Potential contaminants at a dredged spoil placement site, Charles City County, Virginia, as revealed by sequential extraction

Backfills of dredged sediments onto a former sand and gravel mine site in Charles City County, VA may have the potential to contaminate local groundwater. To evaluate the mobility of trace elements and to identify the potential contaminants from the dredged sediments, a sequential extraction scheme was used to partition trace elements associated with the sediments from the local aquifer and the dredged sediments into five fractions: exchangeable, acidic, reducible, oxidizable, and residual phases. Sequential extractions indicate that, for most of the trace elements examined, the residual phases account for the largest proportion of the total concentrations, and their total extractable fractions are mainly from reducible and oxidizable phases. Only Cd, Pb, and Zn have an appreciable extractable proportion from the acidic phase in the filled dredged sediments. Our groundwater monitoring data suggest that the dredged sediments are mainly subject to a decrease in pH and a series of oxidation reactions, when exposed to the atmosphere. Because the trace elements released by carbonate dissolution and the oxidation (e.g., organic matter degradation, iron sulfide and, ammonia oxidation) are subsequently immobilized by sorption to iron, manganese, and aluminum oxides, no potential contaminants to local groundwater are expected by addition of the dredged sediments to this site.


I. INTRODUCTION
A former sand and gravel mine site in Charles City County, VA was mined in the 1980s, backfilled with 10 m of sandy mine spoils, and reclaimed to farmland use. The property owner, i.e., the Weanack Limited Land Partners, bulldozed the reclaimed mine-spoils into a diked basin and imported sediments dredged from the upper Potomac River estuary as fill for the excavated basin in order to convert it to high-quality farmland. However, in theory, the addition of these dredged sediments may influence local groundwater quality. First, the back-filling dredged sediments have the potential of becoming a contaminant source because these dredged estuarine sediments may contain contaminants such as heavy metals that could subsequently enter the groundwater. Second, by adding these dredged sediments into the reclamation basin, the in situ conditions could change, potentially liberating toxic heavy metals/metalloids to local groundwater. Possible processes that could be induced by the addition of the dredged sediments include: ͑1͒ mixing of pore water from the upper Potomac River sediments with the local groundwater, which will affect ionic strength and pH of the dredged sediment pore water and local groundwater; ͑2͒ infiltration of the dredged sediments by rain (pHϳ5.6), which will affect the pH of the dredged sediment pore water; and ͑3͒ oxidizing the dredged sediments by exposing them to the atmosphere and/or by local groundwater, which will also affect the redox conditions of the dredged sediment pore water. Therefore, before developing these dredged sediments into agriculturally productive soils, leachate that exits the sediment disposal site must be monitored and traced. To accomplish this, any potential contaminants from the backfilling sediments must first be determined. In this work, a sequential extraction scheme was used to evaluate the mobility of trace elements in sediment and to reveal any potential contaminants that may be mobilized from the dredged sediments.
The mobility of trace elements in sediments, as well as their potential toxicity, depends on their aqueous and solidphase speciation and the chemical and physical processes to which these elements are subjected. Sequential extraction procedures have been used to identify the ''operationally defined solid-phase speciation'' of trace elements in sediments, as a means to evaluate their mobility in the natural environments. [1][2][3][4][5][6] To ascertain the potential mobility of any contaminants added to a dredged spoil placement site by back-filling with the Potomac River dredged sediments, batch extractions were performed on the local aquifer sediments and on back-filling sediments dredged from the upper Potomac River estuary. The sequential extraction scheme a͒ Author to whom correspondence should be addressed; electronic mail: jtang@odu.edu proposed and outlined by Tessier et al. 5 was used to partition trace elements associated with these sediments into the following fractions: Fraction 1 ͑Exchangeable phase͒. Trace elements, which are weakly associated with clays, hydrated oxides of iron and manganese, and humic acids, and are readily mobilized by changes in ionic strength.
Fraction 2 ͑Acidic phase͒. Trace elements bound to sediment carbonates, which are susceptible to carbonate dissolution as sediments are acidified.
Fraction 3 ͑Reducible phase͒. Trace elements bound to iron and manganese oxides, which will be reduced and solubilized under anoxic conditions ͑i.e., low Eh͒.
Fraction 4 ͑Oxidizable phase͒. Trace elements in reduced metal complexes or bound to organic matter, which can be released into solution under oxidizing conditions. Residual phase. Trace elements held within the crystal structure of primary and secondary minerals, which are not expected to be released into the solution over a reasonable time span under natural conditions. Eight samples of local aquifer sediments and the Potomac River dredged sediments were sequentially extracted using the techniques outlined by Tessier et al. 5 The various batch extraction fluids were subsequently analyzed by inductively coupled plasma mass spectrometry ͑ICP-MS; Finnigan MAT Element II͒ for eleven trace elements ͑Ag, Cd, Sb, Tl, Pb, Cr, Fe, Ni, Cu, Zn, and As͒. From the analytical results, the percentage of the total concentration of each trace element in each fraction is calculated. The total extractable fractions of trace elements and their ''operationally defined solid-phase speciation'' are discussed. Finally, any potential mobility of any contaminants from the dredge sediments as in situ conditions change following disposal at the replacement site is evaluated.

II. STUDY AREA
The dredged spoil placement site is located in Charles City County, VA ͑Fig. 1͒. The site was mined for sand and gravel and backfilled by 10 m of mine spoils with 1 m of natural soil over the fill. In the fall of 2000, backfill mine spoils were excavated and reconfigured into dikes around a large L-shape basin and subsequently used as a disposal basin to receive the sediments being dredged from the upper Potomac River estuary near Alexandria, VA ͑Figs. 1 and 2͒. To the north and east of the site, the slope of the ground is steep, forming a scarp. Numerous monitoring wells were installed at the disposal site ͑Fig. 2͒ to monitor groundwater quality and to evaluate the potential flow paths.
The distribution of aquifers and aquitards at the study site is complex. The complexity stems from the history of cut-and-fill related to the sand-and-gravel mining at this site and the history of stream incision and valley-infilling caused by Pleistocene sea level fluctuations. [7][8][9] According to our stratigraphic analyses, at least six different geologic units are thought to play significant roles in controlling the flow of groundwater in the study region ͑Fig. 3͒. These geologic units are listed in Table I, and include Mining Fill, Kennon Formation, Tabb Formation, Shirley Formation, Nanjemoy-Marlboro unit, and Aquia-Potomac units. [7][8][9] A flow path map ͑Fig. 4͒, generated from hydrologic head data collected monthly at all monitoring wells and staff gauges, indicates that groundwater radiates in nearly all directions from the elevated replacement site. After leaving the bermed area, groundwater passes through highly permeable beds within the Mining Fill and the Tabb Formation. Water draining from the dredged sediments may take as little as one year to more than a decade to reach surface water bodies, depending upon the sediment permeability, distance, and hydraulic gradient along the flow path.

A. Sampling
Eight sediment samples were collected from the local aquifers and the back-filling dredged sediments from the upper Potomac River estuary. Samples 1 and 2 are older dredged sediments from the Potomac River, which were filled onto the replacement site between January and March 2001. Samples 4 and 5 represent the more recent filling dredged sediments, which were filled onto the replacement site between January and March 2002. These four samples were collected from the dredged sediments after they were deposited in the reclamation basin ͑Fig. 2͒. Samples 6 and 7 belong to the Tabb Formation. Sample 6 represents shallow sediments developed within the Tabb Formation, and was collected from the well SW 40 core at a depth of 1.1-1.7 m ͑Fig. 2͒. Sample 7 is from deeper sediments, taken from the well SW44 core at a depth of 2.7-3.4 m ͑Fig. 2͒. Samples 8 and 9 belong to the Shirley Formation. Sample 8 represents shallow sediments, collected from the well SW42DV core at a depth of 0.9-1.5 m ͑Fig. 2͒, whereas sample 9 represents deeper sediments, obtained from the well SW43 core of a depth of 2.7-4.3 m ͑Fig. 2͒.
The sediment samples were stored at 4°C prior to batch extractions. Before batch extractions, sediment samples were dried at ϳ80°C in a forced air oven and then ground with a wooden roller to pass through a 1 mm sieve and homogenized. 0.5 g sediment samples ͑dry weight͒ were used for the initial extraction.

B. Leaching procedures and reagents
The methods used for sequential trace element extractions are those discussed in detail by Tessier et al. 5 In the following, we briefly outline the procedure for each extraction step.

Fraction 1: Exchangeable phase
A 0.5 g ͑dry weight͒ aliquot of sample was extracted into a 50 ml tube with 8 ml of 1 M CH 3 COONa at room temperature and pH 8.2. The mixture was subsequently agitated on a shaker for 1 h.

Fraction 2: Acidic phase
The residue from Sec. III B 1 was leached at room temperature with 8 ml of 1 M CH 3 COONa adjusted to pH 5.0 with CH 3 COOH. The mixture was agitated on a shaker for 5 h.

Fraction 3: Reducible phase
The residue from Sec. III B 2 was extracted with 20 ml of 0.04 M NH 2 OH•HCl in 25% ͑v/v͒ CH 3 COOH for 6 h at 96Ϯ1°C. The mixture was agitated every 30 min.

Fraction 4: Oxidizable phase
The residue from Sec. III B 3 was extracted with 3 ml of 0.02 M HNO 3 and 5 ml of 30% H 2 O 2 , adjusted to pH 2.0 with ultrapure HNO 3 ͑Seastar Chemicals͒. The mixture was heated to 85Ϯ1°C for 2 h with occasional agitation. Then, 3 ml of 30% H 2 O 2 (pH 2.0 adjusted with HNO 3 ) was added and the mixture was heated again to 85Ϯ1°C for 3 h with occasional agitation. After the mixture was cooled to room temperature, 5 ml of 3.2 M CH 3 COONH 4 in 20% ͑v/v͒ HNO 3 was added and the mixture was diluted to 20 ml and agitated for 30 min at room temperature on a shaker.
Between each successive extraction, separation was effected by centrifugation at 10 000 rpm for 10 min. The supernatant was removed and stored in a 50 ml bottle at 4°C until analysis. The residue after each extraction was washed with 8 ml of distilled-de-ionized ͑18 M⍀ cm͒ MilliQ water ͑i.e., Q-water͒. After centrifugation for 10 min, this second supernatant was discarded.

C. Digestion of sediment sample for residual and total trace element analysis
The residue from Sec. III B 4 was first digested in a 50 ml Teflon® beaker with 10 ml of ultrapure HF ͑Seastar Chemicals͒. The mixture was subsequently evaporated to near dryness. Then, 10 ml of ultrapure HNO 3 ͑Seastar Chemicals͒ was added and again, the mixture was evaporated to near dryness. Subsequently, another 10 ml of ultrapure HF was added and the mixture was evaporated to near dryness. The residue was then dissolved with Q-water and diluted up to 25 ml with Q-water.
Finally, 0.2 g initial sediment sample ͑dry weight͒ was digested according to the same procedure for the residual phase and the final solution was diluted to 25 ml with Q-water.

D. Analytical methods
Concentrations of trace elements in extractions, residual phase, and total sediment samples were determined by inductively coupled plasma mass spectrometry ͑ICP-MS; Finnigan MAT Element II; Dr. Z. Chen, analyst͒. The detection limits were below 10 ng/L for Ag, Cd, Sb, Tl, and Pb, and below 1 g/L for Cr, Fe, Ni, Cu, Zn, and As in the extraction fluids. Sequence control blanks and standards prepared from Perkin Elmer multi-element solutions were run regularly during the analyses to monitor the blank level, accuracy, and instrument drift. Analytical precision as relative standard deviation ͑RSD͒, estimated from five replicate analyses, is less than 1.0% for Cd, Sb, Tl, Pb, and Ni. For other elements, analytical precision is between 1.0% and 5.2% RSD.

A. Concentrations and recoveries
Concentrations of the analyzed trace elements in the extractions, residual phase, and total sediment samples are given in Table II. The sequential extraction procedure provides satisfactory recoveries, most of which are within 80%-120% ͑Table II͒.

B. Total extractable fractions
The total extractable fractions of all trace elements in the sediment samples from the filling dredged sediments and the local aquifer sediments are summarized in the following and in Table III 5͒. ͑3͒ Generally, for the trace elements examined, the more recent filling dredged sediments have higher total extractable fractions than the older dredged sediments ͑Table III, Fig. 5͒. ͑4͒ With exception of Tl and Pb, all trace elements examined exhibit higher total extractable fractions in samples of the local aquifer sediments collected from deeper depths than from the shallow depths ͑Table III, Fig. 5͒.

C. ''Operationally defined solid-phase speciation'' of trace element
Having discussed the general features of the total extractable fractions of trace elements, we now discuss their ''operationally defined solid-phase speciation'' in the sediments in detail. The percentages of trace elements in the successive extractions are shown in Table IV.

Fraction 1: Exchangeable phase
In both the dredged sediments and the local aquifer sediments, exchangeable trace elements are generally found to represent a minor fraction of the total metal concentration of the sediment ͑Table IV, Fig. 5͒. The exchangeable fraction is less than 0.5% for most elements. Only Cd has an exchangeable fraction greater than 0.5%, but less than 5.1%, in both the dredged sediments and the local aquifer sediments ͑Table IV, Fig. 5͒. Sb and Tl also have more than 0.5% of the exchangeable fraction, but less than 1.3% of the exchangeable fraction in the dredged sediments.

Fraction 2: Acidic phase
Although the acid-mobilizable fraction still accounts for a small proportion of the total metal for most of the trace elements in the sediment samples, the filling dredged sediments have higher percentages in fraction 2 than the local aquifer sediments ͑Table IV, Fig. 5͒. The higher percentages  in fraction 2 are especially evident for Cd, Pb, and Zn, whose acid-mobilizable fractions account for an appreciable proportion of the total metal in the filling dredged sediments: 17.2%-40.4% Cd; 10.1%-20.4% Pb; 3.4%-18.2% Zn; ͑Table IV, Fig. 5͒. Cu, Sb, Ni, and As also have 2.5%-7.5% of acidic phase.

Fraction 3: Reducible phase
With the exception of Sb and Tl, the reducible fraction of trace elements accounts for a large proportion of the total metal concentrations in both the filling dredged sediments and local aquifer sediments ͑Table IV, Fig. 5͒. In general, reducible trace element fractions exhibit higher proportions of the total metals in the filling dredged sediments than in the local aquifer sediments ͑Table IV, Fig. 5͒.

Fraction 4: Oxidizable phase
With the exception of Sb and As, whose oxidizable fractions are low ͑less than 2.0% in most of samples, Table IV, Fig. 5͒ and Cu and Ag, whose oxidizable fraction is larger in  the filling dredged sediments ͑more than 20.0% in most of the dredged sediments, Table IV, Fig. 5͒, oxidizable fractions also account for 2.0% to ϳ20.0% of the total metals for most of the trace elements in both the filling dredged sediments and local aquifer sediments. In general, the relative mobility in terms of the percentage of the oxidizable trace elements follows the order of the recent filling dredged sediments ͑placed on site in 2002͒Ͼthe older dredged sediments ͑placed on site prior to 2002͒Ͼthe deep local aquifer sedimentsϾthe shallow local aquifer sediments ͑Table IV, Fig. 5͒.

Fraction 5: Residual phase
For most of the trace elements examined the residual fractions account for the largest proportion of the total metals in the sediments ͑Table IV, Fig. 5͒. In some cases, mainly found in the filling dredged sediments, the concentrations of Pb, Cd, Zn, and Cu in the residual phase are lower than those observed in the reducible and oxidizable phases ͑Table IV, Fig. 5͒.

D. The potential contaminants revealed by sequential extractions
To become a potential contaminant in drinking water, a particular trace element must be able to be mobilized. The mobility of trace elements in sediments mainly depends upon its solid-phase speciation and the chemical and physical processes to which it is subject. We first discuss the mobility of trace elements examined as related to their ''operationally defined solid-phase speciation.'' Then, we discuss the possible changes of in situ conditions occurring at the replacement site after disposal of the dredged sediments and the effect of these potential changes on the mobility of trace elements examined.
It is generally agreed that the mobility of trace elements decreases approximately in the order of the extraction sequence, i.e., exchangeableϾacidicϾreducibleϾoxidizableϾ residual. 1,3,10 The exchangeable phase is weakly associated with the sediments and is the easiest to mobilize by increasing ionic strength of sediment pore water under natural conditions. The acidic phase, bound to carbonate, is also relatively easy to mobilize by lowering the pH of sediment pore water. Many natural processes such as the infiltration of acid rain and the degradation of organic matter can result in slow lowering of the pH of sediment pore water. Trace elements in the reducible and oxidizable phases are thought to be more strongly bound to Fe/Mn oxides/oxyhydroxides and organic matter, respectively ͑e.g., Tessier et al. 5 ͒, and thus are not easily mobilized under steady-state, natural conditions. Trace elements in the residual phase are strongly bound, or held, within mineral crystal structure, and thus are almost impossible to be mobilized under the natural conditions. At the dredged spoil placement site, the exchangeable and acidic phases only account for a small proportion of most of the trace elements examined. Indeed, only Cd, Pb, and Zn have an appreciable extractable proportion from the acidic phase in the filling dredged sediments ͑Table IV͒. Cu, Sb, Ni, and As also have 2.9%-7.7% of exchangeable and acidic phases ͑Table IV͒. Therefore, our data suggest that, of the trace elements examined, Cd, Pb, and Zn are most likely to be mobilized into local groundwater at the replacement site. Cu, Sb, Ni, and As are relatively less mobile than Cd, Pb, and Zn, although small fractions of these elements can still be mobilized if pH changes at the replacement site. Other trace elements, such as Cr, Fe, Ag, and Tl, would not be mobilized unless the redox conditions of the dredged sediments have been changed at the replacement site.
Because the residual phase is difficult to mobilize, the overwhelming dominance of the residual fraction for these trace elements ͑Table IV, Fig. 5͒, except Pb, Cd, Zn, and Cu, indicates that trace elements are strongly bound, or held, within mineral crystal structure, and are thus not easily mobilized under the natural conditions. Based on total extractable fractions ͑Table III, Fig. 5͒, the possibility for these trace elements to be mobilized from the dredged sediments may follow the order of Cd, PbϾCu, ZnϾNi, As, FeϾAg, CrϾTl, Sb. Higher total extractable fractions for almost all trace elements examined in the dredged sediments than in the local aquifer sediment samples ͑Table III, Fig. 5͒ indicate that the trace elements examined here are more likely to be liberated from the dredged sediments than from the local aquifer sediments under the natural conditions.
The mobility of trace elements ultimately depends upon the changes of in situ conditions occurring at the replacement site. Table V lists monthly groundwater data for pH and conductivity from two upgradient monitoring wells ͑SDS2 and 3͒ and two downgradient monitoring wells ͑SW 30 and 31͒. Although we have no data for pH and conductivity for the pore water in the dredged sediments from the upper Potomac River, Hall et al. 12 reported some pH and conductivity data for upper Potomac River waters, which are close to the dredged site ͑Table V͒. Compared to conductivity for the upper Potomac River water ͑Table V͒, the local groundwaters have slightly higher conductivities. Because the exchangeable trace elements only account for a minor fraction of the total element concentration of the dredged sediments, the slight increase in ionic strength ͑indicated by the slightly higher conductivities͒ is not sufficient to release trace elements from the dredged sediments into local groundwater at the dredged spoil placement site. Therefore, we do not anticipate any trace element mobilization at this site owing to the change in ionic strength of local groundwaters. However, local groundwaters have much lower pH values than the upper Potomac River waters ͑Table V͒. Thus, the changes in pH are notable for the dredged sediments. Moreover, monthly pH data for the local groundwaters indicate that pH slightly decreases with time. Low pH in local groundwaters is a common problem due to oxidation of sulfides in the Shirley and Tabb Formation at old mining exposures. According to analysis data for the dredged sediments by Virginia Cooperative Extension Soil Testing Laboratory at Virginia Polytechnic Institute and State University, there are 2%-5% of carbonates in the dredged sediments. The changes in pH to which the dredged sediments are subject will result in some carbonate dissolution. Considering their acidic fractions, an appreciable proportion of Cd, Pb, and Zn and some Cu, Sb, Ni, and As may be mobilized by carbonate dissolution.
Because the reducible and oxidizable trace elements account for most of the total exchangeable fractions of trace elements in the dredged sediments, we suggest that oxidation of the dredged sediments may mobilize the trace elements examined in this study, as well as other components of the sediments. When the upper Potomac River sediments were dredged and dumped into the replacement site, a considerable portion was exposed to the atmosphere. As they dried the sediments formed coarse polygonal cracks as much as 0.5 m deep. Along these exposed surfaces, the dark bluish gray sediments altered to a pale gray and then to a tan ͑Fig. 6͒ as oxidation progressed throughout the new soil profile. According to analyses of sediment samples being barged to the replacement area ͑analyzed by Gascoyne Labs Inc., Baltimore, MD͒, dredged sediments contained between 50 and 150 mg/kg dry sediment of sulfate, up to 200 mg/kg dry sediment of sulfide, and up to 2% total organic carbon. Pore water total ammonia ͑i.e., NH 3 ϩNH 4 ϩ ) in the Potomac River sediments is ϳ27.4 mg N/L, as reported by Schlekat et al. 13 from the same location that the dredged sediments were excavated. When ammonia, organic matter, and iron sulfide ͑e.g., FeS 2 ) are oxidized in the dredged sediments at the replacement site, the following geochemical reactions may be expected: These potential reactions would precipitate iron oxides and release hydrogen ions, NO 3 ϩNO 2 , dissolved inorganic carbon ͑DIC͒, and sulfate into local groundwaters. In addition, the incomplete degradation of organic matter ͑large molecu-lar͒ in the dredged sediments may also produce some soluble small molecular organic matter. However, the acidity released by these oxidation reactions would be offset by carbonate buffering reactions. Therefore, after deposition of the dredged sediments at the study site, we expect some levels of increase in NO 3 ϩNO 2 , DIC, DOC, and sulfate concentrations in local groundwaters, but little if any change of pH.
Our monitoring data for local groundwater verify that these potential geochemical reactions have occurred at the study site ͑Tables V and VI͒. Table V indicates that pH only slightly decreases in the monitoring groundwaters with time. Table VI shows that, compared to the baseline analyses, NO 3 ϩNO 2 , and TOC generally increase. Total iron shows higher concentrations at the first post-baseline monitoring analyses but thereafter, iron generally decreases with time in local groundwaters. The oxidation of ammonia, organic matter, and iron sulfides may release the oxidizable trace elements ͑fraction 4 in sequential extractions͒ into local groundwaters. However, considering that iron, manganese, and aluminum oxides exhibit strong adsorption affinity because of their reactivity and large specific surface area, 14 we do not anticipate these reactions would result in any significant water quality risk. Instead, the trace elements released by the proposed mechanism are subsequently absorbed by newly produced iron, manganese, and aluminum oxides and become immobile as long as conditions remain oxidic.
Besides their mobility, the environmental significance of these trace elements is also controlled by their absolute concentrations in the dredged sediments. Figure 5   total concentrations of trace elements and the concentrations of each extractable fraction in the dredged sediments to those in the local aquifer sediments. Pb, Cd, Zn, Ag, and Cu have higher total concentrations and higher concentrations of extractable phases in the dredged sediments than in the local aquifer sediments ͑Fig. 3͒. By comparison, As, Cr, Ni, and Sb have similar total concentrations in both the dredged sediments and the local aquifer sediments, but their concentrations in the extractable phase are higher in the dredged sediments than in the local aquifer sediments.
The ''operationally defined solid-phase speciation'' of the trace elements examined, their absolute concentrations in the dredged sediments, and the changes in in situ conditions indicate that some trace elements, especially Cd, Pb, and Zn, may be released from the dredges sediments. However, because the trace elements released by carbonate dissolution and the oxidation ͑e.g., organic matter degradation, iron sulfide oxidation, and ammonia oxidation͒ are subsequently immobilized by sorption to iron, manganese, and aluminum oxides, these trace elements would not be released into local groundwaters. Therefore, no potential contaminants to local groundwater are expected as revealed by sequential extractions. Our sequential extraction results are generally consistent with our groundwater monitoring results ͑Table VI͒. On 8 May, 2000 ͑prior to placement of the dredged sediments͒, local groundwater samples were collected from wells around the L-shape replacement site. The analyses of these samples represent the baseline groundwater chemistry at the replacement site. After the dredged sediments were filled into the site, local groundwater samples were collected on different dates and analyzed for the same trace elements ͑Table VI͒. The groundwater monitoring data do not clearly indicate that any trace elements were released into local groundwaters from the dredged sediments, because the concentrations of monitoring elements are very low and inconsistent with time. Compared to baseline analyses, only a slight increase was observed in concentrations for some elements in some local groundwater samples. Almost all the concentrations of monitoring elements are below USEPA maximum contaminant levels ͑MCLs͒ for drinking water. Only one monitoring well ͑SDS2͒ had a high Pb concentration of 0.048 mg/L at the first, post-baseline monitoring analyses ͑4/20/2002͒. But later analyses at SDS2 indicate very low levels of Pb in groundwater from the well ͑Table VI͒.

V. CONCLUSIONS
Our sequential extraction results show that the dredged sediments have higher total extractable fractions for almost all trace elements examined and relatively high concentrations for some trace elements, compared to the local aquifer sediments, which indicates that the trace elements are more likely to be mobilized from the dredged sediments than from the local aquifer sediments. However, the overwhelming dominance of the residual fraction for these trace elements, except Pb, Cd, Zn, and Cu, indicates that trace elements are not easily mobilized under the natural conditions. Moreover, under an oxidizing condition, the trace elements released from the dredged sediments by carbonate dissolution and the oxidation ͑i.e., organic matter degradation, iron sulfide, and ammonia oxidation͒ are subsequently absorbed by newly produced iron, manganese, and aluminum oxides and become immobile. No potential contaminants to local groundwater are expected to be released from the dredged sediments.