilitate thewells again early in 1977. Under the existing conditions, re-habilitation of the recovery wells appears to be necessary at leastonce a year™ In fact, some of the recovery wells experience re-duction in capacity within two to three months after rehabilitation-

drilling contractors1 cost of rehabilitating recovery wells in1976 was about $28,000; cost of supervision would be additional .This is a significant expense in view of the continued necessity ofthe recovery program until the waste stabilizes and becomes inertor some other environmentally sound and economically feasible solutionis determined. The incrustation problem could be controlled, andsubstantially reduced,- by controlling and reducing the pumping ratesof the existing recovery veils. If the pumping rates are reduced,the entrance velocity of water and thereby the rate of incrustationwill be

Available information and budgetary constraints would not permit anydetailed and sophisticated analysis of the savings that would berealized by reducing the pimping rates. However, it Is estimatedthat the cost of rehabilitating the recovery veils could be reduced

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ORIGINAL(Red)

by about 50 percent. When the existing large recovery veils (RW-1,KW-2, RW-3 and RW-5) have been phased out of operation the savingswill become significant.

In order to estimate the effects of reduced pumping rates on leachatemigration, water quality and incrustation problems, the pumpingrates of the recovery wells RW-1, RW-4, and RW-5 should be reducedby about 50 percent of the present rates. Subsequently, vaterquality and water levels in these and nearby observation wells shouldbe monitored more frequently, at least once a veek for a jponth ortwo. If the water quality does not deteriorate, the veils couldcontinue operating at the reduced rates and similar modificationscould then be applied to the other veils also. Although installa-tion of recovery wells within and closer to the landfill is themain concern., in view of the incrustation problem rad cost ofrehabilitating the wells, pumping rates of the recovery wells RW-1,and RW-5 could be reduced immediately on a trial basis. The newrecovery wells within the landfill should also be installed as soonas possible. When these wells have been Installed and placed inoperation, it would be possible to reduce the pumping rates of theremaining recovery wells and phase out the distant recovery veils.

RELOCATION OF RECOVERY WELLS

Additional Wells ' " " .

An analysis of the data collected from the recovery and observationwells would indicate that the existing recovery wells have servedtheir primary purpose quite effectively. They have stopped themigration of leachate and contaminated ground water towards ArtesianWater Comaptiy's wells. A ground water divide has been created betweenthe contaminant front and Artesian Water Company's wells. Thehydraulic gradient and migration of the contaminant front has beenreversed towards the recovery wells and the landfill. If not all,most of the contaminanted ground water has been removed from thecontaminated zone south of the recovery wells. The quality of theground water in the area south of the recovery wells RW-1, KW-3 andRW-5 has improved significantly. However, due to continued pumpingof the existing recovery wells, the piezometric head in thePotomac aquifer has declined in an area beneath and surrounding thelandfill. Consequently, leachate continues to discharge into theaquifer at a relatively faster rate and is continuously pulled toas far as the present locations of the recovery wells. To protectthe aquifer from continued contamination, it will be necessary tocontain leachate as close to the landfill as possible and controlits further dispersion.

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ORIGINAL(Red)

In order to localize the discharge of leachate and ground water con-tamination to the immediate vicinity of the landfill, it will benecessary to eventually discontinue pumping of recovery veils RW-1,RW-2, RW-3, RW-4 and RW-5. This should, however, be done in stagesby first reducing and controlling the pumping rates and then removingthem completely from the system. The pumping rates should bereduced in any case to control the incrustation problem which requiresfrequent rehabilitation of the veils. However, to assure* thatleachate does not migrate towards Artesian Water Company's veils,it will be necessary to first install additional wells vtthin thelandfill. Depending upon the effectiveness of the new recoverywells vithin the landfill in controlling migration of leachate,it could also be necessary to install additional recovery wellsalong Army Creek in line with 27, 28, 29 and 31. In any case, thenew recovery wells should be installed in four stages as shown inFigure 8 .

Initially, two recovery wells should be installed and operated withinthe landfill. Based on the analysis of the data collected from thenew wells, their effectiveness and the need for additional recoverywells within the landfill and along Army Creek should be evaluated.When the new wells have been proven effective in interceptingleachate beneath the landfill, all or selected existing wellswould be phased out of operation. Based on the review and analysisof the available water level and water quality information, it isestimated that three to five recovery wells located within the landfillcould potentially intercept almost all the leachate beneath thelandfill. As the refuse within and the material beneath the land-fill are heterogeneous, it is conceivable that leachate fromlocalized zones within the landfill could not be intercepted by thethree to*five wells. In that case, it could be necessary to locateadditional wells within the landfill and along Army Creek. Ifadditional wells along Army Creek are necessary, they should belocated between the existing wells 27, 28, 29 and 31 and at placeswhere access is not a problem. It should be mentioned that newwells must not be located south of the wells 27, 28, and 29, andlogistic problems will not permit locating wells within the Army -Creek Pond.

To assure sufficient well interference among these veils and to •create s hydrologic barrier immediately- south of Army Creek such thatall leachate migrating south of the landfill would be intercepted,it is estimated that six to nine additional wells would be installedalong Army Creek. It is expected that existing and additional smallwells, pumping at about 50 to 75 gpm, could develop a trough alongArmy Creek extending about 100 to 200 feet south of the creek. Thesewells would be expected to interfere with each other such that leachatecould not by-pass them. The drawdown due to interference is ex-pected to be in the range of 5.0 to 10.0 feet. The proposed locations

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ORIGINAL(Red)

of additional wells are also sfiown in Figure 8. However, itmight be necessary to modify their location after the first twowells have been constructed in the landfill.

Operation, of the pumps at low rates would minimize the Incrustationproblem and the need for rehabilitation of wells, which vouldresult in significant savings. Samll capacity but relativelymore efficient wells would require less energy to operate'. -Similarly,a small number of wells located within the landfill wou!4 requireless energy to operate. Thus, the program of relocating he recoverywells is expected to result in more efficient leachate recovery.

Benefits

Available information and budgetary, constraints would not permit anyquantative estimation of benefits in terms of specific dollar amounts.However, it is anticipated that the following benefits will berealized by relocating the recovery wells within the landfill alongAray Creek; most of which will be translatable into eventualcost savings.

o "More efficient collection and recovery of leachate;o Controlled and localized dispersion of leachate;o Additional ground water available to Artesian Water Companyo Less energy requirements due to reduced pumpage by recovery

wells;, and therefore, less operating -cost;o Less frequent rehabilitation and reduced cost of operation

and maintenanceo Less volume of wastewater to be discharged.

Initial expenditure of installing additional wells could be consideredthe only, disadvantage of relocating the recovery wells.

CONCLUSIONS AND RECOMMENDATIONS

Selected hydrologic data were analyzed to evaluate the concept ofrelocating the recovery wells such that leachate and contaminatedground water could be recovered more efficiently.

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A p q n S b 5 2H tt O W i *r *-

Based on the analysis and rationale presented, the following con-clusions and recommendations are made:

Conclusions

o The recovery wells have been successful in containment ofthe leachate plume within the ground water flow south of theArmy Creek Landfill.

o A ground water divide has been developed between- jae ArtesianWater Company's well field and the contaminated zpne of •ground water. The ground water flow in the contaminatedzone between the landfill and the Artesian veil fields hasbeen reversed towards the recovery wells and the ArmyCreek Landfill.

o Army Creek Landfill will continue to produce leachate untilthe refuse becomes inert or some other solution of theproblem is determined.

o The recovery wells RW-1, RW-3, RW-4, and RW-5 continue topull the contaminants to as far as their present locations;these recovery wells could be phased out of the systemin stages by reducing their pumping rates.

o Contaminants appear to be by-passing the recovery wells 27,28 and 29 but are being recovered in RW-1, RW-3 andRW-5.

o It appears that most of the contaminants are discharged intothe Potomac aquifer in an area of the landfill. north of therecovery wells 27, 28 and 29 and in the southwest corner ofthe landfill.

o At the present time, the total pumping rate of the recoverywells Is approximately 1*5 million gallons per day, which isabout 7.5 times more than the average daily rate of potentialleachate production. Leachate vould be recovered more efficientlyIf the wells were located within and closer to the landfill.

•° ffiree to five recovery wells located within the landfill couldpotentially intercept most of the leachate and control itsmigration away from the landfill. However, to assure protectionto Artesian Water Company's wells, it may be necessary to installadditional recovery wells along Army Creek.

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AR30U53

It will be necessary to monitor the vater quality in thevicinity of the recovery wells RW-1, RW-3, 5W-4 and RW-5more frequently than usual when their pumping' rates havebeen reduced. This would assure early detection of anydeterioration caused by reduced pumping rates.

Incrustation has caused a significant problem requiringfrequent rehabilitation of the recovery wells. To controlincrustation problem, the pumping rates of the existingrecovery wells should be further reduced by about»50 percent.* -—Disposal of leachate from the wells within the landfill 'could pose problems relative to volume and concentration which'could be resolved by Increasing retention in the Army Creekpond and by diluting with water from other veils.

When RW-1, RW-2, RW-3, KW-4 and RW-5 have been phased outof the recovery program, more recharge vill be available forArtesian Water Company's veils.

Re commend at ions

o Install two recovery wells within the landfill at the proposedlocations. Test pump the veils and place them into recoverysystem as soon as possible.

o Monitor ground water quality to evaluate the effectivenessof the new recovery wells in removing contaminants and incontrolling their migration.

o If the two wells are effective in controlling migration ofcontaminants, three additional recovery wells should beinstalled within the landfill.

o Reduce pumping rate of well RW-1 by about 50 percent andmonitor the water quality.

o If necessary, install additional recovery veils within thelandfill and along Army Creek.

o Reduce pumping rates of the recovery veils RW-3, RW-4 andRW-5,.

o If the recovery wells within the landfill and along ArmyCreek are successful in intercepting all the leachate nearthe landfill, RW-1, RW-2, RW-3, RW-4 and RW-5 could be phasedout of the system.

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R30U5U

ORJGIKAL(Red)

o The pumping rates of the recovery wells within the landfilland along Army Creek should be controlled at 50 to 75 gpm.

Table 1

Recovery Wells Pumping Rates - *

*

Recovery Pumping Rates (gpm)Wells ————°——————™r f

2-8-77 7-31-77RW-1 Off 200

RW-2 Off Off

RW-3 200 200

KK-4 250 200

RW-5 140 100

KW-6 125 110

27 15 128

28 140 Off

29 80 125 ""

31 Off Off

53 Off 60

ftR30U5-15-

FIGURE 1OF vm>AmGTON SOUTH U.S.G.S. 7Y2 MINUTE TOPOGRAPH/C MAP

SHOWING THE LOCATIONS OF THE ' .AKffJCHSEir. •« LANDFILL AND ALL WELLS^1D BORINGS IN ITS VICINITY, SEPTEMBER, 1972 . ...

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ASAHDOKED KOBSERVATION WELL

1 D TEST BORINC (UMCASED)TEST WELLS THIS STUDY

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NEW CASTLE COUNTY

ARMY CREEK LANDFILLNEW RECOVERY WELLS PUMP TEST

August 1983

Prepared byROY F, WESTON, INC.

Weston WayWest Chester, Pennsylvania 19380

NEW CASTLE COUNTYARMY CREEK LANDFILL

NEW RECOVERY WELLS PUMP TEST

An extended pumping test of the new recovery veils, RW-10,RW-11, RW-12, RW-13 and RW-14, south of Army Cretk Landfillwas conducted starting 10 May 1982. Several weeks., prior tothe extended test individual step-drawdown tests were conduc-ted on each of the wells in order to determine the suitablepumping rates to be used during the extended test. Approximate-ly 48 hours prior to the extended test all existing recoverywells were shut down to allow groundwater levels to recoverto natural static conditions.

The pumping test started with Well RW-12 being turned on at1330 hours on 10 May 1982. Wells RW-11, RW-10, RW-13, andRW-14 were then turned on in sequence at 24-hour intervals afterpumping .started from RW-12. Monitor wells in the vicinity ofthe pumping wells were monitored regularly to determine thedrawdowns caused by.the pumping wells. By 15 May 1982 thenew recovery wells had been pumping continously for periodsranging from 24 hours (RW-14) to 120 hours (RW-12). Between16 May and 17 May 1983 the original recovery wells were broughtback on line, while the new recovery wells continued pumping.So that by 17 May 1982, both the old and the new recoverysystems were in operation.

PUMP TEST DATA INTERPRETATION

During the pumping-test water levels and pumping rates weremeasured in each of the recovery wellsf and water levels weremeasured in observation wells in the vicinity of the pumpingwells. Pumping rates in each of the recovery wells were main-tained at essentially constant rates throughout the test.

Confuted drawdowns and computer-generated time-drawdown curves,for each pumping well and selected observation wells, areattached to this report. Table 1 provides a data 'summary forthe new recovery wells during the pumping tests. -

' --•*

The time-drawdown curves, for the new recovery wells, indicatethat there was little variation in the individual fates ofdrawdown. This would suggest that the wells are efficient andthat well losses are small. The majority of the drawdown re-sults from formation losses which are functions of the aquifercharacteristics. Variations in drawdown were caused by var-iations in pumping rates and/or mutual well interference.The degree of interference among the new recovery wells isgiven in Table 1.

The primary aquifer characteristics that affect ground watermovement are Transmissivity and Storativity. Drawdown, time,and pumping rate data were used in the calculation of the aqui-fer characteristics. Since the new recovery wells are closerto the landfill than the original recovery system and given thefact that the outcrop or recharge area for the Potomac Aquiferis located north of the landfill, several methods for calcu-lating the aquifer characteristics were initially tried in orderto determine if water table conditions, leakey artesian, orartesian conditions exist in the vicinity of the new recoverywells. Transmissivity for a selected observation well wascalculated using the modified straight line method, developedby Jacob, the Theis standard type curve, leakey artesian typecurve, and water table type curve. There was good agreementamong the methods used, and the standard type curve, developedby Theis, was selected for the Transmissivity and Storativitycalculations.

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Transmissivity and Storativity were calculated for observationwells where sufficient drawdown data was collected for thegeneration of time drawdown curves. Table 2 lists the Trans-missivity and Storativity values for the selected observationwells . There is some variation among the Transmissivity valueswhich is due to the nature of the aquifer. The'ltotomac Aquiferexhibits considerable lateral changes in composition. This isdue to the fact that the sediments were laid down in streamchannels along flood plains and shallow embayments, rather thanin homogeneous layers, so Transmissivity will vary directionallydepending on location. This effect is illustrated on Figures1 through 4 which show the distance drawdown effects between thenew recovery wells and selected observation wells on 19 May 1982.In actuality, the distance-drawdowns shown on Figures 1 through4 will not be strictly linear due to recharge effects and theeffects of pumping of the Artesian Water Co. wells.

The distance-drawdown graphs indicate that, with a combinationof pumping the new recovery system and the original recoverysystem, mutual well interference will create a trough-like •depression in the piezometric surface in the Potomac Aquifer.This depression, extending northeast to southwest from well RW-13through well 31,"RW-12, 29, 28,'27, RW-1, RW-3, RW-5, RW-11,RW-10, RW-4, and RW-9 will effectively prevent leachate frommigrating south of the landfill and will recover leachateenhanced groundwater to the south of the recovery system.At the current pumping rate of 1.5 mgd for the original re-covery system, a total of approximately 2.8 mgd of leachate-enhanced groundwater is presently being recovered.

The reason the new recovery system was located close to the•landfill was so that more concentrated leachate could be recov-

R30iu67

TABLE 2

TRANSMISSIVITY AND STORATIVITY

NEW RECOVERY WELLS PUMPING TEST

RW-12 pumping 200 gpm

Well(gpd/ft)

29 76,400 0.00531 40,930 0.00565 69,450 0.03

RW-10 pumping 200 gpm, RW-11 pumping 200 gpm

Well T S(gpd/ft)

RW-4 ,72,330 .00666 44,940 .0167 38,200 .02

RW-13 pumping 200 gpm

Well T S(gpd/ft)

RW-6 71,350 .0139 52,800 .01

RW-14 pumping lOOgpm

Well - T S(gpd/ft)

71 36,970 .003

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©red while pumping lower volumes of groundwater for shorterperiods of time. It is intended that as water quality analysesindicate a decrease in leachate content in the observationwells south of the landfill, pumping of the original recoverysystem would be cut back until it could be shut- iown entirely.In this way, rather than pumping large volumes of dilute leachatefrom the edges of the leachate plume for long periods of time,the new recovery system will effectively recover a higherproportion of leachate, faster and at lower pumping rates,while at the same time preventing migration of leachate tothe south.

In order -to determine the extent of the pumping effects of•the new recovery system using the aquifer characteristicsdetermined during the pumping test, distance drawdown relation-ships were calculated. It was assumed that the original recov-ery system was shut off.

It was also assumed that pumping level equilibrium was reachedafter 5 days of pumping which is suggested by the results ofthe pumping test. Using Theis1 formula,the distance was cal-culated at which point s is less than 0.5 feet, Theis1 formulacan be described as:

s = 114.6 Q W(u)T

where:s s drawdown in ft. at any point in the vicinity of a

well pumping at a constant rate.Q » pumping rate in gpm.

W(u) « well function of u.

where u is defined by the expression:

u « 1.87 r2 S/Tt

-10-

where:r = distance in ft., from center of pumped well to

point where draw down is measured.S = Storativity, dimensionless.T = Treinsmissivity. -^t = time since pumping started, in days.

The drawdown value of 0.5 feet was chosen to represent thegroundwater divide in the piezometric surface caused by thepumping wells. It is recognized that fluctuations will occurin the piezometric surface, due to recharge and the pumpingaffects of other well systems, which will cause the groundwaterdivide to shift. So a distance drawdown of .5 feet or lesswould effectively represent the edge of the cone of depressioncaused by the pumping well.

Table 3 lists the predicted distance from each of 'the new re-covery wells to the edges of their respective cones of depres-sion. It should be understood that Table 3 represents idealconditions, that is an initially horizontal piezometric surface,and no outside influence, either recharge or additional dis-charge, on the aquifer system. In reality the radii of influ-ence are much smaller, as indicated by Figures 1 through 4.Figure 5 represents the southern boundary of the combined conesof depression of the new recovery wells as indicated by Figures1 through 4, and Table 3. With the additional drawdown causedthe pumping of the original recovery system, the radii of influ-ence would actually extend farther to the south. Even withoutthe original recovery system, the new recovery system wouldeffectively isolate the landfill.

HR30U7U

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TABLE 3

DIRECTIONAL RADII OF INFLUENCE

NEW RECOVERY WELLS AFTER 5 DAYS

RW-12 0=200 gpm

Direction Distance(ft) * Drawdown(ft)

Northeast-Southwest 2800 " 0.46

Northwest-Southeast 1000 0.46

RW-10 and RW-11 combined 0=400 gpm

Northeast-Southwest 2800 0.46

Northwest-South-Southeast 1850 0.48

RW-13 0 200 gpm

Northeast-Southwest 1800 0.44

East-West 2000 0.41

RW-14 0 100 gpm

Northwest-Southeast 2200 0.45

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-13-

Utilizing this pump test data, historical ground waterelevation and flow data, and historical water qualitydata available for the Army Creek Landfill, an evaluationof the feasibility of phasing out some of the recoverywells was made. The following provides a background ofthe well recovery program and factors used in determiningpotential recovery wells to be phased out. -f*

RECOVERY WELL PROGRAM

Following the combined pumping test of the new recoverywells {RW-10 through 14) from 10 to 15 May 1982, thesenew wells were incorporated into the ground-water re-covery program for the Army Creek Landfill. In June1983, when all the operational recovery wells were on-line, a total of 15 wells were recovering ground waterand creating a trough-like depression south of the landfill.Between June 1982 and April 1983 these recovery wells dis-charged between 1.37 mgd and 2.14 mgd, averaging 1.667 mgd.During the same period, the Artesian Water Company pumpedbetween 1.57 mgd and 1.97 mgd, averaging 1.895 mgd.'

Fluctuations in pumping rates of the recovery wells were dueto various wells being off line at times for repairs andthe gradual loss of well efficiency due to well screenand discharge pipe clogging.

The clogging of well screens and discharge lines by ironprecipitate is"a continuous problem that is dealt withthrough a regular program of well rehabilitation and pumprepair. During the period June 1982 through April 1983at least one well was off-line during any given month,with the exception of June 1982 when all wells were on-line, for maintenance, repair or rehabilitation.

-14-

Table 3 tabulates the average daily pumping rate, in gpm,of the recovery wells and the Artesian Water Company wellfield. It can be seen that many of the wells show de-creasing pumping rates due to loss of efficiency throughtime. The effects of rehabilitation can also be seen inthe increase in the average daily pumping rate of RW-1from 83 gpm to 263 gpm.

- *

The recovery program could be made more cost effectiveby eliminating some of the less productive wells andmaximizing the pumping rates and efficiencies of recoverywells closer to the landfill* Listed below are the cur-rent average pumping rates for the recovery wells for May1983 and for comparison the initial pumping rates, afterwell construction, when the wells were most efficient:

Current Most EfficientPumping Rate Pumping Rate 4

Well (gpm)___ ___(gpm)____

RW-1 200 200RW-3 34 200RW-4 103 200RW-6 12 150RW-9 50 80RW-10 220 250RW-11 118 200RW-12 45 200RW-13 69 200RW-14 ' 19 100.27 33 ' 15028 127 16029 137 15031 67 165

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From the listing above it can be seen that most of therecovery wells are operating well below 50 percentefficiency. The cost-effectiveness of the recoveryprogram could be improved by eliminating the marginallyproductive wells that are some distance from the land-fill while maximizing the use of the recovery wellscloser to the landfill. This would also increase the

**i§quantity of leachate recovered since the recovery wellscloser to the landfill pump a higher proportion ofleachate versus ground water as opposed to the recoverywells located farther downgradient.

•

In order to determine which wells could be taken off-linethe pumping records (Table 3), general performance, andwater quality data for the recovery wells were examined.Table 2 lists 'the average total dissolved concentrationsfor the recovery wells from June 1982 to April 1983.Total dissolved solids was chosen for analysis sincethis parameter is conservative in that, once in theground-water flow system, it is attenuated principallyby physical means such as dilution and dispersion.Table 4 indicates that most of the wells have adissolved solids 'content below the level of 250 mg/1set for EPA interim drinking water standards, althoughthe wells directly downgradient of the landfill generallyshow higher dissolved solids than wells farther removed.

A review of the existing data suggests that recoverywells RW-3, RW-4, RW-5 and RW-6 may be taken off-linewithout deterioration of the overall recovery program.The pumping records and water quality data indicate thatif the remaining recovery wells, RW-1, RW-9, RW-10, RW-11,

H U U V i

Table 4: AVERAGE TDS CONCENTRATIONSJUNE 1982 - APRIL 1983

TDS Average TDSJ^RangeWell (mg/1) (

RW-1 243 137 --300RW-3 94 63 - 136RW-4 133 88 - 195RW-5 152 . 37 - 185RW-6 115 . 90 - 160RW-9 219 74 - 273RW-10 111 81 - 135RW-11 164 110 - 231RW-12 193 96 - 252RW-13 100 70 - 124RW-14 191 166 - 22527 203 131 - 28528 431 416_^45629 380 " 324 - 42831 133 65 - 220

-18-

RW-12, RW-13, RW-14, 27, 28, 29 and 31 are maintained ateven 70 percent of full efficiency, the recovery programwould be pumping .1.87 mgd which is higher than the averagepumping rate for the full system from 'June 1982. throughApril 1983. The four wells (RW-3, RW-4, RW-5, and RW-6)suggested for removal from the system have had generallypoor performance records, are in the radii of "o,gfluenceof more productive wells, are farther from the T.andfi'11,or whose TDS values indicate a low leachate to ground-water ratio.

The pumping tests results from the combined pumping testconducted .in May 1982 indicate that the most recently in-stalled recovery wells (RW-10, RW-11, RW-12, RW-13 andRW-14) could, at full efficiency, effectively limitleachate migration. The continued use of recovery wellsRW-1, RW-9, 27, 28, 29 and 31 would allow flexibilityin the program for maintenance and well rehabilitation,and allow the recovery program to operate effectivelyunder real world conditions of less than full efficiency.The key to the effective operation of the recovery pro-gram with the removal of the four wells mentioned, isthe need for continuing the surveillance and maintenanceof the remaining wells in order to issue the maximumpossible efficiency. ......

-19-

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