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Article

Dissolved Silica Effects on Adsorption and Co-Precipitation of Sb(III) and Sb(V) with Ferrihydrite

by
Shuang Zhou
1,*,
Tsutomu Sato
2,* and
Tsubasa Otake
2
1
Graduate school of Engineering, Hokkaido University, Kita 13 Nishi 8, Kita-ku, Sapporo 060-8628, Hokkaido, Japan
2
Faculty of Engineering, Hokkaido University, Kita 13 Nishi 8, Kita-ku, Sapporo 060-8628, Hokkaido, Japan
*
Authors to whom correspondence should be addressed.
Minerals 2018, 8(3), 101; https://doi.org/10.3390/min8030101
Submission received: 9 January 2018 / Revised: 28 February 2018 / Accepted: 2 March 2018 / Published: 5 March 2018
(This article belongs to the Special Issue Environmental Mineralogy)
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Abstract

:
Elevated antimony concentrations in aqueous environments from anthropogenic sources are becoming of global concern. In this respect iron oxides are known to strongly adsorb aqueous antimony species with different oxidation states, but the effect of silica on the removal characteristics is not well understood despite being a common component in the environment. In this study, ferrihydrite was synthesized at various Si/Fe molar ratios to investigate its adsorption and co-precipitation behaviors with aqueous antimony anionic species, Sb(III) and Sb(V). The X-ray diffraction analyses of the precipitates showed two broad diffraction features at approximately 35° and 62° 2θ, which are characteristics of 2-line ferrihydrite, but no significant shifts in peak positions in the ferrihydrite regardless of the Si/Fe ratios. The infrared spectra showed a sharp band at ~930 cm−1, corresponding to asymmetric stretching vibrations of Si–O–Fe bonds which increased in intensity with increasing Si/Fe molar ratios. Further, the surface charge on the precipitates became more negative with increasing Si/Fe molar ratios. The adsorption experiments indicated that Sb(V) was preferentially adsorbed under acidic conditions which decreased dramatically with increasing pH while the adsorption rate of Sb(III) ions was independent of pH. However, the presence of silica suppressed the adsorption of both Sb(III) and Sb(V) ions. The results showed that Sb(III) and Sb(V) ions were significantly inhibited by co-precipitation with ferrihydrite even in the presence of silica by isomorphous substitution in the ferrihydrite crystal structure.

1. Introduction

Antimony (Sb) is widely used in industry as a catalyst in plastics, flame retardants, storage batteries, and ammunition [1,2,3]. It is the ninth most mined metal for industrial uses worldwide [4,5], and one result of this is elevated concentrations of Sb in many soils and waters, especially around mining and smelting areas [6,7,8,9,10,11,12]. There has been a growing concern over the adverse effect of Sb on human health due to its toxicity. Sb has been increasingly identified as a toxic heavy metal with implications for it being a carcinogen [13]. This has caused Sb and its compounds to be listed as a leading pollutant by the United States Environmental Protection Agency [14] and the Council of the European Union [15].
Sb may be present in a variety of oxidation states (−III, 0, III, V) because of its s2p3 outer orbital electron configuration, however it is mainly found in the two oxidation states (III and V) in environmental, biological, and geochemical environments [1,5]. The toxicity of Sb depends strongly on its oxidation state, and reduced Sb(III) species are ten times more poisonous than oxidized Sb(V), similar to the case of arsenic [16]. In spite of the widespread usage and the substantial toxicity, the geochemical behaviors of antimony in soil and aquatic systems are poorly understood [17,18].
Recent studies have shown that both Sb(III) and Sb(V) appear to adsorb strongly onto iron oxides [10,18,19,20], which thereby strongly influence the speciation, mobility, and final states of Sb in the environment. Sb is preferentially associated with iron(III) (oxyhydr)oxide in soils and sediments on the basis of direct evidence using extended X-ray absorption fine structure spectroscopy (EXAFS) [6,10,21]. This would suggest that adsorption and incorporation processes into the iron(III) (oxyhydr)oxide phases would be able to control the mobility of Sb in natural environments. Several experimental studies have investigated the Sb adsorption mechanism on iron(III) oxyhydroxides, focusing on Sb speciation at the solid-liquid (water) interface using EXAFS [10,22]. However, the surface structure of Sb(III) and Sb(V) binding with iron(III) oxyhydroxides is still unclear. A further important process, co-precipitation with iron(III) (oxyhydr)oxides, does not appear to have been reported. In natural systems, iron(III)(hydro)oxides are often identified in precipitates from the oxidation of iron(II) in the presence of the relevant anions. Thus, the precipitation process may be as important as adsorption, as a sequestration process of Sb species by iron (III) (oxyhdr)oxides when groundwater with natural or added Fe comes in contact with air or oxygenated water takes place.
Further, as iron minerals are closely associated with silica, one of the most common ligands present in natural environments, pure ferrihydrite is not, strictly speaking, present in nature. Silica always associates with ferrihydrite in the structure or on the ferrihydrite surface. This could mean that silica may affect the crystallization behavior as well as the capacity of ferrihydrite to regulate hazardous element recycling. The effect of silica on arsenic adsorption has been reported for ferrihydrite [23], but no reports of the effect of silica on Sb adsorption or co-precipitation have been reported for other oxides.
Based on the above, the objectives of this study were (1) to compare the relative adsorption capabilities of Sb(III) and Sb(V) onto ferrihydrite; (2) to evaluate the effect of dissolved silica during the adsorption and co-precipitation of Sb(III) and Sb(V) on ferrihydrite; and also (3) to better understand the differences between the adsorption and co-precipitation processes of Sb.

2. Materials and Methods

2.1. Synthesis

A stock solution of ferric iron (Fe(III), 0.05 mol/L), was prepared by dissolving reagent grade Fe(NO3)3·9H2O (Kanto, 99%, Tokyo, Japan) in ultrapure water (18 M·Ω·cm). Tetraethylorthosilicate (TEOS; Alfa Aesar, 98%, Heysham, United Kingdom) was then added to 500 mL of the Fe solution to achieve silica concentrations of 0 to 20 × 10−3 mol/L (i.e., Si/Fe = 0.4). These solutions containing both silica and Fe(III) were stirred for about 30 min to dissolve the TEOS completely before pH adjustment. The initial pH of the solution was about 1.8, which was adjusted to about 7.0 ± 0.1 by titrating 1.0 M NaOH (Kanto, 97%, Tokyo, Japan). Addition of the NaOH hydrolyzes the Fe(III) in the solution resulting in formation of a slurry of dark brown precipitate. The slurries were stirred for an additional 15 min to allow the pH to stabilize. The resulting 500 mL slurries were then equally divided into 50 mL polypropylene bottles and then washed in the bottles at least four times with deionized water to remove the salts and freeze-dried for at least 24 h. Samples with different silica concentrations were replicated to evaluate the reproducibility of the experimental results.

2.2. Adsorption Experiments

Stock solutions of Sb(V) were prepared by dissolving KSb(OH)6 powder (Wako, 50%, Tokyo, Japan) into deionized water, and of Sb(III) by dissolving Sb2O3 powder (Wako, 98%, Tokyo, Japan) into 2 mol/L HCl (Kanto, 37%, Tokyo, Japan) solution. The initial concentration of both the Sb(III) and Sb(V) was 100 µM. A control experiment showed that neither Sb(III) nor Sb(V) precipitated under this initial concentration. The adsorption experiments with both Sb(III) and Sb(V) were conducted at a solid concentration of 0.5 g/L with a background ionic strength of 0.01 M NaCl. Triplicates of 40 mL suspensions with a fixed amount of solids (20 mg) and 100 µM solute concentrations were prepared in 50 mL polypropylene bottles. The experiments were conducted at a pH range of 3–12. The pH of the suspensions was adjusted using small volumes of 0.5 M HCl or 0.5 M NaOH during the experiments. Suspensions were agitated on a rotary shaker (110 rpm) for 24 h at 20.5 °C. After the reaction, the suspensions were centrifuged and then filtered through a 0.2 µm cellulose membrane filter for further analysis.

2.3. Co-Precipitation Experiments

The Sb(III) and Sb(V) co-precipitation experiments were conducted by hydrolysis of silica and Fe(III) solution and either Sb(III) or Sb(V) in deionized water, following the method of Waychunas et al. [24]. Co-precipitated samples were prepared by simultaneous addition either of 100 µM Sb(III) or Sb(V), 0.05 M Fe(III) solution, and TEOS to yield the different Si/Fe ratios of the precipitate (Si/Fe = 0–0.4). In all cases, the Si/Fe ratios of the samples were determined assuming complete precipitation of all added Fe and silica. The 500 mL mixed solutions were maintained at the experimental pH (7.0 ± 0.1) by the addition of 1.0 M NaOH. After precipitation and approximately 30 min of pH stabilization, the co-precipitates were washed at least four times with deionized water by centrifugation with a 50 mL plastic tube, then the suspensions were filtered through a 0.2 µm cellulose membrane filter for further analysis.

2.4. Analytical Methods

The powder X-ray diffraction (XRD) analyses were conducted to determine the mineralogy of the dark brown precipitates. Synthesized precipitates were analyzed by XRD using a Rigaku RINT2000 (Rigaku Co., Tokyo, Japan) X-ray diffractometer operated at 40 kV and 40 mA, equipped with a Cu target and graphite monochromator, and diffraction profiles were collected from 10° to 70° 2θ.
To identify the chemical bonds in the initial adsorbents, Fourier transform infrared spectroscopy (FTIR) analyses were conducted. The FTIR spectra were recorded from 400 to 4000 cm−1 by a JASCO FTIR-4100 spectrometer (JASCO international Co., Ltd., Tokyo, Japan) with a 1.0 cm−1 spectral resolution. The potassium bromide (KBr) used to prepare the sample was heated at 110 °C for two hours prior to analysis to remove water. The blank KBr sample (i.e., pure KBr only, in pellet form) was measured first in order to account for the matrix background. Pellets for analyzing were prepared by pulverizing the precipitates and mixing with KBr at a 1.5 mg precipitate to 250 mg KBr ratio.
To examine the surface charge properties of the initial adsorbents, the ζ-potential measurements at different pH were conducted. The ζ-potential of the samples was measured using a Zetasizer Nano ZS90 (Malvern Zetasizer Nano series Nano-ZS90, Malvern Instruments Ltd., Malvern, United Kingdom). Freeze-dried precipitates were re-suspended in 10 mL deionized water to obtain a final mineral concentration of 100 mg/L. The auto-titration was initiated at pH values from 2 to 12 (in 0.5 pH increments) adjusting the pH with dilute HNO3 or NaOH solution.
To measure the concentration of Sb, Inductively Coupled Plasma (ICP)-Atomic Emission Spectroscopy (AES) analyses were conducted. Filtrates were analyzed for Sb(III) and Sb(V) as total Sb by ICP-AES (ICPE-9000, Shimadzu Corp., Kyoto, Japan). The detection limit of this method was 0.1 µg/L. The pH of the solutions was measured with a pH meter (HORIBA, D-55) calibrated by using commercial pH 4.0, 7.0, and 10.0 buffer solutions. The amount of solute adsorbed was calculated using the difference between the initial and final dissolved solute concentrations.
The XRD data were processed by Match (version 3.3.0) software (Crystal Impact. Bonn, Germany), FTIR data were processed by Spectra ManagerTM software (JASCO international Co., Ltd. Tokyo, Japan). All the graphs were exported by Sma4 (Version 1.47) software (T. Suzuki, Kyoto, Japan) and Microsoft office 2013.

3. Results and Discussion

3.1. Characterization of Initial Adsorbents

XRD. The XRD analyses were conducted to determine the mineralogy of the dark brown precipitates. In all of the samples with the various initial ratios of Si/Fe, the XRD analyses of the dark brown precipitates, which were used as adsorbents in the following adsorption experiments, were characterized by two broad maxima centered at approximately 35° and 62° 2θ (Figure 1), consistent with the presence of 2-line ferrihydrite [25,26]. No significant shifts or changes in the width of the ferrihydrite peaks in these precipitates were observed in the range of silica concentration studied.
FTIR Spectroscopy. To identify the chemical bonds in the initial adsorbents, FTIR analyses were conducted, and the infrared spectra of the initial adsorbents were generally consistent with published data on ferrihydrite [25]. Two distinct regions can be identified in the spectra (Figure 2). First, the area from ~1300 to ~1700 cm−1, where relatively sharp adsorption bands at ~1350, ~1480, and ~1650 cm−1 corresponding to the vibrations of adsorbed water are observed. The most significant changes with increasing Si concentration are observed in the second region, where a relatively sharp band at ~930 cm−1 corresponding to asymmetric stretching vibrations of Si–O–Fe bonds appears and increases in intensity with increasing concentration of silica [27]. Swedlund [28] reported that the presence of a small amount of polymeric silica could be observed at ~1060 cm−1 in high Si/Fe ratio. However, no peaks were observed at this position in this study, this may be explained by the relatively higher background in high Si/Fe ratio, which masks the vibrations in this region.
ζ-Potential. To examine the surface charge properties of the initial adsorbents, the ζ-potential measurements at different pH were conducted. The ζ-potentials of the initial precipitates are shown as a function of pH in Figure 3. In general, the pHpzc (point of zero charge) of ferrihydrite decreases with increasing silica content during the synthesis. For instance, the pHpzc of ferrihydrite in the absence of silica was 8.2 and that of ferrihydrite at Si/Fe = 0.4 was 4.8, suggesting that the surface of the initial precipitates was more negatively charged after the silica loading.
The XRD results indicate that the Si/Fe of the precipitating solution does not influence the mineralogy of the initial precipitates. Rapid hydrolysis of the Fe(III) in solution due to the addition of NaOH resulted in the co-precipitation of silica and Fe into poorly ordered ferrihydrite. The FTIR data show that silica became closely associated with the ferrihydrite via the formation of Si–O–Fe groups, indicating that silica was incorporated into the structure of ferrihydrite. Pokrovski [29] demonstrated that aqueous silica may form stable iron silicate aqueous complexes with polymeric ferric oxy-hydroxide species. However, recent studies have shown that silica could also occur on the surface [30,31,32]. Detailed infrared spectra studies of adsorbed silica on ferrihydrite surfaces show the formation of bidentate surface complexes composed of monomeric silicate species at low silica ratios, similar to the concentrations used in this study [33]. Formation of these silica surface complexes results in a net release of protons that decreases the positive charge on the precipitate surface [34]. This is consistent with the changes in the ζ-potential observed with increasing Si/Fe ratios (Figure 3). At high silica ratios, the surface can be expected to become more negative as the silica polymerizes and creates more acidic surface complexes [28].

3.2. Adsorption of Sb(III) and Sb(V) on Ferrihydrite

3.2.1. Sb(III) and Sb(V) Adsorption in the Absence of Silica

The adsorbed ratios of Sb(III) and Sb(V) ions onto ferrihydrite in 0.01 M NaCl solutions is shown as a function of pH in Figure 4. The adsorption rate of Sb(V) was over 90% between pH 3 and 6. With increasing pH, from 6 to 12, the adsorption rate of Sb(V) rapidly decreased from 90% to 10%. A strong pH dependence on Sb(V) adsorption was reported when goethite and ferrihydrite were used as adsorbents ([22,35]). The effect of pH on Sb(III) adsorption however was much weaker, showing a constant adsorbed fraction ~95% over the whole of the pH range investigated here, from 3 to 12. This is in good agreement with earlier studies [19,22]. The difference in adsorption efficiency of Sb(III) and Sb(V) ions may mainly be due to differences in the electrostatic interactions between the sorbent surface and Sb oxyanions present in the solutions. The Sb(OH)6− is the dominant Sb(V) species over the wide pH range, here pH 3–10 [1]. The surface charge of ferrihydrite is positive below pH ~8.2, pHpzc (point of zero charge), and electrostatic attraction between the Sb(OH)6− and the surface of ferrihydrite can be expected to be stronger under acidic conditions since Sb(OH)6− is negatively charged under the conditions here, leading to electrostatic forces playing an important role in the Sb(V) adsorption. For Sb(III), a trihydroxy neutral species, Sb(OH)30, is the dominant species over a wide pH range of 2–11 [1], and only minor or no electrostatic effects may be expected for the Sb(III) adsorption.
A specific interaction (so-called surface complexation) may also play an important role between the adsorbate and adsorbent in addition to the electrostatic effect. To evaluate the effects of surface complexation reactions of Sb(III) and Sb(V) on ferrihydrite, ζ-potential measurements were carried out after the adsorption experiments at different pH values. A ζ-potential analysis is able to indirectly discriminate between inner- and outer-sphere surface complexes on mineral solid surfaces, as the formation of charged inner-sphere surface complexes changes the ζ-potential values and the pHpzc because the ion adsorption occurs inside the shear plane [36]. The ζ-potential over a wide pH range, from 3 to 12, and a significant pHpzc shift was observed (Figure 5) for both Sb(III) and Sb(V) adsorption on ferrihydrite. The pHpzc of the ferrihydrite after adsorbing Sb(V) is 7.1, which is higher than the 6.1 of Sb(III) (Figure 5). The shifts in pHpzc are likely due to negative charges generated by inner-sphere complexation of Sb ions on the surface of ferrihydrite, and the results of the ζ-potential measurements suggest that Sb(V) ions are adsorbed on the ferrihydrite surface but not as strongly as Sb(III) ions. The strong pH dependence on Sb(V) adsorption (Figure 4) suggests that electrostatic interactions play an important role for Sb(V) ions, and the strong pH dependence and shifts in pHpzc. Together, these results imply that both outer- and inner-sphere complexes rather than only inner-sphere complexes contribute to the adsorption of Sb(V) ions on the ferrihydrite. Wang [37] reported a combination of outer and inner-sphere complexes for Sb(V) adsorption on iron modified aerobic granules, which is consistent with the results for Sb(V) adsorption here.
At the same time, the steep decrease in the pHpzc by Sb(III) adsorption on ferrihydrite suggests that the uncharged Sb(III) is bound strongly to the surface of ferrihydrite by inner-sphere complexation, and the surface complexation between Sb(III) and Fe species is likely the dominating mechanism for Sb(III) adsorption, which would also be consistent with the pH independence of Sb(III) adsorption (Figure 4). An inner-sphere formation for bidentate mononuclear edge-sharing between Sb(III) and HFO was reported by using EXAFS [22]. However, further spectroscopic evidence is necessary to understand the adsorption mechanism of Sb(III) and Sb(V) on the mineral surface in more detail.
All of the above results suggest that Sb(III) showed a higher adsorption efficiency toward ferrihydrite than Sb(V) in the pH range 6–12. Previous studies also reported more effective removal of Sb(III) than Sb(V) by ferric chloride over a broad pH range and under a variety of competing ions such as phosphate and humic acid [38].The comparison in mobility between the two Sb species appears to be different from that for the As(III) and As(V) species despite Sb and As belonging to the same group of the periodic table. Here the relatively stronger adsorption of Sb(III) compared to As(III) could be attributed to antimonite being a stronger Lewis base than arsenite [19] having a higher pKa value (pKa1(H3AsO3) = 9.22; pKa(Sb(OH)3) = 11.9). Ferrihydrite is frequently amphoteric, and if considering the surface sites of ferrihydrite as Lewis acids, this would explain the stronger binding of Sb(III).

3.2.2. Sb(III) and Sb(V) Adsorption in the Presence of Silica

The effect of silica on the adsorption of Sb was investigated by varying the Si/Fe ratio of the precipitates at pH 7. The results demonstrated that both Sb(III) and Sb(V) are significantly affected by the presence of silica, with the adsorbed fraction decreasing with increasing Si/Fe ratios (Figure 6). Both Sb(III) and Sb(V) adsorption were suppressed in the presence of silica. The adsorbed fractions of Sb(III) and Sb(V) ions decreased from >96% at Si/Fe = 0–60% at Si/Fe = 0.4 and from >75% at Si/Fe = 0–30% at Si/Fe = 0.4, respectively. This shows that Sb(V) was affected more significantly by silica than Sb(III). The drop in Sb(V) adsorption efficiency is likely a result of decreased electrostatic interactions between Sb(V) ions and the surface of ferrihydrite by the decreased surface charge of ferrihydrite due to the presence of silica on the ferrihydrite surface (Figure 3), as discussed in the previous Section 3.1. Swedlund [23] also suggested that the decreasing surface charge of ferrihydrite by increasing silica concentrations could be an important factor in inhibiting As adsorption. Besides the effect of silica to decrease the surface charge, silica may also suppress adsorption of Sb by occupying surface sites by inner sphere complexation. No apparent pHpzc shift was observed after adsorption of either Sb(III) or Sb(V) on ferrihydrite synthesized at Si/Fe = 0.2 (Figure 7). This suggests that Sb(III) or Sb(V) ions could not make enough inner-sphere complexes with surface ≡FeOH groups on ferrihydrite to change the ζ-potential because potential surface sites were already occupied by silica. This effect would be more important with Sb(III) ions since inner-sphere complexation is the dominating adsorption mechanism for Sb(III) ion onto ferrihydrite. Jordan [39] also showed that silicic acid could inhibit the retention of oxyanions of selenium onto hematite surfaces by competition with the surface sites of hematite. This suggests that a competition for surface sites on ferrihydrite could be a possible mechanism for inhibition of Sb adsorption.

3.3. Sb(III) and Sb(V) Co-Precipitation Process with Different Si/Fe Ratios

The co-precipitation efficiencies were calculated using the difference between the initial and final dissolved solute concentrations. Figure 8 shows the co-precipitation rates of Sb(III) and Sb(V) ions with different Si/Fe ratios of ferrihydrite at pH 7. The co-precipitation efficiencies were ~100% for both Sb(III) and Sb(V) in the absence of silica (Si/Fe = 0). No effect of silica was observed even at the highest Si/Fe ratio in this study (Si/Fe = 0.4). Here the Sb(V) octahedra may replace Fe octahedra due to their structural compatibility. By using EXAFS analysis, Scheinost [6] reported that the Sb(V) can form both edge-sharing and corner-sharing of inner-sphere complexes to iron oxides in shooting range soils, which would be consistent with our findings.
In the case of Sb(III) co-precipitation, with octahedral or tetrahedral structures absent in Sb(III), the Sb(III) ions could alternatively be surrounded by Fe hydroxides, which would increase the co-precipitation efficiency. However, there is little previous study regarding the co-precipitation mechanism of Sb(III) with ferrihydrite, more specific evidence is necessary to discuss issues related to this.
The absence of any effect of silica on the Sb(III) and Sb(V) co-precipitation process may be because of isomorphous substitution during the simultaneous addition of silica and Sb to the co-precipitation system. Specifically, the Si occupies a tetrahedral environment, being surrounded by four oxygen centers. These tetrahedral structures may share corners with two adjacent edge-sharing Fe octahedra. This has been proposed by Pokrovski [29] on the basis of Fe K-edge EXAFS studies of Fe(III) hydrolyzed in the presence of silica. In addition, the tetrahedral Si could also coordinate with Fe tetrahedral structures since the ferrihydrite also has a tetrahedral structure as was demonstrated by a previous study [40]. If so, the silica may incorporate into the ferrihydrite structure during the co-precipitation process, which makes it more likely to have only a minor effect on the Sb retention.
Significant differences were observed in the results of the adsorption and co-precipitation experiments. The co-precipitation of Sb(III) and Sb(V) with ferrihydrite is much more effective than that of the adsorption with or without Sb(III) and Sb(V) in aqueous environments. Intuitively, the adsorption process in our experiments was solely due to adsorption onto the ferrihydrite surface, a surface complexation reaction. The co-precipitation process in principle could include the formation of phases containing Sb(III) and Sb(V) in the structure as well as adsorbing Sb(III) and Sb(V) as an impurity onto the surface of ferrihydrite. This implies that Fe minerals can act as effective scavengers of Sb in natural environments where ferrihydrite is formed.

4. Conclusions and Implications

This study examined dissolved silica effects on the adsorption and co-precipitation of Sb(III) and Sb(V) with ferrihydrite. The Sb(V) adsorption onto ferrihydrite increased under more acidic conditions. Overall, Sb(III) adsorption was constant over a broad pH range. The adsorption of Sb(III) and Sb(V) appeared to be significantly affected by the presence of silica, while co-precipitation of Sb(III) and Sb(V) with ferrihydrite was not inhibited by silica. Further, the co-precipitation process took place with higher efficiency than that of the adsorption.
Our findings on the behavior of Sb(III) and Sb(V) adsorption and co-precipitation with ferrihydrite and Si-ferrihydrite have important implications for determining the role of ferrihydrite in controlling the final state of Sb in the environments in which it is released. Although ferrihydrite is an excellent substance for capturing Sb, its use as a medium in a natural Si-rich system should be considered with caution because it will tend towards inhibition of Sb capture induced by the Si-rich environment. However, this may be different in the case of co-precipitation processes. In the present study, we found that silica and Sb(III) and Sb(V) can be incorporated into ferrihydrite and that these three are structurally compatible with ferrihydrite. The co-precipitation process of Sb(III) and Sb(V) would not be greatly influenced by the silica factor. Thus, Sb(III) and Sb(V) co-precipitation with ferrihydrite would be more efficient than Sb(III) and Sb(V) adsorption by ferrihydrite. This finding will be important when making predictions of the final state of Sb associated with ferrihydrite in natural Si-rich systems.

Acknowledgments

Shuang Zhou thanks the China Scholarship Council (CSC) and Hokkaido University for financial support.

Author Contributions

Shuang Zhou and Tsutomu Sato conceived and designed the experiments; Shuang Zhou performed the experiments; Shuang Zhou analyzed the data; Shuang Zhou wrote the paper; Tsutomu Sato and Tsubasa Otake performed revisions; Tsutomu Sato and Tsubasa Otake gave final approval for the paper to be published.

Conflicts of Interest

The authors declare no conflict of interest.

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Figure 1. X-ray diffraction (XRD) spectra of the initial synthetic precipitates with different Si/Fe ratios.
Figure 1. X-ray diffraction (XRD) spectra of the initial synthetic precipitates with different Si/Fe ratios.
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Figure 2. Fourier transform infrared (FTIR) spectra of the initial synthetic precipitates with different Si/Fe ratios.
Figure 2. Fourier transform infrared (FTIR) spectra of the initial synthetic precipitates with different Si/Fe ratios.
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Figure 3. Changes in the ζ-potential of ferrihydrite at different Si/Fe ratios as a function of pH in 0.01 M NaCl.
Figure 3. Changes in the ζ-potential of ferrihydrite at different Si/Fe ratios as a function of pH in 0.01 M NaCl.
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Figure 4. Adsorption of Sb(III/V) onto ferrihydrite as a function of the pH in 0.01 M NaCl solutions. The initial Sb(III/V) concentration were 100 µM for each sample. The concentrations of suspended solids were 0.5 g/L.
Figure 4. Adsorption of Sb(III/V) onto ferrihydrite as a function of the pH in 0.01 M NaCl solutions. The initial Sb(III/V) concentration were 100 µM for each sample. The concentrations of suspended solids were 0.5 g/L.
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Figure 5. Changes in the ζ-potential of ferrihydrite after adsorbing Sb(III/V) as a function of pH in 0.01 M NaCl. The initial Sb(III/V) concentrations were 100 µM for all samples. The concentrations of suspended solids were 0.5 g/L.
Figure 5. Changes in the ζ-potential of ferrihydrite after adsorbing Sb(III/V) as a function of pH in 0.01 M NaCl. The initial Sb(III/V) concentrations were 100 µM for all samples. The concentrations of suspended solids were 0.5 g/L.
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Figure 6. Adsorption of Sb(V) onto ferrihydrite with different Si/Fe ratios in 0.01 M NaCl solution at pH 7. The initial Sb(III) concentration were 100 µM. The concentrations of suspended solids were 0.5 g/L.
Figure 6. Adsorption of Sb(V) onto ferrihydrite with different Si/Fe ratios in 0.01 M NaCl solution at pH 7. The initial Sb(III) concentration were 100 µM. The concentrations of suspended solids were 0.5 g/L.
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Figure 7. Changes in the ζ-potential of Si-ferrihydrite (Si/Fe = 0.2) after adsorbing Sb(III/V) as a function of pH in 0.01 M NaCl. The initial Sb(III/V) concentrations were 100 µM for all samples. The concentrations of suspended solids were 0.5 g/L.
Figure 7. Changes in the ζ-potential of Si-ferrihydrite (Si/Fe = 0.2) after adsorbing Sb(III/V) as a function of pH in 0.01 M NaCl. The initial Sb(III/V) concentrations were 100 µM for all samples. The concentrations of suspended solids were 0.5 g/L.
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Figure 8. Co-precipitation of Sb(III/V) with different Si/Fe ratios of ferrihydrite at pH 7. The initial Sb(III/V) concentrations were 100 µM for all samples.
Figure 8. Co-precipitation of Sb(III/V) with different Si/Fe ratios of ferrihydrite at pH 7. The initial Sb(III/V) concentrations were 100 µM for all samples.
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MDPI and ACS Style

Zhou, S.; Sato, T.; Otake, T. Dissolved Silica Effects on Adsorption and Co-Precipitation of Sb(III) and Sb(V) with Ferrihydrite. Minerals 2018, 8, 101. https://doi.org/10.3390/min8030101

AMA Style

Zhou S, Sato T, Otake T. Dissolved Silica Effects on Adsorption and Co-Precipitation of Sb(III) and Sb(V) with Ferrihydrite. Minerals. 2018; 8(3):101. https://doi.org/10.3390/min8030101

Chicago/Turabian Style

Zhou, Shuang, Tsutomu Sato, and Tsubasa Otake. 2018. "Dissolved Silica Effects on Adsorption and Co-Precipitation of Sb(III) and Sb(V) with Ferrihydrite" Minerals 8, no. 3: 101. https://doi.org/10.3390/min8030101

APA Style

Zhou, S., Sato, T., & Otake, T. (2018). Dissolved Silica Effects on Adsorption and Co-Precipitation of Sb(III) and Sb(V) with Ferrihydrite. Minerals, 8(3), 101. https://doi.org/10.3390/min8030101

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