A RECONNAISSANCE OF GROUND-WATER CONTAMINATION

AT SELECTED LANDFILLS IN COLORADO

By Paul A. Schneider, Jr., and John T. Turk

U.S. GEOLOGICAL SURVEY

Water-Resources Investigations Report 83~^021

Prepared in cooperation with the

COLORADO DEPARTMENT OF HEALTH

Lakewood, Colorado 1983

UNITED STATES DEPARTMENT OF THE INTERIOR

JAMES G. WATT, Secretary

GEOLOGICAL SURVEY

Dallas L. Peck, Director

For additional write to:

information

Colorado District Chief U.S. Geological Survey, MS 415 Box 25046, Denver Federal Center Lakewood, CO 80225

For sale by:

Open-File Services Section Western Distribution Branch U.S. Geological Survey, MS 306 Box 25425, Federal Center Denver, CO 80225

Telephone: (303) 234-5888

CONTENTS

Abstract----------------------------Introduct jon------------------------Data collection---------------------Results and discussion--------------

Hydrology of the landfills---- 1Boulder County------------City and County of Denver- El Paso County------------La Plata County-----------Larimer County------------Weld County---------------

Water quality of the landfills-Summary----------- 1References cited-- 1 Water-quality data-

Page 1 1 3

6111118182323282829

LLUSTRATIONS

Figure 1. Map showing location of study sites----------------------'2. Generalized section showing types of landfill and ground-

water intefaction---------------------------------------

3. Map showing location of test wells and sump at the Golden Rubble si te---------------------------------------------

4-10. Maps showing location of test wells at the:4. Marshall site---------------------------------------5. Cherry Creek site-----------------------------------6. Place Junior High School site-----------------------7. Hancock Road and Academy Boulevard site-------------8. Bodo Industrial Park site-------------- -------- 9. Fort Coll ins site-------------------- -- -------

10. Brighton-Fort Lupton site---------------------------

Page 2

1213 16 19 21 2k

i i i

Table 1,

2-8,

TABLES

Physical data for wells and sump sampled at the Golden Rubble site- - -- --- -- - -- ---

Physical data for wells sampled at the:2. Marshall site- ~ 3. Cherry Creek site---------- ---- --------- __________k. Place Junior High School site------------------- --- 5. Hancock Road and Academy Boulevard site-----------------6. Bodo Industrial Park site------- ----------------------7. Fort Coll ins site--------------- ------------ ---_ -.8. Brighton-Fort Lupton site------- ---------------- ----

Water-quality rank of samples from sump or wells at eachlandf i 11 si te- --- - - - -- -- -

Page

10 Ik 15 17 20 2225

26

METRIC CONVERSIONS

The inch-pound units used in this report may be converted to SI national System of Units) by use of the following conversion factors:

(Inter-

Multiply inch-pound unit By

inch 25.40foot 0.3048mile 1.609foot per mile 0.1894micromho per centimeter at 1.0

25° Celsius

To obtain SI unit

mi 11imeter meter ki lometermeter per kilometer microsiemen per centimeter

at 25° Celsius

National Geodetie Vertical Datum of 2929: A geodetic datum derived from a general adjustment of the first-order level nets of both the United States and Canada, and formerly called mean sea level, is referred to as sea level in this report.

IV

A RECONNAISSANCE OF GROUND-WATER CONTAMINATION AT SELECTED LANDFILLS IN COLORADO

By Paul A. Schneider, Jr., and John T. Turk

ABSTRACT

A reconnaissance study of eight landfills in Colorado shows that they have contaminated the shallow ground-water system. Contamination is indi­ cated by values of specific conductance and concentrations of major ions and trace elements. Because only shallow ground water was sampled, it was not possible to determine whether deeper ground-water systems also are contami­ nated.

The major effects on water quality caused by contaminants in the land­ fills were increased salinity, nitrogen, iron, manganese, and phenols in the shallow ground-water system.

INTRODUCTION

The location of landfills in the past commonly was based on proximity to population centers and transportation costs rather than on possible effects on the ground water. Disposal of domestic and industrial wastes directly into the ground water by pit excavation or in areas of rapid infiltration has resulted in hazards, including methane-gas generation and ground-water con- tami nation.

The U.S. Geological Survey, in cooperation with the Colorado Department of Health, conducted a reconnaissance of landfills in Colorado, seven of which are within the urbanized Front Range area between Fort Coll ins and Colorado Springs. The remaining landfill is in Durango (fig. 1). This study, the first such study in Colorado, has documented the presence and the nature of chemical changes in water quality in the vicinity of the landfills. The results are presented both on maps and in tables to facilitate rapid assess­ ment of the relative hazards in various directions from the landfills.

Landfill studies have been conducted in many parts of the country in recent years. In humid climates, contamination by infiltration of rain and snowmelt through the waste is common; typical examples of such contamination are well documented for two Long Island, N.Y., landfills (Kimmel and Braids,

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1975; 1977). In these studies the authors found detectable leachate plumes following the general ground-water movement at least 10,600 feet downgradient from the sites studied. The plumes were observed to extend vertically beneath the landfills to the first relatively impermeable layer, mixing and traveling with ground water in the downgradient direction until dilution and interac­ tion with the aquifer matrix made the plume indistinguishable from the ambi­ ent ground water.

In arid and semiarid climates, landfills may not contaminate ground water as extensively as in humid climates. The great depth to water in many areas of Colorado can prevent direct contact between waste and the water table, while the small ratio of precipitation to evaporation can limit the effective infiltration of water into the waste. In such cases, landfills in arid or semiarid locales may be effectively isolated from the ground water, and the leachates from these landfills react primarily with the oxygen in the unsaturated soil to release carbon dioxide, methane, and ammonia to the soil atmosphere.

To determine the nature of landfill and ground-water interactions in Colorado requires consideration of the likely geochemical reactions between the waste, the soil atmosphere, the soil itself, and water. Discussion with landfill operators revealed the landfill material to be primarily paper, con­ struction debris, and food waste. Incomplete oxidation of organic matter in such material produces reducing conditions in the immediate vicinity of these wastes. While some major ions can be expected to be leached from construction debris, such as wallboard, and from bleached paper, the principal contribu­ tions are likely to be carbon and nitrogen species liberated by the incom­ plete oxidation of organic material and soil constituents dissolved under the reducing, carbon dioxide-rich conditions resulting from waste decomposition. Thus, iron, manganese, calcium, and magnesium from the soil and bicarbonate, ammonia, organic nitrogen, and organic carbon from the waste might be expect­ ed to increase in ground water contaminated by landfills. Such contamination, if it occurs, will be most severe at the waste site, and its transport will be controlled by the ground-water movement near the site.

DATA COLLECTION

Wells were installed in and around the landfill sites by drilling with an auger, installing 3" or 4-inch diameter perforated polyvinyl-chloride casing, and sealing the hole with material from the auger cuttings. Caps were installed immediately, and perforations above ground level were sealed with tape. Full-length perforation was necessary to allow the wells to be used for the sampling of methane, as well as for the collection of water samples. The presence of impermeable surficial materials minimized any possible effect from infiltration around the casing; in addition, samples were not collected during or immediately after periods of rain or snowmelt.

In many cases the wells from which the water samples were drawn had filled with sand and some fine gravel to within the upper foot or so of the zone of saturation, so only the uppermost part could be sampled. Therefore, samples of water exclusively from the upper part may not represent the entire saturated zone. Samples from the upper part might, for example, contain lesser dissolved-solids and transition-metal concentrations than might be found in deeper samples because of changes caused by density stratification and oxidation in the upper samples.

The holes were drilled and cased by contractors under the direction of the individual health departments in whose jurisdiction the particular land­ fills were situated. The wells were constructed primarily for methane sampling.

Well locations were selected based upon an assumed direction of ground- water flow and the landfill extent, when known. Wells could not be completed successfully in every case, primarily because of slumping of the unconsoli- dated sand and gravel in the saturated zone. Although all wells yielding sufficient water were sampled for specific conductance, detailed chemical analyses were performed on only three wells at each landfill. These wells were selected, based on specific-conductance data, to represent the most dilute, intermediate, and most concentrated water at each landfill.

After completion, the wells were bailed to remove water; normally, three well volumes were removed before sample collection. Immediately after collection, the unfiltered samples were tested for temperature, specific conductance, and pH by methods described by Skougstad and others (1979). The large concentration of suspended material made it necessary to fill plastic containers with the sample and allow the sealed container to stand for approximately one-half hour prior to filtration to allow sufficient settling of suspended solids. No discoloration was observed. The samples then were analyzed by the methods described by Skougstad and others (1979).

RESULTS AND DISCUSSION

Hydrology of the Landfills

Those landfills chosen for the study were constructed on three different types of geologic terrain (fig. 2). Five landfills were constructed on sand and gravel deposits, one was constructed on permeable bedrock, and two were constructed on relatively impermeable bedrock. In all the landfills the water table was either intercepted during the excavation phase, or a perched water table formed during the filling and compaction phase.

Are

a o

f w

ate

r perc

ola

tion

thro

ugh

un

satu

rate

d l

an

d­

fill t

o u

nd

erlyi

ng

ro

cks

LA

ND

FIL

L

CO

VE

R-

Loc

ally

de

rive

d m

ater

ial

LA

ND

FIL

L-

Mos

tly

soli

d w

aste

SAN

D A

ND

GR

AV

EL

- A

lluv

ial

depo

sits

of

near

by s

trea

ms

and

rive

rs

EXPLANATION

WEATHERED SHALE

UNWEATHERED SHALE

WEATHERED SANDSTONE

.UNWEATHERED SANDSTONE

DIR

EC

TIO

N O

F G

RO

UN

D-

WA

TE

R F

LO

W-

Lar

ge

arro

ws

indi

cate

gre

ater

fl

ow.

Smal

l ar

row

s in

di­

cate

les

s fl

ow

Fig

ure

2.-

Gen

eral

ized

sec

tion

sho

win

g ty

pes

of l

andf

ill

and

grou

nd-w

ater

int

erac

tion

.

Boulder County

The Golden Rubble and Marshall landfills in Boulder County (figs. 3 and A and tables 1 and 2) each had drains constructed to lessen the impact of potential leachate plumes on the shallow ground water. Both drains were constructed on the upgradient side of each landfill to intercept the shallow water table. The drains along the south and west side of the Golden Rubble site made the gradient of the water in that landfill so flat the direction of movement was indeterminate. The water from the Golden Rubble site was pumped from a collection sump into a concrete ditch which conveyed the water from the site to St. Vrain Creek, whereas water intercepted by the drain at the Marshall site flowed into a natural drainage north of the Community Ditch.

Water levels measured in wells constructed for the study showed the activity associated with the landfills has little or no effect on the config­ uration of the regional water table. The flatness of the shallow water table within the Golden Rubble landfill is due to the presence of the drains. Out­ side the area of this site the regional water table has a gradient of about 25 feet per mile, mostly to the east (unpublished data on file at the Colo­ rado District Office, U.S. Geological Survey). This site, a gravel pit exca­ vated in the alluvium of St. Vrain Creek, now is covered and inactive. The thickness of the fill was not determined.

The Marshall landfill (fig. k) is excavated through a veneer of alluvium into the underlying sandstone and shale. The alluvium is about 25 feet thick at the south side of the site and thins toward the Community Ditch on the north. A gravity drain, constructed from near the southwest corner of the landfill at the alluvium-bedrock contact, extends northward along the west side of the fill area. Test holes drilled and cased into the bedrock, where possible, were used to collect water samples and monitor water levels.-Water- level measurements indicate there is hydraulic connection between the allu- vium and the underlying bedrock. The gradient of the potentiometric surface, therefore, is continuous from near the south boundary of the landfill north­ ward to Cowdrey Reservoir No. 2, and northeast out of the site area. Between Marshall Lake and test wells 2 and 3» the direction of the ground-water move­ ment is inferred from the topographic relief and the eroded bedrock surface. The erosion surface of the bedrock has been mapped from test holes which pen­ etrate it, a prelandfill stream which was incised into it, and several con­ tact springs which seep along the cut of the current Tnanmade drainage course. This gradient indicates some water is leaving the area by flowing across the subcrop and outcrop and entering the surface drainage and some is entering the deeper aquifer. Test drilling at this landfill did not fully penetrate the thickest parts of the fill.

40

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N.

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ne

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p)

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vel

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eter

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er f

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n of

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Feet

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AN

AT

ION

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TE

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LL

OR

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NU

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F ^^

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Fig

ure

3.--

Loc

atio

n of

tes

t w

ells

and

sum

p at

the

Gol

den

Rub

ble

site

.

39°57'30"

T.1S.

105°12'30" R.70W.

EXPLANATION

> 2 TEST WELL AND NUMBER

APPROXIMATE LIMIT OF LANDFILL

To *- National Center forAtmospheric Research

400i

800 1200 1600 FEET_]____I____)

400 METERS

Figure 4.-- Location of test wells at the Marshall site.

Table

].--

Phys

ical

dat

a fo

r we

lls

and

sump sa

mple

d at

th

e Golden Rubble

site

Wel

1

Lat

i tud

e sump No.

Wate

r elevation

Long

itud

e (feet

above

sea

leve

l)

Bedrock

elev

atio

n (f

eet

above

sea

leve

l)

Land

-

surf

ace

elev

atio

n (f

eet

abov

e sea

leve

l)

Wate

r tempera­

ture

(degrees

Cels

ius)

Spec

i fie

cond

ucta

nce

(micromhos

per

centimeter

at 25

°C)

Wate

r-

qual i

ty

data

1 2 3"

4--

5

*6

40°09'30"

40°09'23"

40°09'27"

40°09'24"

40°0

9'28

"40°09'32"

105°07

I11"

105°07'10"

105°07'07"

105°07'03"

105°07'01n

105°07'06M

^,951.9

^,95

1.9

^,95

1.8

^,951.6

^,951.9

**, 950

.0

^,9^

8.3

^,95

0.6

^,9^

7.6

^,9^

5.9

^,9^

3.7

^,9^3-2

4,96

0.8

4,959.6

4,958.8

4,95

4.9

4,955.7

13-5

13.0

13.0

11.0

12.5 9.0

4,50

02,

400

4,25

02,

600

3,10

01,

050

No.

No.

Yes.

No.

Yes.

Yes.

*Sump

for

inte

rcep

tor

ditc

h.

Table

2.--

Phys

ical

data fo

r we

lls

sampled at t

he M

arshall

site

Well

No

.

1

2 3~

4--

5

6

7"

8

9

10--

11

--

Latitude

39°57'12"

39°5

7'22

" 39°57'18"

39°57'02"

39°57'04"

39°56'59"

39°5

6'51

" 39

°56'

43"

39°56'36"

39°56'36"

39°5

6'57

"

Long

itud

e

105°

12I00"

105

011'

53"

105

e11'50"

105

012'

12"

105°12'14"

105

012'12"

105

012'

21"

105°

12'2

3"

105°12'12"

105°

11'5

5"

105e1

1'5V'

Wate

r elevation

(feet

abov

e sea

level)

5,6*18.8

5,60

7.**

5,623.1

5,67

6.5

5,65

7.3

5,679.5

5, 698

. *i

5,69

5.^

5,70

3.1

5,71

8.2

5,68*1.8

Bedrock

elevation

(fee

t ab

ove

sea

level)

5,60

4.5

5,62

0.3

5,65

8.5

5,65

7.4

5,69

7.2

5,69

2.4

5,71

1.5

Land

- su

rfac

e elevation

(fee

t ab

ove

sea

level)

5,67

0.2

5,612.5

5,62

7.3

5,681.5

5,660.4

5,702.5

5,713.2

5,715.4

5,723.5

5,73

2.7

5,71

6.5

Wate

r te

mper

a­

ture

(d

egre

es

Cels

ius)

10.5

13

.0

9.5

9.0

14.0

12.0

13.5

13.0

13

.5

12.5

Specific

conductance

(micromhos

per

cent

imet

er

at 25°C)

4,25

0 1,

100

850

1,250

750

330

450

200

310

380

Wate

r-

qual ? ty

data Yes.

No

. Yes.

No.

No.

No.

No.

No.

No.

Yes.

No

.

City and County of Denver

The landfill sites investigated in the city and county of Denver at Cherry Creek and Place Junior High School (figs. 5 and 6 and tables 3 and k) were formerly sand and gravel pits. After the mining was discontinued, the city and county refilled them with rubbish. The full extent of the areas occupied by the landfills during their active phase is not known. After they were filled, compacted, and covered, the landfills were converted to con­ struction sites by developers. The Cherry Creek site has had differential settling, resulting in damage to some of the structures. Water-level meas­ urements showed that the fill was partly saturated. They also showed that the landfills had little effect on the regional water-table gradient. The thickness of the fill material is as much as 10 feet at the Cherry Creek site and as much as 15.5 feet at the Place Junior High School site.

El Paso County

The landfill site near the intersection of Hancock Road and Academy Bou­ levard in Colorado Springs (fig. 7 and table 5) was excavated in the alluvium of a tributary to Fountain Creek. The converted gravel pit, used as a land­ fill for several years, now is inactive. The extent of the area occupied by this landfill during its active phase is not known. Exploratory drill holes were located in and adjacent to the site, and fill penetrated was as much as 20.5 feet thick.

The shallow water table slopes more at this landfill than at others studied which also were located in alluvium. This slope and the beds of well- sorted coarse sand and fine gravel in the saturated zone give the site the most potential for transport of contaminants away from the landfill. Logs of holes 1, 2, k, and 8 show thicknesses up to 21 feet of coarse sand to fine gravel interbedded below the water table and adjacent to the landfill. These permeable beds are expected here because the site was originally excavated to mine the sand and gravel for construction products.

The eastern part of the landfill between holes 5 and 8 has an ellipti- cally shaped dry area about 100 feet long. Four holes drilled to a maximum of 32 feet within this area encountered no saturated material above the bedrock. This drained area is topographically high, and the shallow ground water on the north and west drain toward the East Fork Sand Creek, which is a losing stream. During the study the creek had water flowing continually in the chan­ nel. This created a ground-water mound which expanded from directly beneath the creek out to an indeterminate distance and caused the shallow ground water to flow, in part, downstream parallel to the mound.

11

ALAMEDA AVE R.68W.

EXPLANATION

2 TEST WELL AND NUMBER

LIMIT OF LANDFILL NOT KNOWN

104°56*30"

39°42'30"

T.4S.

EXPOSITION AVE

500i

1000I

1500 2000 FEET _I

500 METERS

Figure 5. Location of test wells at the Cherry Creek site.

12

104°54'30'' R.67W.

EXPLANATION

2 TEST WELL AND NUMBERLIMIT OF LANDFILL

NOT KNOWN

39°41'30"-

T.4S.

500 1000t

1500 >

2000 FEET

500 METERS

Figure 6. Location of test wells at the Place Junior High School site.

13

Tab

le

3-~

-Ph

ysic

al

data

for

wel

ls

sam

pled

at

the

Che

wy

Cre

ek s

ite

Well

No.

1

2 3 4

5~

6 7"

8--

Lati

tude

Longitude

39°42'19"

104°56'30"

39°4

2'18

" 104°56'34"

39042'20"

104056'

36"

39°4

2'19

" 10

4056

'39"

39°4

2'23

" 104°56'39"

39°42'28"

104056'

46"

39042'32"

104°56'49"

39°4

2'33

" 104°56'45"

Water

elev

at ion

(feet

abov

e sea

level)

5,320.8

5,32

6.7

5,319.6

5,322.4

5,316.6

5,312.4

5,30

8.9

5,30

9.9

Bedr

ock

elev

atio

n (feet

above

sea

leve

l)

5,298.0

5,32

6.3

5,288.9

Land-

surf

ace

elevation

(fee

t above

sea

level)

5,335.0

5,340.3

5,33

3.6

5,33

1.7

5,32

7.6

5,32

6.9

5,32

3.9

5,32

0.8

Water

temp

era­

tu

re

(deg

rees

Ce

lsiu

s)

15.0

10.0

13-5

14.5

11.0

14.0

10.5

Specific

cond

ucta

nce

(micromhos

per

centimeter

at 25°C)

1,15

0 85

0 75

0

1 ,100

900

880

1,700

Wate

r-

qual i ty

da

ta Yes.

No.

No.

No.

Yes.

No.

Yes.

No.

Tabl

e 4. Ph

ysic

al da

ta f

or wel

ls sa

mple

d at th

e Pl

ace

Junior

Hig

h Sc

hool

site

\r\

Well

No.

2

3"

4

5~

6--

7~

8

Latitude

39°4

1 '24"

39°4

1 '25"

39°41 '27"

3904T24"

39°4

1 '26"

39°41

I23"

39°4

1 '11"

39°41 '12"

Long

itud

e

104°

54I29"

104°54'26"

104054'11"

104°54'07"

104°

54'2

0"

104°54'28"

104°54'10"

104°54'05"

Water

elevation

(fee

t above

sea

level)

5,377.0

5,386.1

5,389.1

5,392.9

5,38

9.2

5,375.1

5,395.9

5,398.0

Bedr

ock

elev

atio

n (feet

above

sea

level)

5,367.6

5,382.3

5,36

3.2

Land

- surface

elev

atio

n (feet

above

sea

level)

5,387.6

5,400.9

5,403.0

5,40

4.2

5,403.1

5,387.2

5,40

7.2

5,407.0

Water

temp

era­

ture

(degrees

Cels

ius

)

12.0

13

.5

12.0

12.0

13.0

14.5

10.5

11.0

Speci fi

e conductance

(mic

romh

os

per

cent

imet

er

at 25

°C)

1,30

0 1,230

900

900

1,900

1,500

1,250

980

Water-

qual

i ty

data No.

No.

No.

Yes.

Yes.

Yes.

No.

No.

R.66W. 104°45'30"

EXPLANATION 2 TEST WELL AND NUMBER

LIMIT OF LANDFILL NOT KNOWN

T.14S.

38°37'30" -

500 1000I

1500I

.2000 FEET _I

I 500 METERS

Figure 7.-- Location of test wells at the Hancock Road and Academy Boulevard site.

16

Tabl

e 5.

--Ph

ysic

al data

for

wells

sampled

at the Hancock Rood and Aca

demy

Boulevard

site

Well

No

.

1--

2 3

4--

5

6 7"

8-

Lat

i tude

38°47'32"

38°47'29"

38°47'37"

38°4

7'32

"

38°4

7'32

"38°47'42"

38°4

7'46

"38°47'46"

Wate

r el

evat

ion

Long

itud

e (f

eet

above

sea

level

)

104°45'49"

5,86

5.0

104°45'42"

5,85

9.2

104°45'43"

5,87

7-3

104°45'41"

5,870.4

104°45'34"

5,87

8.5

104°45'39"

5,88

1.2

104°45'35"

5,888.4

104°45'28"

5,887.1

Bedr

ock

elev

at ion

(fee

t above

sea

level)

5,83

3.1

5,81

4.1

5,86

6.4

5,84

1.7

5,86

9-5

5,87

0.7

5,885.1

5,88

1.6

Land

- surface

elev

atio

n (f

eet

above

sea

level)

5,879.1

5,87

5.6

5,88

2.4

5,88

5.7

5,893-5

5,88

6.7

5,89

9-1

5,92

2.6

Wate

r tempera­

ture

(degrees

Cel

s i us)

13-0

11.0

12.0

13-0

12.0

11.5

12.0

11.5

Specific

cond

ucta

nce

(mi cromhos

per

centimeter

at 25°C)

1 ,0

00 700

650

1 ,0

00

5,50

056

080

062

5

Wate

r-

qua

1 i ty

data No.

Yes.

No.

No.

Yes.

No.

No.

Yes.

La Plata County

The Bodo Industrial Park site (fig. 8 and table 6) is approximately 1 mile south of the city of Durango and about 1 mile west of the Animas River. The site was excavated in colluvium overlying shale. The colluvium was derived from the surrounding steep sandstone cliffs, and the base of the excavation is in the underlying shale. The surface topography slopes steeply towards the Animas River from the cliffs bordering the site. The grade from the middle of the site to the river alluvium is approximately 10 percent.

Several wells not shown in figure 8 completed in the shale bedrock out­ side of the limits of the landfill were dry--both upgradient and downgradient from the fill. Saturated material was penetrated in wells completed within the landfill limits. The water table is maintained by recharge entering the colluvium and fill material at the site.

Larimer County

The Fort Coll ins landfill (fig. 9 and table 7) is on relatively imperme­ able bedrock. The north side is truncated by Fossil Creek, which is an intermittent stream until it receives irrigation-return flow from areas down­ stream from the landfill. The shallow water table within the site probably has no hydraulic connection with ground water in the surrounding areas. Because most of the landfill is not excavated into the shale but is on the graded surface and is buried by locally derived material, the fill is slowly increasing in height above the original natural land surface. Water levels in test wells 8, 7, 6, and 5 which cross the landfill from west to east showed less than 3 feet of saturated material at the base of the fill when the wells were first measured.

Water levels, measured regularly in the test wells from July through October 1979» showed that during this time the landfill was only intermit­ tently saturated. Water from precipitation and water applied for dust sup­ pression moves down through the fill material and then east along the top of the bedrock. Because of the fill material, shale filler, compaction, and cover, water movement through the fill is very slow. This is also indicated by a relatively steep gradient of approximately 90 feet per mile along the north side near Fossil Creek. The top of the water table here generally is below the bed of Fossil Creek, but during wet seasons water from the landfill may contribute to the flow of the creek.

The gradient across the south part of the site is less steep because the ground-water table is intercepted by a ditch which is normal to the ground- water flow but causes a shift in direction. Most of the water from this part of the landfill leaves the area as a surface stream.

All test holes drilled at the Fort Coll ins landfill were within the lim­ its of the site, and only test well 2 did not penetrate fill. The 38.5 feet of fill in test well 8 was the thickest penetrated.

18

EXPLANATION

2 TEST WELL AND NUMBER

APPROXIMATE LIMIT OF LANDFILL

R.9W. 107°52'30'

37°15' -

T.34V4N.

10001

2000i

3000 4000 FEET

1000 METERS

Figure 8. Location of test wells at the Bodo Industrial Park site.

19

Tabl

e &.

--Ph

ysic

al data f

or w

ells sa

mple

d at

the

Bodo In

dust

rial

Par

k si

te

S3 o

Well

No

.

2--

3"

5"

Lat

i tude

37°1

4'20

" 37

°14'

19"

37

°14'

18"

37°1

4'22

" 37

°14'

25"

Long

i tu

de

107

053'

01"

107

052'56"

107

053'07"

107°

53'0

4"

107

052'

52"

11 ^

D j

. La

nd-

Wate

r Be

droc

k ,.

.. ,

, su

rfac

e Water

elevation

elevation

, / £

f j

- el

evat

ion

tempera-

(feet

(fee

t /,

^ J

, u

(fee

t ture

above

above

, /

, ,

. ,

. ab

ove

(deg

rees

arbitrary

arbi

trar

y ,

. .:

, .

N ,

\ j

4. \

arbitrary

Cels

ius)

datum)

datu

m)

, \

896.

0850.0

jj^' f-

914.

7ICC. 1

__.

/:>:> 2

963

937

959

919

766

.8

12.0

.7

5.0

.6

12.5

.9

9.0

.5

10.5

Spec! fi

eco

nduc

tanc

e ..

/ .

, Wa

ter-

(mi cr

omho

s qu

al i ty

Per

j «.

. ^

data

cent i me

ter

at 25

°C)

5,000

No.

2,50

0 Yes.

2,100

Yes.

1,75

0 Ye

s.

2,400

No.

105°07'30" R.69W.

EXPLANATION

2 TEST WELL AND NUMBER

APPROXIMATE LIMIT OF LANDFILL

T.6N.

40°30'

400 800 1200 1600 FEET

400 METERS

Figure 9. Location of test wells at the Fort Collins site.

21

Tab

le

1.-

-Ph

ysic

al

data

for

wel

ls

sam

pled

at

the

For

t C

oll

ins

site

ro

ro

Well

No.

1--

2~3-

4

5

6--

7"

8 9

Lati

tude

4003

0'06

"40

030'12"

40°30

I09"

40°30

I12"

40°30

I30"

40°3

0'31

"^0°30'31"

^0°30

I28"

40030'

12"

Longitude

105°

06I57"

105°

06I57"

105°07

I10"

105

007'

08"

105°06'56"

105°

07I09"

105°

07I21"

105007'

30"

105°07

I18"

Wate

r elevation

(feet

abov

e sea

level)

5,07

2.'*

5,07

^.2

5,080.1

5,08

2.8

5,08

7.7

5,096.8

5,117.9

5,15

2.5

5,12

0.6

Bedrock

elevation

(fee

t ab

ove

sea

leve

l)

5,058.1

5,06

2.1

5,07

6.1

5,07

2.2

5,08^.0

5,07

3-1

5,10

4.2

5,1*

5.1

5,111.4

Land

- surface

elev

atio

n (f

eet

abov

e se

a le

vel)

5,080.1

5,082.1

5,089.1

5,08

6.2

5,12

0.0

5,12

0.6

5,14

4.2

5,185.1

5,12

6.4

Wate

r tempera­

ture

(degrees

Cel si

us)

22.0

22.0

20.0

16.0

17.5

17-0

23.0

18.5

25.5

Spec

i fi

e co

nduc

tanc

e (m

icro

mhos

per

cent

imet

er

at 25

°C)

8,000

11 ,100

8,000

4,250

9,90

0

3,000

3,100

7,000

6,00

0

Water-

qual

i ty

data No.

Yes.

No.

Yes.

Yes.

No.

No.

No.

No.

Weld County

The towns of Brighton and Fort Lupton converted a gravel pit into a landfill (fig. 10 and table 8). The excavation was completed below the top of the water table in the alluvium of the South Platte River.

The regional water table slopes north-northwest at 10 feet per mile (unpublished data, on file at the Colorado District Office, U.S. Geological Survey) and is affected by both surface-water application and ground-water pumpage for large-scale irrigation. The presence of large-capacity irrigation wells and the proximity of the South Platte River also preclude any effects of the landfill site on the major ground-water features. None of the test holes fully penetrated the fill material.

Water Quality of the Landfills

The results of the analyses of all water samples collected during this study are tabulated in the "Water-Quality Data" section of this report. The data are useful not only in determining whether the water quality is suitable for specific uses but also for indicating the extent and nature of interac­ tion between the wastes and the ground-water system.

To facilitate the investigation of waste and ground-water interactions, selected data have been ranked in table 9- Three wells at each landfill were selected for water-quality analysis. One sample was collected from each well. Six indicators (specific conductance, iron, manganese, nitrogen, chemical- oxygen demand, and phenols) of chemical interaction between the waste and ground water in the landfills were selected to compare the relative well- water quali ty.

A ranking of the wells by each indicator is shown in table 9« For a given landfill site in table 9, the top row lists the well number having the smallest value for an indicator. The middle or second row lists the well number having the intermediate value. The third or bottom row lists the well number having the largest value for an indicator.

To rank the wells for a combined score, count the number of occurrences of the well number in row 1. Each occurrence is given the value of 1. Next, count the number of occurrences of the well number in row 2 and then in row 3. Each occurrence in row 3 is given the value of 3-

For example: Well No. 10 at the Marshall landfill occurs

321

timestimestime

ininin

rowrowrow

123

3x1=(3)2x2= (M1x3=(3)

For a combined score of (10)

23

40°02'30" -

T.1N

EXPLANATIONTEST WELL AND NUMBER

APPROXIMATE LIMIT OF LANDFILL

R.66W. 104°49'

1000I

2000 i

3000 4000 FEET_I

1000 METERS

Figure 10.-- Location of test wells at the Brighton-Fort Lupton site.

Tab

le

8.--

Phys

ica

l da

ta fo

r w

ells

sa

mpl

ed a

t th

e B

rig

hto

n-F

ort

L

upto

n si

te

Well

No

.

1--

2

3"

4--

5

Lat

i tude

40°02'08"

40°02'04"

40°01 '59"

40°02'06"

40°02' 14"

Long

! tude

104

049'00"

104

049'00"

104°49'02"

104°

49'0

8"

104°49'09"

Water

elevation

(fee

t above

sea

level)

A, 921

. 7

M21.8

A, 923

. 5

*t, 921

.14,919-6

Bedrock

elevat ion

(fee

t ab

ove

sea

level)

Land-

surface

elevation

(fee

t above

sea

1 evel

)

4,9^

0.9

4,94

2.8

4,94

1.8

4,933.9

4,92

5.1

Water

tempera­

ture

(d

egre

es

Celsius)

13.0

15

.0

13.0

10.0

Speci fie

conductance

(mi cr

omho

s pe

r cent ime

ter

at 25°C)

2,02

5 1,275

1,30

0 1,

250

Water-

qua

1 i t

y da

ta Yes.

Ye

s.

No.

No.

Yes.

ro

Table 9- --Wat&r-quality rank of samples from sump or wellsat each landfill site

[For each landfill site, the sump or the number of the well with the smallestval uenumbernumberue ofrow 2,

for each 1 iof the welof the wel

1 for each

sted1 wi1 wi

water-qua 1 i tyth theth the

occurrenceand a value of 3 for

and recorded in parentheses

Row *«*"'<:conductance

1--2 3

Sump53

1 ron

Sump35

characteristicintermediate valuelargestin row

value is 11, a value

each occurrence inbeside

Manganese

Golden

the

Ni

isis 1 i sted in

listed in rowisted inof 2row

wel 1 number

trogen

for3,in

Chemical oxygen demand

row 3 G i

row 1 , the2, and theving a val-

each occurrence inthe values are summedthe last column]

Phenols Combi ned score

Rubble siteSump

35

Marshal1--2 3

1--2 3"

1031

751

310

1

715

1031

Cherry175

Place Junior1--2 3"

465

645

465

Hancock Road and1--2 3"

825

( )0)5

825

Sump53

1 site31

10

Sump53

1031

Sump53

310

1

Sump(6)5(14)3(16)

3(9)10(10)1(17)

Creek site175

High School si645

175te645

Academy Boulevard s

Bodo Industri1 2 3"

432

432

342

Fort Col 11 2--3

452

245

245

Brighton-Fort1 2--3"

521

(i)( ! )

1

215

528

al Park432

ins site542

Lupton521

(((

si te

si te

i)M!)

432

524

125

177

465

ite825

432

245

0)0)5

1(9)7(13)5(14)

4,6(9)4,6(9)5(18)

8(6)2(8)5(13)

4(7)3(11)2(18)

2(11)4(12)5(13)

2(7)5(11)1(18)

^Analysis was performed, but constituent was not present at concentra­ tions above the detection limit.

26

The sum of all scores for a sample is in parentheses next to the sample number. It should be emphasized that these scores have only relative values in determining which samples are most likely to represent the degradation of water quality caused by the interaction with wastes. A score of 10, for exam­ ple, does not necessarily imply a water quality twice as degraded as a score of 5« Neither are the scores transferable from site to site; they are valid only within a given site. Also, the arbitrary choice of the indicators of chemical interaction can affect the score for a given sample and perhaps its rank relative to the other samples.

In selecting wells for sampling, an attempt was made to obtain wells suspected of intercepting water representing no interaction with wastes, the most interaction, and an intermediate level of interaction or mixing between leachate and unaffected water typical of the aquifer. Thus, if it is desired to estimate the worst-case water quality which is likely to move downgradient from a given site, the analysis of the sample with the largest combined score shown in table 9 can be used as a guide. In some instances, such as the samples from the Marshall or Hancock Road and Academy Boulevard sites, this water quality may be unsuitable for many uses. Recommended and mandatory standards (U.S. Environmental Protection Agency, 1977) are available to judge the suitability of water for various uses. On the basis of these standards for the more restrictive uses, such as for drinking supplies or as a source of water to stream or lake systems containing aquatic life, concentrations commonly exceeded standards with respect to iron (300 micrograms per liter, recommended), manganese (50 micrograms per liter, recommended), phenols (l microgram per liter), nitrate as nitrogen (10 milligrams per liter, manda­ tory), and salinity (250 milligrams per liter, recommended, of chloride or sulfate). Constituents in some water samples representing the least contami­ nated perhaps uncontaminated water at a site may exceed these standards because of the quality of water in the surrounding deposits or bedrock or the use of land for purposes other than landfill. The presence of reducing condi­ tions within or beneath a landfill may even cause a decrease in sulfate con­ centrations by the reduction of sulfate to sulfide followed by precipitation of the sulfide. Similarly, the nitrogen standard is 10 milligrams per liter of nitrate plus nitrite expressed as nitrogen, whereas reducing conditions favorable to nitrogen generation in landfills typically produce ammonia or organic nitrogen. Oxidation of these reduced nitrogen species to nitrate may occur if contaminated ground water moves away from the landfill and mixes with oxygenated ground water or interacts with oxygen in the soil atmosphere.

The data collected in this study are useful in estimating the direction from the landfill that ground-water deterioration may occur, the probable chemical nature, and the magnitude of the degradation. For sites with many wells intercepting the water table, variations in the specific-conductance values (tables 1-8) may be used as a guide in delineating the areal extent of present degradation.

27

SUMMARY

The eight landfills sampled in this study all have interacted with the shallow ground water to some extent, as exemplified by the variation in specific conductance and the analytical data for major and trace chemical species. This study of the contamination of the ground water generally was restricted to the geographical limits of the original landfills, although a few nearby wells have been sampled; however, data are not sufficient to rule out the contamination of nearby surface-water systems at some sites. Similar­ ly, data are not sufficient to rule out the contamination of deeper ground- water systems at some sites.

Water-quality degradation at the sites was similar in nature to the deg­ radation at other sites in other studies. Decomposition products of organic matter (ammonia, organic nitrogen, and phenols), increased salinity caused by leaching debris or increased weathering of soil materials, and dissolution of metals from the soil materials caused by reducing conditions (iron and manga­ nese) occur to some extent at all of the sites. Some samples thought to represent water uncontaminated by the landfills exceeded standards for drink­ ing-water supplies or water used by aquatic life, as did all samples thought to represent contaminated well water.

Data from this study are useful in predicting the direction of possible ground-water degradation now or in the future. The data also are useful in estimating the chemical nature and possibly the worst-case magnitude of ground-water degradation shown at each site.

REFERENCES CITED

Kimrnel, G. E., and Braids, 0. C., 1975, Preliminary findings of leachate study on two landfills in Suffolk County, New York: U.S. Geological Survey Journal of Research, v. 3, no. 3» P« 273'280.

___1977, Leachate plumes in ground water from Babylon and Islip landfills, Long Island, New York: U.S. Geological Survey Open-File Report 77~583, 72 p.

Skougstad, M. W., Fishman, M. J., Friedman, L. C., Erdmann, D. E., and Duncan, S. S., 1979, Methods of analysis of water and fluvial sediments: U.S. Geological Survey Techniques of Water-Resources Investigation, Book 5, Chapter A-l, 626 p.

U.S. Environmental Protection Agency, 1977, Quality criteria for water: Wash­ ington, D.C., U.S. Government Printing Office, 256 p.

28

WATER-QUALITY DATA

29

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ro roco o en 4k

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0 1

oCO 3*O O CD CO 1-1

co i 1-1 5»m ) » »r~ m i 1 1. o

O O 1

3 o -n co m i

m

m xa 3

a* i i o

m co

e? 5 cr z

i c -fc CO

MULTIPLE STATION

LIST

ING

DATE OF

SAMP

LE

03-2

0-80

03-2

0-80

03-2

0-80

11-2

8-79

11-2

8-79

11-2

8-79

11-0

9-79

11-0

9-79

11-09-79

12-0

3-79

12-0

3-79

12-0

3-79

11-2

9-79

11-2

9-79

11-2

9-79

12-1

7-79

12-17-79

12-1

7-79

12-0

4-79

12-0

4-79

12-0

4-79

11-2

7-79

11-2

7-79

11-27-79

NITRO­

GEN,

AMMONIA

DIS­

SOLV

ED(MG/L

AS N

)

1.1

14 14.10

.20

.05

.03

.13

3.5 .14

13.4

0.04

.34

.10

.09

.12

4.4

24 17

.04

.09

1.9

NITRO-

GEN,

AM­

MONI

A +

ORGANIC

DIS.

(MG/L

AS N

)

1.4

25 46.66

.97

.73

.94

.89

39.77

14 2.1 .44

3.6 .49

1.3

2.4

8.7

28 19

.49

2.7

4.2

NITRO­

GEN,

N02+

N03

DIS­

SOLV

ED(MG/L

AS N

)

.51

.02

.07

2.3 .03

2.4

4.3

2.1 .10

10* .1

04.

89.6 .03

.21

30; 65* 4.9 .04

.08

3.3

60* .1

5

PHOS­

PHORUS,

DIS­

SOLV

ED(M

G/L

AS P

)

.010

.010

.010

.000

.010

.020

.000

.040

.000

.080

.010

.120

.180

.020

.010

.050

.020

.060

.380

.030

.020

.000

.000

CARBON,

ORGANIC

TOTAL

(MG/

LAS

C)

15 32 9.0

92 23 37 28 160 19 52 22 4.6 .0 5.1

7.6

9.3

24 130

110 26 31 28

HARD­

NESS

(MG/L

ASCA

C03)

1100

1300

1400 270

3100 310

370

360

590

310

370

310

110

3900 430

460

810

440

2300

2500 570

3700

3300

HARD

­NESS,

NONC

AR-

BONA

TE(MG/L

CAC0

3)

580

300

220

110

2400 16 90 100 0 0 0 0 59

1400 110

260

510 0

1500

1700 360

3300

2700

CALCIUM,

DIS­

SOLV

ED(M

G/L

AS C

A)

230

280

310 78 790 91 120

120

170

100

110

100 35

1200 91 130

230

120

450

500

140

1200 110

MAGN

E­SI

UM,

DIS­

SOLV

ED(M

G/L

AS M

G)

130

140

140 18 280 19 17 15 39 14 23 14 4.

522

0 50 33 58 34 280

300 54 160

730

SODI

UM,

DIS­

SOLVED

(MG/

LAS

NA

)

110

110

160 46 38 19 64 220

110

180

110 99 5.

113

0 90 120

230

110

390

160 55

1300

1700

SODI

UMAD

­SO

RP­

TION

RATIO

1.4

1.3

1.9

1.2 .3 .5 1.4

5.0

2.0

4.5

2.5

2.5 .2 .9 1.9

2.4

3.5

2.3

3.6

1.4

1.0

9.4

13

SODIUM

PERC

ENT

18 15 20 33 4 15 27 56 27 56 36 40 9 7 31 44 46 42 26 12 17 43 93

10

MULT

IPLE

STATION

LIST

ING

DATE OF

SAMP

LE

03-2

0-80

03-20-80

03-20-80

11-2

8-79

11-2

8-79

11-2

8-79

11-0

9-79

11-09-79

11-0

9-79

12-03-79

12-03-79

12-03-79

11-29-79

11-29-79

11-29-79

12-17-79

12-17-79

12-17-79

12-0

4-79

12-04-79

12-0

4-79

11-2

7-79

11-2

7-79

11-27-79

SODIUM+

POTAS­

SIUM

,DI

S­SO

LVED

(MG/L

AS NA)

120

140

190 51 43 21 71 230

170

180

150

110 5.

913

0 90 130

240

130

510

280 58

1300 480

1700

POTAS­

SIUM

,DI

S­SO

LVED

(MG/L

AS K)

6.2

29 28 5.0

5.1

1.9

7.1

7.1

59 4.3

42 9.8 .8 1.2 .4

10 12 20 120

120 3.

132 79 19

CHLO­

RIDE,

DIS­

SOLVED

(MG/L

AS C

L)

15 36 220 25

1800*

14 39 250

190 73 48 47 4.

9470* 32 140

220

160*

350 64 9.

7130.

310

150

1

SULF

ATE,

DIS­

SOLV

ED(M

G/L

AS S04)

740*

430*

190

170 15 31 140

190 80 220

110

140 34 I5*

260

210.

410 54 80 17 450*

6200*

1100*

6100

1

FLUO

-RIDE,

DIS­

SOLV

ED(MG/L

AS F) .3 .2 .4 .3 .1 .1 .5 .6 .6

1.3

1.2

1.2 .9 .5 3.5 .6 .6 .8 .9 .4 1.4 .1 .3 .2

SILI

CA,

DIS­

SOLV

ED(M

G/L

ASSI02)

14 19 22 17 26 35 30 34 39 26 29 24 17 18 17 26 27 21 23 33 8.3

11 17 15

ARSENIC,

DIS­

SOLV

ED(U

G/L

AS A

S) 1 3 3 1 9 1 2 2 1 6 5 1 8 2 1 1 2 8 3 1 1 6 31

BORO

N,DIS­

SOLV

ED(U

G/L

AS B

)

260

500

800 80 200 40 80 110 250

550

230 20 210 50 380

500

310*

1800*

1300 140

490*

1200

*78

0

7cn

CADMIUM,

DIS­

SOLV

ED(U

G/L

AS C

D)

0 0 0 <1 0

<10 0 -- 3 2 2 3 0 2

<!1

<1^ 10* 10 2 1 0 0

2m

CHRO­

MIUM,

DIS­

SOLV

ED(U

G/L

AS C

R)

0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 10 0 10 0 0 10 0 10 1

COPP

ER,

DIS­

SOLVED

(UG/

LAS C

U)

2 2 2 0 0 0 2 0 -- 0 0 1 0 2 0 0 0 0 0 0 0 0 0 01

IRON,

DIS­

SOLV

ED(U

G/L

AS FE

)

40*

9800*

23000 20*

65000 20 20 10*

17000 20 80

<10*

570*

5000

0<io

<10 40 <10*

5900*

8000 20 80

*5200*

9800

lonn

MU

LTIP

LE

STA

TIO

N

LIS

TIN

G

VjO

V

jO

DATE OF

SAM

PLE

03-2

0-80

03

-20-

80

03-2

0-80

11

-28-

79

11-2

8-79

11-2

8-79

11

-09-

79

11-0

9-79

11-0

9-79

12-0

3-79

12-0

3-79

12

-03-

79

11-2

9-79

11

-29-

7911

-29-

79

12-1

7-79

12

-17-

79

12-1

7-79

12

-04-

79

12-0

4-79

12-0

4-79

11

-27-

79

11-2

7-79

11

-27-

79

LEAD

,DI

S­SOLVED

(UG/L

AS PB)

1 1 0 0 0 0 0 0 1 0 1 1 4 1 1 0 0 1 1 0 0 0 0

Un

MANGA­

NESE,

DIS­

SOLVED

(UG/L

AS M

N)

1200*

noo*

1600

.1200*

7000 110 10*

1300*

2900 230 *

1400*

550 20*

22000*

360

100

310*

3700*

990*

1300 2*51

0*58

0*3100 l«;n

ZINC,

DIS­

SOLV

ED(UG/L

AS Z

N)

10 10 10 <3 20 <30 0 <3 8 <3 <3 30 <3 8 40 6 80 20 <3 200 0 0

1 nn

n

LITH

IUM,

DIS­

SOLV

ED(U

G/L

AS L

I)

180 70 40 20 70 40 20 30 ~ 40 30 40 10 40 40 40 30 30 60 40 40

2500 230

1300

SELE

­NIUM,

DIS­

SOLV

ED(UG/L

AS SE)

0 0 1 3 0 0 4 6 Is* 0 3 0 0 0 2 3 1 0 0 3*

180 1 1

1m

PHEN

OLS

(UG/L)

2* 8* 20* 1* 35 0 1* 8* 19* 2 * 3* 5 6

1000* 5 0 3* 20*

13 3* o* 7* 11 1

SOLI

DS,

SUM

OFCO

NSTI

­TU

ENTS

,DIS­

SOLV

ED

(MG/L)

1570

1650

1780 467

3450 396

605

1000

1060 866

782

649

174

3620 738

923

1660 810

2050

1650 863

9540

3340

9210

SOLIDS,

DIS­

SOLV

ED(TONS

PER

AC- FT)

2.14

2.24

2.42 .64

4.69 .54

.82

1.36

1.44

1.18

1.06 .88

.24

4.92

1.00

1.26

2.26

1.10

2.79

2.24

1.17

13.0 4.54

12.5

NITRO­

GEN,

AMMONIA,

DIS­

SOLVED

(MG/L

AS N

H4)

1.4

18 18.1

3.2

6

.06

.04

.17

4.5 .18

17.5

2.0

5.4

4.1

3

.12

.15

5.7

31 22

.05

.12

73 2.4

MERCURY,

DIS­

SOLVED

(UG/L

AS H

G)

.0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 .0 1,

1 U

.S.

En

viro

nm

en

tal

Pro

tectio

n

Age

ncy,

19

76,

Drin

kin

g-w

ate

r crite

rio

n.

2 U

.S.

Envi

ronm

enta

l P

rote

ctio

n

Age

ncy,

19

76,

Irrig

atio

n-w

ate

r crite

rio

n.

Equ

als

or

exce

eds

U.S

. E

nvi

ron

me

nta

lP

rote

ction

Age

ncy,

19

76,

Wa

ter-

qu

alit

y

crite

rion.