Field Tests of Nylon-Screen Diffusion Samplers and Pushpoint ...

Field Tests of Nylon-Screen Diffusion Samplers and Pushpoint Samplers for Detection of Metals in Sediment Pore Water, Ashland and Clinton, Massachusetts, 2003

By Marc J. Zimmerman, Don A. Vroblesky, Kimberly W. Campo, Andrew J. Massey, and Walter Scheible

In cooperation with the U.S. Environmental Protection Agency Measurement and Monitoring for the 21st Century Initiative

Scientific Investigations Report 2005-5155

U.S. Department of the InteriorU.S. Geological Survey

U.S. Department of the InteriorGale A. Norton, Secretary

U.S. Geological SurveyP. Patrick Leahy, Acting Director

U.S. Geological Survey, Reston, Virginia: 2005

For sale by U.S. Geological Survey, Information Services Box 25286, Denver Federal Center Denver, CO 80225

For more information about the USGS and its products: Telephone: 1-888-ASK-USGS World Wide Web: http://www.usgs.gov/

Any use of trade, product, or firm names in this publication is for descriptive purposes only and does not imply endorsement by the U.S. Government.

Suggested citation:Zimmerman, M.J., Vroblesky, D.A., Campo, K.W., Massey, A.J., and Scheible, Walter, 2005, Field Tests of Nylon-Screen Diffusion Samplers and Pushpoint Samplers for Detection of Metals in Sediment Pore Water, Ashland and Clinton, Massachusetts, 2003: U.S. Geological Survey Scientific Investigations Report 2005-5155, 51 p.

iii

Contents

Abstract ……………………………………………………………………………………… 1Introduction …………………………………………………………………………………… 2Study Areas …………………………………………………………………………………… 3Study Design ………………………………………………………………………………… 6Preliminary Laboratory Testing and Analysis ………………………………………………… 6

Sampler Equilibration …………………………………………………………………… 6Equipment Blanks ……………………………………………………………………… 7

Sediment Pore Water Field-Sampling Techniques …………………………………………… 11Nylon-Screen Diffusion Samplers ……………………………………………………… 11Pushpoint Samplers ……………………………………………………………………… 12Site Selections …………………………………………………………………………… 13Quality-Control Sampling and Results …………………………………………………… 13

Comparison of Metal Concentrations in Pore Water Collected with Nylon-Screen Diffusion and Pushpoint Samplers …………………………………………………… 15

Time Series of Nylon-Screen Diffusion Sampler Data …………………………………… 16Comparison of all Nylon-Screen Diffusion Samples and Pushpoint Samples by Site …… 17

Summary and Conclusions …………………………………………………………………… 18Acknowledgments …………………………………………………………………………… 19References Cited ……………………………………………………………………………… 19

Figures 1–3. Photographs showing: 1. The 125-milliliter nylon-screen diffusion sampler ……………………………… 2 2. PVC shovel for inserting nylon-screen diffusion sampler into sediments ……… 3 3. A, The 91-centimeter PushPoint Extreme Sampler; and B, Detail of tip ……… 3 4. Map showing locations of study areas: A, Mill Pond, Sudbury River, Ashland,

Massachusetts; and B, Rigby Brook, Clinton, Massachusetts ……………………… 4 5, 6. Graphs showing: 5. Comparisons of A, concentrations; and B, relative percent differences

between water samples obtained from the test container and from nylon-screen diffusion samplers after 4 days of equilibration ………………… 7

6. Laboratory quality-control data for A, barium; and B, zinc for components of sampling equipment ………………………………………………………… 10

7. Photograph showing collection of a field sample from nylon-screen diffusion sampler by using syringe, filter, and hypodermic …………………………………… 12

8. Schematic showing distribution of sampling sites at the A, Nyanza study area, Ashland; and B, Rigby Brook study area, Clinton …………………………………… 14

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9, 10. Boxplots showing: 9. Selected metals concentrations in 25 samples collected with nylon-

screen diffusion samplers and 35 samples collected with pushpoint samplers at the Nyanza study area, Ashland, May 2003 ……………………… 16

10. Selected metals concentrations in 24 samples collected with nylon- screen diffusion samplers and 34 samples collected with pushpoint samplers at the Rigby Brook study area, Clinton, May to June 2003 ………… 17

11–14. Graphs showing: 11. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron;

F, manganese; and G, zinc at the Nyanza study area, Ashland, May 2003 …… 21 12. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron;

F, manganese; and G, zinc at the Rigby Brook study area, Clinton, May to June 2003 ……………………………………………………………………… 25

13. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Nyanza study-area sampling sites, Ashland, May 2003 …………………………………………………………… 29

14. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, June 2003 ……………………………………………………………… 35

Tables 1. Concentrations of solutes in water collected from bucket by using peristaltic

pump and from 125-micron-mesh nylon-screen diffusion samplers immersed in the bucket, November 2000 ……………………………………………………… 6

2. Concentrations of metals detected during quality-control testing of the sampling process …………………………………………………………………… 8

3. Target analytes, their project action limits, and minimum reporting levels used for this study ………………………………………………………………………… 9

4. Medians of paired relative percent-difference values for individual metals in nylon-screen diffusion samples and pushpoint samples collected at the Nyanza study area, Ashland, Massachusetts, and at the Rigby Brook study area, Clinton, Massachusetts …………………………………………………………… 15

5. Concentrations of metals detected in ground water 20 cm below sediment surface at selected well locations for the Nyanza Superfund Site, Ashland, June 2001 …………………………………………………………………………… 18

6. Concentrations of metals in quality-control samples during field studies at the Nyanza study area, Ashland, and the Rigby Brook study area, Clinton ………… 41

7. Concentrations of metals detected in samples from the Nyanza study area, Ashland …………………………………………………………………………… 46

8. Concentrations of metals detected in samples from Rigby Brook study area, Clinton ……………………………………………………………………………… 49

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Conversion Factors, Datum, and Abbreviations

Multiply By To obtain

centimeter (cm) 0.3937 inch (in.)

liter (L) 0.2642 gallon (gal)

meter (m) 1.094 yard (yd)

micron (µ) 0.00003937 inch (in.)

milliliter (mL) 61,020 cubic inch (in3)

millimeter (mm) 0.03937 inch (in.)

Horizontal coordinate information is referenced to the North American Datum of 1983 (NAD 83).

Specific conductance is given in microsiemens per centimeter at 25 degrees Celsius (µS/cm at 25°C).

Concentrations of chemical constituents in water are given either in milligrams per liter (mg/L) or micrograms per liter (µg/L).

Ag silver Al aluminum As arsenic Ba barium Be beryllium Cd cadmium Co cobalt Cr chromium Cu copper Fe iron Hg mercury Mn manganese Mo molybdenum Ni nickel Pb lead Sb antimony V vanadium Zn zinc DO dissolved oxygen ICP-MS inductively coupled plasma—mass spectrometry NSDS nylon-screen diffusion sampler PAL project action limit PPS pushpoint sampler RPD relative percent difference USEPA U.S. Environmental Protection Agency USGS U.S. Geological Survey VOC volatile organic compound

Field Tests of Nylon-Screen Diffusion Samplers and Pushpoint Samplers for Detection of Metals in Sediment Pore Water, Ashland and Clinton, Massachusetts, 2003

By Marc J. Zimmerman1, Don A. Vroblesky2, Kimberly W. Campo1, Andrew J. Massey1, and Walter Scheible3

AbstractEfficient and economical screening methods are needed

to detect and to determine the approximate concentrations of potentially toxic trace-element metals in shallow ground-water-discharge areas (pore water) where the metals may pose threats to aquatic organisms; such areas are likely to be near hazardous-waste sites. Pushpoint and nylon-screen diffusion samplers are two complementary options for use in such environments.

The pushpoint sampler, a simple well point, is easy to insert manually and to use. Only 1 day is required to collect samples. The nylon-screen diffusion sampler is well suited for use in sediments that do not allow a pump to draw water into a pushpoint sampler. In this study, both types of devices were used in sediments suitable for the use of the pushpoint sampler. Sampling with the nylon-screen diffusion sampler requires at least two site visits: one to deploy the samplers in the sediment, and a second to retrieve the samplers and collect the samples after a predetermined equilibration period.

Extensive laboratory quality-control studies, field testing, and laboratory analysis of samples collected at the Nyanza Chemical Waste Dump Superfund site along the Sudbury River in Ashland, Massachusetts, and at a Superfund site-assessment location on Rigby Brook in Clinton, Massachusetts, indicate that these two devices yield com-parable results for most metals and should be effective tools

for pore-water studies. The nylon-screen diffusion samplers equilibrated within 1–2 days in homogeneous, controlled conditions in the laboratory. Nylon-screen diffusion samplers that were not purged of dissolved oxygen prior to deployment yielded results similar to those that were purged. Further test-ing of the nylon-screen diffusion samplers in homogeneous media would help to resolve any ambiguities about the data variability from the field studies.

Comparison of data from replicate samples taken in both study areas shows that even samples taken from sites within a half-meter radius of one another have distinct differ-ences in pore-water trace-element concentrations. Sequential replicate samples collected with the pushpoint sampler yield consistent results; moving the pushpoint sampler even 5 to 10 centimeters, however, generally produces a second set of data that differs enough from the first set of data to indicate a heterogeneous environment. High concentration biases for barium and zinc in laboratory and field samples collected with nylon-screen diffusion samplers, however, may make their use inappropriate for studies of these metals.

Analyzing samples with high iron concentrations required sample dilution by factors of 2 or 10. Because these dilutions caused increases in the reporting levels by the same proportion, a substantial fraction of the data was censored. The results from undiluted samples, however, indicate that both devices should be useful for sampling ground water with metal concentrations close to reporting limits.

1U.S. Geological Survey, Northborough, Massachusetts.2U.S. Geological Survey, Columbia, South Carolina.3Columbia Analytical Services, Rochester, New York.

Abstract 1

IntroductionMetal-enriched ground water may pose threats to aquatic

organisms in ground-water discharge areas in many environ-mental settings, particularly near hazardous-waste sites. The development of efficient and economical screening devices to detect metal-enriched ground water in streambed sediments near the ground-water/surface-water interface would enable investigators to assess potential threats to aquatic organisms and to identify areas of contaminated ground-water discharge. The data obtained from such reconnaissance-level sampling would then provide a basis for intensive site investigations. Because of this need for reconnaissance-level sampling devices, the U.S. Geological Survey (USGS), in coopera-tion of the U.S. Environmental Protection Agency (USEPA), through the Measurement and Monitoring for the 21st Century Initiative (21M2), conducted an investigation of the effective-ness during 2003 of the stainless-steel push-point sampler (PPS) and the nylon-screen diffusion sampler (NSDS). This Office of Solid Waste and Emergency Response (OSWER) ini-tiative is designed to identify and encourage the use of promis-ing measurement and monitoring technologies in response to waste-management and site-cleanup program needs by matching existing and emerging technologies with OSWER program and client needs. The investigation was carried out at two study areas with previously reported contamination: the Nyanza Chemical Waste Dump Superfund site (Campbell and others, 2002) along the Sudbury River in Ashland, MA, and at a Superfund site-assessment location along Rigby Brook in Clinton, MA. In particular, screening with these devices was intended to determine whether trace-metal concentra-tions exceeded guidelines (Project Action Limits, or PALs, also known as Surface Water Benchmarks, including Ambient Water Quality Criteria; Bart Hoskins, Ecological Risk Assessor, U.S. Environmental Protection Agency, written com-mun., 2002) intended to protect aquatic life, not to determine whether drinking-water criteria were exceeded or to detect these metals at trace-level concentrations.

The report includes results of laboratory-based quality-control studies. The chemical analyses for this investigation include results for 21 metals; however, the report focuses on the few metals that were most frequently detected.

The NSDS consists of a 63-mm diameter, 125-mL polypropylene jar (Thomas Scientific) with the center of the cap removed, and with only a screw-on rim for securing a piece of 120-µ nylon-screen mesh (Small Parts, Inc.). The mesh, approximately 10 cm by 10 cm, is placed over the jar’s mouth and secured by screwing the rim back onto the jar (fig. 1). The 125-mL volume of the NSDS is sufficient to meet the USEPA laboratory’s 100-mL sample-volume requirement. In practice, the NSDS is filled with deionized water, buried in the sediment and allowed to equilibrate with its environment. To minimize the possibility of contaminating the site with a metal shovel when inserting the NSDS into the sediment, a

shovel-like device constructed from 10-cm polyvinyl chloride (PVC) pipe (with 6.4-mm wall thickness) is used for sam-pler deployment (fig. 2). Beveled edges enable this shovel to penetrate even the coarsest sediments to a depth of at least 20 cm. Preliminary tests showed that concentrations of inor-ganic constituents in well water and arsenic (As) in streambed sediments in samples collected by NSDSs compared favorably with concentrations measured in samples collected by other methods (Vroblesky and others, 2002).

A PPS is designed to sample sediment pore water with minimal disturbance to the site. The PushPoint Extreme Sampler (fig. 3), the commercially produced model used in this study, consists of a 6.4-mm diameter, stainless-steel tube with a machined point and 4-cm-long slotted screen (0.635-mm slots) near the tip (Henry, 2001); this study used a 91-cm-long version of the sampler. An internal guard rod positioned within the bore adds rigidity to the sampler during insertion.

Filter

Hypodermic needle

MeshJar rim

Jar

Nylonelectrical tie

Figure 1. The 125-milliliter nylon-screen diffusion sampler.

2 Field Tests of Samplers for Detection of Metals in Sediment Pore Water, Ashland and Clinton, MA, 2003

The PPS has been used to collect water for analysis of volatile organic compounds (VOCs) (Henry, 2001; Church and others, 2002; Zimmerman and others, 2005), but has not been tested for characterization of metals in pore water. Although USGS manuals recommend against using metal sampling devices to collect samples for metal analysis (Wilde and others 1999), that guidance is intended for sampling to determine low-level concentrations near detection levels, not the higher concentrations usually associated with contamination.

Not all sediments have physical characteristics that allow water to be drawn in readily through the PPS; fine organic material, silt, and clay may block the openings (Zimmerman and others, 2005). In these situations, the NSDS, which can be left buried in the sediments for any length of time, may prove more appropriate. Therefore, the efficacy of both tools was examined in this study.

Study AreasThe study areas (fig. 4) were selected because the com-

position and texture of their sediments differ from one another and may affect the efficacy of the two sampling devices. According to a previous study (Roy F. Weston, Inc., 2001), the Nyanza study area is within a zone affected by a ground-water plume that includes organic contaminants and metals such as As, beryllium (Be), chromium (Cr), cobalt (Co), manganese (Mn), and mercury (Hg). The local hydrogeologic setting includes glacial lake deposits, till, and fractured granite. The surficial streambed sediments at the Nyanza site contain decayed and living plant material.

Figure 2. PVC shovel for inserting nylon-screen diffusion sampler into sediments.

Figure 3. A, The 91-centimeter PushPoint Extreme Sampler; and B, Detail of tip. Screen is 4 centime-ters long and tube diameter is 6.4 millimeters.

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Study Areas 3

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The Rigby Brook study area, which was the subject of a Superfund site-assessment investigation (Forest Lyford, U.S. Geological Survey, oral commun., 2002), is impounded by a beaver dam. An abandoned manufacturing plant and a former waste dump adjacent to the impounded area on Rigby Road were thought to be sources of contamination, prompting the

site assessment. The sediments of flooded areas of the Rigby Brook study area contained the remnants of plant matter, but many sampling sites there were primarily silty or sandy in nature. The coarse, sandy sediments of the Rigby Brook study area contrasted with the fine-grained sediments of the Nyanza study area.

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STUDY AREA SHOWN IN SCHEMATIC IN FIGURE 8B

EXPLANATION

Base from Massachusetts Executive Office of Environmental Affairs, MassGIS, 1:24,000, 2004Polyconic projection, 1983 North American DatumMassachusetts coordinate system mainland zone

RIGBY BROOK STUDY AREA, CLINTON, MASSACHUSETTS4B.

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Figure 4—Continued. Locations of study areas: A, Mill Pond, Sudbury River, Ashland, Massachusetts; and B, Rigby Brook, Clinton, Massachusetts.

Study Areas 5

Study DesignThe study was divided into two distinct phases. First,

the equilibration time for the NSDS units was determined. Equilibration was tested at the USGS’s South Carolina Water Science Center in Columbia, SC, and at Columbia Analytical Services in Rochester, NY. Quality-control testing was done at the MA-RI Water Science Center in Northborough, MA, to determine whether the NSDSs, PPSs, or other equipment used introduced unacceptable contamination to samples. A com-mercial laboratory in South Carolina and Columbia Analytical Services analyzed the equilibration samples; the USEPA Region I Laboratory in Chelmsford, MA, used inductively coupled plasma-mass spectrometry (ICP-MS) to analyze the quality-control and field samples for dissolved metals.

The field investigation with the two types of sampling devices constituted the second phase of the study. The NSDS units were deployed for up to 2 weeks at 15 sites in each study area. One to five NSDSs were left at each site. Samples were collected at intermediate times at five sites in each study area. At the end of the 2-week period, the remaining NSDS and PPS samples were collected.

The field-study design, which included the insertion of multiple NSDS units at the same sites, was based on the implicit assumption of a homogeneous sedimentary envi-ronment. Coarse, and occasionally impenetrable, substrate, however, made it difficult to place samplers within 20 cm of each other. In practice, multiple samplers were deployed within about a 0.5-m radius. In addition, the PPSs were expected to capture the same pore water as the NSDSs dur-ing the same time intervals. Nonetheless, variability among the NSDS samples, in particular, and between the NSDS and PPS samples was expected. Replicate PPS samples collected without removing and reinserting the PPSs were expected to produce the most consistent results; replicate PPS samples collected from the same site after removing and reinserting the PPS 5 to 20 cm away from the original position were expected to demonstrate more variability than the other replicate PPS samples.

Preliminary Laboratory Testing and Analysis

Before deployment and sampling, the samplers were subjected to a series of laboratory quality-control tests. These tests determined the rate at which water inside the NSDS units equilibrated with the external environment and whether either the equipment or the sampling process could provide a source of sample contamination.

Sampler Equilibration

To determine the minimum time required for equilibra-tion with the external medium, various NSDS units were filled with deionized water and placed in a bucket of water contain-ing arsenic and chloride at concentrations of about 230 µg/L and 265 mg/L, respectively. On the first and fourth days of equilibration, one NSDS unit was removed from the bucket to provide a water sample for analysis. On the seventh day, two NSDS units were removed to provide duplicate water samples. On each of these days, water also was pumped from the test bucket for analysis. Arsenic and chloride concentra-tions in the NSDS units had equilibrated with concentrations in the test-bucket water by the first day (table 1). In a separate test, NSDSs were filled with deionized water and allowed to equilibrate in test containers holding solutions of 16 dissolved metals. Once a day, during a 4-day period, one NSDS was removed and samples from the NSDS and the test container were analyzed. After 4 days, concentrations of all but one metal in water from the samplers corresponded closely to con-centrations in the test solution (fig. 5). Only the results for Ag had a high relative percent difference (RPD); this difference probably was a result of decreased analytical accuracy because the Ag concentration was lower than that of the other analytes.

Table 1. Concentrations of solutes in water collected from bucket by using peristaltic pump and from 125-micron-mesh nylon-screen diffusion samplers immersed in the bucket, Novem-ber 2000.

[NS, not sampled; NSDS, nylon-screen diffusion samplers]

Day

Arsenic, in micrograms per liter

Chloride, in milligrams per liter

Sample pumped

from bucket

Sample from NSDS

Sample pumped

from bucket

Sample from NSDS

0 NS 0 NS 01 240 240 260 2704 240 250 270 2607 240 250 270 2607 230 240 270 270


Equipment Blanks

NSDS parts, PPSs, and other pieces of sampling equip-ment were subjected to a series of equipment-blank tests in triplicate under controlled laboratory conditions. These tests were designed to determine if the equipment would release metals in concentrations high enough to interfere with the interpretation of analytical results from field-sampling applications.

Various NSDS units were separated into their constituent parts and soaked in 5 percent HCl in 19-L acid-cleaned plastic buckets for 3 days. The units were then rinsed with tap water and deionized water before soaking for 7 days in 4 L of deion-ized water obtained from the USEPA Region I Laboratory. Samples were collected from all of the containers and acidi-fied to pH 2 with Ultrex-grade nitric acid, as were all samples in this study. All samples were analyzed by the USEPA. The

data (table 2) indicate that, over the 7-day period, the plas-tic components did not release metals in concentrations that would compromise an investigation of a contaminated site. Three metals were detected: Barium (Ba), Copper (Cu), and Zinc (Zn). Ba was detected at the reporting level of 0.2 µg/L in a single sample; Cu was detected in two samples at con-centrations slightly higher than the reporting level of 1.0 µg/L (according to the official USEPA laboratory-data reports, the low-level Cu concentrations detected were caused by labora-tory or trip-blank contamination); and only one set of samples (the water from the bucket containing the plastic NSDS jar bottoms and nylon mesh) yielded consistent indications of a metal leaching from the sampler components; these samples had a mean (n=3, where n is the number of samples) Zn con-centration of 15 µg/L, approximately 12.5 percent of the PAL (table 3).

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Figure 5. Comparisons of A, concentrations; and B, relative percent differences between water samples obtained from the test container and from nylon-screen diffusion samplers after 4 days of equilibration.

Preliminary Laboratory Testing and Analysis 7

Table 2. Concentrations of metals detected during quality-control testing of the sampling process.—Continued

[All laboratory (lab) blank water was obtained from the U.S. Environmental Protection Agency. Concentrations in micrograms per liter (parts per billion); NSDS, nylon-screen diffusion sampler; nd, not detected; PPS, pushpoint sampler; SS, stainless steel]

Quality-control sample Barium Calcium Copper Chromium Lead Manganese Nickel Zinc

Soaking NSDS Components

Lab blank water nd nd nd nd nd nd nd ndLab blank water nd nd nd nd nd nd nd ndLab blank water nd nd nd nd nd nd nd nd

Lab blank water collected from bucket 0.20 nd 1.2 nd nd nd nd 8.3Lab blank water collected from bucket nd nd 1.1 nd nd nd nd 7.2Lab blank water collected from bucket nd nd nd nd nd nd nd 7.1

Lab blank water from bucket with plastic jars and nylon mesh

nd nd nd nd nd nd nd 16





Lab blank water from bucket with plastic jar caps nd nd nd nd nd nd nd ndLab blank water from bucket with plastic jar caps nd nd nd nd nd nd nd ndLab blank water from bucket with plastic jar caps nd nd nd nd nd nd nd nd

NSDS Sampling Procedure

Lab blank poured from NSDS that was assembled then disassembled

nd 100 nd nd nd nd nd 29


nd nd nd nd nd nd nd nd


nd nd nd nd nd nd nd 5.8

Lab blank from NSDS using syringe only nd nd nd nd nd 0.21 nd 13Lab blank from NSDS using syringe only nd nd nd nd nd nd nd 11Lab blank from NSDS using syringe only nd nd nd nd nd nd nd 10

Lab blank from NSDS using syringe and SS hypodermic

0.23 nd 1.0 nd nd nd nd 16


.26 nd 2.0 nd 1.2 nd 0.5 23


nd nd 2.0 nd 1.1 nd nd 15

Lab blank from NSDS using syringe, SS hypodermic, and filter

23 nd 2.0 nd nd nd nd 5.5


30 nd nd nd nd nd nd nd


51 nd 1.0 nd nd nd nd 17


Table 2. Concentrations of metals detected during quality-control testing of the sampling process.—Continued

[All laboratory (lab) blank water was obtained from the U.S. Environmental Protection Agency. Concentrations in micrograms per liter (parts per billion); NSDS, nylon-screen diffusion sampler; nd, not detected; PPS, pushpoint sampler; SS, stainless steel]

Quality-control sample Barium Calcium Copper Chromium Lead Manganese Nickel Zinc

PPS Sampling Procedure

PPS external rinse water nd nd 2.0 2.8 nd 1.9 2.7 41PPS external rinse water nd nd nd .73 nd 1.1 .76 16PPS external rinse water nd nd 1.0 1.9 nd 1.0 2.4 29

Peristaltic pump and tubing nd nd nd nd nd nd nd 7.8Peristaltic pump and tubing nd nd nd nd nd nd nd 7.3Peristaltic pump and tubing nd nd nd nd nd nd nd 8.1

Peristaltic pump, tubing, and PPS nd nd nd nd nd 10 .75 12Peristaltic pump, tubing, and PPS nd nd nd nd nd 9.5 .45 11Peristaltic pump, tubing, and PPS 6.3 nd nd nd nd 12 .54 11

Peristaltic pump, tubing, PPS, and filter nd nd nd nd nd 11 .7 ndPeristaltic pump, tubing, PPS, and filter 16 nd nd nd nd .61 nd ndPeristaltic pump, tubing, PPS, and filter 10 nd nd nd nd .34 nd nd

Table 3. Target analytes, their project action limits, and mini-mum reporting levels used for this study.

[na, not available]

AnalyteProject action limit

(micrograms per liter)

Reporting level (micrograms

per liter)

Aluminum (Al) 87 5Antimony (Sb) 30 .5Arsenic (As) 150 .5Barium (Ba) 4 .2Beryllium (Be) .66 .2

Cadmium (Cd) 2.2 .2Calcium (Ca) 116,000 100Chromium (Cr) 74 .5Cobalt (Co) 23 .2Copper (Cu) 9 .2

Iron (Fe) 1,000 50Lead (Pb) 2.5 .2Magnesium (Mg) 82,000 100Manganese (Mn) 120 .2Molybdenum (Mo) na .5

Nickel (Ni) 52 .2Selenium (Se) 5 1.0Silver (Ag) .36 .2Thallium (Tl) 12 .5Vanadium (V) 20 .2Zinc (Zn) 120 5

Preliminary Laboratory Testing and Analysis 9

In addition, a second series of quality-control tests assessed the capacity for the sampling process to contaminate samples (table 2). Samples of deionized water were collected as components were sequentially added to the sampling appa-ratus. For example, an NSDS sample was first collected with only a syringe; next, a sample was collected with a syringe and a hypodermic needle; finally, a sample was collected after a 0.45-µ Millipore HPF Millex-HN filter unit was added to the syringe and hypodermic needle. Zn was detected in most of the samples; the highest average Zn concentration, 18 µg/L (n=3), or 15 percent of the PAL, was associated with the use of the stainless-steel hypodermic needle to collect the sample. Ba, at an average concentration (n=3) of 35 µg/L, was detected in association with the filter apparatus; this concentration exceeds the PAL (4 µg/L). On the other hand, use of the filter may have decreased the Zn concentrations in the samples. Detections of Cu were ascribed by the laboratory analytical data report to lab-blank or trip-blank contamination, not to the samples themselves. Other analytes were detected sporadically and at concentrations below their respective PALs.

A similar series of tests was performed on the PPS sam-pling components. Some Ba contamination was again detected in association with the filter. Cu, Cr, Mn, nickel (Ni), and Zn were detected in the external rinse water (fig. 6). The highest concentrations of Zn, the only commonly detected metal in these tests, was found in external rinse-water samples from the PPS at 41 µg/L, substantially less than the PAL of 120 µg/L. Cu was once more ascribed to lab or trip-blank contamina-tion. The concentrations of Cr, Mn, and Ni were also substan-tially less than their PALs of 74 µg/L, 120 µg/L, and 52 µg/L, respectively.

As stated previously, this process generally showed that maximum detected analyte concentrations were lower than the PALs. Ba exceeded its PAL in these quality-control tests only when the filter unit was included. Thus, if appropriate quality-control samples are collected, it is reasonable to assume that contamination from these devices is unlikely to affect data interpretations when investigating suspected sites of possible high contamination.

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Figure 6. Laboratory quality-control data for A, barium; and B, zinc for components of sampling equipment. (NSDS, nylon-screen diffusion sampler; PPS, pushpoint sampler)


Sediment Pore Water Field-Sampling Techniques

Field work was done during May and June 2003. Field activities consisted of the deployment and retrieval of NSDSs and the collection of water samples from the NSDSs and the PPSs.

Nylon-Screen Diffusion Samplers

The NSDS units were assembled in the laboratory prior to transport to the study areas. Preliminary testing during a previous investigation indicated that deployment of sam-plers containing oxygenated water might affect the measured concentrations of contaminants (Forest P. Lyford, Hydrologist, U.S. Geological Survey, oral commun., 2003); there was con-cern that iron hydroxides could precipitate on the mesh screen and prevent dissolved metals from diffusing into the NSDS. To prevent this precipitation, the NSDS units were assembled in water that had been purged of dissolved oxygen (DO) by

sparging with nitrogen for at least 1 hour. Nitrogen was con-tinuously bubbled through the 19-L buckets in which the sam-plers were being prepared. These samplers were transported to the field sites in the buckets under a nitrogen atmosphere that was maintained by keeping the buckets covered except during the removal of a sampler. Because maintaining low DO con-centrations proved difficult, several NSDS units were prepared and deployed with deionized water that had not been purged of DO to determine whether deoxygenating made an appreciable difference in the results.

To deploy, or insert, the NSDSs into the sediment, the PVC shovel was pushed into the sediment and used to create a hole that would allow the sampler to be buried approximately 20 cm below the sediment surface. Each NSDS was covered with sediment after the shovel was removed. Samplers were placed on their sides to decrease the danger of puncturing the mesh during insertion and retrieval. To locate the samplers for retrieval, each NSDS unit was wrapped tightly with a nylon electrical tie attached to nylon monofilament and a brightly colored fishing bobber. During the study period, two bobbers were lost; because the monofilaments remained attached to

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Figure 6—Continued. Laboratory quality-control data for A, barium; and B, zinc for components of sampling equipment. (NSDS, nylon-screen diffusion sampler; PPS, pushpoint sampler)

Sediment Pore Water Field-Sampling Techniques 11

the samplers, however, they were all retrieved. Although some force was occasionally required to pull an NSDS loose from the sediment, it was usually possible to remove a sampler by gently gripping its sides. Any sediment covering the mesh usually fell off while the NSDS was being lifted through the overlying water. When it was necessary to use a gloved finger-tip to flick off a small amount of retained sediment, negligible loss of water from the sampler resulted.

NSDS samples were collected by using a 60-mL disposable syringe with a 13-gage, 8.9-cm hypodermic needle and a 25-mm, 0.45-µm filter unit (Millipore HPF Millex-HN) mounted between the syringe and hypodermic. After the NSDS was retrieved, the sharp tip of the hypodermic was thrust through the nylon mesh to extract the sample (fig. 7). Two withdrawals were required to retrieve a volume (100 mL) sufficient for analysis. Occasionally, more than one filter unit was required because of the build-up of solids on the filter membrane.

Pushpoint Samplers

During this study, a peristaltic pump was used to draw samples through the PPS. Approximately 2 m of silicone tubing connected the pump directly to the PPS. One of the Millipore filter units was attached to the opposite end of the tubing where the sample flowed into the 125-mL, high-density-polyethylene sample container before being acidified with Ultrex-grade nitric acid. After setting the PPS in the sediment at the desired depth, the guard rod was removed and samples were drawn with a peristaltic pump. During the flush-ing of the PPS and tubing prior to the collection of an envi-ronmental sample, specific conductance was monitored with a multiprobe meter to ensure that the PPS samples represented pore water and not infiltrating surface water.

Figure 7. Collecting a field sample from nylon-screen diffusion sampler by using syringe, filter, and hypodermic.


Site Selections

On May 12, 2003, 15 sites were selected approximately 0.5 to 1.5 m from shore in the Sudbury River (fig. 8A) at the Nyanza study area in Ashland. Samplers were inserted about 20 cm below the sediment surface in water 15 to 30 cm deep and were retrieved on May 13, 15, 19, 27, and 28, 2003.

On May 20, on either side of Rigby Road, Clinton, 15 sites (fig. 8B) were selected in sediments at the bottom of ditches or a beaver-dammed impoundment. All sampling sites remained submerged during the sampling period. As at the Nyanza study area, samplers were inserted about 20 cm below the sediment surface. Samples were collected on May 21, 23, 28, June 4, and June 5, 2003.

Quality-Control Sampling and Results

Field quality-control sampling for the NSDS units consisted of retrieving duplicate samplers deployed in close proximity to each other at some of the 15 sites. Quality-control sampling for the PPSs included equipment blanks, sequential replicate samples from the same site without removal of the PPS, and replicate samples from a nearby spot at the same site. NSDS and PPS replicate sample results are discussed with the other field data.

After the PPS had been flushed out and its exterior rinsed with deionized water supplied by the USEPA laboratory, equipment blanks were collected. Approximately 1 L of deion-ized water was pumped from a Pyrex 1-L beaker through the PPS before a sample was collected. This volume was approxi-mately the same volume of water that was used to flush the sampling system before routine sample collection.

Analysis of the PPS field-equipment blanks (table 6, at back of report) indicated that neither sampling equipment nor procedure introduced contamination to the field samples sufficient to qualify the use of the samplers in detecting con-tamination near or above PALs. Only two metals, As and Ba, were detected in the samples: As detected once at 0.71 µg/L and Ba at an average concentration of 3.3 µg/L (n=5). (Cu was detected in the laboratory analysis, but these detections were ascribed to contamination of laboratory blanks.) Ba likely came from the filter unit, as observed during lab quality-control studies.

High concentrations of iron (Fe) and Mn in the envi-ronmental samples required the analysts to dilute samples to minimize interferences affecting the analyses. Diluting the samples increased reporting levels for all metals by the same factor. Field-blank samples were not all segregated from envi-ronmental samples during analysis, however, and, thus, some were diluted by the laboratory. The dilution increased their reporting levels and effectively censored some of the data. In particular, the field blanks from Nyanza were all diluted 10:1 and the Rigby Brook field blanks were undiluted.

Variability in the results by method at each study area was calculated by using the medians of Relative Percent Difference (RPD) (table 4); reporting levels were substi-tuted for nondetects. In this case, this substitution may have diminished the RPD values. A comparison of the nitrogen-sparged NSDS units and those that were not sparged (NSDSX in tables 4; 6–8, at back of report) yields ambiguous results. Reporting levels in the Nyanza samples higher than in the Rigby Brook samples make the Nyanza results appear less variable than those from Rigby Brook. In reality, the concen-trations of numerous nondetects among the metals at Nyanza were replaced by reporting-level concentrations for the RPD calculations. The large number of 0.0 median RPD values (As, Co, lead (Pb), Ni, and V) at the Nyanza site reflects this situation. Because the lower number of nondetects at the Rigby Brook site allowed calculations to be based on real measured concentrations, the median RPD values were higher. Overall, the median RPD calculations indicate a high variability between the NSDS and NSDSX units. The differ-ences between the units may be exaggerated because there are fewer NSDSX than NSDS samples. If the NSDS is to become a common field-sampling device, additional testing in more homogeneous media may be useful.

Sequential replicate samples collected at the same loca-tion with the PPSs (PP1 in tables 4, 6–8) generally exhibit low median RPD values. Only the results for Zn are higher than for other metals. The higher median RPD values for PP2 samples (replicate samples collected from sites within a 0.5-m radius of one another) at both study areas further demonstrate substan-tial environmental variability over short distances.

Sediment Pore Water Field-Sampling Techniques 13

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Comparison of Metal Concentrations in Pore Water Collected with Nylon-Screen Diffusion and Pushpoint Samplers

The distribution, frequency of detection, and concentra-tions of metals differed at sampling sites within each of the Nyanza and Rigby Brook study areas (tables 7 and 8). Some of these differences may reflect matrix interferences that, in all but the first eight samples from the Nyanza study area, made it necessary for the analyst to dilute the sample by a factor of 10; this dilution effectively raised the reporting level by the same factor, and probably caused a decrease in the frequency of low-level detections in these samples. Similarly, 46 of 78 sam-ples from the Rigby Brook site required 2:1 dilution because of interference caused by the high concentrations of Fe in the samples. Thus, differences in the extent of matrix interference between samples from the Nyanza and Rigby Brook study areas may account more for concentration differences in As, Cr, Pb, Mo, V, and Zn than differences between the physical characteristics of the study areas (tables 7 and 8; figs. 9 and 10). These decreases in analytical method sensitivities to low concentrations of metals, however, should not be considered as affecting the capacity of the two types of sampling devices to provide acceptable data from highly contaminated environ-ments.

Although the Nyanza and Rigby Brook sampling areas were expected to yield detections of a large number of metals in concentrations substantially exceeding their PALs and, therefore, classifying the concentrations as toxic, this result

did not prove to be the case. At Nyanza, only aluminum (Al), Ba, Fe, and Mn were detected frequently at concentrations higher than their PALs. These elements are not generally classified with the trace elements or contaminants of concern As, cadmium (Cd), Cr, Cu, Hg, Pb, and Ni. These results con-trast with findings from a Nyanza Chemical Dump Superfund Site monitoring study (ICF Consulting, 2003) conducted in June 2001 (table 5). Single water samples collected from 20-cm sediment depths in three monitoring wells in the vicinity of the present study site (fig. 4) and analyzed by ICP-MS yielded data with relatively high concentrations of metals; the con-centrations of Al, As, Cr, Pb, V, and Zn were particularly high in comparison with the concentrations detected during this study. The differences were generally consistent irrespective of whether the Superfund monitoring well was located within the plume zone (wells MP-03A-03 and MP-003-01) or outside the zone (well UR-002).

At Rigby Brook, concentrations of As, Ba, Fe, Mn, and Zn frequently exceeded their PALs. For these reasons, comparisons are limited primarily to these frequently detected trace metals (Al, As, Ba, Co, Fe, Mn, and Zn). The low concentrations and relatively infrequent detections reported for antimony (Sb), Cu, Cr, Pb, molybdenum (Mo), Ni, and V, however, show that even the metallic PPS can collect samples yielding barely detectable concentrations of these metals.

Boxplots noting the actual reporting levels and substitut-ing these reporting levels for nondetects (figs. 9 and 10) are useful in comparing the results for the two devices at the two study areas. This substitution may create an overestimation in the concentration distribution of frequently detected metals, but the inclusion of the reporting levels provides perspective and shows how the different reporting levels affect the data.

Table 4. Medians of paired relative percent-difference values for individual metals in nylon-screen diffusion samples and pushpoint samples collected at the Nyanza study area, Ashland, Massachusetts, and at the Rigby Brook study area, Clinton, Massachusetts.

[For these calculations, values for censored data were set at the reporting level (table 3). NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler inserted without nitrogen sparging; PP1, pushpoint sampler—sequential replicate-sample pairs collected without moving sampler; PP2, pushpoint sampler—discrete sample pairs collected from nearby, but separate, locations]

Sampler type Aluminum Arsenic Barium Cobalt Iron Lead Manganese Nickel Vanadium Zinc

Nyanza

NSDS only 26.1 0.0 7.1 4.3 40.0 0.0 7.2 0.0 0.0 22.2NSDS and NSDSX 16.5 .0 6.5 .0 54.9 .0 18.2 .0 .0 48.5PP1 only 2.3 .0 6.4 .0 .0 .8 2.1 .0 1.4 25.4PP1 and PP2 12.8 .0 6.7 20.3 17.8 .0 6.1 23.9 .0 18.2

Rigby

NSDS only 44.3 25.4 12.1 29.2 33.1 40.0 7.9 21.3 24.2 5.1NSDS and NSDSX 58.3 32.5 8.1 26.1 39.8 68.8 46.6 55.8 29.1 4.4PP1 only 2.3 .0 6.4 .0 .0 .8 2.1 .0 1.4 25.4PP1 and PP2 16.2 16.2 10.4 40.5 18.2 27.3 12.2 23.0 22.2 40.0

Comparison of Metal Concentrations in Pore Water Collected with Nylon-Screen Diffusion and Pushpoint Samplers 15

For most of the metals depicted in the boxplots for the Nyanza study area (fig. 9), the reporting level was 2.0 µ/L; the exceptions were Al, 50 µ/L; As, 5 µ/L; Fe, 500 µ/L; and Zn, 50 µ/L. Medians for As, Pb, and V for both devices did not exceed the reporting level; that is, most of the data were censored. At the Rigby Brook study area, the reporting level was generally 0.4 µ/L, with the result that most of the data that appear in the boxplots were uncensored (fig.10).

For the uncensored data, the boxplots show that the ranges of concentrations for the two devices are comparable (figs. 9 and 10). For the most part, the median concentrations for the two devices lie within each other’s interquartile ranges. Only Al and Ba at the Nyanza study area and Ba and Zn at the Rigby Brook study area do not conform to this pattern; in these cases, except for the Al comparison, the median concen-trations associated with the NSDS samples were higher than the median concentrations for the PPS samples. Therefore, for a general screening study in an area where conditions were unfavorable for the use of the PPS, the NSDS could serve as an adequate alternative method, if these concerns are adequately considered.

Time Series of Nylon-Screen Diffusion Sampler Data

In general, the metal concentrations from the NSDS units increased slightly after 1 day or remained approximately the same (figs. 11 and 12, at back of report). If the unit is used, 1 week would seem to suffice for the water inside NSDS units in sediments comparable to those studied here to reach concentrations comparable with concentrations in the outside water. Notable differences in metal concentrations among specific locations further indicate the environmental hetero-geneity of the two study areas. Fe, Mn, and Zn concentrations at Nyanza site 12 were highest early in the study period, and then gradually decreased (fig. 11). Some of the changes in concentrations reflected variations in reporting levels between sampling dates. This situation was most apparent for As and Zn in the Nyanza time series. With the need for dilution, the As reporting level changed from 0.5 µg/L on the first sampling date to 5.0 µg/L for the remainder of the samples; thus, As was detected at first, but not thereafter. Similarly, the reporting

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30 25 30 25 30 25 30 25 30 25 30 25 30 25 30 25 30 25 30 25

30 NUMBER OF SAMPLES

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HIGHEST DATA POINTWITHIN 1.5 TIMES THEINTERQUARTILE RANGEABOVE THE BOX

LOWEST DATA POINTWITHIN 1.5 TIMES THEINTERQUARTILE RANGEBELOW THE BOX

THIRD QUARTILE

MEDIAN

FIRST QUARTILE

OUTLIER GREATER THAN3.0 TIMES INTERQUARTILE RANGE ABOVE THE BOX

OUTLIER GREATER THAN3.0 TIMES INTERQUARTILE RANGE BELOW THE BOX

OUTLIER BETWEEN 1.5AND 3.0 TIMES THE INTERQUARTILE RANGEABOVE THE BOX

OUTLIER BETWEEN 1.5AND 3.0 TIMES THE INTERQUARTILE RANGEBELOW THE BOX

PPS -- Pushpoint Sampler

NSDS -- Nylon-Screen Diffusion Sampler

1

10

100

1,000

10,000

100,000

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Detection Limit = 5

Detection Limit = 50


Figure 9. Selected metals concentrations in 25 samples collected with nylon-screen diffusion samplers and 35 samples collected with pushpoint samplers at the Nyanza study area, Ashland, Massachusetts, May 2003.


level for Zn changed from 5.0 to 50 µg/L, which likely caused the nondetects or censored values at sites 3, 9, and 15 on and after May 19.

At the Rigby Brook study area, most of the concentration patterns for individual metals during the 2-week period were similar among the stations (fig. 12). In general, the final con-centrations of Co, Fe, Mn, and Zn were relatively high (com-pared to all sites) at sites 12 and 15 on the edge of the beaver-dam impoundment. Most of the initial and final concentrations did not differ substantially.

Comparison of all Nylon-Screen Diffusion Samples and Pushpoint Samples by Site

Comparing the results from samples collected from all sites at both study areas (figs. 13 and 14, at back of report) after the 2-week study period provides more insight into the relative usefulness of the two sample-collection devices. Because of the differences in detection frequencies and reporting levels (tables 6 and 7) between study areas, compar-

ing results for the same sets of metals is not practical. For example, the detections of Zn were infrequent at Nyanza, but frequent at Rigby Brook (figs. 11G and 12F).

The differences at the Nyanza sites for the NSDS and PPS results for Al were striking (fig. 13A). At sites 1 through 9 and 15, the PPS samples had higher Al concentrations than the NSDS samples. The mean Al concentration in the PPS samples was 519 µg/L, but 103 µg/L in the NSDS samples; the PPS sample concentrations were generally 300 µg/L or greater, whereas the NSDS sample concentrations were generally less than 200 µg/L. For sites 10 through 14, the concentrations of Al were approximately equal, but low. The similarity of values at these sites suggests that a local environmental difference, pH, for example, may have affected the chemical form in which Al occurred and retarded the diffusion of Al into the NSDS units at sites 1 through 9, but did not affect passage through the openings of the PPS. The similarities in Al con-centrations for both methods at Rigby Brook further support this hypothesis (fig. 14A).

x

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1,000,00034 24 34 24 34 24 34 24 34 24 34 24 34 24 34 24 34 24 34 24

30 NUMBER OF SAMPLES

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HIGHEST DATA POINTWITHIN 1.5 TIMES THEINTERQUARTILE RANGEABOVE THE BOX

LOWEST DATA POINTWITHIN 1.5 TIMES THEINTERQUARTILE RANGEBELOW THE BOX

THIRD QUARTILE

MEDIAN

FIRST QUARTILE

OUTLIER GREATER THAN3.0 TIMES INTERQUARTILE RANGE ABOVE THE BOX

OUTLIER GREATER THAN3.0 TIMES INTERQUARTILE RANGE BELOW THE BOX

OUTLIER BETWEEN 1.5AND 3.0 TIMES THE INTERQUARTILE RANGEABOVE THE BOX

OUTLIER BETWEEN 1.5AND 3.0 TIMES THE INTERQUARTILE RANGEBELOW THE BOX

PPS -- Pushpoint Sampler

NSDS -- Nylon-Screen Diffusion SamplerAlum

inum

, PPS

Aluminu

m, N

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ic, P

PS

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Cobalt

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Iron,

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, PPS

Lead

, NSDS

Man

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se, P

PS

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Vanad

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Detection Limit = 0.4

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Figure 10. Selected metals concentrations in 24 samples collected with nylon-screen diffusion samplers and 34 samples collected with pushpoint samplers at the Rigby Brook study area, Clinton, Massachusetts, May to June 2003.

Comparison of Metal Concentrations in Pore Water Collected with Nylon-Screen Diffusion and Pushpoint Samplers 17

With the exceptions of site 10 at Nyanza and site 11 at Rigby Brook, Ba concentrations in the NSDS samples at both study areas were generally two to three times higher than in the collocated PPS samples (figs. 13B and 14C). The Ba concentrations had a smaller range in the NSDS samples at Nyanza than those at Rigby Brook, but the ratio between the concentrations of Ba measured in the NSDS and PPS samples was approximately the same for the two study areas. Because there is no reason to expect the environmental concentra-tions of Ba in the NSDS samples to exceed those in the PPS samples, it seems reasonable to assume that Ba came either from the plastic containers or the filter units. The concentra-tions of As in samples taken by the PPS and NSDS at Rigby Brook (fig. 14B) did not indicate any systematic differences. Moreover, the concentrations of As in duplicate NSDS and PPS samples hardly differed.

Co concentrations in the Nyanza study-area samples (fig. 13C) were generally less than 40 µg/L, but differed sys-tematically between the PPS and NSDS. In a manner similar to that for Al, a local environmental condition may be respon-sible for the differences in Co concentrations between the PPS and NSDS. The PPS concentrations are generally higher than

the NSDS sample concentrations. The mean Co concentration in PPS samples was 37 µg/L, but 27 µg/L in the NSDS sam-ples. The differences were most obvious for sites 3 through 9, where all concentrations ranged from about 10 to 75 µg/L.

Fe and Mn concentrations from Nyanza showed similar distribution patterns at all sites (figs. 13D and 13E). At sites 1 through 9, the concentrations were lowest and varied little. At sites 10 through 14, the concentrations increased markedly as did their variations. At site 15, the concentrations converged again. There was no pattern of difference in concentrations between the two types of samplers for the Nyanza or Rigby Brook study areas (figs. 14D and 14E). At Rigby Brook sites 1 through 12 and 15, the concentrations of Fe and Mn were highest and most variable. At sites 13 and 14, Fe concentra-tions were lowest and varied only slightly; Mn concentrations were slightly lower at sites 13 and 14, but generally consistent between the samplers.

The concentrations of Zn in the NSDS samples from Rigby Brook were approximately an order of magnitude greater than those in the PPS samples (fig. 14F); generally, the concentration ranges were from 150 to 300 µg/L and from 10 to 25 µg/L for the NSDS and PPS samples, respectively. Only at site 11 were both PPS sample concentrations higher than those from the NSDS. Because Zn was commonly detected in the laboratory-blank samples from plastics, it is possible that leaching of Zn from the NSDS units was a source of the elevated concentrations.

Summary and ConclusionsTo assist investigators of environmental hazards in mak-

ing reconnaissance surveys of the sources and distribution of potentially hazardous metal concentrations, simple and economical devices are needed. The USGS, in cooperation with the USEPA, tested nylon-screen diffusion samplers and stainless-steel pushpoint samplers to determine and compare their efficacies in sampling shallow pore water for metal con-taminants. The investigation was carried out at two study sites with previously reported contamination: the Nyanza Chemical Waste Dump Superfund site along the Sudbury River in Ashland, MA, and a Superfund site-assessment location along Rigby Brook in Clinton, MA.

Clearly, nylon-screen diffusion samplers and pushpoint samplers can serve as field screening tools for most metals. Laboratory quality-control samples indicate that some low-concentration detections result from the use of either type of sampling device or from laboratory or field procedures. The results from the field studies indicate that metal concentrations in the PPS samples seem less affected by the sampler itself than those in the NSDS samples. With the exceptions of data that indicate leaching of Ba and Zn from the plastic NSDS, the

Table 5. Concentrations of metals detected in ground water 20 cm below sediment surface at selected well locations for the Nyanza Superfund Site, Ashland, Massachusetts, June 2001.

[Data from ICF Consulting, 2003. Concentrations in micrograms per liter; --, not detected]

MetalMonitoring wells

UR-002 MP-03A-03 MP-003-01

Aluminum 22,300 98,900 1,610Antimony 3.7 -- --Arsenic 20.8 43.6 4.5Barium 169 396 48.4

Beryllium 2.2 17.4 --Cadmium 2.4 6.4 .5Calcium 15,500 141,000 13,700Chromium 46.4 165 --

Cobalt 31.3 58.3 5.9Copper 45.4 103 --Iron 29,500 128,000 4,100Lead 192 191 28.2

Magnesium 6,380 50,800 3,660Manganese 1,210 30,500 673Nickel 20.7 59.1 --Silver -- 4.1 --

Vanadium 57.3 246 --Zinc 995 2,630 --


differences in concentrations and frequencies of detection of the other metals among sites appear to be real, not artifacts of the devices used. The general comparability among the data from the PPS and NSDS samples show that the NSDS should prove effective at sites where the physical characteristics of the substrate might interfere with PPS use. The PPS is simpler and more convenient to use than the NSDS, however, because the NSDS requires assembly, preparation, insertion, and two site visits. In contrast, only one site visit is required to collect a sample with the PPS. Although NSDS units were left in place for 2 weeks during this study, the time-series data indicate that 1 week would have allowed adequate time to obtain a repre-sentative sample given the environmental heterogeneity that contributes to substantial variation in concentrations.

Most of the samples prepared for analysis were diluted by factors of 2 or 10 because of interferences affecting the analytical equipment. These dilutions raised the reporting levels for the metals by the same proportion and caused more analyses of the diluted samples than of undiluted samples to be reported as nondetects. The dilutions made it impossible to compare all sample concentrations with the lowest possible detection limits.

The data from samples from sparged and unsparged NSDS units analyzed for this report do not indicate that the use of the unsparged NSDS units would seriously affect the outcome of a screening survey of a contaminated site. Additional testing of NSDS units at sites with a greater variety of detectable metals could provide further support for this conclusion. Although demonstrating the use of the stainless-steel PPS for detecting low-level concentrations of trace-ele-ment metals was not an objective of this study, the results from undiluted samples indicate that the PPS may be useful in studies where low concentrations of trace metals are expected. With adequate quality-control sampling, scientifically sound results can be obtained for many applications.

AcknowledgmentsForest P. Lyford, Hydrologist, U.S. Geological Survey,

and Richard Willey, Hydrologist, U.S. Environmental Protection Agency, proposed this study and developed its ini-tial framework. The support and cooperation of Sharon Hayes, Remedial Program Manager, U.S. Environmental Protection Agency, is greatly appreciated. The authors would particularly like to recognize the field and office assistance provided by student aid Vicki-Rose Siegel. The authors gratefully acknowl-edge the residents and property owners who provided access to the study areas. Suggestions made by USGS colleague review-ers Matthew Petkewich and Kathryn M. Hess substantially improved this report.

References Cited

Campbell, J.P., Lyford, F.P., and Willey, R.E., 2002, Comparison of vapor concentrations of volatile organic compounds with ground-water concentrations of selected contaminants in sediments beneath the Sudbury River, Ashland, Massachusetts, 2000: U.S. Geological Survey Open-File Report 02-143, 33 p.

Church, P.E., Lyford, F.P., and Clifford, Scott, 2002, Volatile organic compounds, specific conductance, and tem-perature in the bottom sediments of Mill Pond, Ashland, Massachusetts, April 2001: U.S. Geological Survey Open-File Report 02-35, 10 p.

Henry, M.H., 2001, PushPoint Sampler Operators Manual and Applications Guide, last accessed on June 15, 2004, at http://www-personal.engin.umich.edu/~markhen/ MHE-instructions-ver-2.00.doc

ICF Consulting, 2003, Semi-annual ground water monitor-ing report—Spring 2003: Ashland, MA, Nyanza Chemical Waste Dump Superfund Site Operable Unit II, variously paged.

Roy F. Weston, Inc., 1999, Evaluation of contamination, Nyanza Chemical Waste Dump Superfund Site, Ashland, Massachusetts: Manchester, NH, variously paged.

Roy F. Weston, Inc., 2001, Draft groundwater toxicity evalua-tion report, Nyanza Chemical Waste Dump Superfund Site, Ashland, Massachusetts: Manchester, NH, variously paged.

Vroblesky, D.A., Petkewich, M.D., and Campbell, T.R., 2002, Field tests of diffusion samplers for inorganic constitu-ents in wells and at a ground-water-discharge zone: U.S. Geological Survey Water-Resources Investigations Report 02-4031, 24 p.

Wilde, F.D., Radtke, D.B., Gibs, J., Iwatsubo, R.T., 1999, Processing of water samples, in Wilde, F.D., Radtke, D.B., Gibs, J., and Iwatsubo, R.T., eds., National Field Manual for the Collection of Water-Quality Data: U.S. Geological Survey Techniques of Water-Resources Investigations, Book 9, chap A5, variously paged.

Zimmerman, M.J., Massey, A.J., and Campo, K.W., 2005, Pushpoint sampling for defining spatial and temporal variations of contaminant concentrations in sediment pore water near the ground-water/surface-water interface: U.S. Geological Survey Scientific Investigations Report 2005-5036, 70 p.

References Cited 19

Figures 11–14 and Tables 6–8


0

50

100

150 A

LUM

INU

M C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R

Site 3Site 6Site 9Site 12Site 15

Mean of Two Values

Reporting Level = 50Reporting Level = 5.0

A.

5/13

/200

3

5/15

/200

3

5/17

/200

3

5/19

/200

3

5/21

/200

3

5/23

/200

3

5/25

/200

3

5/27

/200

3

5/29

/200

3

DATE

0

0.5

1.0

1.5

2.0

2.5

AR

SE

NIC

CO

NC

EN

TR

AT

ION

,IN

MIC

RO

GR

AM

S P

ER

LIT

ER


Mean of Two Values

Reporting Level = 2.0Reporting Level = 0.20

Not detected in any samples after 5/13/2003

B.

Figure 11. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron; F, manganese; and G, zinc at the Nyanza study area, Ashland, Massachusetts, May 2003. Site locations are shown in figure 8.

Figures 11–14 21

0

50

100

150

200

250

300

350

BA

RIU

M C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two Values


5/13

/200

3

5/15

/200

3

5/17

/200

3

5/19

/200

3

5/21

/200

3

5/23

/200

3

5/25

/200

3

5/27

/200

3

5/29

/200

30

5

10

15

20

25

30

CO

BA

LT C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two Values


DATE

D.

C.

Figure 11—Continued. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron; F, manganese; and G, zinc at the Nyanza study area, Ashland, Massachusetts, May 2003. Site locations are shown in figure 8.


IRO

N C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two Values

Reporting Level = 500Reporting Level = 50

0

5,000

10,000

15,000

20,000

25,000

30,000

35,000

40,000

E.

5/13

/200

3

5/15

/200

3

5/17

/200

3

5/19

/200

3

5/21

/200

3

5/23

/200

3

5/25

/200

3

5/27

/200

3

5/29

/200

3

MA

NG

AN

ES

E C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two ValuesReporting Level = 2.0Reporting Level = 0.2

DATE

0

100

200

300

400

500

600

700

800

900

1,000

1,100

1,200

F.


Figures 11–14 23

5/13

/200

3

5/15

/200

3

5/17

/200

3

5/19

/200

3

5/21

/200

3

5/23

/200

3

5/25

/200

3

5/27

/200

3

5/29

/200

30

50

100

150

200

ZIN

C C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two ValuesReporting Level = 50Reporting Level = 5.0

DATE

G.



0

30

15

45

60

90

120

135

105

180

ALU

MIN

UM

CO

NC

EN

TR

AT

ION

, IN

MIC

RO

GR

AM

S P

ER

LIT

ER


Mean of Two ValuesReporting Level = 10Reporting Level = 5

75

150

165

5/21

/200

3

5/23

/200

3

5/25

/200

3

5/27

/200

3

5/29

/200

3

5/31

/200

3

6/2/

2003

6/4/

2003

6/6/

2003

0

100

200

300

400

500

600

AR

SE

NIC

CO

NC

EN

TR

AT

ION

, IN

MIC

RO

GR

AM

S P

ER

LIT

ER



DATE

B.

A.

Figure 12. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron; F, manganese; and G, zinc at the Rigby Brook study area, Clinton, Massachusetts, May to June 2003. Site locations are shown in figure 8.

Figures 11–14 25

0

100

200

300

400

500

BA

RIU

M C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R


Mean of Two Values


C.

5/22

/200

3

5/24

/200

3

5/26

/200

3

5/28

/200

3

5/30

/200

3

6/1/

2003

6/3/

2003

6/6/

2003

0

5

10

15

20

CO

BA

LT C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R



D.

DATE

Figure 12—Continued. Time series data for A, aluminum; B, arsenic; C, barium; D, cobalt; E, iron; F, manganese; and G, zinc at the Rigby Brook study area, Clinton, Massachusetts, May to June 2003. Site locations are shown in figure 8.


IRO

N C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R



0

40,000

80,000

120,000

160,000

E.

5/22

/200

3

5/24

/200

3

5/26

/200

3

5/28

/200

3

5/30

/200

3

6/1/

2003

6/3/

2003

6/6/

2003

0

500

1,000

1,500

2,000

2,500

3,000

MA

NG

AN

ES

E C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R



DATE

F.


Figures 11–14 27

5/22

/200

3

5/24

/200

3

5/26

/200

3

5/28

/200

3

5/30

/200

3

6/1/

2003

6/3/

2003

6/6/

2003

0

50

100

150

200

250

300

ZIN

C C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R



DATE

G.



SITE

0

200

400

600

800

1,000

1,200

1,400

ALU

MIN

UM

CO

NC

EN

TR

AT

ION

, IN

MIC

RO

GR

AM

S P

ER

LIT

ER

NSDSNSDSXPP1PP2

10 155 20 25 300

1 2 3 4 5 6 7 8 9 10 11 12 13 14 15

DISTANCE FROM REFERENCE STARTING POINT, IN METERSA.

Figure 13. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Nyanza study-area sampling sites, Ashland, Massachusetts, May 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

Figures 11–14 29

SITE

0

100

200

300

400

BA

RIU

M C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2

1050 15 20 25 30

DISTANCE FROM REFERENCE STARTING POINT, IN METERS

1 2 3 4 5 6 7 8 9 10 11 12 13 14 15

B.

Figure 13—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint sam-plers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Nyanza study-area sampling sites, Ashland, Massachusetts, May 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.


Figure 13—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint sam-plers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Nyanza study-area sampling sites, Ashland, Massachusetts, May 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler ini-tially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

SITE

0

20

40

60

80

CO

BA

LT C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2


1 2 3 4 5 6 7 8 9 10 11 12 13 14 15

1050 15 20 25 30

C.

Figures 11–14 31

Figure 13—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, barium; C, cobalt; D, iron; E, manganese; and F, zinc at all Nyanza study-area sampling sites, Ashland, Massachusetts, May 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

0

20,000

40,000

60,000

80,000

IRO

N C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2


SITE

1 2 3 4 5 6 7 8 9 10 11 12 13 14 15

1050 15 20 25 30

D.



0

500

1,000

1,500

2,000

MA

NG

AN

ES

E C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2


SITE

1 2 3 4 5 6 7 8 9 10 11 12 13 14 15

1050 15 20 25 30

E.

Figures 11–14 33


SITE

0

200

400

600

800

ZIN

C C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSF.

111 2 3333 44 56 777 8 9 10 11 12 13 14 15


SITE

0

50

100

150

200

ALU

MIN

UM

CO

NC

EN

TR

AT

ION

, IN

MIC

RO

GR

AM

S P

ER

LIT

ER

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSA.

111 2 3333 44 56 777 8 9 10 11 12 13 14 15

Figure 14. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

Figures 11–14 35

SITE

AR

SE

NIC

CO

NC

EN

TR

AT

ION

, IN

MIC

RO

GR

AM

S P

ER

LIT

ER

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSB.

111 2 3333 44 56 777 8 9 10 11 12 13 14 150

200

400

600

800

1,000

1,200

Figure 14—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler ini-tially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.


Figure 14—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint sam-plers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

SITE

0

100

200

300

400

500

BA

RIU

M C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSC.

111 2 3333 44 56 777 8 9 10 11 12 13 14 15

Figures 11–14 37

Figure 14—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler ini-tially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

SITE

0

50,000

100,000

150,000

200,000

250,000

IRO

N C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSD.

111 2 3333 44 56 777 8 9 10 11 12 13 14 15


Figure 14—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint samplers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.

SITE

0

1,000

2,000

3,000

4,000

MA

NG

AN

ES

E C

ON

CE

NT

RA

TIO

N,

IN M

ICR

OG

RA

MS

PE

R L

ITE

R

NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSE.

111 2 3333 44 56 777 8 9 10 11 12 13 14 15

Figures 11–14 39

1111 222 333333 444444 55566666666 7777788888 999999 10101010 111111 1212121212121212 1313131313 14141414 1515151515151515

SITE

0

200

400

600

800NSDSNSDSXPP1PP2

0 10 20 30 40 50 60 70 80 90 100 110

DISTANCE FROM REFERENCE STARTING POINT, IN METERSF.

ZIN

C C

ON

CE

NT

RA

TIO

N, I

N M

ICR

OG

RA

MS

PE

R L

ITE

R

Figure 14—Continued. Results for final round of sampling with nylon-screen diffusion samplers and pushpoint sam-plers for A, aluminum; B, arsenic; C, barium; D, iron; E, manganese; and F, zinc at all Rigby Brook study-area sampling sites, Clinton, Massachusetts, June 2003. NSDS, nylon-screen diffusion sampler; NSDSX, nylon-screen diffusion sampler initially filled with aerated deionized water; PP1, sample from first pushpoint-sampling location; PP2, sample from second pushpoint-sampling location. Site locations are shown in figure 8.


Tabl

e 6.

Co

ncen

tratio

ns o

f met

als

in q

ualit

y-co

ntro

l sam

ples

dur

ing

field

stu

dies

at t

he N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts, a

nd th

e Ri

gby

Broo

k st

udy

area

, Clin

ton,

M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

Rep

ortin

g le

vel f

or b

old

data

was

10

times

the

nom

inal

rep

ortin

g le

vel (

tabl

e 3)

; rep

ortin

g le

vel f

or s

hade

d da

ta w

as tw

ice

the

nom

inal

rep

ortin

g le

vel.

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Sam

ple

iden

tifie

rs a

nd s

ite n

umbe

rs p

rece

ded

by th

e le

tter

R a

re a

ssoc

iate

d w

ith th

e R

igby

B

rook

stu

dy a

rea;

oth

ers

are

from

the

Nya

nza

stud

y ar

ea. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st

push

poin

t-sa

mpl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

iden

t-

ifier

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

NSD

S D

uplic

ates

181

5-27

-200

310

25N

SDS

100

ndnd

260

ndnd

29nd

nd4.

85,

000

nd2.

475

0nd

ndnd

6519

15-

27-2

003

1035

NSD

S13

0nd

nd26

0nd

nd31

nd5.

03.

059

0nd

3.0

710

ndnd

nd67

284

5-27

-200

312

10N

SDS

90nd

nd29

0nd

nd34

nd17

.04.

01,

500

nd2.

572

0nd

5.2

ndnd

294

5-27

-200

312

20N

SDS

nd28

nd27

0nd

nd32

ndnd

7.0

8,70

0nd

2.4

670

nd5.

0nd

nd

325

5-27

-200

301

10N

SDS

93nd

nd29

0nd

nd31

nd23

.029

.01,

800

nd2.

366

0nd

8.4

ndnd

335

5-27

-200

301

25N

SDS

110

ndnd

270

ndnd

31nd

25.0

6.0

1,30

0nd

2.3

690

nd8.

5nd

nd34

55-

27-2

003

0135

NSD

SX21

0nd

nd30

0nd

nd31

nd17

.08.

074

0nd

2.3

690

nd8.

3nd

82

376

5-27

-200

314

20N

SDS

110

ndnd

280

ndnd

32nd

43.0

4.0

1,40

0nd

2.3

750

nd18

.0nd

6538

65-

27-2

003

1430

NSD

S62

ndnd

280

ndnd

28nd

13.0

4.0

5,90

0nd

2.1

640

nd6.

5nd

nd

427

5-27

-200

303

15N

SDS

55nd

nd27

0nd

nd28

ndnd

4.8

1,80

0nd

2.1

620

nd2.

9nd

nd43

75-

27-2

003

0325

NSD

SXnd

ndnd

260

ndnd

28nd

nd4.

03,

500

nd2.

263

0nd

ndnd

nd

468

5-27

-200

304

00N

SDS

ndnd

nd31

0nd

nd25

nd4.

811

.02,

000

nd1.

955

0nd

4.0

ndnd

478

5-27

-200

304

15N

SDS

65nd

nd27

0nd

nd25

nd4.

64.

02,

100

nd2.

057

0nd

4.3

ndnd

5310

5-27

-200

305

40N

SDS

nd31

nd30

0nd

nd31

ndnd

11.0

18,0

00nd

1.7

1,00

0nd

ndnd

120

5410

5-27

-200

306

00N

SDS

65nd

nd28

0nd

nd29

ndnd

18.0

24,0

00nd

1.8

770

ndnd

nd15

0

5711

5-28

-200

309

40N

SDS

78nd

nd36

0nd

nd21

ndnd

5.2

31,0

00nd

1.6

570

ndnd

nd28

058

115-

28-2

003

1000

NSD

S 64

ndnd

290

ndnd

34nd

nd6.

645

,000

nd2.

41,

100

ndnd

nd16

059

115-

28-2

003

1010

NSD

SX73

ndnd

290

ndnd

27nd

nd24

.031

,000

nd1.

978

0nd

ndnd

170

6212

5-28

-200

310

45N

SDS

84nd

nd28

0nd

nd22

ndnd

4.0

11,0

00nd

1.1

650

ndnd

nd82

6312

5-28

-200

311

00N

SDS

150

ndnd

240

ndnd

26nd

nd12

.025

,000

nd1.

269

0nd

ndnd

120

6713

5-28

-200

311

30N

SDS

59nd

nd25

0nd

nd29

ndnd

7.0

30,0

00nd

1.5

1,20

0nd

ndnd

140

6813

5-28

-200

311

37N

SDS

180

ndnd

320

ndnd

31nd

nd9.

020

,000

nd1.

71,

300

ndnd

nd66

6913

5-28

-200

311

42N

SDSX

ndnd

nd30

0nd

nd34

ndnd

24.0

15,0

00nd

2.7

1,00

0nd

ndnd

76

R29

R4

6-4-

2003

1205

NSD

S30

nd15

919

0nd

nd20

2.30

2.40

3.0

60,0

00nd

3.20

1,55

0nd

1.6

1.10

152

R30

R4

6-4-

2003

1209

NSD

S50

nd21

624

0nd

nd26

4.40

2.80

3.3

70,0

000.

443.

701,

720

nd1.

401.

7016

4R

31R

46-

4-20

0313

07N

SDSX

15nd

111

28nd

nd13

.52

4.60

1.0

23,5

00.8

52.

4073

0nd

.74

.79

15

Tables 6–8 41

Tabl

e 6.

Co

ncen

tratio

ns o

f met

als

in q

ualit

y-co

ntro

l sam

ples

dur

ing

field

stu

dies

at t

he N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts, a

nd th

e Ri

gby

Broo

k st

udy

area

, Clin

ton,

M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

Rep

ortin

g le

vel f

or b

old

data

was

10

times

the

nom

inal

rep

ortin

g le

vel (

tabl

e 3)

; rep

ortin

g le

vel f

or s

hade

d da

ta w

as tw

ice

the

nom

inal

rep

ortin

g le

vel.

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Sam

ple

iden

tifie

rs a

nd s

ite n

umbe

rs p

rece

ded

by th

e le

tter

R a

re a

ssoc

iate

d w

ith th

e R

igby

B

rook

stu

dy a

rea;

oth

ers

are

from

the

Nya

nza

stud

y ar

ea. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st

push

poin

t-sa

mpl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

iden

t-

ifier

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

NSD

S D

uplic

ates

—Co

ntin

ued

R37

R6

6-4-

2003

1419

NSD

S9.

6nd

4819

4nd

nd14

nd5.

102.

030

,700

3.7

1.90

1,22

02.

72.

700.

8816

3R

38R

66-

4-20

0314

30N

SDS

7.7

nd60

219

ndnd

200.

503.

802.

034

,700

1.7

2.70

1,32

02.

11.

60.6

916

1R

39R

66-

4-20

0314

40N

SDSX

16nd

4319

3nd

nd12

nd3.

602.

021

,800

5.3

1.60

789

2.0

4.50

.89

157

R43

R7

6-4-

2003

1527

NSD

S91

nd24

030

0nd

nd35

1.80

6.40

8.0

120,

000

nd5.

103,

100

nd1.

801.

6015

0R

44R

76-

4-20

0315

37N

SDS

58nd

280

240

ndnd

201.

602.

705.

084

,000

nd3.

102,

100

nd1.

101.

3015

0

R47

R8

6-4-

2003

1625

NSD

S66

nd26

029

0nd

nd18

1.50

4.20

5.0

88,0

001.

73.

102,

100

nd1.

201.

9020

0R

48R

86-

4-20

0316

31N

SDS

41nd

210

270

ndnd

15nd

3.10

4.0

63,0

00nd

2.20

1,40

0nd

1.10

.86

190

R49

R8

6-4-

2003

1640

NSD

SX56

nd29

028

0nd

nd17

1.20

3.70

4.0

84,0

00.8

62.

901,

700

nd1.

201.

9019

0

R55

R10

6-4-

2003

1822

NSD

Snd

nd93

240

ndnd

14nd

4.80

3.0

56,0

001.

21.

801,

300

2.7

2.00

.56

160

R56

R10

6-4-

2003

1825

NSD

Snd

nd12

025

0nd

nd17

nd4.

606.

071

,000

1.6

2.10

1,40

04.

01.

80.7

716

0

R63

R12

6-5-

2003

1045

NSD

S35

nd33

038

0nd

nd18

nd15

.00

4.0

110,

000

7.3

2.50

1,60

03.

46.

601.

2028

0R

64R

126-

5-20

0310

50N

SDS

19nd

850

480

ndnd

23nd

11.0

05.

018

0,00

01.

22.

801,

500

3.8

4.10

1.00

280

R68

R13

6-5-

2003

1145

NSD

S33

nd56

290

ndnd

6.6

nd1.

403.

012

,000

1.2

1.40

810

nd.8

3nd

170

R69

R13

6-5-

2003

1150

NSD

S32

nd40

260

ndnd

7.8

nd1.

302.

011

,000

.91

1.50

980

nd.6

7.4

812

0

R72

R14

6-5-

2003

1220

NSD

S47

nd49

250

ndnd

8.4

nd1.

705.

013

,000

2.8

1.60

1,40

0nd

.86

.95

150

R73

R14

6-5-

2003

1230

NSD

S32

nd96

210

ndnd

9.6

nd1.

603.

019

,000

1.7

2.00

1,30

0nd

.85

1.20

160

R77

R15

6-5-

2003

1325

NSD

S79

1.3

140

340

ndnd

18nd

14.0

05.

011

0,00

03.

82.

902,

400

nd3.

301.

5023

0R

78R

156-

5-20

0313

35N

SDS

160

3.3

170

350

ndnd

113.

7019

.00

5.0

190,

000

5.7

3.10

2,50

01.

26.

604.

1021

0

PPS

Fiel

d B

lank

s

212

5-27

-200

310

55nd

ndnd

2.5

ndnd

ndnd

nd2.

0nd

ndnd

ndnd

ndnd

nd39

75-

27-2

003

1445

ndnd

nd5.

6nd

ndnd

ndnd

6.0

ndnd

ndnd

ndnd

ndnd

6413

5-28

-200

311

10nd

ndnd

3nd

ndnd

ndnd

12.0

ndnd

ndnd

ndnd

ndnd

R27

46-

4-20

0311

40nd

ndnd

1.5

ndnd

ndnd

nd.3

ndnd

ndnd

ndnd

ndnd

R61

126-

5-20

0310

15nd

nd0.

714

ndnd

ndnd

nd.2

ndnd

ndnd

ndnd

ndnd


Tabl

e 6.

Co

ncen

tratio

ns o

f met

als

in q

ualit

y-co

ntro

l sam

ples

dur

ing

field

stu

dies

at t

he N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts, a

nd th

e Ri

gby

Broo

k st

udy

area

, Clin

ton,

M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

Rep

ortin

g le

vel f

or b

old

data

was

10

times

the

nom

inal

rep

ortin

g le

vel (

tabl

e 3)

; rep

ortin

g le

vel f

or s

hade

d da

ta w

as tw

ice

the

nom

inal

rep

ortin

g le

vel.

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Sam

ple

iden

tifie

rs a

nd s

ite n

umbe

rs p

rece

ded

by th

e le

tter

R a

re a

ssoc

iate

d w

ith th

e R

igby

B

rook

stu

dy a

rea;

oth

ers

are

from

the

Nya

nza

stud

y ar

ea. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st

push

poin

t-sa

mpl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

iden

t-

ifier

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

PPS

Sequ

entia

l and

Dup

licat

e Sa

mpl

es

Nya

nza

161

5-27

-200

310

00P

P1

130

ndnd

85nd

nd29

nd2.

913

.03,

700

nd2.

660

0nd

3.3

ndnd

171

5-27

-200

310

10P

P2

450

ndnd

77nd

nd32

nd4.

325

0.0

1,10

0nd

2.4

730

nd3.

7nd

nd

202

5-27

-200

310

45P

P1

300

ndnd

86nd

nd35

nd5.

07.

62,

600

nd2.

887

0nd

4.3

ndnd

222

5-27

-200

311

05P

P2

290

ndnd

90nd

nd38

nd7.

860

.02,

800

nd3.

086

0nd

4.9

ndnd

305

5-27

-200

312

30P

P1

850

ndnd

94nd

nd30

nd53

.09.

0nd

nd2.

162

0nd

41.0

nd16

031

55-

27-2

003

1250

PP

251

0nd

nd10

0nd

nd31

nd45

.05.

052

0nd

2.2

680

nd23

.0nd

nd

356

5-27

-200

314

00P

P1

630

ndnd

91nd

nd31

nd41

.03.

0nd

nd2.

368

0nd

25.0

ndnd

366

5-27

-200

314

10P

P2

600

6.2

nd93

ndnd

32nd

74.0

19.0

5,20

0nd

2.3

740

nd65

.0nd

140

407

5-27

-200

314

50P

P1

420

ndnd

96nd

nd31

nd29

.06.

0nd

nd2.

365

0nd

18.0

ndnd

417

5-27

-200

303

05P

P2

220

ndnd

94nd

nd30

nd11

.03.

065

0nd

2.1

640

nd6.

8nd

nd

448

5-27

-200

303

35P

P1

1,20

0nd

nd90

nd5.

030

nd44

.04.

0nd

110

2.1

630

nd32

.0nd

110

458

5-27

-200

303

45P

P2

970

ndnd

87nd

nd30

nd40

.013

0.0

ndnd

2.0

640

nd34

.0nd

71

489

5-27

-200

304

25P

P1

670

ndnd

100

ndnd

29nd

27.0

3.0

1,00

0nd

2.0

730

nd17

.0nd

5349

95-

27-2

003

0435

PP

278

0nd

nd90

ndnd

30nd

31.0

11.0

1,10

0nd

2.1

740

nd22

.0nd

nd

5110

5-27

-200

305

00P

P1

ndnd

nd29

0nd

nd35

ndnd

5.3

43,0

00nd

1.9

1,60

0nd

ndnd

nd52

105-

27-2

003

0520

PP

2nd

ndnd

270

ndnd

33nd

nd5.

962

,000

nd2.

01,

700

ndnd

nd77

5511

5-28

-200

309

15P

P1

90nd

nd12

0nd

nd35

nd4.

74.

012

,000

nd2.

685

0nd

3.5

ndnd

5611

5-28

-200

309

25P

P2

84nd

nd11

0nd

nd35

nd4.

64.

912

,000

nd2.

683

0nd

2.8

ndnd

6012

5-28

-200

310

25P

P1

ndnd

nd12

0nd

nd33

ndnd

4.6

16,0

00nd

1.3

1,10

0nd

ndnd

nd61

125-

28-2

003

1035

PP

255

ndnd

110

ndnd

31nd

10.0

13.0

4,50

0nd

1.9

780

nd4.

0nd

68

6513

5-28

-200

311

20P

P1

51nd

nd21

0nd

nd35

ndnd

3.0

23,0

00nd

2.2

1,50

0nd

ndnd

nd66

135-

28-2

003

1122

PP

167

11nd

210

ndnd

35nd

nd12

.023

,000

nd2.

21,

500

ndnd

ndnd

7014

5-28

-200

311

55P

P1

81nd

nd10

0nd

nd33

ndnd

4.0

13,0

00nd

2.3

730

ndnd

ndnd

7114

5-28

-200

312

00P

P1

80nd

nd10

0nd

nd32

ndnd

5.0

13,0

00nd

2.3

710

ndnd

ndnd

7214

5-28

-200

312

10P

P2

90nd

nd11

0nd

nd33

ndnd

38.0

12,0

00nd

2.8

520

ndnd

ndnd

7515

5-28

-200

312

40P

P1

490

ndnd

84nd

nd28

nd12

.012

.01,

700

nd2.

164

0nd

9.5

nd14

076

155-

28-2

003

1255

PP

224

0nd

nd85

ndnd

30nd

9.4

18.0

4,90

0nd

2.0

680

nd6.

6nd

nd

Tables 6–8 43

Tabl

e 6.

Co

ncen

tratio

ns o

f met

als

in q

ualit

y-co

ntro

l sam

ples

dur

ing

field

stu

dies

at t

he N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts, a

nd th

e Ri

gby

Broo

k st

udy

area

, Clin

ton,

M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

Rep

ortin

g le

vel f

or b

old

data

was

10

times

the

nom

inal

rep

ortin

g le

vel (

tabl

e 3)

; rep

ortin

g le

vel f

or s

hade

d da

ta w

as tw

ice

the

nom

inal

rep

ortin

g le

vel.

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Sam

ple

iden

tifie

rs a

nd s

ite n

umbe

rs p

rece

ded

by th

e le

tter

R a

re a

ssoc

iate

d w

ith th

e R

igby

B

rook

stu

dy a

rea;

oth

ers

are

from

the

Nya

nza

stud

y ar

ea. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st

push

poin

t-sa

mpl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

iden

t-

ifier

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

PPS

Sequ

entia

l and

Dup

licat

e Sa

mpl

es—

Cont

inue

d

Rigb

yR

161

6-4-

2003

0902

PP1

30nd

267

30nd

nd18

nd0.

341.

029

,800

0.71

2.40

1,51

0nd

0.65

0.73

18R

171

6-4-

2003

0920

PP1

310.

5426

636

ndnd

18nd

.35

1.0

29,7

00.6

42.

501,

490

nd.8

0.7

526

R18

16-

4-20

0306

44PP

228

nd23

625

ndnd

17nd

.65

1.0

27,9

00.6

32.

301,

380

nd.9

0.8

319

R20

26-

4-20

0310

05PP

125

nd22

724

ndnd

18nd

.97

.533

,400

.22.

301,

300

nd.6

9.6

512

R21

26-

4-20

0310

17PP

221

nd21

324

ndnd

170.

80.6

1.7

26,0

00.8

32.

0093

0nd

.79

.83

13

R23

36-

4-20

0310

50PP

151

nd68

54nd

nd18

1.60

.76

2.0

31,5

00nd

2.50

1,21

0nd

1.30

.90

20R

243

6-4-

2003

1107

PP2

44nd

8064

ndnd

212.

50.7

81.

034

,400

nd2.

901,

480

nd1.

501.

1024

R26

46-

4-20

0311

37PP

157

nd12

666

ndnd

214.

501.

302.

041

,500

nd3.

401,

270

nd1.

501.

7015

R28

46-

4-20

0312

00PP

254

nd16

264

ndnd

224.

901.

703.

060

,100

.41

3.10

1,03

0nd

1.30

2.90

14

R32

56-

4-20

0313

22PP

145

nd21

221

1nd

nd27

2.90

3.80

4.1

76,5

00nd

4.20

1,89

0nd

1.40

1.60

130

R33

56-

4-20

0313

27PP

231

nd49

39nd

nd12

nd1.

301.

012

,800

1.4

2.10

538

nd.8

7.8

76.

1

R35

66-

4-20

0313

50PP

117

nd10

789

ndnd

201.

9010

.00

1.0

51,7

004.

52.

202,

060

5.5

4.30

1.90

106

R36

66-

4-20

0314

05PP

220

nd10

883

ndnd

191.

7011

.00

12.0

47,2

003.

72.

202,

030

5.1

5.20

2.10

60

R40

76-

4-20

0314

53PP

170

nd16

073

ndnd

202.

501.

503.

354

,600

nd3.

401,

820

nd1.

101.

5012

R41

76-

4-20

0314

57PP

170

nd16

078

ndnd

191.

001.

503.

058

,000

nd3.

001,

900

nd1.

101.

2020

R42

76-

4-20

0315

05PP

277

nd11

081

ndnd

221.

401.

304.

062

,000

nd3.

402,

000

nd1.

301.

2018

R45

86-

4-20

0315

51PP

135

nd19

069

ndnd

168.

308.

302.

047

,000

.37

3.20

2,10

0nd

.68

.97

12.0

0R

468

6-4-

2003

1615

PP2

46nd

150

58nd

nd11

nd1.

602.

038

,000

.47

2.40

1,60

0nd

.54

1.20

14

R50

96-

4-20

0317

00PP

131

nd22

092

ndnd

11nd

7.30

3.0

54,0

007.

42.

102,

000

3.2

2.30

2.00

30R

519

6-4-

2003

1717

PP2

25nd

350

110

ndnd

10nd

2.60

1.0

72,0

00.9

91.

601,

800

3.1

1.10

1.30

13

R53

106-

4-20

0317

59PP

122

nd15

010

0nd

nd11

nd9.

802.

048

,000

2.5

1.80

1,40

02.

95.

001.

1049

R54

106-

4-20

0318

10PP

217

nd13

076

ndnd

9.5

nd6.

501.

049

,000

1.9

1.50

1,40

02.

43.

10.8

018

R57

116-

5-20

0309

40PP

114

nd45

034

0nd

nd21

nd36

.00

2.0

110,

000

1.3

2.90

2,30

03.

312

.00

.69

420

R58

116-

5-20

0309

50PP

213

nd43

035

0nd

nd23

nd33

.00

2.0

120,

000

.91

3.30

2,40

04.

312

.00

.73

700


Tabl

e 6.

Co

ncen

tratio

ns o

f met

als

in q

ualit

y-co

ntro

l sam

ples

dur

ing

field

stu

dies

at t

he N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts, a

nd th

e Ri

gby

Broo

k st

udy

area

, Clin

ton,

M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

Rep

ortin

g le

vel f

or b

old

data

was

10

times

the

nom

inal

rep

ortin

g le

vel (

tabl

e 3)

; rep

ortin

g le

vel f

or s

hade

d da

ta w

as tw

ice

the

nom

inal

rep

ortin

g le

vel.

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Sam

ple

iden

tifie

rs a

nd s

ite n

umbe

rs p

rece

ded

by th

e le

tter

R a

re a

ssoc

iate

d w

ith th

e R

igby

B

rook

stu

dy a

rea;

oth

ers

are

from

the

Nya

nza

stud

y ar

ea. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st

push

poin

t-sa

mpl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

iden

t-

ifier

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

PPS

Sequ

entia

l and

Dup

licat

e Sa

mpl

es—

Cont

inue

d

Rigb

y—Co

ntin

ued

R60

126-

5-20

0310

05PP

115

nd67

021

0nd

nd20

nd6.

908.

013

0,00

0nd

2.80

1300

1.9

2.50

0.75

ndR

6212

6-5-

2003

1030

PP2

17nd

1,20

023

0nd

nd20

nd5.

001.

016

0,00

0nd

2.80

1200

2.5

1.60

nd11

R65

136-

5-20

0311

08PP

133

nd32

46nd

nd9.

7nd

.60

2.0

10,0

006

1.90

580

nd1.

10.6

033

R66

136-

5-20

0311

20PP

133

nd33

49nd

nd9.

9nd

.58

3.0

10,0

005.

91.

9060

0nd

1.10

.62

28R

6713

6-5-

2003

1128

PP2

38nd

2743

ndnd

7.6

nd.6

51.

011

,000

2.6

1.60

790

nd.6

1.7

512

R70

146-

5-20

0312

00PP

151

nd32

51nd

nd7.

6nd

.44

4.0

12,0

006.

21.

6095

0nd

.75

.82

18R

7114

6-5-

2003

1210

PP2

43nd

3233

ndnd

7.6

nd.7

53.

010

,000

2.9

1.60

820

nd.7

1.6

6nd

R74

156-

5-20

0312

55PP

113

02

160

150

ndnd

133.

5019

.00

4.0

210,

000

.73.

8026

00nd

3.90

2.50

12R

7515

6-5-

2003

1257

PP1

140

2.1

160

160

ndnd

143.

7019

.00

3.0

210,

000

.67

3.90

2600

nd3.

902.

5017

R76

156-

5-20

0313

20PP

290

nd16

015

0nd

nd23

1.20

8.60

3.0

150,

000

nd4.

2023

00nd

2.80

1.30

14

Tables 6–8 45

Tabl

e 7.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om th

e N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts.—

Cont

inue

d

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

10:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re 1

0 tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st p

ushp

oint

-sam

plin

g lo

catio

n; P

P2, s

ampl

e fr

om s

econ

d pu

shpo

int-

sam

plin

g lo

catio

n; n

d, n

ot d

etec

ted]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

eSa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

13

5-13

-200

312

05N

SDS

15nd

0.78

270

ndnd

15nd

0.3

2.0

770

0.37

1.3

290

nd1.

40.

2282

26

5-13

-200

312

25N

SDS

45nd

nd17

00.

27nd

25nd

17.0

2.0

3,30

0nd

1.9

550

nd10

.0nd

433

95-

13-2

003

1240

NSD

S17

nd.5

300

ndnd

19nd

.71.

02,

900

nd1.

541

0nd

1.7

nd78

412

5-13

-200

312

50N

SDS

38nd

.74

220

ndnd

8.8

nd.2

3.0

5,50

01.

9.7

250

nd1.

1nd

200

515

5-13

-200

313

05N

SDS

32nd

nd23

0.2

4nd

190.

802.

72.

05,

500

nd1.

651

0nd

3.2

nd88

63

5-15

-200

311

45N

SDS

14nd

nd22

0nd

nd14

nd.4

1.0

2,80

0nd

1.3

290

nd2.

0nd

327

65-

15-2

003

1155

NSD

S 14

ndnd

230

ndnd

25nd

.93.

07,

300

nd1.

758

0nd

2.4

nd48

89

5-15

-200

312

10N

SDS

12nd

nd24

0nd

nd16

nd.6

1.0

5,10

0nd

1.4

350

nd1.

9nd

529

125-

15-2

003

1220

NSD

S nd

ndnd

300

ndnd

27nd

nd2.

533

,000

nd1.

51,

100

ndnd

nd17

010

155-

15-2

003

1230

NSD

S 57

ndnd

320

ndnd

29nd

2.4

2.0

8,10

0nd

2.1

700

nd3.

4nd

80

113

5-19

-200

311

40N

SDS

ndnd

nd29

0nd

nd24

ndnd

nd3,

000

nd1.

855

0nd

ndnd

nd12

65-

19-2

003

1150

NSD

S 78

ndnd

310

ndnd

30nd

19.0

11.0

1,30

0nd

2.1

690

nd5.

9nd

6613

95-

19-2

003

1200

NSD

S nd

ndnd

270

ndnd

19nd

nd6.

73,

200

nd1.

541

0nd

ndnd

nd14

125-

19-2

003

1210

NSD

S 51

ndnd

290

ndnd

31nd

nd3.

429

,000

nd1.

499

0nd

ndnd

140

1515

5-19

-200

312

20N

SDS

ndnd

nd25

0nd

nd20

ndnd

2.4

7,50

0nd

1.4

460

ndnd

ndnd

161

5-27

-200

310

00PP

113

0nd

nd85

ndnd

29nd

2.9

13.0

3,70

0nd

2.6

600

nd3.

3nd

nd17

15-

27-2

003

1010

PP2

450

ndnd

77nd

nd32

nd4.

325

0.0

1,10

0nd

2.4

730

nd3.

7nd

nd18

15-

27-2

003

1025

NSD

S10

0nd

nd26

0nd

nd29

ndnd

4.8

5,00

0nd

2.4

750

ndnd

nd65

191

5-27

-200

310

35N

SDS

130

ndnd

260

ndnd

31nd

5.0

3.0

590

nd3.

071

0nd

ndnd

6720

25-

27-2

003

1045

PP1

300

ndnd

86nd

nd35

nd5.

07.

62,

600

nd2.

887

0nd

4.3

ndnd

212

5-27

-200

310

55B

LA

NK

ndnd

nd2.

5nd

ndnd

ndnd

2.0

ndnd

ndnd

ndnd

ndnd

222

5-27

-200

311

05PP

229

0nd

nd90

ndnd

38nd

7.8

60.0

2,80

0nd

3.0

860

nd4.

9nd

nd23

25-

27-2

003

1115

NSD

S26

0nd

nd19

0nd

nd37

nd2.

13.

093

0nd

2.9

830

nd2.

3nd

nd24

35-

27-2

003

1135

PP1

290

ndnd

88nd

nd31

nd33

.05.

03,

200

nd2.

274

0nd

19.0

nd52

253

5-27

-200

311

45N

SDS

54nd

nd27

0nd

nd31

ndnd

5.0

3,50

0nd

2.2

650

ndnd

ndnd

264

5-27

-200

311

50PP

157

0nd

nd85

ndnd

31nd

41.0

6.0

1,00

0nd

2.3

670

nd25

.0nd

nd27

45-

27-2

003

1200

PP2

460

ndnd

98nd

nd31

nd17

.021

.055

0nd

2.3

680

nd10

.0nd

nd28

45-

27-2

003

1210

NSD

S90

ndnd

290

ndnd

34nd

17.0

4.0

1,50

0nd

2.5

720

nd5.

2nd

nd29

45-

27-2

003

1220

NSD

Snd

28nd

270

ndnd

32nd

nd7.

08,

700

nd2.

467

0nd

5.0

ndnd

305

5-27

-200

312

30PP

185

0nd

nd94

ndnd

30nd

53.0

9.0

ndnd

2.1

620

nd41

.0nd

160


Tabl

e 7.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om th

e N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts.—

Cont

inue

d

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

10:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re 1

0 tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st p

ushp

oint

-sam

plin

g lo

catio

n; P

P2, s

ampl

e fr

om s

econ

d pu

shpo

int-

sam

plin

g lo

catio

n; n

d, n

ot d

etec

ted]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

eSa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

315

5-27

-200

312

50PP

251

0nd

nd10

0nd

nd31

nd45

.05.

052

0nd

2.2

680

nd23

.0nd

nd32

55-

27-2

003

110

NSD

S93

ndnd

290

ndnd

31nd

23.0

29.0

1,80

0nd

2.3

660

nd8.

4nd

nd33

55-

27-2

003

125

NSD

S11

0nd

nd27

0nd

nd31

nd25

.06.

01,

300

nd2.

369

0nd

8.5

ndnd

345

5-27

-200

313

5N

SDSX

210

ndnd

300

ndnd

31nd

17.0

8.0

740

nd2.

369

0nd

8.3

nd82

356

5-27

-200

314

00PP

163

0nd

nd91

ndnd

31nd

41.0

3.0

ndnd

2.3

680

nd25

.0nd

nd

366

5-27

-200

314

10PP

260

06.

2nd

93nd

nd32

nd74

.019

.05,

200

nd2.

374

0nd

65.0

nd14

037

65-

27-2

003

1420

NSD

S11

0nd

nd28

0nd

nd32

nd43

.04.

01,

400

nd2.

375

0nd

18.0

nd65

386

5-27

-200

314

30N

SDS

62nd

nd28

0nd

nd28

nd13

.04.

05,

900

nd2.

164

0nd

6.5

ndnd

397

5-27

-200

314

45B

LA

NK

ndnd

nd5.

6nd

ndnd

ndnd

6.0

ndnd

ndnd

ndnd

ndnd

407

5-27

-200

314

50PP

142

0nd

nd96

ndnd

31nd

29.0

6.0

ndnd

2.3

650

nd18

.0nd

nd

417

5-27

-200

330

5PP

222

0nd

nd94

ndnd

30nd

11.0

3.0

650

nd2.

164

0nd

6.8

ndnd

427

5-27

-200

331

5N

SDS

55nd

nd27

0nd

nd28

ndnd

4.8

1,80

0nd

2.1

620

nd2.

9nd

nd43

75-

27-2

003

325

NSD

SXnd

ndnd

260

ndnd

28nd

nd4.

03,

500

nd2.

263

0nd

ndnd

nd44

85-

27-2

003

335

PP1

1,20

0nd

nd90

nd5.

030

nd44

.04.

0nd

110

2.1

630

nd32

.0nd

110

458

5-27

-200

334

5PP

297

0nd

nd87

ndnd

30nd

40.0

130.

0nd

nd2.

064

0nd

34.0

nd71

468

5-27

-200

340

0N

SDS

ndnd

nd31

0nd

nd25

nd4.

811

.02,

000

nd1.

955

0nd

4.0

ndnd

478

5-27

-200

341

5N

SDS

65nd

nd27

0nd

nd25

nd4.

64.

02,

100

nd2.

057

0nd

4.3

ndnd

489

5-27

-200

342

5PP

167

0nd

nd10

0nd

nd29

nd27

.03.

010

00nd

2.0

730

nd17

.0nd

5349

95-

27-2

003

435

PP2

780

ndnd

90nd

nd30

nd31

.011

.01,

100

nd2.

174

0nd

22.0

ndnd

509

5-27

-200

344

5N

SDS

ndnd

nd24

0nd

nd17

ndnd

3.0

6,10

0nd

1.4

410

ndnd

ndnd

5110

5-27

-200

350

0PP

1nd

ndnd

290

ndnd

35nd

nd5.

343

,000

nd1.

91,

600

ndnd

ndnd

5210

5-27

-200

352

0PP

2nd

ndnd

270

ndnd

33nd

nd5.

962

,000

nd2.

01,

700

ndnd

nd77

5310

5-27

-200

354

0N

SDS

nd31

nd30

0nd

nd31

ndnd

11.0

18,0

00nd

1.7

1,00

0nd

ndnd

120

5410

5-27

-200

360

0N

SDS

65nd

nd28

0nd

nd29

ndnd

18.0

24,0

00nd

1.8

770

ndnd

nd15

055

115-

28-2

003

915

PP1

90nd

nd12

0nd

nd35

nd4.

74.

012

,000

nd2.

685

0nd

3.5

ndnd

5611

5-28

-200

392

5PP

284

ndnd

110

ndnd

35nd

4.6

4.9

12,0

00nd

2.6

830

nd2.

8nd

nd57

115-

28-2

003

940

NSD

S78

ndnd

360

ndnd

21nd

nd5.

231

,000

nd1.

657

0nd

ndnd

280

5811

5-28

-200

310

00N

SDS

64nd

nd29

0nd

nd34

ndnd

6.6

45,0

00nd

2.4

1,10

0nd

ndnd

160

5911

5-28

-200

310

10N

SDSX

73nd

nd29

0nd

nd27

ndnd

24.0

31,0

00nd

1.9

780

ndnd

nd17

060

125-

28-2

003

1025

PP1

ndnd

nd12

0nd

nd33

ndnd

4.6

16,0

00nd

1.3

1,10

0nd

ndnd

nd

Tables 6–8 47

Tabl

e 7.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om th

e N

yanz

a st

udy

area

, Ash

land

, Mas

sach

uset

ts.—

Cont

inue

d

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

10:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re 1

0 tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. N

SDS,

nyl

on-s

cree

n di

ffus

ion

sam

pler

; NSD

SX, n

ylon

-scr

een

diff

usio

n sa

mpl

er in

itial

ly f

illed

with

aer

ated

dei

oniz

ed w

ater

; PP1

, sam

ple

from

fir

st p

ushp

oint

-sam

plin

g lo

catio

n; P

P2, s

ampl

e fr

om s

econ

d pu

shpo

int-

sam

plin

g lo

catio

n; n

d, n

ot d

etec

ted]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

eSa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

6112

5-28

-200

310

35PP

255

ndnd

110

ndnd

31nd

10.0

13.0

4,50

0nd

1.9

780

nd4.

0nd

6862

125-

28-2

003

1045

NSD

S84

ndnd

280

ndnd

22nd

nd4.

011

,000

nd1.

165

0nd

ndnd

8263

125-

28-2

003

1100

NSD

S15

0nd

nd24

0nd

nd26

ndnd

12.0

25,0

00nd

1.2

690

ndnd

nd12

064

135-

28-2

003

1110

BL

AN

Knd

ndnd

3nd

ndnd

ndnd

12.0

ndnd

ndnd

ndnd

ndnd

6513

5-28

-200

311

20PP

151

ndnd

210

ndnd

35nd

nd3.

023

,000

nd2.

21,

500

ndnd

ndnd

6613

5-28

-200

311

22PP

167

11nd

210

ndnd

35nd

nd12

.023

,000

nd2.

21,

500

ndnd

ndnd

6713

5-28

-200

311

30N

SDS

59nd

nd25

0nd

nd29

ndnd

7.0

30,0

00nd

1.5

1,20

0nd

ndnd

140

6813

5-28

-200

311

37N

SDS

180

ndnd

320

ndnd

31nd

nd9.

020

,000

nd1.

71,

300

ndnd

nd66

6913

5-28

-200

311

42N

SDSX

ndnd

nd30

0nd

nd34

ndnd

24.0

15,0

00nd

2.7

1,00

0nd

ndnd

7670

145-

28-2

003

1155

PP1

81nd

nd10

0nd

nd33

ndnd

4.0

13,0

00nd

2.3

730

ndnd

ndnd

7114

5-28

-200

312

00PP

180

ndnd

100

ndnd

32nd

nd5.

013

,000

nd2.

371

0nd

ndnd

nd72

145-

28-2

003

1210

PP2

90nd

nd11

0nd

nd33

ndnd

38.0

12,0

00nd

2.8

520

ndnd

ndnd

7314

5-28

-200

312

20N

SDS

51nd

nd31

0nd

nd30

ndnd

3.0

9,90

0nd

2.1

780

ndnd

ndnd

7414

5-28

-200

312

30N

SDS

ndnd

nd29

0nd

nd29

ndnd

11.0

6,40

0nd

2.0

570

ndnd

ndnd

7515

5-28

-200

312

40PP

149

0nd

nd84

ndnd

28nd

12.0

12.0

1,70

0nd

2.1

640

nd9.

5nd

140

7615

5-28

-200

312

55PP

224

0nd

nd85

ndnd

30nd

9.4

18.0

4,90

0nd

2.0

680

nd6.

6nd

nd77

155-

28-2

003

110

NSD

S78

ndnd

310

ndnd

28nd

2.0

3.0

2,70

0nd

2.1

620

ndnd

ndnd


Tabl

e 8.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om R

igby

Bro

ok s

tudy

are

a, C

linto

n, M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

2:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re tw

o tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. NSD

S,

nylo

n-sc

reen

dif

fusi

on s

ampl

er; N

SDSX

, nyl

on-s

cree

n di

ffus

ion

sam

pler

initi

ally

fill

ed w

ith a

erat

ed d

eion

ized

wat

er; P

P1, s

ampl

e fr

om f

irst

pus

hpoi

nt-s

ampl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

R1

35-

21-2

003

1040

NSD

S23

nd33

265

ndnd

6.6

nd1.

503.

021

,900

0.84

1.00

548

nd0.

920.

2419

9R

26

5-21

-200

310

55N

SDS

39nd

1832

3nd

nd7.

3nd

2.60

4.0

12,4

0018

1.00

615

1.0

1.60

.73

283

R3

95-

21-2

003

1105

NSD

S32

nd37

371

ndnd

10nd

5.50

4.0

27,5

007.

81.

401,

400

1.6

3.00

1.00

292

R4

125-

21-2

003

1115

NSD

S36

0.52

6831

7nd

nd15

nd11

.00

4.0

44,3

009.

12.

001,

670

2.7

4.30

1.10

243

R5

155-

21-2

003

1130

NSD

S42

1.00

3225

1nd

nd3.

8nd

3.20

5.0

19,9

0011

.75

552

nd1.

70.8

522

8

R6

35-

23-2

003

1010

NSD

S14

.51

6622

5nd

nd13

nd2.

203.

054

,300

.37

1.90

1,14

0.6

.87

.38

157

R7

65-

23-2

003

1020

NSD

S43

nd30

251

ndnd

9.4

nd3.

204.

022

,100

161.

2085

72.

22.

10.8

720

7R

89

5-23

-200

310

35N

SDS

50nd

3722

8nd

nd5.

4nd

3.30

4.0

14,9

0035

.99

604

1.3

2.00

1.20

212

R9

125-

23-2

003

1045

NSD

S30

nd14

733

5nd

nd22

0.80

17.0

06.

084

,800

6.4

2.90

2,51

06.

06.

401.

6020

9R

1015

5-23

-200

310

55N

SDS

82.9

810

322

1nd

nd5.

5.6

15.

704.

042

,700

121.

1088

4.6

2.30

1.70

171

R11

35-

28-2

003

1600

NSD

S17

.710

412

0nd

nd19

nd1.

402.

066

,500

.31

2.70

1,62

0.6

.93

.43

80R

126

5-28

-200

316

15N

SDS

30nd

2514

1nd

nd16

nd5.

602.

035

,500

8.4

2.10

1,59

02.

53.

10.9

213

3R

139

5-28

-200

316

25N

SDS

63.5

154

123

ndnd

8.2

nd3.

6021

.026

,500

181.

3081

01.

72.

001.

3014

2R

1412

5-28

-200

316

35N

SDS

31nd

246

222

ndnd

19nd

14.0

02.

089

,300

7.1

2.90

1,78

03.

06.

301.

2018

8R

1515

5-28

-200

316

50N

SDS

64.8

531

016

5nd

nd18

.80

12.0

02.

098

,600

122.

602,

800

1.1

3.30

1.80

123

R16

16-

4-20

0390

2PP

130

nd26

730

ndnd

18nd

.34

1.0

29,8

00.7

12.

401,

510

nd.6

5.7

318

R17

16-

4-20

0392

0PP

131

.54

266

36nd

nd18

nd.3

51.

029

,700

.64

2.50

1,49

0nd

.80

.75

26R

181

6-4-

2003

644

PP2

28nd

236

25nd

nd17

nd.6

51.

027

,900

.63

2.30

1,38

0nd

.90

.83

19R

191

6-4-

2003

947

NSD

S29

.52

209

201

ndnd

31.5

49.

202.

068

,600

.53

3.90

2,33

02.

13.

001.

6016

2R

202

6-4-

2003

1005

PP1

25nd

227

24nd

nd18

nd.9

7.5

33,4

00.2

2.30

1,30

0nd

.69

.65

12

R21

26-

4-20

0310

17PP

221

nd21

324

ndnd

17.8

0.6

1.7

26,0

00.8

32.

0093

0nd

.79

.83

13R

222

6-4-

2003

1020

NSD

S28

nd23

815

4nd

nd17

.93

3.10

4.6

30,0

001.

52.

101,

020

nd2.

10.9

714

3R

233

6-4-

2003

1050

PP1

51nd

6854

ndnd

181.

60.7

62.

031

,500

nd2.

501,

210

nd1.

30.9

020

R24

36-

4-20

0311

07PP

244

nd80

64nd

nd21

2.50

.78

1.0

34,4

00nd

2.90

1,48

0nd

1.50

1.10

24R

253

6-4-

2003

1125

NSD

S26

nd19

520

0nd

nd24

3.60

2.70

2.0

79,3

00nd

3.40

1,84

0nd

1.40

1.50

139

R26

46-

4-20

0311

37PP

157

nd12

666

ndnd

214.

501.

302.

041

,500

nd3.

401,

270

nd1.

501.

7015

R27

46-

4-20

0311

40B

LA

NK

ndnd

nd1.

5nd

ndnd

ndnd

.3nd

ndnd

ndnd

ndnd

ndR

284

6-4-

2003

1200

PP2

54nd

162

64nd

nd22

4.90

1.70

3.0

60,1

00.4

13.

101,

030

nd1.

302.

9014

R29

46-

4-20

0312

05N

SDS

30nd

159

190

ndnd

202.

302.

403.

060

,000

nd3.

201,

550

nd1.

61.

1015

2R

304

6-4-

2003

1209

NSD

S50

nd21

624

0nd

nd26

4.40

2.80

3.3

70,0

00.4

43.

701,

720

nd1.

401.

7016

4

Tables 6–8 49

Tabl

e 8.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om R

igby

Bro

ok s

tudy

are

a, C

linto

n, M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

2:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re tw

o tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. NSD

S,

nylo

n-sc

reen

dif

fusi

on s

ampl

er; N

SDSX

, nyl

on-s

cree

n di

ffus

ion

sam

pler

initi

ally

fill

ed w

ith a

erat

ed d

eion

ized

wat

er; P

P1, s

ampl

e fr

om f

irst

pus

hpoi

nt-s

ampl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

R31

46-

4-20

0313

07N

SDSX

15nd

111

28nd

nd13

0.52

4.60

1.0

23,5

000.

852.

4073

0nd

0.74

0.79

15R

325

6-4-

2003

1322

PP1

45nd

212

211

ndnd

272.

903.

804.

176

,500

nd4.

201,

890

nd1.

401.

6013

0R

335

6-4-

2003

1327

PP2

31nd

4939

ndnd

12nd

1.30

1.0

12,8

001.

42.

1053

8nd

.87

.87

6.1

R34

56-

4-20

0313

30N

SDS

18nd

2816

4nd

nd16

nd2.

502.

07,

840

.64

2.40

583

nd1.

80.7

048

R35

66-

4-20

0313

50PP

117

nd10

789

ndnd

201.

9010

.00

1.0

51,7

004.

52.

202,

060

5.5

4.30

1.90

106

R36

66-

4-20

0314

05PP

220

nd10

883

ndnd

191.

7011

.00

12.0

47,2

003.

72.

202,

030

5.1

5.20

2.10

60R

376

6-4-

2003

1419

NSD

S9.

6nd

4819

4nd

nd14

nd5.

102.

030

,700

3.7

1.90

1,22

02.

7nd

.88

163

R38

66-

4-20

0314

30N

SDS

7.7

nd60

219

ndnd

20.5

03.

802.

034

,700

1.7

2.70

1,32

02.

11.

60.6

916

1R

396

6-4-

2003

1440

NSD

SX16

nd43

193

ndnd

12nd

3.60

2.0

21,8

005.

31.

6078

92.

04.

50.8

915

7R

407

6-4-

2003

1453

PP1

70nd

160

73nd

nd20

2.50

1.50

3.3

54,6

00nd

3.40

1,82

0nd

1.10

1.50

12

R41

76-

4-20

0314

57PP

170

nd16

078

ndnd

191.

001.

503.

058

,000

nd3.

001,

900

nd1.

101.

2020

R42

76-

4-20

0315

05PP

277

nd11

081

ndnd

221.

401.

304.

062

,000

nd3.

402,

000

nd1.

301.

2018

R43

76-

4-20

0315

27N

SDS

91nd

240

300

ndnd

351.

806.

408.

012

0,00

0nd

5.10

3,10

0nd

1.80

1.60

150

R44

76-

4-20

0315

37N

SDS

58nd

280

240

ndnd

201.

602.

705.

084

,000

nd3.

102,

100

nd1.

101.

3015

0R

458

6-4-

2003

1551

PP1

35nd

190

69nd

nd16

8.30

8.30

2.0

47,0

00.3

73.

202,

100

nd.6

8.9

712

.00

R46

86-

4-20

0316

15PP

246

nd15

058

ndnd

11nd

1.60

2.0

38,0

00.4

72.

401,

600

nd.5

41.

2014

R47

86-

4-20

0316

25N

SDS

66nd

260

290

ndnd

181.

504.

205.

088

,000

1.7

3.10

2,10

0nd

1.20

1.90

200

R48

86-

4-20

0316

31N

SDS

41nd

210

270

ndnd

15nd

3.10

4.0

63,0

00nd

2.20

1,40

0nd

1.10

.86

190

R49

86-

4-20

0316

40N

SDSX

56nd

290

280

ndnd

171.

203.

704.

084

,000

.86

2.90

1,70

0nd

1.20

1.90

190

R50

96-

4-20

0317

00PP

131

nd22

092

ndnd

11nd

7.30

3.0

54,0

007.

42.

102,

000

3.2

2.30

2.00

30

R51

96-

4-20

0317

17PP

225

nd35

011

0nd

nd10

nd2.

601.

072

,000

.99

1.60

1,80

03.

11.

101.

3013

R52

96-

4-20

0317

30N

SDS

31nd

5839

0nd

nd9.

9nd

4.70

5.0

38,0

005.

71.

601,

200

1.8

2.10

1.60

290

R53

106-

4-20

0317

59PP

122

nd15

010

0nd

nd11

nd9.

802.

048

,000

2.5

1.80

1,40

02.

95.

001.

1049

R54

106-

4-20

0318

10PP

217

nd13

076

ndnd

9.5

nd6.

501.

049

,000

1.9

1.50

1,40

02.

43.

10.8

018

R55

106-

4-20

0318

22N

SDS

ndnd

9324

0nd

nd14

nd4.

803.

056

,000

1.2

1.80

1,30

02.

72.

00.5

616

0

R56

106-

4-20

0318

25N

SDS

ndnd

120

250

ndnd

17nd

4.60

6.0

71,0

001.

62.

101,

400

4.0

1.80

.77

160

R57

116-

5-20

0394

0PP

114

nd45

034

0nd

nd21

nd36

.00

2.0

110,

000

1.3

2.90

2,30

03.

312

.00

.69

420

R58

116-

5-20

0395

0PP

213

nd43

035

0nd

nd23

nd33

.00

2.0

120,

000

.91

3.30

2,40

04.

312

.00

.73

700

R59

116-

5-20

0310

00N

SDS

15nd

220

380

ndnd

16nd

12.0

04.

075

,000

22.

201,

500

4.1

4.10

.76

260

R60

126-

5-20

0310

05PP

115

nd67

021

0nd

nd20

nd6.

908.

013

0,00

0nd

2.80

1,30

01.

92.

50.7

5nd


Tabl

e 8.

Co

ncen

tratio

ns o

f met

als

dete

cted

in s

ampl

es fr

om R

igby

Bro

ok s

tudy

are

a, C

linto

n, M

assa

chus

etts

.—Co

ntin

ued

[See

tabl

e 3

for

defi

nitio

ns o

f at

omic

sym

bols

(an

alyt

es).

All

conc

entr

atio

ns a

re in

mic

rogr

ams

per

liter

, exc

ept f

or c

alci

um a

nd m

agne

sium

, whi

ch a

re in

mill

igra

ms

per

liter

. Con

cent

ratio

ns in

bol

d ty

pe

exce

ed th

e pr

ojec

t act

ion

limit.

Sha

ded

data

rep

rese

nt s

ampl

es th

at w

ere

dilu

ted

2:1

due

to s

ampl

er in

terf

eren

ces.

Rep

ortin

g le

vels

for

thos

e sa

mpl

es a

re tw

o tim

es th

e no

min

al r

epor

ting

leve

ls (

tabl

e 3)

. NSD

S,

nylo

n-sc

reen

dif

fusi

on s

ampl

er; N

SDSX

, nyl

on-s

cree

n di

ffus

ion

sam

pler

initi

ally

fill

ed w

ith a

erat

ed d

eion

ized

wat

er; P

P1, s

ampl

e fr

om f

irst

pus

hpoi

nt-s

ampl

ing

loca

tion;

PP2

, sam

ple

from

sec

ond

push

poin

t-sa

mpl

ing

loca

tion;

nd,

not

det

ecte

d]

Sam

ple

num

ber

Site

nu

mbe

r (fi

g. 8

)D

ate

Tim

e Sa

mpl

er

type

Al

SbA

sB

aB

eCd

CaCr

CoCu

FePb

Mg

Mn

Mo

Ni

VZn

R61

126-

5-20

0310

15B

LA

NK

ndnd

0.71

4nd

ndnd

ndnd

0.2

ndnd

ndnd

ndnd

ndnd

R62

126-

5-20

0310

30PP

217

nd1,

200

230

ndnd

20nd

5.00

1.0

160,

000

nd2.

801,

200

2.5

1.60

nd11

R63

126-

5-20

0310

45N

SDS

35nd

330

380

ndnd

18nd

15.0

04.

011

0,00

07.

32.

501,

600

3.4

6.60

1.20

280

R64

126-

5-20

0310

50N

SDS

19nd

850

480

ndnd

23nd

11.0

05.

018

0,00

01.

22.

801,

500

3.8

4.10

1.00

280

R65

136-

5-20

0311

08PP

133

nd32

46nd

nd9.

7nd

.60

2.0

10,0

006

1.90

580

nd1.

10.6

033

R66

136-

5-20

0311

20PP

133

nd33

49nd

nd9.

9nd

.58

3.0

10,0

005.

91.

9060

0nd

1.10

.62

28R

6713

6-5-

2003

1128

PP2

38nd

2743

ndnd

7.6

nd.6

51.

011

,000

2.6

1.60

790

nd.6

1.7

512

R68

136-

5-20

0311

45N

SDS

33nd

5629

0nd

nd6.

6nd

1.40

3.0

12,0

001.

21.

4081

0nd

.83

nd17

0R

6913

6-5-

2003

1150

NSD

S32

nd40

260

ndnd

7.8

nd1.

302.

011

,000

.91

1.50

980

nd.6

7.4

812

0R

7014

6-5-

2003

1200

PP1

51nd

3251

ndnd

7.6

nd.4

44.

012

,000

6.2

1.60

950

nd.7

5.8

218

R71

146-

5-20

0312

10PP

243

nd32

33nd

nd7.

6nd

.75

3.0

10,0

002.

91.

6082

0nd

.71

.66

ndR

7214

6-5-

2003

1220

NSD

S47

nd49

250

ndnd

8.4

nd1.

705.

013

,000

2.8

1.60

1,40

0nd

.86

.95

150

R73

146-

5-20

0312

30N

SDS

32nd

9621

0nd

nd9.

6nd

1.60

3.0

19,0

001.

72.

001,

300

nd.8

51.

2016

0R

7415

6-5-

2003

1255

PP1

130

216

015

0nd

nd13

3.50

19.0

04.

021

0,00

0.7

3.80

2,60

0nd

3.90

2.50

12R

7515

6-5-

2003

1257

PP1

140

2.1

160

160

ndnd

143.

7019

.00

3.0

210,

000

.67

3.90

2,60

0nd

3.90

2.50

17

R76

156-

5-20

0313

20PP

290

nd16

015

0nd

nd23

1.20

8.60

3.0

150,

000

nd4.

202,

300

nd2.

801.

3014

R77

156-

5-20

0313

25N

SDS

791.

314

034

0nd

nd18

nd14

.00

5.0

110,

000

3.8

2.90

2,40

0nd

3.30

1.50

230

R78

156-

5-20

0313

35N

SDS

160

3.3

170

350

ndnd

113.

7019

.00

5.0

190,

000

5.7

3.10

2,50

01.

26.

604.

1021

0

Tables 6–8 51

Field Tests of Nylon-Screen Diffusion Samplers and Pushpoint ...

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