# Sulfur Speciation in the Surface Sediments of Lakes from Different Regions, China: Characterization by S K-Edge XANES Spectroscopy

Authors: Wang Jingfu; Chen Jingan; Dai Zhihui; Yang Haiquan; Ma Chenyan
Journal: Journal of Chemistry
 (2016)

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## Abstract

X-ray absorption near edge structure (XANES) spectroscopy affords the opportunity to determine redox status for element S in the aquatic ecosystems. However, there have been relatively few studies of S XANES spectroscopy in the terrestrial aquatic ecosystems. In this study, XANES technology was used to examine changes in S speciation in the sediments collected from Taihu Lake, Qinghai Lake, Dianchi Lake, Caohai Lake, and Hongfeng Lake located in distinct geological background areas of China. The results showed that sedimentary S in Qinghai Lake has a high proportion of sulfate averaged 88.9% due to physical weathering of watershed rocks, while deposited S in Taihu Lake has a high fraction of intermediate S (36.5%), which may be the response of the agricultural nonpoint source pollution in drainage basin. The three lakes located in Southwest China have similar composition characteristics of S species, indicating similar S sources including chemical weathering of carbonate and atmospheric deposition. 60–90% of S compounds in the surface sediments were in the form of sulfate and FeS. In deeper layers, the ratio of FeS2 and the intermediate S significantly increased, suggesting rapid processes of sulfate reduction and sulfide reoxidation with the increasing depths.


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## Body

## 1. Introduction

Sediment is an important repository and sink for sulfur (S) [1]. The biogeochemical cycles of S in sediments were highly complex, because the aquatic ecosystems have anaerobic zones which strongly affect the chemical forms of S [2, 3]. In the previous studies, the wet-chemical speciation method was generally used to analyze the S speciation in sediments and reveal its geochemical processes in the aquatic ecosystems [4–9]. In fact and often neglected, S in natural samples existed in a large variety of organic and inorganic forms with different electronic oxidation states, ranging from −2 (inorganic sulfide) to +6 (sulfate) [10]. This made traditional wet-chemical S speciation complicated [11]. Therefore, sensitive analytical methods are needed to analyze and monitor many functions and transformations of S species in biochemical reactions and in our environment [12]. X-ray absorption near edge structure (XANES) spectroscopy affords the opportunity to determine redox status and coordination environment for a wide variety of elements, including sulfur, carbon, and nitrogen within these sediments [13]. The method has become especially attractive for the speciation of S in sediments and other environmental samples, most prominently at the S K-edge [10, 12, 14, 15].In previous investigations, XANES spectroscopy has been applied to the analysis of the chemical form and oxidation state of S in soil and marine sediments [10, 12, 16], providing information about the deposition and diagenesis of organic matter and S mineralogy. However, there have been relatively few studies of S XANES spectroscopy in sediments of the terrestrial aquatic ecosystems [17]. Particularly, comparative studies of the oxidation states of sedimentary S in different types of lakes from distinct geological background areas are scarce. In this study, we used the K-edge XANES to determine S speciation in the sediments collected from Taihu Lake (Eastern China), Qinghai Lake (Western China), Hongfeng Lake (Southwest China), Caohai Lake (Southwest China), and Dianchi Lake (Southwest China). The object is to understand the S speciation and its transformation in sediments of the terrestrial aquatic ecosystems.


## 2. Materials and Methods

### 2.1. Area Description

In this study, five lakes were chosen based on economic and geographic status in the Yangtze River region, Southwest Plateau, and Qinghai-Tibet Plateau, China (Figure1). Geographic and limnological features for the five selected lakes are shown in Table 1 [18, 22]. Taihu Lake is the third largest freshwater lake in China located at the downstream of the Changjiang River. More than 200 brooks, canals, and rivers discharge industrial wastewater, mostly from nearby cities, into the lake. Many effluents contain pesticides, toxic chemicals, or heavy metals. Southwest Plateau China is the largest karst area in China. According to previous lake chemistry surveys [23], one slightly polluted lake (Caohai Lake) and two heavily polluted lakes (Dianchi and Hongfeng Lakes) were selected in this area. Qinghai Lake, a closed-basin lake, is the largest inland saline lake in China. The amount of evaporation (~1400 mm/year) is in excess of the mean annual precipitation (~400 mm/year), resulting in the development of a saline lake.Table 1
Geographic and limnological features of the studied lakes [18–21].
Parameters
Eastern China
Southwestern China
Western China
Taihu Lake
Hongfeng Lake
Dianchi Lake
Caohai Lake
Qinghai Lake
Positions
30°05′–32°08′N,119°08′–121°55′E
26°25′–34′N,106°20′–28′E
24°40′–25°02′N,102°36′–°47′E
26°49′–53′N,104°12′–18′E
36°32′–37°15′N,99°36′–100°47′E
Surface area (km2)
2338
56
306
20
4583
Elevation (m)
5
1235
1886
2171
3196
Maximum depth (m)
2.6
45.0
8.0
2.5
32.8
Water
pH
8.36
8.40
7.37
8.78
9.35
DO (mg/L)
10.1
8.8
8.9
9.4
ND
Salinity (g/L)
<1.0
<1.0
<1.0
<1.0
12.5
Sulfate (mg/L)
100
80
60
40
2500
Sediment
Organic matter (%)
6.5
5.4
6.5
ND
2.4
TN (%)
ND
0.31
0.33
1.38
0.50
TP (%)
0.08
0.16
0.15
0.07
ND
Fe (%)
2.65
5.98
ND
ND
2.50
Climate type
Warm, humid
Warm, semihumid
Warm, semihumid
Warm, semihumid
Cool, semiarid
Deposition rate (cm/yr)
ND
0.16
0.20
0.25
0.10Figure 1
Location of the studied lakes.


### 2.2. Sampling Procedures

Sediment core samples were obtained from the five lakes in September 2013, nearly in the centre of the lakes. A plastic static gravity corer with 30 cm length and 6 cm diameter Plexiglas cylinder tube was employed to obtain the sediment cores. The core samples were sliced with intervals of 2 cm, with the exception of the core from Qinghai Lake sectioned at 1 cm intervals. Sediments were handled under protective nitrogen atmospheres (purity 99.9%, Guiyang Shenjian Gas Co., Ltd.). All samples were put in sealed plastic bag and immediately transferred to laboratory in iceboxes (<4°C) and freeze-dried. After that, the samples were frozen with liquid nitrogen. Before XANES analysis, dry samples were ground and sieved with a standard 100-mesh sieve.


### 2.3. Sulfur K-Edge XANES

The sulfur K-edge XANES spectra were recorded at 4B7A beamline (medium X-ray beamline 2100–6000 eV) using synchrotron radiation from Beijing Synchrotron Radiation Facility, the Institute of High Energy Physics, the Chinese Academy of Sciences. The samples were pressed into thin films before analysis. The storage ring was operated at the energy of 2.5 GeV with Si (111) double crystals. Spectra were scanned at step widths of 0.3 eV in the region between 2420 and 2520 eV, with fluorescence mode using a fluorescent ion chamber Si (Li) detector (PGT LS30135). Additional filters were placed between the sample and the detector to reduce the fluorescence signal derived from Si in the samples.Fe monosulfide (FeS), pyrite (FeS2), R-SH, RSOR′, Na2SO3, NaRSO3, and Na2SO4 were chosen as the standard compounds. Electronic oxidation states, white-line energies, and intensities of reference S compounds were shown in Table 2. The X-ray energy was calibrated with reference to the spectrum of the highest resonance energy peak of Na2SO4 at 2480.4 eV. For all edge-normalized spectra, the contribution of different S species to total S was calculated using the software package ATHENA (Ravel and Newville, 2005). Linear combination fitting (LCF) was carried out in the energy range 2466–2487 eV using the ATHENA [10].Table 2
Electronic oxidation states, white-line energies, and intensities of reference S compounds.
Compound
Electronic oxidation state
White-line energy (eV)
White-line intensity
FeS
−2
2472.2
1.17
FeS2
−1
2472.8
1.33
RSH
+0.5
2473.4
1.58
RSOR′
+2
2476.2
1.81
Na2SO3
+3.68
2478.4
2.03
NaRSO3
+5
2481.2
2.33
Na2SO4
+6
2482.6
2.54


### 2.4. Analysis of the Total Sulfur

Total S contents were measured with an elemental analyzer (vario MACRO cube, Elementar, Germany), with an experimental error of 0.5%. Two certified reference materials (RTS-2 and KZK-1, State Key Laboratory of Environmental Geochemistry, Institute of Geochemistry, CAS) were used as calibration standard. Concentrations of total S in sediments of the five studied lakes were shown in Table3.Table 3
Concentrations of total S in sediments of Taihu Lake, Hongfeng Lake, Dianchi Lake, Caohai Lake, and Qinghai Lake.
Depth cm
Taihu Lake
Hongfeng Lake
Dianchi Lake
Caohai Lake
Qinghai Lake
0–2
0.170
0.695
0.662
1.227
0.393
3-4
0.066
0.657
0.509
1.428
0.375
5-6
ND
0.795
0.622
1.659
0.384
7-8
ND
0. 810
0.469
1.495
0.523
9-10
ND
1.175
0.911
1.221
0.417
11-12
ND
0.926
0.817
0.850
ND
13-14
ND
0.618
0.483
1.168
ND
15-16
ND
ND
0.527
0.388
ND
17-18
ND
ND
0.425
0.559
ND
19-20
ND
ND
0.326
0.512
ND
21-22
ND
ND
0.381
0.346
ND
23-24
ND
ND
0.136
0.425
ND


## 2.1. Area Description

In this study, five lakes were chosen based on economic and geographic status in the Yangtze River region, Southwest Plateau, and Qinghai-Tibet Plateau, China (Figure1). Geographic and limnological features for the five selected lakes are shown in Table 1 [18, 22]. Taihu Lake is the third largest freshwater lake in China located at the downstream of the Changjiang River. More than 200 brooks, canals, and rivers discharge industrial wastewater, mostly from nearby cities, into the lake. Many effluents contain pesticides, toxic chemicals, or heavy metals. Southwest Plateau China is the largest karst area in China. According to previous lake chemistry surveys [23], one slightly polluted lake (Caohai Lake) and two heavily polluted lakes (Dianchi and Hongfeng Lakes) were selected in this area. Qinghai Lake, a closed-basin lake, is the largest inland saline lake in China. The amount of evaporation (~1400 mm/year) is in excess of the mean annual precipitation (~400 mm/year), resulting in the development of a saline lake.Table 1
Geographic and limnological features of the studied lakes [18–21].
Parameters
Eastern China
Southwestern China
Western China
Taihu Lake
Hongfeng Lake
Dianchi Lake
Caohai Lake
Qinghai Lake
Positions
30°05′–32°08′N,119°08′–121°55′E
26°25′–34′N,106°20′–28′E
24°40′–25°02′N,102°36′–°47′E
26°49′–53′N,104°12′–18′E
36°32′–37°15′N,99°36′–100°47′E
Surface area (km2)
2338
56
306
20
4583
Elevation (m)
5
1235
1886
2171
3196
Maximum depth (m)
2.6
45.0
8.0
2.5
32.8
Water
pH
8.36
8.40
7.37
8.78
9.35
DO (mg/L)
10.1
8.8
8.9
9.4
ND
Salinity (g/L)
<1.0
<1.0
<1.0
<1.0
12.5
Sulfate (mg/L)
100
80
60
40
2500
Sediment
Organic matter (%)
6.5
5.4
6.5
ND
2.4
TN (%)
ND
0.31
0.33
1.38
0.50
TP (%)
0.08
0.16
0.15
0.07
ND
Fe (%)
2.65
5.98
ND
ND
2.50
Climate type
Warm, humid
Warm, semihumid
Warm, semihumid
Warm, semihumid
Cool, semiarid
Deposition rate (cm/yr)
ND
0.16
0.20
0.25
0.10Figure 1
Location of the studied lakes.


## 2.2. Sampling Procedures

Sediment core samples were obtained from the five lakes in September 2013, nearly in the centre of the lakes. A plastic static gravity corer with 30 cm length and 6 cm diameter Plexiglas cylinder tube was employed to obtain the sediment cores. The core samples were sliced with intervals of 2 cm, with the exception of the core from Qinghai Lake sectioned at 1 cm intervals. Sediments were handled under protective nitrogen atmospheres (purity 99.9%, Guiyang Shenjian Gas Co., Ltd.). All samples were put in sealed plastic bag and immediately transferred to laboratory in iceboxes (<4°C) and freeze-dried. After that, the samples were frozen with liquid nitrogen. Before XANES analysis, dry samples were ground and sieved with a standard 100-mesh sieve.


## 2.3. Sulfur K-Edge XANES

The sulfur K-edge XANES spectra were recorded at 4B7A beamline (medium X-ray beamline 2100–6000 eV) using synchrotron radiation from Beijing Synchrotron Radiation Facility, the Institute of High Energy Physics, the Chinese Academy of Sciences. The samples were pressed into thin films before analysis. The storage ring was operated at the energy of 2.5 GeV with Si (111) double crystals. Spectra were scanned at step widths of 0.3 eV in the region between 2420 and 2520 eV, with fluorescence mode using a fluorescent ion chamber Si (Li) detector (PGT LS30135). Additional filters were placed between the sample and the detector to reduce the fluorescence signal derived from Si in the samples.Fe monosulfide (FeS), pyrite (FeS2), R-SH, RSOR′, Na2SO3, NaRSO3, and Na2SO4 were chosen as the standard compounds. Electronic oxidation states, white-line energies, and intensities of reference S compounds were shown in Table 2. The X-ray energy was calibrated with reference to the spectrum of the highest resonance energy peak of Na2SO4 at 2480.4 eV. For all edge-normalized spectra, the contribution of different S species to total S was calculated using the software package ATHENA (Ravel and Newville, 2005). Linear combination fitting (LCF) was carried out in the energy range 2466–2487 eV using the ATHENA [10].Table 2
Electronic oxidation states, white-line energies, and intensities of reference S compounds.
Compound
Electronic oxidation state
White-line energy (eV)
White-line intensity
FeS
−2
2472.2
1.17
FeS2
−1
2472.8
1.33
RSH
+0.5
2473.4
1.58
RSOR′
+2
2476.2
1.81
Na2SO3
+3.68
2478.4
2.03
NaRSO3
+5
2481.2
2.33
Na2SO4
+6
2482.6
2.54


## 2.4. Analysis of the Total Sulfur

Total S contents were measured with an elemental analyzer (vario MACRO cube, Elementar, Germany), with an experimental error of 0.5%. Two certified reference materials (RTS-2 and KZK-1, State Key Laboratory of Environmental Geochemistry, Institute of Geochemistry, CAS) were used as calibration standard. Concentrations of total S in sediments of the five studied lakes were shown in Table3.Table 3
Concentrations of total S in sediments of Taihu Lake, Hongfeng Lake, Dianchi Lake, Caohai Lake, and Qinghai Lake.
Depth cm
Taihu Lake
Hongfeng Lake
Dianchi Lake
Caohai Lake
Qinghai Lake
0–2
0.170
0.695
0.662
1.227
0.393
3-4
0.066
0.657
0.509
1.428
0.375
5-6
ND
0.795
0.622
1.659
0.384
7-8
ND
0. 810
0.469
1.495
0.523
9-10
ND
1.175
0.911
1.221
0.417
11-12
ND
0.926
0.817
0.850
ND
13-14
ND
0.618
0.483
1.168
ND
15-16
ND
ND
0.527
0.388
ND
17-18
ND
ND
0.425
0.559
ND
19-20
ND
ND
0.326
0.512
ND
21-22
ND
ND
0.381
0.346
ND
23-24
ND
ND
0.136
0.425
ND


## 3. Results and Discussion

### 3.1. S Species in Lake Sediments

Our sediment samples each contain both oxidized and reduced sulfur species as shown in Figure2. Two major absorption bands were observed in these K-edge XANE spectra: one near 2472 eV region for the reduced S compounds (e.g., FeS and FeS2) and another near 2483 eV region for oxidized S species (e.g., S
O
4
2
-), suggesting that sulfate and FeS were the most important component of elemental S in all lakes. However, in different lakes, the compositions of the oxidation state of S in sediments were still very different. Figure 2 showed that the overall absorption intensity of S was the lowest in the sediment of Taihu Lake, indicating the lowest concentration of S component in the sediments. Further, organic state S obviously occupied a relatively high proportion of in the oxidation state of S in sediments of Taihu Lake, compared with other lakes. In the three lakes located in the Southwestern China, that is, Dianchi Lake, Caohai Lake, and Hongfeng Lake, the oxidation state of the sedimentary S presented similar composition characteristics. The concentrations of sulfate, FeS, and S
2
O
3
2
- were high of the top three, and the contents of other S forms were relatively low. In the sediments of Qinghai Lake, the oxidation states of S were mainly sulfate, FeS, and FeS2 and almost no organic sulfur. Moreover, FeS2 was found in the surface sediments of Taihu Lake and Qinghai Lake and did not exist in the surface sediments of the three lakes located in Southwestern China.Figure 2
Vertical variations of oxidation states of different S compounds in sediment profiles of Taihu Lake, Qinghai Lake, Dianchi Lake, Caohai Lake, and Hongfeng Lake, China.
(a)
Taihu Lake
(b)
Qinghai Lake
(c)
Dianchi Lake
(d)
Caohai Lake
(e)
Hongfeng LakeFigure2 also demonstrated that the absorption intensity of S significantly reduced with the increasing depths in all sediment profiles, revealing a reduction of the concentration of S in deeper layers. Figure 3 showed the vertical variation of the oxidation states of S in the sediment profiles, suggesting that S in sediments changed from the oxidation state to the reduced state with the increasing depths. Oxidation states of S in Dianchi Lake showed that sulfate and FeS were major forms in the top 10 cm sediment, which were considered to be the most stable in all oxidation states of S in sediments. In the deeper layers, the ratio of FeS2 and organic S forms in the total S was significantly increased, suggesting that sulfate was chemically or biologically reduced in the deep part of the sediments. S in sediments of Caohai and Hongfeng Lake showed similar composition and change characteristics with that in Dianchi Lake. In Qinghai Lake, the proportion of the FeS and FeS2 slightly increased in 0–6 cm sediment layer then reduced in the depths of 6–10 cm. Accordingly, the proportion of sulfate reduced first and then increased, suggesting an occurrence of S reduction and reoxidation processes.Figure 3
Mass percentages of sulfur in FeS, FeS2, R-SH, RSOR′, S
O
3
2
-, R
S
O
3
-, and S
O
4
2
- as calculated by Linear Combination Fitting on S K-Edge XANES spectra.In the large-scale, the five lakes in this study were located in three different natural regions, which have the varied climatic, economic, and geological features. Qinghai Lake basin was an arid climate area in the Northwestern China, where it usually received low inputs of mean annual precipitation and had high potential evapotranspiration [24]. Acid deposition was mainly formed from SO2 emitted to the atmosphere, largely because of fossil-fuel combustion [25]. Qinghai Lake area was essentially unaffected by acid deposition, indicating that atmospheric S has a relatively low concentration [26]. Thus S in sediments of this lake mainly derived from physical weathering of watershed rocks. Taihu Lake was located in the economically developed eastern coastal areas of China. As shown in Figure 3, largely organic S, originated from industry and agriculture in the lake basin, occupied a high proportion in total S in the sediments. S in sediments of Taihu Lake, on the one hand, reflected the composition of the soil S of the lake basin and, on the other hand, was affected by human activities such as industry, agriculture, and atmospheric deposition. For the three lakes located in the largest karst region in Southwestern China, that is, Dianchi Lake, Caohai Lake, and Hongfeng Lake, chemical weathering of carbonate was the most important source of S. The previous studies demonstrated that considerable emissions of S compounds mainly occurred in southern and Southwestern China due to subsequent consumption of coal and oil, which increased rapidly since the 1970s [26]. Dry and wet deposition of atmospheric S caused by the coal combustion may be another important source for these three lakes.Furthermore, the eutrophic status of lakes may impact on the S deposition in the lake environment. In our study, most of the lakes have changed from oligotrophy to of meso- or eutrophic conditions during the past decades because of nutrient loading from wastewater and fertilizers, especially Taihu Lake and Dianchi Lake [19, 20]. Only Qinghai Lake was still in the oligotrophy condition. Holmer and Storkholm [27] indicated that deposition of S was generally higher in eutrophic than in oligotrophic lakes because of a number of factors: a higher rate of sulfate reduction, enhanced sedimentation of organic S, and less reoxidation as a result of reduced penetration of oxygen into the sediments, a lack of faunal activity, and rooted macrophytes. Our survey data as shown in Figure 3 showed that the proportion of S2− and S
2
2
- in the sedimentary S in the eutrophic lakes, such as Taihu Lake, was indeed significantly higher than that in Qinghai Lake, which was consistent with the results of previous studies [27]. Currently, there is, however, still a general lack of understanding of the interactions between S cycling and eutrophication. One example is the interaction between S cycling and benthic fauna and rooted macrophytes, as they may be significantly impacted by eutrophication [27]. However, we believed that the impacts of S bacteria were more reasonable. S reduced from varied oxidation states into sulfides through the complex biochemical processes was generally assumed to be the dominant pathway for the permanent removal of S in the sediment [5]. Reduction of S in sediments is mainly dominated by SRB, while the eutrophic lakes generally have a high SRB in sediment layers; thus the proportion of most reduced S (oxidation state < 0) in the sediment of eutrophic lake is higher than in oligotrophic lakes. In particular, Hongfeng Lake was a seasonally stratified deep-water lake. After destratification and during winter, the anoxic hypolimnion becomes mixed with overlying oxic water, which enhances oxygen penetration into the sediments. This leads to an increased oxidation of reduced S, followed by a higher sulfate concentration [28].


### 3.2. Composition Ratio of Different S Compounds in Sediment Profiles

The composition ratios of different S species in sediment cores were shown in Figure3. XANES fitting procedures revealed that 60–90% of the total S compounds near the surface (0–10 cm depth) of the lake sediment samples were in the form of sulfate and FeS. FeS2 and the S species with intermediate oxidation states between 0 and +6 accounted for a high proportion of total S in the deeper layers.Figure3 showed that there were wide variations in the fractions of the sedimentary S species in different lakes. In the surface sediment of Taihu Lake, sulfate, FeS2, and FeS accounted for 38.9%, 12.6%, and 11.0% of the total S, while the S species with intermediate oxidation states between 0 and +6 accounted for 36.5%. In Dianchi Lake, the composition ratio of FeS declined from 53.5% in surface to 30.2% in bottom with the increasing depths in the sediments, and the fraction of sulfate declined from 44.3% to 11.3%. FeS2 was found below the 10 cm depth, and its relative proportion rapidly increased from 5.4% to 30.2% in the deep layers. The fraction of S species with intermediate oxidation states between 0 and +6 ranged from 2.3% to 25.6% in the 10–24 cm sediments. The composition of sedimentary S species in Caohai Lake and Hongfeng Lake was similar to that in Dianchi Lake.In particular, sediments from Qinghai Lake contained a very high proportion of sulfate, with an average value of 88.9%. The proportion of the sulfate slightly decreased from 94.3% to 83.5% in the depths that ranged from 0 to 6 cm then slightly increased from 83.5% to 88.3% in the 6–10 cm sediments. The contribution of FeS and FeS2 was very low, while the FeS + FeS2 content varied between 4.7 and 15.6% in all samples. There was no indication of other sulfur species with intermediate oxidation states between 0 and +6 in the core profile of Qinghai Lake.The combination of S speciation helps to constrain the depositional environment present in these sediments. Similar percentages of most reduced S (oxidation state < 0), intermediated S (oxidation state from 0 to +5), and most oxidized S (oxidation state +6) in the sediments of Dianchi Lake and Qinghai Lake were calculated by LCF (Figure4). Our results indicated that the ratio of most oxidized S reduced in the surface (0–8 cm) sediment of Dianchi Lake; correspondingly, the proportion of most reduced S increased, implying the transformation from sulfate to sulfide iron through a strong activity of SRB in the top layer. Sulfate reduction was usually not limited by the sulfate in surface layers, as the concentration exceeds K
m for SRB [29]. But limitation may occur deeper in the sediment, because sulfate usually penetrates only to <10 cm into freshwater sediments due to its low concentration [27]. As shown in Figure 4(a), at a depth of 8–12 cm layer, the proportion of most reduced S rapidly declined; correspondingly, the proportion of most oxidized S increased, revealing a limitation of sulfate reduction and an occurrence of reoxidation of reduced S in the anaerobic condition. Similar phenomenon was also found in the sediment profile of Qinghai Lake (Figure 4(b)). In the deeper (>12 cm) layers, intermediated S gradually occupied a high ratio in the total sedimentary S, indicating that the SRB was significantly reduced in those layers, because if any, the bacteria mediated disproportionation reaction will lead to the transition from the unstable intermediate S to the more stable reduced S and sulfate. The intermediated S in deep sediments found in our study was likely to be the major product of sulfide reoxidation in the absence of microorganisms and iron ions.Figure 4
Mass percentages of most reduced S (oxidation state < 0), intermediated S (oxidation state from 0 to +5), and most oxidized S (oxidation state +6) in the sediments from (a) Dianchi Lake and (b) Qinghai Lake.
(a)
(b)It should be noted that the intermediate S was stable below 15 cm depth in sediments from Dianchi Lake, as shown in Figure4(a). Experiments with 35S labeled S
2
O
3
2
- demonstrated that S
2
O
3
2
- was disproportionated throughout all redox zones in the upper 10 cm, where disproportionating bacteria were abundant in the sediments [30]. The intermediate S was not commonly found in surface layer sediments because it reacted fast with Fe3+ and was further oxidized to sulfate. Although Fe3+ oxidizes pyrite rapidly in the sediment surface, iron-oxidizing bacteria can increase the oxidation rate by several orders of magnitude [31], supplying Fe3+ for pyrite oxidation. Then in the deep layers where Fe3+ was not available, the intermediate S might be the major end product of pyrite reoxidation [6]. Due to the absence of microorganisms and iron ions, the intermediate S can keep stable in deep sediments, which was consistent with the results observed in our studies lakes.


## 3.1. S Species in Lake Sediments

Our sediment samples each contain both oxidized and reduced sulfur species as shown in Figure2. Two major absorption bands were observed in these K-edge XANE spectra: one near 2472 eV region for the reduced S compounds (e.g., FeS and FeS2) and another near 2483 eV region for oxidized S species (e.g., S
O
4
2
-), suggesting that sulfate and FeS were the most important component of elemental S in all lakes. However, in different lakes, the compositions of the oxidation state of S in sediments were still very different. Figure 2 showed that the overall absorption intensity of S was the lowest in the sediment of Taihu Lake, indicating the lowest concentration of S component in the sediments. Further, organic state S obviously occupied a relatively high proportion of in the oxidation state of S in sediments of Taihu Lake, compared with other lakes. In the three lakes located in the Southwestern China, that is, Dianchi Lake, Caohai Lake, and Hongfeng Lake, the oxidation state of the sedimentary S presented similar composition characteristics. The concentrations of sulfate, FeS, and S
2
O
3
2
- were high of the top three, and the contents of other S forms were relatively low. In the sediments of Qinghai Lake, the oxidation states of S were mainly sulfate, FeS, and FeS2 and almost no organic sulfur. Moreover, FeS2 was found in the surface sediments of Taihu Lake and Qinghai Lake and did not exist in the surface sediments of the three lakes located in Southwestern China.Figure 2
Vertical variations of oxidation states of different S compounds in sediment profiles of Taihu Lake, Qinghai Lake, Dianchi Lake, Caohai Lake, and Hongfeng Lake, China.
(a)
Taihu Lake
(b)
Qinghai Lake
(c)
Dianchi Lake
(d)
Caohai Lake
(e)
Hongfeng LakeFigure2 also demonstrated that the absorption intensity of S significantly reduced with the increasing depths in all sediment profiles, revealing a reduction of the concentration of S in deeper layers. Figure 3 showed the vertical variation of the oxidation states of S in the sediment profiles, suggesting that S in sediments changed from the oxidation state to the reduced state with the increasing depths. Oxidation states of S in Dianchi Lake showed that sulfate and FeS were major forms in the top 10 cm sediment, which were considered to be the most stable in all oxidation states of S in sediments. In the deeper layers, the ratio of FeS2 and organic S forms in the total S was significantly increased, suggesting that sulfate was chemically or biologically reduced in the deep part of the sediments. S in sediments of Caohai and Hongfeng Lake showed similar composition and change characteristics with that in Dianchi Lake. In Qinghai Lake, the proportion of the FeS and FeS2 slightly increased in 0–6 cm sediment layer then reduced in the depths of 6–10 cm. Accordingly, the proportion of sulfate reduced first and then increased, suggesting an occurrence of S reduction and reoxidation processes.Figure 3
Mass percentages of sulfur in FeS, FeS2, R-SH, RSOR′, S
O
3
2
-, R
S
O
3
-, and S
O
4
2
- as calculated by Linear Combination Fitting on S K-Edge XANES spectra.In the large-scale, the five lakes in this study were located in three different natural regions, which have the varied climatic, economic, and geological features. Qinghai Lake basin was an arid climate area in the Northwestern China, where it usually received low inputs of mean annual precipitation and had high potential evapotranspiration [24]. Acid deposition was mainly formed from SO2 emitted to the atmosphere, largely because of fossil-fuel combustion [25]. Qinghai Lake area was essentially unaffected by acid deposition, indicating that atmospheric S has a relatively low concentration [26]. Thus S in sediments of this lake mainly derived from physical weathering of watershed rocks. Taihu Lake was located in the economically developed eastern coastal areas of China. As shown in Figure 3, largely organic S, originated from industry and agriculture in the lake basin, occupied a high proportion in total S in the sediments. S in sediments of Taihu Lake, on the one hand, reflected the composition of the soil S of the lake basin and, on the other hand, was affected by human activities such as industry, agriculture, and atmospheric deposition. For the three lakes located in the largest karst region in Southwestern China, that is, Dianchi Lake, Caohai Lake, and Hongfeng Lake, chemical weathering of carbonate was the most important source of S. The previous studies demonstrated that considerable emissions of S compounds mainly occurred in southern and Southwestern China due to subsequent consumption of coal and oil, which increased rapidly since the 1970s [26]. Dry and wet deposition of atmospheric S caused by the coal combustion may be another important source for these three lakes.Furthermore, the eutrophic status of lakes may impact on the S deposition in the lake environment. In our study, most of the lakes have changed from oligotrophy to of meso- or eutrophic conditions during the past decades because of nutrient loading from wastewater and fertilizers, especially Taihu Lake and Dianchi Lake [19, 20]. Only Qinghai Lake was still in the oligotrophy condition. Holmer and Storkholm [27] indicated that deposition of S was generally higher in eutrophic than in oligotrophic lakes because of a number of factors: a higher rate of sulfate reduction, enhanced sedimentation of organic S, and less reoxidation as a result of reduced penetration of oxygen into the sediments, a lack of faunal activity, and rooted macrophytes. Our survey data as shown in Figure 3 showed that the proportion of S2− and S
2
2
- in the sedimentary S in the eutrophic lakes, such as Taihu Lake, was indeed significantly higher than that in Qinghai Lake, which was consistent with the results of previous studies [27]. Currently, there is, however, still a general lack of understanding of the interactions between S cycling and eutrophication. One example is the interaction between S cycling and benthic fauna and rooted macrophytes, as they may be significantly impacted by eutrophication [27]. However, we believed that the impacts of S bacteria were more reasonable. S reduced from varied oxidation states into sulfides through the complex biochemical processes was generally assumed to be the dominant pathway for the permanent removal of S in the sediment [5]. Reduction of S in sediments is mainly dominated by SRB, while the eutrophic lakes generally have a high SRB in sediment layers; thus the proportion of most reduced S (oxidation state < 0) in the sediment of eutrophic lake is higher than in oligotrophic lakes. In particular, Hongfeng Lake was a seasonally stratified deep-water lake. After destratification and during winter, the anoxic hypolimnion becomes mixed with overlying oxic water, which enhances oxygen penetration into the sediments. This leads to an increased oxidation of reduced S, followed by a higher sulfate concentration [28].


## 3.2. Composition Ratio of Different S Compounds in Sediment Profiles

The composition ratios of different S species in sediment cores were shown in Figure3. XANES fitting procedures revealed that 60–90% of the total S compounds near the surface (0–10 cm depth) of the lake sediment samples were in the form of sulfate and FeS. FeS2 and the S species with intermediate oxidation states between 0 and +6 accounted for a high proportion of total S in the deeper layers.Figure3 showed that there were wide variations in the fractions of the sedimentary S species in different lakes. In the surface sediment of Taihu Lake, sulfate, FeS2, and FeS accounted for 38.9%, 12.6%, and 11.0% of the total S, while the S species with intermediate oxidation states between 0 and +6 accounted for 36.5%. In Dianchi Lake, the composition ratio of FeS declined from 53.5% in surface to 30.2% in bottom with the increasing depths in the sediments, and the fraction of sulfate declined from 44.3% to 11.3%. FeS2 was found below the 10 cm depth, and its relative proportion rapidly increased from 5.4% to 30.2% in the deep layers. The fraction of S species with intermediate oxidation states between 0 and +6 ranged from 2.3% to 25.6% in the 10–24 cm sediments. The composition of sedimentary S species in Caohai Lake and Hongfeng Lake was similar to that in Dianchi Lake.In particular, sediments from Qinghai Lake contained a very high proportion of sulfate, with an average value of 88.9%. The proportion of the sulfate slightly decreased from 94.3% to 83.5% in the depths that ranged from 0 to 6 cm then slightly increased from 83.5% to 88.3% in the 6–10 cm sediments. The contribution of FeS and FeS2 was very low, while the FeS + FeS2 content varied between 4.7 and 15.6% in all samples. There was no indication of other sulfur species with intermediate oxidation states between 0 and +6 in the core profile of Qinghai Lake.The combination of S speciation helps to constrain the depositional environment present in these sediments. Similar percentages of most reduced S (oxidation state < 0), intermediated S (oxidation state from 0 to +5), and most oxidized S (oxidation state +6) in the sediments of Dianchi Lake and Qinghai Lake were calculated by LCF (Figure4). Our results indicated that the ratio of most oxidized S reduced in the surface (0–8 cm) sediment of Dianchi Lake; correspondingly, the proportion of most reduced S increased, implying the transformation from sulfate to sulfide iron through a strong activity of SRB in the top layer. Sulfate reduction was usually not limited by the sulfate in surface layers, as the concentration exceeds K
m for SRB [29]. But limitation may occur deeper in the sediment, because sulfate usually penetrates only to <10 cm into freshwater sediments due to its low concentration [27]. As shown in Figure 4(a), at a depth of 8–12 cm layer, the proportion of most reduced S rapidly declined; correspondingly, the proportion of most oxidized S increased, revealing a limitation of sulfate reduction and an occurrence of reoxidation of reduced S in the anaerobic condition. Similar phenomenon was also found in the sediment profile of Qinghai Lake (Figure 4(b)). In the deeper (>12 cm) layers, intermediated S gradually occupied a high ratio in the total sedimentary S, indicating that the SRB was significantly reduced in those layers, because if any, the bacteria mediated disproportionation reaction will lead to the transition from the unstable intermediate S to the more stable reduced S and sulfate. The intermediated S in deep sediments found in our study was likely to be the major product of sulfide reoxidation in the absence of microorganisms and iron ions.Figure 4
Mass percentages of most reduced S (oxidation state < 0), intermediated S (oxidation state from 0 to +5), and most oxidized S (oxidation state +6) in the sediments from (a) Dianchi Lake and (b) Qinghai Lake.
(a)
(b)It should be noted that the intermediate S was stable below 15 cm depth in sediments from Dianchi Lake, as shown in Figure4(a). Experiments with 35S labeled S
2
O
3
2
- demonstrated that S
2
O
3
2
- was disproportionated throughout all redox zones in the upper 10 cm, where disproportionating bacteria were abundant in the sediments [30]. The intermediate S was not commonly found in surface layer sediments because it reacted fast with Fe3+ and was further oxidized to sulfate. Although Fe3+ oxidizes pyrite rapidly in the sediment surface, iron-oxidizing bacteria can increase the oxidation rate by several orders of magnitude [31], supplying Fe3+ for pyrite oxidation. Then in the deep layers where Fe3+ was not available, the intermediate S might be the major end product of pyrite reoxidation [6]. Due to the absence of microorganisms and iron ions, the intermediate S can keep stable in deep sediments, which was consistent with the results observed in our studies lakes.


## 4. Conclusion

The vertical distributions of sulfur speciation in sediment cores collected from five lakes of China were investigated using XANES spectroscopy. The results showed that S in the sediment of Qinghai Lake (saline lake) had a high proportion of sulfate averaged 88.9% due to physical weathering of watershed rocks, while S in the sediment of Taihu Lake (freshwater lake) had a high fraction of intermediate S (36.5%) which may be the response of the agricultural nonpoint source pollution in drainage basin. The three freshwater lakes located in Southwestern China had similar composition characteristics of S species, indicating similar sources including chemical weathering of carbonate and atmospheric deposition. In this study, 60–90% of S compounds near the surface (0–10 cm depth) sediment were in the form of sulfate and FeS. In deeper layers, the ratio of FeS2 and the intermediate S, such as R-SH, RSOR′, S
2
O
3
2
-, and R
S
O
3
-, significantly increased, suggesting rapid processes of sulfate reduction and sulfide reoxidation with the increasing depths. Our results show that K-Edge XANES spectroscopy has unique advantages in morphological analysis of sulfur in sediments. XANES has provided an important analysis tool in the study of the geochemical cycle of sulfur in the aquatic ecosystem.



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*Source: 3672348-2016-05-16.xml*