Prepared in cooperation with 

U.S. Environmental Protection Agency 

Preliminary Results of Sequential Extraction Experiments 

for Selenium on Mine Waste and Stream Sediments from 

Vermont, Maine, and New Zealand 

By N. M. Piatak, R. R. Seal II, R.F. Sanzolone, P. J. Lamothe, and Z. A. Brown 

Open-File Report 2006–1184 

U.S. Department of the Interior 

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

Dirk Kempthorne, Secretary 

U.S. Geological Survey 

P. Patrick Leahy, Acting Director 

U.S. Geological Survey, Reston, Virginia 2006 

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Suggested citation: 


Piatak, N.M., Seal, R.R., II, Sanzolone, R.F., Lamothe, P.J., Brown, Z.A., 2006, Preliminary Results of 


Sequential Extraction Experiments for Selenium on Mine Waste and Stream Sediments from Vermont, 


Maine, and New Zealand: U.S. Geological Survey Open-File Report 2006-1184, 21 p.


Any use of trade, product, or firm names is for descriptive purposes only and does not imply 


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ii 
Contents 

Contents ..............................................................................................................................................................................iii


Figures .................................................................................................................................................................................iii


Tables ..................................................................................................................................................................................iii


Conversion Factors ...........................................................................................................................................................iv


SI to Inch/Pound ............................................................................................................................................................iv


Abstract................................................................................................................................................................................1


Introduction .........................................................................................................................................................................2


Methods ...............................................................................................................................................................................2


Sample Descriptions..........................................................................................................................................................5


Results ..................................................................................................................................................................................6


Mineralogy .......................................................................................................................................................................6


Total Selenium.................................................................................................................................................................9


Extraction Experiments................................................................................................................................................14


Conclusions .......................................................................................................................................................................17


Acknowledgments............................................................................................................................................................18


References Cited ..............................................................................................................................................................18


Figures 

Figure 1. Schematic of sequential extraction procedure............................................................................................4


Figure 2. Estimates of mineral abundances (wt %) for the crystalline portion of samples. Results based on a 


Figure 3. Estimates of amorphous content (wt. %) based on splits spiked with Al2O3 and determined using 


Figure 9. Selenium concentrations from sequential extractions for (A) stream sediments, (B) mine waste, 


Rietveld refinement of powder X-ray diffraction patterns using Siroquant. ...........................................................7


Siroquant..............................................................................................................................................................................8


Figure 4. Total Se determined using HG-AAS.. .............................................................................................................9


Figure 5. Locations, total Se, and sequential extraction results for samples from the Elizabeth mine............11


Figure 6. Locations, total Se, and sequential extraction results for samples from the Ely mine. ......................12


Figure 7. Locations, total Se, and sequential extraction results for samples from the Pike Hill mines site. ...13


Figure 8. Calculated Se totals from extractions versus total from untreated samples. ......................................15


and (C) flotation-mill tailings...........................................................................................................................................16


Tables 

Table 1.Sample descriptions............................................................................................................................................3


Table 2. The results of sequential extractions experiments for Se........................................................................10


iii 
Conversion Factors 

SI to Inch/Pound 

Multiply By To obtain 

Length 

centimeter (cm) 

millimeter (mm) 

meter (m) 

kilometer (km) 

meter (m) 

0.3937

0.03937 

3.281 

0.6214 

1.094 

 inch (in.) 

inch (in.) 

foot (ft) 

mile (mi) 

yard (yd) 

liter (L) 33.82 ounce, fluid (fl. oz) 

liter (L) 2.113 pint (pt) 

liter (L) 1.057 quart (qt) 

liter (L) 0.2642 gallon (gal) 

Mass 

gram (g) 

kilogram (kg) 

0.03527 

2.205 

ounce, avoirdupois (oz) 

pound avoirdupois (lb) 

Temperature in degrees Celsius (°C) may be converted to degrees Fahrenheit (°F) as follows: 

°F=(1.8×°C)+32 

iv 
Preliminary Results of Sequential Extraction 

Experiments for Selenium on Mine Waste and Stream 

Sediments from Vermont, Maine, and New Zealand 

By N. M. Piatak1, R. R. Seal II1, R.F. Sanzolone2, P. J. Lamothe2, and Z. A. Brown2 

Abstract 

We report the preliminary results of sequential partial dissolutions used to characterize the 

geochemical distribution of selenium in stream sediments, mine wastes, and flotation-mill tailings. 

In general, extraction schemes are designed to extract metals associated with operationally defined 

solid phases. Total Se concentrations and the mineralogy of the samples are also presented. 

Samples were obtained from the Elizabeth, Ely, and Pike Hill mines in Vermont, the Callahan mine 

in Maine, and the Martha mine in New Zealand. These data are presented here with minimal 

interpretation or discussion. Further analysis of the data will be presented elsewhere. The total 

concentrations of Se range from 0.43 to 44 mg/kg for stream-sediment samples (n=8), from 2.5 to 

140 mg/kg for oxidized mine waste (n=7), and from 1.7 to 17 mg/kg for oxidized and unoxidized 

flotation-mill tailings (n=4). The highest total concentrations are for the burnt or roasted minewaste samples from Vermont. The extraction technique employed the following dissolution 

reagents, each nominally targeting specific solid-phase forms (given in parentheses): 0.1 M 

KH2PO4 (step 1- soluble and exchangeable), 15% CH3COOH (step 2- carbonates), 0.1 M Na4P2O7 

(step 3- organic material), 0.25 M NH2OH⋅HCl- 0.10 M HCl (step 4- amorphous Fe- and Alhydroxides and amorphous and crystalline Mn-oxides), 1.0 M NH2OH⋅HCl- 25% CH3COOH (step 

5- crystalline Fe-oxides), KClO3 + concentrated HCl (step 6- sulfides and selenides), and a mixture 

of concentrated HF + HNO3 + HClO4 (step 7- residual). The largest fractions of Se were extracted 

in steps 5, 6, and 7. For stream-sediment samples, Se was detected only in leachates from these last 

three steps in which more aggressive reagents were used. The last three steps liberated greater than 

88% of the Se in oxidized mine-waste samples. Approximately half or more of the Se in the 

flotation-mill tailings from the Elizabeth and Callahan mines was found in leachate from step 6. In 

contrast, step 5 leachate for the Martha-mine tailings contains the majority of the Se. Overall, 10% 

or less of the Se was extracted in each of the first four steps for all media. Only oxidized mine 

waste from Vermont and the flotation-mill tailings from Maine contain detectable concentrations of 

Se in the ligand exchangeable fraction (step1). The results presented here have important 

implications for the release to the environment and potential bioavailability of Se from these minewaste and stream-sediment samples. 

1

 U.S. Geological Survey, 12201 Sunrise Valley Dr., Reston, VA 20192 2

 U.S. Geological Survey, Denver Federal Center, Denver, CO 80225 

1

Introduction 

Sequential partial dissolutions were used to characterize the distribution of selenium in 

stream sediments, mine wastes, and flotation-mill tailings at several sites including the Elizabeth, 

Ely, and Pike Hill mines in Vermont, the Callahan mine in Maine, and the Martha mine in New 

Zealand. In general, extraction techniques are developed to extract metals associated with 

operationally defined solid phases giving insight into speciation. The release of Se to the 

environment and toxicity to the biosphere are related to its speciation and partitioning among 

various organic and inorganic solid phases, rather than to its total concentration. The oxidized 

form of selenium, selenate, is highly mobile and toxic and readily bioavailable because its salts are 

soluble and it is weakly adsorbed by particulates. Selenite predominates under mildly reducing 

conditions, is immobilized by adsorption onto particulates, and is less toxic than selenate. Under 

highly reducing, acidic or organic-rich conditions, elemental Se and selenide are the main forms of 

Se, and are generally insoluble and therefore not bioavailable (McNeal and Balistrieri, 1989). 

Selenide is the species expected to be present in solid solution in primary sulfide minerals such as 

pyrite, pyrrhotite, and chalcopyrite. Sulfate also plays a role in Se toxicity in that sulfate inhibits 

the uptake of selenate by microorganisms (Mayland and others, 1989). 

This study was prompted by concerns for stream sediments raised by the preliminary 

Baseline Ecological Risk Assessment (BERA) at the Elizabeth mine. The results of this study will 

be used to characterize better the forms of Se in the sediment and relate this to its potential toxicity. 

Of the nineteen samples analyzed, six are stream-sediment samples from the Elizabeth mine. 

Samples of mine waste from the Elizabeth mine were included to constrain potential sources of Se 

found in the stream sediments. Samples from the others sites were included for comparison 

purposes. 

Methods 

Minerals were identified by X-ray diffraction analysis (XRD). Powder patterns were 

collected using a Scintag X1 automated powder diffractometer equipped with a Peltier detector 

with CuKα radiation. The XRD patterns were analyzed using Material Data Inc.’s JADE software 

and standard reference patterns. Relative amounts of phases were estimated using the Siroquant 

computer program that utilizes the full XRD profile in a Rietveld refinement (Taylor and Clapp, 

1992). Amorphous content was determined using Siroquant on patterns of samples spiked with 15 

wt. % Al2O3. The analytical uncertainty of the Siroquant results is approximately ± 5 wt. %. The 

colors of the samples were determined using soil color charts (Munsell Soil Color Charts, 1994). 

Seven-step sequential extractions were performed on nineteen mine-waste and streamsediment samples, on three duplicates, and on two blanks (Table 1). One blank was used for 

analytical calibration purposes. Samples are either grab or composites. Most composites consist of 

a minimum of 30 sample increments sampled over a measured area divided into a stratified grid. 

One stream-sediment composite (Ely-SD-09) consists of three increments from different 

depositional areas in the stream. Samples were air-dried, sieved to <2 mm (or <180 μm for sample 

1139830-SD, stream sediment from Pike Hill), and homogenized (Table 1). A split of the original 

untreated sample was analyzed for Se by hydride-generation atomic absorption spectrometry (HGAAS) after digestion with a mixture of HNO3-HF-HClO4 (Hageman and others, 2002). Also, 

residues remaining after extraction steps 5 and 6 were analyzed after digestion by HG-AAS. 

Extraction solutes were analyzed for Se by inductively coupled plasma-mass spectrometry (ICPMS) (Lamothe and others, 2002). The accuracy for ICP-MS and HG-AAS analysis is 

approximately ±10%. 

2

Table 1. Sample descriptions. 

Sample ID Extract ID Mine Type Locations Latitude Longitude Date MBlank A - blank Blank - - - EMV-SED-LOC05 B Elizabeth stream Copperas Brook below weir at sediment basin 43.82814 -72.32739 June-05 

sediment outlet. 

EMV-SED-LOC05­ C Elizabeth stream Copperas Brook below weir at sediment basin 43.82814 -72.32739 June-05 Dup1 sediment outlet. Duplicate. 

EMV-SED-LOC06 D Elizabeth stream Copperas Brook below flume at mouth. 43.83129 -72.32686 June-05 

sediment 

EMV-SED-04 E Elizabeth stream Copperas Brook upstream from flume at mouth. 43.83112 -72.32710 June-05 

sediment 

EMV-SED-06 F Elizabeth stream Copperas Brook down-gradient from decant and 43.82814 -72.32730 June-05 

sediment sediment basin drainage confluence. 

EMV-SED-701 G Elizabeth stream Copperas Brook at confluence with decant 43.82903 -72.32760 June-05 

sediment diversion. 

EMV-SED-702 H Elizabeth stream Copperas Brook downstream from confluence 43.83050 -72.32746 June-05 

sediment with decant diversion. 

Ely-SD-09 I Ely stream Ely Brook downstream of culvert, upstream from 43.91873 -72.28652 Dec-1-05 co

sediment confluence with Schoolhouse Brook 

1139830-SD J Pike Hill stream Pike Hill Brook above Richardson Road at weir. 44.06389 -72.30194 Aug-2-05 co

sediment 

04Smith3 K Pike Hill mine waste Lowermost mine-waste dump below main adit at 44.05464 -72.30517 Oct-19-04 co

the Smith mine. 

CLHN-TP-2 L Callahan tailings Tailings pile at edge of wetlands. 44.34306 -68.80556 Jul-19-04 Blank M - blank Blank - - - EMV-SED-LOC05­ N Elizabeth stream Copperas Brook below weir at sediment basin 43.82814 -72.32739 June-05 Dup2 sediment outlet. Duplicate. 

TP1-S-unox O Elizabeth tailings Tailings pile 1 (TP1) near base of TP2. 43.82332 -72.32990 Jul-20-04 TP1-S-unox-Dup P Elizabeth tailings Tailings pile 1 (TP1) near base of TP2. Duplicate 43.82332 -72.32990 Jul-20-04 TP1-S-ox Q Elizabeth tailings Tailings pile 1 (TP1) near base of TP2. 43.82332 -72.32990 Jul-20-04 02TP3A R Elizabeth mine waste TP3 yellow pile below road. 43.82139 -72.33611 Oct-10-02 co02TP3C S Elizabeth mine waste TP3 roasted pile below road. 43.82056 -72.33639 Oct-10-02 co02Ely2A T Ely mine waste Upper mine waste pile. 43.92756 -72.28572 Oct-8-02 co02Ely10A U Ely mine waste Roast beds. 43.92389 -72.28556 Oct-8-02 co04PKHL9 V Pike Hill mine waste Partly burnt red tailings pile above the mine road. 44.06258 -72.30519 Oct-20-04 co

04PKHL11 W Pike Hill mine waste Large mine-waste dump below the mine access 44.06353 -72.30511 Oct-20-04 co

road. 

NZ-Newmont-A X Martha tailings Tailings pile. -37.38592 175.84292 Dec-16-05 

3

The selenium distributions determined by sequential extractions were operationally defined 

by the reagents used, the reaction times, temperatures, and sample to volume extract ratio for each 

step. Not one reagent, time, and temperature can be applied to all sample types to recover a given 

phase; extractions were matrix-dependent. Also, this extraction procedure attempted to 

differentiate the amorphous (step 4) versus crystalline (step 5) Fe-oxide and Fe-hydroxide phases. 

There is a gradation from amorphous to cryptocrystalline to crystalline Fe-oxides and hydroxides 

and Hall and others (1996a) discussed the subtleties in differentiating among the phases depending 

on reagent strength. Additional complicating factors included the possibility that occluded grains 

may persist past their designated dissolution step or factors such as grain size, mineralogy, or solid 

solution may affect the reactivity of phases. The sequential extraction procedure used in this study 

is outlined below and illustrated in Figure 1. The procedure was a combination of methods 

developed by Chao (1972), Chao and Sanzolone (1977; 1989), Chao and Zhou (1983), Chester and 

Hughes (1967), Hall and others (1996a, b), and Kulp and Pratt (2004). The hypothetically targeted 

species in each step are given in italics. The species or phases dissolved by each step will be 

investigated by chemical and mineralogical analysis and discussed in future studies. 

Figure 1. Schematic of sequential extraction procedure. After extract step 5, half of sample was 

digested and analyzed by HG-AAS and the other half was treated in step 6. Because of the potential 

for Se volatilization in step 6, Se in extract 6 was calculated from the difference between Se in 

residue from step 5 and Se in residue from step 6. 

4

• 	Step 1: (soluble, adsorbed, and exchangeable Se fraction) Combine 1.0 g of sample with 25 mL 

0.1 M KH2PO4, agitate for 2 hours at 25oC. Centrifuge for 10 minutes (15,000 rpm, Sorvall 

RC2-B refrigerated supercentrifuge), decant extract and dilute with deionized water (DIW) to 

50 mL. Add 500 μL concentrated ultrapure HNO3. Analyze extract by ICP-MS (Extract 1). 

• 	Step 2: (Se associated with carbonates) Combine residue with 25 mL 15% acetic acid, agitate 

for 2 hours, centrifuge, decant, fill to 50 mL volume with DIW. Analyze extract by ICP-MS 

(Extract 2). 

• 	Step 3: (organic Se) Combine residue with 25 mL 0.1 M sodium pyrophosphate and agitate for 

1 hour. Centrifuge and decant. Add another 25 mL 0.1 M Na4P2O7 to residue, agitate for 1 

hour, centrifuge, decant, add to first split and bring to 50 mL volume with DIW. Analyze 

extract by ICP-MS (Extract 3). 

• 	Step 4: (amorphous Fe- and Al-hydroxides and amorphous and crystalline Mn-oxides) Mix 

residue with 25 mL 0.25 M NH2OH·HCl (hydroxylamine hydrochloride)- 0.10 M HCl for 30 

minutes in a water bath at 50-54oC. Stir occasionally. Centrifuge, decant and fill to 50 mL 

with DIW. Add 500 μL concentrated ultrapure HNO3 and analyze by ICP-MS (Extract 4). 

• 	Step 5: (crystalline “Xl” Fe-oxides) Combine residue with 20 mL 1.0 M NH2OH·HCl in 25% 

CH3COOH. Cap and shake. Place in boiling water (~90o C) bath for 3 hours uncapped, mix 

occasionally. Centrifuge and decant. Rinse residue with 10 mL 25% CH3COOH, by handshaking and then centrifuge and decant into first split. Carry out a second leach with 20 mL 1.0 

M NH2OH·HCl in 25% CH3COOH but heat in boiling water bath for 1.5 hours. Mix 

occasionally. Centrifuge and decant into first split. Fill to 50 mL with DIW. Analyze extract 

by ICP-MS (Extract 5). 

• 	Residue 5: (sulfides and selenides and residual Se) Dry residue at approximately 100°F 

(~38°C) and then disaggregate to homogenize. Split residue in half. Analyze half by HG-AAS 

(Residue 5). Treat other half of residue in next step. 

• 	Step 6: (sulfides and selenides- acid volatile phases volatilized; step may potentially attack 

surfaces, corners, or edges of silicate minerals) Add 0.5 g of KClO3 to residue and mix. 

Slowly add 10 mL concentrated HCl and mix. Let sit for 45 minutes with occasional gentle 

shaking. Add 10 mL of DI, mix, centrifuge, and discard. To the residue, add 10 mL 4 N HNO3 

and heat in boiling water bath for 20 minutes, centrifuge and discard. Add 10 mL DI, shake 

and centrifuge for 10 minutes, also discard. Because some sulfide and selenides may be 

volatilized, calculate step 6 fraction by subtracting Se in residue from step 5 from Se in residue 

from step 6 (Residue 5 – Residue 6). 

• 	Step 7: (residual Se) Dry residue at approximately 100°F (~38°C). Digest sample with mixture 

of HF + HNO3 + HClO4 and analyze by HG-AAS (Residue 6) following procedure of Hageman 

and others (2002). 

Sample Descriptions 

Samples used in the sequential extractions from the abandoned mines in Vermont include 

stream sediments, oxidized mine waste, and flotation-mill tailings, whereas only tailings were used 

from the Callahan mine in Maine and from the Martha mine in New Zealand (Table 1). The 

Elizabeth, Ely, and Pike Hill mines are Superfund sites in the Vermont copper belt that were mined 

intermittently from 1793 to 1958. These deposits, mined primarily for Cu and Zn, are Besshi-type 

5

massive sulfides composed of pyrrhotite, chalcopyrite, and minor sphalerite and pyrite (Slack and 

others, 2001). Flotation-mill tailings from the Elizabeth mine include very dark gray sulfidic 

unoxidized tailings (TP1-S-unox) collected at depth and the overlying yellow oxidized material 

(TP1-S-ox) (Hammarstrom and others, 2001). Samples of oxidized mine waste (not processed in a 

flotation mill) include yellow jarositic waste (02TP3A) and yellowish red hematitic waste 

(02TP3C) that was partly roasted during copperas production (Table 1; Hammarstrom and others, 

2003). The six stream-sediment samples in Table 1 from the Elizabeth mine were collected in 

Copperas Brook downstream from the oxidized mine-waste piles and flotation-mill tailings. Colors 

of stream sediments include brownish yellow, dark yellowish brown, and strong brown based on 

soil color charts (Munsell Soil Color Charts, 1994). The chemistry of the mine drainage from 

Copperas Brook was described by Seal and others (2001). 

Samples used in the extractions from the Ely mine include reddish yellow mine waste 

(02Ely2A) from the upper waste piles and red mine waste (02Ely10A) from roast beds in the lower 

waste piles (Table 1). Mine waste at this site was characterized in detail in Piatak and others 

(2004). One three-composite stream sediment from Ely Brook (Ely-SD-09) was collected 

downstream from the mine site and upstream from the confluence with Schoolhouse Brook 

(Table1). The sample is strong brown probably because of Fe-rich precipitates coating the 

streambed. 

Three samples of mine waste from the Pike Hill mines include olive yellow colored waste 

from the Smith mine (03Smith3), a partly burnt yellowish brown mine waste (04PKHL9), and a 

yellow oxidized mine waste (04PKHL11; Table 1). The two latter samples are from near the top of 

Pike Hill near the Union and Eureka mines. Locations and detailed characterizations of the these 

samples were given in Piatak and others (2006). One strong brown stream sediment (1139830-SD) 

downstream from the Union and Eureka mines is also included in this study (Table 1). 

The Callahan mine, a Superfund site in Brooksville, Maine, exploited a Kuroko-type 

massive sulfide deposit. Massive bodies of pyrite, sphalerite, and chalcopyrite were mined by 

open-pit methods and underground workings from 1968 to 1972 for Zn, Cu, Pb, and Au (Bouley 

and Hodder, 1984). Light gray, fine-grained tailings (CLHN-TP-2) were collected from the 

approximately 45,000 m2 (11-acre) tailings pile at the Callahan mine (USEPA, 2005). 

The Martha mine in Waihi, New Zealand, is an epithermal Au-Ag deposit that was mined 

by underground workings from 1878 to 1952. Mining recommenced in 1988 by open-pit methods 

and is planned to continue until 2007 (Castendyk and others, 2005). Light gray, fine-grained 

flotation-mill tailings (NZ-Newmont-A) were used in the extraction experiments for this study. 

Results 

Mineralogy 

The quantitative mineralogy of the samples was determined by powder X-ray diffraction. 

The relative amount of phases in each sample in weight percent is given in Figure 2 and is for the 

crystalline part of the sample only. Estimates of the amorphous content were determined on spiked 

splits and are shown in Figure 3. The detection limit for XRD is on the order of a few weight 

percent and therefore phases present in trace amounts are likely below reliable detection. As 

shown, most samples primarily are composed of silicates including quartz, feldspar, hornblende, 

mica, chlorite, and clay. Phases such as quartz, feldspar, mica, and hornblende are expected to be 

resistant to extraction reagents in steps 1 through 6 and may persist until attack with concentrated 

acids in step 7. Additional studies will attempt to assess their dissolution behavior. 

6

Based on XRD, most feldspars are plagioclase. The sample from the Martha mine is the 

only one that contains significant alkali feldspar. Muscovite is generally the most common sheet 

silicate. Chlorite is present in lesser amounts. The exception is the tailings from the Callahan mine 

that contains nearly 30 wt. % chlorite and only approximately 7 wt. % mica. Clay minerals include 

kaolinite, talc, vermiculite, and a phase having an intense broad peak at a spacing of approximately 

11.5 to 12 Å, ascribed by the software to sepiolite in the XRD patterns (Figure 2). Sepiolite 

commonly forms in shallow seas and lakes and is not likely to be found in mine waste so this peak 

is assigned to hydrous altered biotite (Poppe and others, 2001). According to Rebertus and others 

(1986), biotite weathers to interstratified biotite-vermiculite (hydrobiotite), thus this low angle peak 

may be a result of varying degrees of biotite alteration. Hornblende was detected in most samples 

having a maximum of 12 wt. % in roasted mine waste (02Ely10A) from the Ely mine. The only 

sample containing detectable pyroxene is tailings from the Martha mine with ~2 wt. % augite. 

Figure 2. Estimates of mineral abundances (wt. %) for the crystalline part of samples. Results 

based on a Rietveld refinement of powder X-ray diffraction patterns using Siroquant. 

The only sample that contains significant carbonate is the tailings from the Callahan mine 

(CLHN-TP-2) having nearly 20 wt. % calcite. Based on Siroquant results, two mine-waste samples 

from Pike may contain trace calcite (<0.8 wt. %). The most intense diffraction peak spacing for 

calcite overlaps the most intense diffraction peak for chalcopyrite [CuFeS2]; these two Pike samples 

may contain minor (~2 wt. %) chalcopyrite. These estimated weight percentages are also near the 

reliable detection limits. The second step using acetic acid was aimed at dissolving carbonate 

minerals such as calcite [CaCO3] and dolomite [CaMg(CO3

)2] (Kulp and Pratt, 2004). 

7

Step 4 of the extraction procedure targeted amorphous Fe- and Al-hydroxides and 

amorphous and crystalline Mn-oxides (Chao, 1972; Chao and Zhou, 1983; Hall and others, 1996a). 

No crystalline Mn-oxide phases were detected by XRD. Using splits of the samples spiked with 

Al2O3, the amount of amorphous material in the samples was estimated using Siroquant. The 

amorphous fraction likely consists of Al, Fe, and Si-rich compounds for these samples and 

hypothetically includes the amorphous Fe- and Al-hydroxides targeted in step 4. The weight 

percentages of amorphous material in Figure 3 range from 15 to 62. Some of the lowest estimates 

are for mine waste from Pike Hill; some of the highest are for fine-grained flotation-mill tailings 

from the Callahan and Martha mines. 

Figure 3. Estimates of amorphous content (wt. %) based on splits spiked with Al2O3 and determined 

using Siroquant. 

The crystalline Fe-oxide and Fe-hydroxysulfate minerals found in these samples include 

goethite [FeOOH], hematite [Fe2O3], and jarosite [K2Fe6(SO4)4(OH)12]. Most stream-sediment 

samples from the Elizabeth mine do not contain detectable amounts of these phases. However, 

EMV-SED-LOC05 collected downstream from a sediment basin outlet below the tailings pile in 

Copperas Brook does contain nearly 6 wt. % goethite and 9 wt. % jarosite (Figure 2). The stream 

sediments from Ely and Pike Hill contain detectable goethite and jarosite. Both of these samples 

and EMV-SED-LOC05 were collected in areas of the stream where Fe-rich precipitates coated the 

streambed. Oxidized mine-waste samples and the oxidized tailings sample from the mines in 

Vermont contain detectable jarosite (3 to 20 wt. %) and goethite (5 to 27 wt. %). Significant 

hematite was found in three samples including 02TP3C (23 wt. %), 02Ely10A (11 wt.%), and 

04PKHL9 (7 wt. %). All three are burnt or roasted mine waste. Hematite is not present in 

significant quantities in the ore or host rocks at these mines. Roasting or burning of the pyrrhotiterich ores would have driven off much of the sulfur and left a residue of ferric oxide (hematite). 

Chester and Hughes (1967) reported the dissolution of crystalline Fe-oxide minerals (goethite and 

hematite) using the reagents in step 5. Only partial dissolution of jarosite was expected based on a 

study by Filipek and Theobald (1981). 

Several samples likely contain minor to trace amounts of sulfides based on the semiquantitative mineralogy. Estimates of ~2 wt. % chalcopyrite [CuFeS2] were determined for two 

8

mine-waste and one stream-sediment sample from Pike Hill. Several samples contain ~3 wt. % or 

more pyrite [FeS2] and include tailings from the Callahan, Elizabeth, and Martha mines (Figure 2). 

The only sample having detectable pyrrhotite [Fe1-xS] is the unoxidized tailings from TP1 (TP1-Sunox) at the Elizabeth mine having nearly 15 wt. %. Sphalerite [ZnS] was found in a few weight 

percent in the Callahan tailings (CLHN-TP-2) and oxidized mine waste from Elizabeth (02TP3A). 

The reagent used in step 6 of the extraction procedure should have oxidized, possibly volatilized, 

and decomposed sulfides and selenides (Chao and Sanzolone, 1977). 

Total Selenium 

Total Se in the original bulk samples is illustrated in Figure 4 by sample type and mine site. 

Values are given in Table 2. Figures 5, 6, and 7 show locations and total Se concentrations for 

samples collected from the Elizabeth, Ely, and Pike Hill mines. (In Figure 5, the north toe of TP1 

has been regraded to a less steep slope and stream-sediment samples were collected after regrading. 

Although the site was modified, the figure illustrates the overall site configuration.) The 

concentrations of Se in stream sediments from the Elizabeth mine found in this study range from 

0.43 to 12 mg/kg. Most contain less than 2 mg/kg with the exception of EMV-SED-LOC05 with 

12 mg/kg Se (Figure 5). This sample is unique mineralogically in that it is the only streamsediment sample from Elizabeth that contains detectable goethite and jarosite. As shown in Figure 

4, the concentrations of total Se in stream sediments from the Ely (43 mg/kg Se) and Pike Hill (44 

mg/kg Se) mines are similar and are significantly higher than in those from the Elizabeth mine. 

These samples also contain detectable goethite and jarosite (Figure 2). The Pike Hill stream 

sediment is a finer-sized material than the others because it was sieved with a smaller mesh size. 

The effect of size fraction on Se concentrations was not examined in this study but may influence 

Se content. 

Figure 4. Total Se determined using HG-AAS. Samples are grouped according to sample type and 

color coded according to mine site. 

9

Table 2. The results of sequential extractions experiments for Se. Concentrations (mg/kg) are for extracts 1 throu

concentrations in leached solid), for residues remaining after steps 5 and 6, and in the original bulk sample. AbbrMS (inductively coupled plasma-mass spectrometry), HG-AAS (hydride-generation atomic absorption spectromet(crystalline). Less than sign (<) is shown for concentrations below the detection limit. Sample A was a blank useICP-MS and therefore not given. Duplicate HG-AAS analysis of bulk sample EMV-SED-LOC05 is given in parenthe

extract/residue (step) extract 1 extract 2 extract 3 extract 4 extract 5 residue 5 residue 5 - residue 

(step 1) (step 2) (step 3) (step 4) (step 5) (step 6) 

fraction hypothetically exchangeable carbonate organic amorphous Fe Xl Fe sulfides/selenides sulfide/selenide extracted & Al, all Mn oxides & residual 

method ICP-MS ICP-MS ICP-MS ICP-MS ICP-MS HG-AAS calculated 

Sample ID Extract ID mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg 

EMV-SED-LOC05 B <0.2 <0.2 <0.2 <0.2 0.7 7.4 5.1 EMV-SED-LOC05-Dup1 C <0.2 <0.2 <0.2 <0.2 1.0 7.4 5.1 EMV-SED-LOC06 D <0.2 <0.2 <0.2 <0.2 <0.2 0.31 >0.21 

EMV-SED-04 E <0.2 <0.2 <0.2 <0.2 <0.2 0.52 >0.42 

EMV-SED-06 F <0.2 <0.2 <0.2 <0.2 <0.2 0.75 0.53 EMV-SED-701 G <0.2 <0.2 <0.2 <0.2 <0.2 0.15 >0.05 

EMV-SED-702 H <0.2 <0.2 <0.2 <0.2 <0.2 0.47 0.18 Ely-SD-09 I <0.2 <0.2 <0.2 0.2 4.9 29 26.5 

1139830-SD J <0.2 <0.2 <0.2 <0.2 6.5 37 27.7 

04Smith3 K <0.2 <0.2 <0.2 <0.2 6.1 16 9.8 

CLHN-TP-2 L 0.3 0.3 <0.2 0.4 0.8 2.9 >2.8 Blank M <0.2 <0.2 <0.2 <0.2 <0.2 - - EMV-SED-LOC05-Dup2 N <0.2 <0.2 <0.2 <0.2 1.2 9.6 8 

TP1-S-unox O <0.2 <0.2 <0.2 <0.2 <0.2 16 11.6 TP1-S-unox-D P <0.2 <0.2 <0.2 <0.2 <0.2 16 12.9 TP1-S-ox Q <0.2 <0.2 <0.2 0.3 2.3 3.8 2.94 

02TP3A R 0.8 0.2 1.8 0.9 6.4 22 19.4 02TP3C S 2.6 0.3 4.5 2.6 16.0 84 45 02Ely2A T 0.3 <0.2 0.5 0.4 10.7 32 29.2 

02Ely10A U 1.1 <0.2 3.4 1.3 21.2 47 20 04PKHL9 V 1.8 0.3 10.4 2.7 15.3 100 45 04PKHL11 W 0.4 0.3 0.7 0.8 12.7 33 28 

NZ-Newmont-A X <0.2 <0.2 <0.2 <0.2 2.7 0.60 0.38 

10

Figure 5. Locations, total Se, and sequential extraction results for samples from the Elizabeth 

mine. Concentrations of total Se are shown as color-coded circles at sampling location. Relative 

amounts of Se extracted in each step are shown in pie graphs next to sampling site. 

11 
Figure 6. Locations, total Se, and sequential extraction results for samples from the Ely mine. 

Concentrations of total Se are shown as color-coded circles at sampling location. Relative amounts 

of Se extracted in each step are shown in pie graphs next to sampling site. Modified from Piatak 

and others (2004). 

12 
Figure 7. Locations, total Se, and sequential extraction results for samples from the Pike Hill mines 

site. Concentrations of total Se are shown as color-coded circles at sampling location. Relative 

amounts of Se extracted in each step are shown in pie graphs next to sampling site. Modified from 

Piatak and others (2006); original base map from White and Eric (1944). 

The concentrations of Se are generally higher in mine waste compared to stream sediments 

(Figure 4). The three highest bulk concentrations, reaching 140 mg/kg Se, are for mine waste from 

Vermont that has been either roasted or burnt (02TP3C, 02Ely10A, 04PKHL9). These samples are 

also mineralogically unique in that they contain significant hematite that likely formed during 

roasting or burning (Figure 2). The mine waste with the least amount of Se is from the Smith mine 

(2.5 mg/kg Se), which is the smallest of the three mines at the Pike Hill site (Figure 7). At the 

Elizabeth mine, unoxidized tailings (17 mg/kg Se) and oxidized tailings (10 mg/kg Se) contain Se 

in concentrations close to those found in one stream sediment directly downstream of the tailings 

13

piles (EMV-SED-LOC05; Figure 5). Tailings from the Callahan (5.8 mg/kg Se) and Martha (1.7 

mg/kg Se) mines contain lower concentrations compared to Elizabeth tailings in Figure 4. 

As stated earlier, the toxicity of Se is a function of its speciation and partitioning among 

various organic and inorganic solid phases, rather than its total concentration. Nonetheless, soil 

and sediment criteria or ratings have been set for total Se concentrations and are used here for 

comparison purposes. Mine waste and flotation-mill tailings are compared to soil criteria whereas 

stream sediments are compared to sediment hazard ratings. The guidelines set for the aquatic 

environment (sediment) are usually over an order of magnitude lower than those for the terrestrial 

environment (soil). 

The USEPA Preliminary Remediation Goal (PRG) for industrial soil is 5,100 mg/kg Se and 

390 mg/kg Se for residential soil (USEPA, 2004). PRGs are guidelines, not legally enforceable 

standards, used for initial evaluations of potentially contaminated sites. The total concentrations of 

Se in mine waste and tailings are well below the PRGs for both industrial and residential soils 

(Figure 4). The range in concentrations of Se found in soils in the Eastern United States is <0.1 to 

3.9 mg/kg as reported by Shacklette and Boerngen (1984). Although the samples do not exceed 

PRGs, the concentrations in mine waste and tailings are higher than the range for eastern soils, 

except for the sample from the Smith mine and the Martha tailings (Table 2). 

Selenium in sediments can be absorbed or ingested by aquatic organisms and 

bioaccumulates through the food chain (Lemly, 1997). A protocol for conducting a hazard 

assessment of Se was developed by Lemly (1995) based on five ecosystem components: water, 

sediments, benthic macroinvertebrates, fish eggs, and aquatic bird eggs. The hazard assessment is 

a sum of the hazard rating for all five categories to assess food-chain bioaccumulation and 

reproductive impairment in fish and aquatic birds. In this study, the hazard rating for the sediment 

component was examined. Selenium concentrations in four stream sediments from the Elizabeth 

mine are below the no-hazard rating of <1 mg/kg and one has a minimal hazard rating (1-2 mg/kg). 

Selenium concentrations in the sediment directly downstream from the sediment basin outlet below 

TP1 at Elizabeth (EMV-SED-LOC05) and in the sediment from Ely (Ely-SD-09) and Pike Hill 

(1139830-SD) fall in the high hazard rating field of >4 mg/kg. 

Extraction Experiments 

The concentrations of Se leached from the solids in steps 1 through 5 are given in Table 2. 

Selenium extracted from the solid was calculated from extract concentrations and solid to 

extraction solution ratios. Selenium in residues from steps 5 and 6 and in original untreated 

samples determined after digestion with concentrated HF, HNO3, and HClO4 are also in Table 2. 

The difference between the step 5 residue and the step 6 residue concentrations (Table 2; values in 

italics) is the Se extracted by step 6 solvents (selenide/sulfide fraction; see Figure 1). Direct 

measurement of Se in extract solution 6 was not used because some sulfides and selenides have 

been volatilized by the acids utilized in step 6. 

The sum of the concentrations of Se leached from the solids in steps 1 through 5 plus the 

residue after step 5 (calculated total) should be equal to the original total Se concentration of the 

solid (bulk total). In Figure 8, the calculated total Se correlates with the total Se in the untreated 

sample with a R2 value of 0.97 for the linear regression. The only sample that significantly deviates 

from the trend is the mine waste from the Smith mine (04Smith3) that has a sum of Se from the 

extraction steps significantly higher than that found in the bulk sample. 

14

Figure 8. Calculated Se totals from extractions versus total from untreated samples. Calculated 

total for each sample is the sum of Se in extracts 1, 2, 3, 4, and 5 and in the residue after step 5. For 

extracts with Se less than the detection limit, half of the detection limit was used in calculations. A 

linear regression (dashed line) and the equation for the line and R2 are also shown. 

As mentioned previously, the fractions of Se leached were a result of extraction reagent, 

time, temperature, and sample to volume ratio. Each step of the extraction was designed to 

dissolve a specific fraction but the success must be investigated by chemical and/or mineralogical 

studies. This discussion focuses on the results of Se extracted in each step with only minor 

emphasis on implications of Se speciation and specific minerals or phases hosting the Se. 

References to specific phases are used liberally in the following discussion and dissolution of 

phases will be assessed in future studies. 

Figure 9 shows the sequential partial dissolution results for Se in stream sediments, mine 

waste, and tailings from all the mines. Figures 5, 6, and 7, discussed above, show sampling 

locations, total Se, and fractionation of Se in extracts for the Elizabeth, Ely, and Pike Hill mines, 

respectively. The only detectable Se for stream-sediment samples is in extracts from steps 5, 6, and 

7 where more aggressive reagents are employed (Figure 5-7 and 9). For most stream sediments, 

the highest fraction of Se (between 38% and 100%) was found in extraction step 6 using KClO3 and 

concentrated HCl (Figure 9). This procedure should have oxidized, possibly volatilized, and 

decomposed sulfides and selenides (Figure 1; Chao and Sanzolone, 1977). Based on mineralogy 

from XRD, these samples contain trace to non-detectable concentrations of sulfides such as 

chalcopyrite, pyrite, and pyrrhotite, and sphalerite. However, the detection limit for XRD is not 

low enough to exclude sulfides and selenides as potential sources. 

15

Figure 9. Selenium concentrations from sequential extractions for (A) stream sediments, (B) mine 

waste, and (C) flotation-mill tailings. 

16 
In some stream sediments, Se was also found in the residual fraction (step 7; up to 62% Se 

extracted), likely in the structure of or as inclusions in silicates (i.e., quartz, feldspar, muscovite) or 

other refractory minerals (i.e., rutile), and in an acidic leach using hydroxylamine hydrochloride 

and acetic acid (step 5; up to 15% Se extracted). The solution in step 5 has been found to dissolve 

crystalline Fe-oxide minerals (Chester and Hughes, 1967). Goethite was the only Fe-oxide 

identified in the stream sediments by XRD. Jarosite is a Fe-hydroxysulfate found in several stream 

sediment samples, as well as mine waste and oxidized tailings. In a study by Filipek and Theobald 

(1981), only 20% of a nearly monominerallic jarosite sample was dissolved using a extractant 

solution similar but more dilute to the step 5 extract. Filipek and Theobald (1981) used a 0.25 M 

NH2OH·HCl in 25% acetic acid solution whereas the present study used 1.0 M NH2OH·HCl in 25 

% acetic acid. The extent to which jarosite is resistant to these dissolution reagents will be 

examined in future studies. These results suggest Se in the stream sediments is not easily leached. 

Like the stream sediments, Se in mine waste was predominantly mobilized in the last few 

extracts that hypothetically target crystalline Fe-oxides such as goethite or hematite (step 5: 12­

29% Se extracted), sulfides and selenides (step 6: 27-67% Se extracted), and residual minerals (step 

7: 6-42% Se extracted) as shown in Figures 5, 6, 7 and 9. Like stream sediments, significantly 

more Se was extracted in step 6 compared to the other steps, except for roasted or burnt mine waste 

(02TP3C, 02Ely10A, and 04PKHL9) which contains comparable concentrations of Se in steps 6 

and 7. Four to eight percent of the Se extracted from these three samples was found in the step 3 

extract. According to Hall and others (1996b), the sodium pyrophosphate used in step 3 should 

target the organic component of the samples. The step 3 extracts for the other mine-waste samples 

contain between 1 and 6% of the total Se leached. Small fractions of Se were leached from 

extraction steps 1 and 4 suggesting a few percent of the Se may be found in the 

exchangeable/soluble fraction (step 1; Chao and Sanzolone, 1989) and the amorphous Fe- and Alhydroxides and amorphous and crystalline Mn-oxides (step 4; Chao, 1972; Chao and Zhou, 1983; 

Hall and others, 1996a;). 

Approximately three-fourths of the total Se in unoxidized sulfide-rich tailings (TP1-S-unox) 

from the Elizabeth mine was found in the step 6 extract (sulfides/selenides), the remainder being in 

the residual step 7 fraction (Figures 5 and 9). In the oxidized tailings (TP1-S-ox), Se was also 

found in significant concentrations in step 5, which targeted crystalline Fe-oxides (Figures 5 and 9). 

In contrast to the unoxidized tailings, TP1-S-ox contains up to 5 wt. % goethite and jarosite based 

on XRD. 

Selenium in tailings from the Callahan mine predominately resides in the step 6 fraction 

(sulfide/selenide) with minor amounts being in steps 4 and 5 and below or near detection for steps 

1 and 2 (Figure 9). In contrast to the tailings from Vermont and Maine, most Se in the Marthamine tailings was extracted in step 5, which targeted the dissolution of crystalline Fe-oxide 

minerals. This is inconsistent with mineralogy based on XRD, which found no detectable 

crystalline Fe-oxide phases. The sample does contain a few weight percent pyrite. 

Conclusions 

The results from the sequential extractions on stream sediments, mine waste, and flotationmill tailings suggest that most Se in these samples was not found in the readily soluble or ligand 

exchangeable fractions that hypothetically should be leached with the potassium phosphate solution 

in first step of the scheme, presumably as selenate or selenite. For all stream-sediment samples, the 

concentrations of Se in this fraction is less than the detection limit. The highest concentrations in 

this fraction is from roasted or burnt mine waste from the Elizabeth (02TP3C: 2.6 mg/kg), Ely 

(02Ely10A: 1.1 mg/kg) and Pike Hill (04PKHL9: 1.8 mg/kg) mines. Only mine-waste samples 

17

contain detectable Se in the extraction using sodium pyrophosphate, which has been shown to 

extract humic and fulvic complexes in soils (step 3, organic fraction). Again, the highest 

concentrations were leached from the burnt or roasted mine wastes and reach 10.4 mg/kg Se. 

These three samples also contain the highest bulk concentrations of Se (up to 140 mg/kg). 

Generally, the largest fractions of Se were found in the leaches using the most aggressive 

reagents. These included potassium chlorate and concentrated hydrochloric acid to oxidize and 

decompose sulfides and selenides (step 6) and the concentrated multi-acid digestions used to 

decompose the final residual matrix (step 7). Selenium in stream sediments was predominantly 

mobilized in step 6 extract. In a few stream-sediment samples and in the mine waste and oxidized 

tailings, Se was also found in the extract from step 5. The solution for this step was hydroxylamine 

hydrochloride in dilute acetic acid and has been shown to extract metals bound to crystalline Feoxides such as goethite and hematite. Overall, these extraction results suggest that most of the Se 

in these samples was partitioned into crystalline Fe-oxides and insoluble sulfides, selenides, or 

silicates. Future efforts will investigate specific phases or species leached by each extraction step 

by conducting multielement chemical and mineralogical studies. 

Acknowledgments 

The authors would like to thank Ed Hathaway, U.S. Environmental Protection Agency, and 

Scott Acone, U.S. Army Corps of Engineers, for facilitating this project. The study was funded by 

the U.S. Environmental Protection Agency as part of the remedial investigation that is being 

implemented through an interagency agreement with the U.S. Army Corps of Engineers and by the 

Mineral Resources Program of the U.S. Geological Survey. The authors are grateful to Jeff Mauk 

from The University of Auckland for providing the sample from the Martha mine. We also thank 

Jason Clere, Kate McDonald, and Frederik Schuele from the URS Corporation for providing 

stream-sediment samples from the Elizabeth and Ely mines. Jane Hammarstrom, John Jackson, 

and Tim Muzik from the U.S. Geological Survey helped collect and characterize several samples 

from the mines in Vermont. The manuscript benefited from reviews by Avery Drake, Jane 

Hammarstrom, and Ed Hathaway. 

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21