Synthesis, Characterization, and Adsorptive Properties of Fe<sub>3</sub>O<sub>4</sub>/GO Nanocomposites for Antimony Removal

Yang, Xiuzhen; Zhou, Tengzhi; Ren, Bozhi; Shi, Zhou; Hursthouse, Andrew

doi:https://doi.org/10.1155/2017/3012364

Journal of Analytical Methods in Chemistry

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Research Article | Open Access

Volume 2017 | Article ID 3012364 | https://doi.org/10.1155/2017/3012364

Synthesis, Characterization, and Adsorptive Properties of Fe₃O₄/GO Nanocomposites for Antimony Removal

Xiuzhen Yang,¹Tengzhi Zhou,¹Bozhi Ren,¹Zhou Shi,^2,3and Andrew Hursthouse^1,4

Academic Editor: Ricardo Jorgensen Cassella

Received28 Feb 2017

Revised01 Jun 2017

Accepted06 Jun 2017

Published20 Jul 2017

Abstract

A magnetic Fe₃O₄/GO composite with potential for rapid solid-liquid separation through a magnetic field was synthesized using GO (graphene oxide) and Fe₃O₄ (ferriferous oxide). Characterization of Fe₃O₄/GO used scanning electron microscope (SEM), X-ray diffractometer (XRD), Fourier transform infrared spectrometer (FT-IR), and Vibrating Sample Magnetometer (VSM). A number of factors such as pH and coexisting ions on adsorbent dose were tested in a series of batch experiments. The results showed that GO and Fe₃O₄ are strongly integrated. For pH values in the range of 3.0~9.0, the removal efficiency of Sb(III) using the synthesized Fe₃O₄/GO remained high (95%). The adsorption showed good fit to a pseudo-second-order and Langmiur model, with the maximum adsorption capacity of 9.59 mg/g maintained across pH 3.0–9.0. Thermodynamic parameters revealed that the adsorption process was spontaneous and endothermic. Analysis by X-ray photoelectron spectroscopy (XPS) showed that the adsorption process is accompanied by a redox reaction.

1. Introduction

Antimony has recently gained considerable attention as a toxic heavy metal [1]. By binding with sulfhydryl groups inside human body, antimony and antimony compounds can interfere in enzyme activity or destroy intracellular ionic equilibrium which leads to cell hypoxia, causing metabolic disorders and injury to the nervous system and other organs [2].

Antimony has been classified as a priority pollutant by European Union (EU) and United States Environmental Protection Agency (EPA) in 1976 and 1979, respectively [3, 4]. The Environmental Protection Department of Japan also listed it as a pollutant of concern and stipulated a maximum acceptable concentration of 2 ug/L [5]. In China, the maximum concentration of antimony limited by GHZBl and Drinking Water Health Standards is 5 ug/L [6], which is consistent with the standards of World Health Organization [7].

China has the largest reserve and capacity for production of antimony in the world [8]. Over 80% of total world antimony production is in China in the past several decades, and use is wide spread as a catalyst in cPET production, in flame retardants, in alloys, and in the electronics industry. The main production areas are in Hunan in the southwest of China, where the 100-year-old mine, Xikuangshan, is known as the World Antimony Capital. The region has a history of nearly 200 years of antimony ore production and, therefore, antimony pollution in this region is of concern. Research shows that the antimony content of water in the mining area can exceed 7,000 ug/L [9]. The severity of antimony pollution has threatened the health of residents surrounding the mine. Therefore, cost effective methods to control antimony pollution in China, especially in the southwest, have become an imperative.

Toxicity of antimony is mainly affected by its valence state and the nature of compounds with the toxicity of trivalent antimony being ten times higher than that of pentavalent antimony [10–12]. Hence, trivalent antimony is chosen as the target oxidation state of this pollutant.

A variety of methods have been developed to remove antimony from solution, of which approaches using adsorption are popular due to the effectiveness and availability of of reactive solid phases. Due to the huge specific surface area (2,630 m²/g) [13], Graphene Oxide (GO) has been widely applied in water treatment; however, its strong sorption makes it difficult to desorb after reaction. The preparation of Fe₃O₄/GO nano composites for effective pollutant removal has been demonstrated [14] showing strong affinity and reversibility for a number of pollutants and was prepared in this experiment to evaluate removal of antimony from water.

2. Materials and Methods

2.1. Reagent and Instrument

Raw Material and Reagent. Graphene Oxide (prepared by modified Hummers’ method) and the regents (antimony potassium tartrate, sodium hydroxide, hydrochloric acid, etc.) were analytically pure.

Key Instruments. The key instruments are Scanning electron microscope (JSM-6700F, Japan, JEOL); X-ray diffractometer (D8/ADVANCE, Germany, BRUKER); Fourier transform infrared spectrometer (IRAffinity-1, Japan Shimadzu); magnetometer (MPMS-XL-7, the United States, Quantum Design Company); atomic absorption spectrophotometer (AA-7000, Japan, JEOL).

2.2. Preparation of Fe₃O₄/GO

Fe₃O₄ particles were prepared by coprecipitation method. The successful in situ growth of Fe₃O₄ nanoparticles on GO surface during the synthetic process of Fe₃O₄/GO composites was ascribed to the oxygen-containing functional groups of GO. The as-synthesized composites in this study not only have the excellent adsorption properties of GO, but also possess the superparamagnetism of Fe₃O₄ nanoparticles. Hence, the proportion of Fe₃O₄ to GO needed optimization during the preparation of composites to take advantage of the strong adsorption properties of GO and the magnetism of Fe₃O₄.

GO (15 mg) was dispersed into DI water (30 ml) by ultrasonication for 30 min. To this suspension, 50 ml solution of FeCl₃ (110 mg) and FeCl₂ (43 mg) in DI water was added at room temperature. Then the temperature was raised to 85°C and a 30% ammonia solution was added increasing the pH to 10.0. After being rapidly stirred for 1 h the solution was cooled to room temperature. The resulting black precipitate was centrifuged at 4500 rpm for 10 min and washed three times with DI water and finally dried in a vacuum oven at 60°C for overnight to yield the Fe₃O₄/GO composite.

2.3. Adsorption Experiments

The model wastewater with varying concentration of Sb(III) was prepared using antimony potassium tartrate. Aliquots of 50 ml of model wastewater with the appropriate Sb concentration and a quantity of Fe₃O₄/GO were added. Batch adsorption experiments were undertaken at a constant temperature with shaking prior to magnetic separation of the residue. The supernatant was filtered using a 0.45 um membrane, and the concentration of residual Sb(III) in solution was measured by atomic absorption spectrophotometry. The factors influencing sorption investigated included the initial pH value, the Fe₃O₄/GO dose, adsorption time, and temperature.

The removal rate (%) was calculated fromwhere and are the initial and final concentrations of Sb(III) in the solution (mg/l), respectively.

It was a static adsorption experiment, and the experimental arrangement is shown in Figure 1.

3. Result and Discussion

3.1. Solid Characterization

3.1.1. SEM

Figure 2 showed the SEM images of GO and Fe₃O₄/GO at different magnification. The SEM images (b) and (c) show the Fe₃O₄ Nps added as bright dots that were uniformly spread over the surface of the GO, which indicated that the Fe₃O₄ was coated on the GO successfully. Magnetic Fe₃O₄ nanoparticles formed in alkaline condition could be firmly loaded on GO because the Fe³⁺ and Fe²⁺ in solution reacted with the carboxyl functional groups of GO to form coordination compounds that were easily deposited on the surface of GO.

(a)

(b)

(c)

The reaction processes are previously identified as (2)–(4) [15].

3.1.2. FT-IR

The images in Figure 3 show the FT-IR spectrum for Fe₃O₄/GO composites. Two strong vibration stretch peaks appeared at 570 cm⁻¹ and 468 cm⁻¹, which were characteristic absorption peaks of Fe-O bond [16]. The absorption peaks at 3438 cm⁻¹, 1629 cm⁻¹, 1230 cm⁻¹, and 1120 cm⁻¹ were related to the vibration peak of molecular adsorption, the vibration absorption peak of C=O in carboxyl, C=O-H or vibration of ketone skeleton, and the vibration of C-O-C, respectively [17]. The results indicated that a large amount of oxygen-containing functional groups exist on the surface of the GO and Fe₃O₄ nanocomposite.

3.1.3. XRD

The powder X-ray diffraction pattern in Figure 4 for Fe₃O₄/GO composites shows the diffraction basal spacing (001) is due to the crystalline GO (with 2θ at 10.9°). Seven distinct diffraction peaks of varying FWHM are identified for 2θ at 30.1°, 35.4°, 43.1°, 53.2°, 62.7°, and 74.0° and correspond to cubic phase crystal structure of Fe₃O₄ which were (220), (311), (400), (422), (440), and (533), respectively [18]. Moreover, it can be noted that there was no other impurity peak in XRD, which means the in situ growth of GO and Fe₃O₄ did not affect the structure of Fe₃O₄ during the synthesis of the Fe₃O₄/GO composites. The cubic structure of Fe₃O₄ is confirmed.

3.1.4. Vibrating Sample Magnetometer

The plot in Figure 5 shows the hysteresis loop of the composite adsorbent. The specific magnetism was up to 87.3 emu/g, which indicated that the composite could achieve fast solid-liquid separation under the applied magnetic field.

The hysteresis loop of Fe₃O₄/GO was close to “S,” and the surplus magnetic strength and magnetic coercive force were nearly zero and thus it belongs to soft magnetism. It confirms that Fe₃O₄/GO composites were superparamagnetic. The results confirm good separation potential as reported elsewhere, and strong potential for recovery and reuse in sorption treatment systems [19].

3.2. Evaluation of the Performance of Fe₃O₄/GO Composite in the Adsorption of Sb(III)

3.2.1. The Effect of pH

An experiment on the effect of pH on Sb(III) adsorption was carried out over the pH range of 2.0–11.0. The initial concentration of antimony was mg/L; and the dose of Fe₃O₄/GO was 100 mg/50 ml; the reaction temperature was K; reaction time was min, with the mixing speed of 120 r/min. Experimental results are shown in Figure 6.

Figure 6 indicated that the adsorption of Sb(III) by using Fe₃O₄/GO was not affected in the pH range of 3.0–9.0, and the maximum removal rate was over 95%. This phenomenon is because the species of Sb(III) are pH dependent: when the pH is below 3.0, the predominant species of Sb(III) are SbO⁺ and Sb(OH)²⁺, when the pH ranges from 3.0 to 9.0 Sb(OH)₃ and HSbO₂ are the main species of Sb(III), and only SbO²⁻ exists when the pH is above 9.0 [20]. Since the highest adsorption is achieved at pH 3.0–9.0 and pH value of the aquatic environment is usually around 7.0, thus pH 7.0 is selected in further experiments.

3.2.2. Effect of Sorbent Dose

10 × 50 ml samples of Sb(III) solution with an initial concentration of 10 mg/L were taken. The solution was added in a 100 ml polyethylene bottle, and pH was adjusted to 7.0. Finally, the solution was mixed in a constant temperature shaker (298 K) for 120 minutes.

As shown in Figure 7, adsorption removal rate of Sb(III) increased with the Fe₃O₄/GO dose. Initially, there was a sharp increase in the rate of adsorption, which later slowed down. The adsorption equilibrium was achieved at a dose of 60 mg. This might be explained by the fact that the contact area between adsorbate and adsorbent became larger and the adsorption points of Fe₃O₄/GO increased with the addition of Fe₃O₄/GO. Furthermore, the difference in Sb(III) concentration between initial adsorbent and adsorbate was relatively large and more Sb(III) could be adsorbed by Fe₃O₄/GO, which also leaded to a fast adsorption at the initial stage. With the increase of sorbent dose, adsorption of Sb(III) could reach up to 100%. In subsequent experiments, 60 mg/50 ml was chosen as the optimum dose.

3.2.3. Effect of Coexisting Ions

Effect of various anions on Sb(III) adsorption efficiency was investigated. A series of experiments using Cl⁻, , , , , and were selected to simulate background interference. Ion concentrations used were 0, 50, 150, 350, and 500 mg/L and the dose was 60 mg/50 ml. The results were illustrated in Figure 8.

As shown in Figure 8, Sb(III) adsorption efficiency was all over 97% for all ions. It should be noted that the removal efficiency showed a relatively low decrease with increase in anion concentration. The order of decrease in removal efficiency was . Actually, this phenomenon was related to the degree of association of above ions with soluble Sb species impacting on removal efficiency.

3.3. Adsorption Kinetics

In order to study the kinetics of Fe₃O₄/GO absorbing Sb(III), a series of Sb(III) solutions with concentration of 10 mg/L and initial pH value of 7.0 were taken and 60 mg of Fe₃O₄/GO was added to each solution. When temperature was 298 K, the variation of adsorption with the change of time was measured. Pseudo-first-order kinetic model and pseudo-second-order kinetic model were adapted to analyze characteristics of adsorption kinetics. Model equations are listed as Formula (5) [18].where and (mg/g) are the amounts of Sb(III) adsorbed onto Fe₃O₄/GO at time and at equilibrium, respectively; is the rate constant, determined by plotting versus ; and is the rate constant.

For the first-order kinetic equation of specified initial concentration, to time was plotted, and the linear fitting was done. The first-order and second-order kinetics fit lines (Figure 9) were obtained by the fitted parameters. Similarly, for second-order kinetic equation, to time was graphed and the linear fitting was undertaken. The second-order kinetics fit line in Figure 9 was based on the best fit parameters.

From Figure 9, it is clear that the adsorption of Sb(III) by Fe₃O₄/GO is more suitable for the pseudo-first-order kinetics model which implies a simple sorption mechanism rather than chemical reaction.

3.4. Adsorption Thermodynamics

In order to study the thermodynamic characteristics of Sb(III) adsorption by Fe₃O₄/GO, a series of Sb(III) solutions with various concentrations and initial pH value of 7.0 were taken. The solutions were put in constant temperature incubation box (298 K) and the adsorption was performed for 24 hours. The equilibrium absorption capacity as a function of equilibrium concentration at the different temperatures was plotted as the adsorption isotherms of Sb(III) in Figure 8.

Data were fitted using the Langmuir [21] and Freundlich [22] isotherm models, and the equations for both models are presented as Formula (6).where is the mass concentration of Sb(III) when the solution is in the state of adsorption equilibrium; is the Langmuir adsorption constant. is a Freundlich constant related to adsorption capacity and is an empirical parameter giving an indication of the favorability of adsorption. It is conducted that when 1/ is between 0.1 and 0.5 the adsorbate is easily adsorbed, while when is larger than 2.0 it is difficult to adsorb [6].

From Figure 10, it can be seen that the adsorption reaction matches the Langmuir isothermal adsorption model, which indicated that the adsorption of Sb(III) onto Fe₃O₄/GO was the monolayer adsorption. Moreover, adsorbing capacity increased with an increase in temperature. Meanwhile, in Table 1, which meant that the reaction was thermodynamically favourable.

Thermodynamic parameters were calculated by the formulas shown below [23]:where is the solid-liquid distribution coefficient [24]; is the Gibbs free energy change value in adsorption process, kJ/mol; is the caloric value in adsorption process, kJ/mol; is the entropy change value in adsorption, J/(mol·K).

Based on the experimental results of the adsorption of Sb(III) onto Fe₃O₄/GO, the linear imitation was graphed in Figure 11 1/ was the abscissa while was the ordinate. According to Formula (9) and the obtained slope and intercept of the straight line, and were calculated, and in the corresponding temperature was calculated by Formula (7). The results were presented in Table 2.

Table 2 showed that the adsorption reaction was a spontaneous process when the Gibbs free energy change value () was below zero. And when , the adsorption process increased the entropy of the process. As for the , the adsorption reaction was an endothermic process when its value was over zero and thus the temperature rise was helpful to move the reaction forward.

3.5. Analysis of Adsorption Mechanism

The XPS results of Fe₃O₄/GO after the adsorption of Sb(III) were depicted in Figure 12. There was a peak of Sb in the spectrum, which coincided with the peak of O1s. The spectrum of Sb after adsorption was presented in Figure 14. The spectra of the surface oxygen of Fe₃O₄/GO (before and after adsorption) were shown in Figures 13 and 14, respectively.

The binding energies of Sb(3d_5/2) and Sb(3d_3/2) detected by XPS were 530.11 eV and 539.75 eV. According to the XPS chemical state database, the superficial antimony on the Fe₃O₄/GO exists as Sb₂O₅, in which the antimony was pentavalent. However, the antimony of K(SbO)C₄H₄O₆·1/2H₂O used for preparing stock solutions was as a trivalent species. It demonstrated that the absorption process was accompanied with redox reaction, oxidizing the Sb III.

In order to further analyze the relation between bind energy displacement of O(1s) and surface charge, De Jong et al. [25] constructed a simplified mathematical model (10):where is charge of oxygen atom (esu); is binding energy measured by XPS (eV).

The charge variation of oxygen atom before and after the adsorption of Sb(III) onto GO was calculated by Formula (10), and the results are presented in Table 3.

Table 3 shows the charge of oxygen atom was changed from −0.871/esu to −0.738/esu during the adsorption of antimony onto Fe₃O₄/GO. Therefore, it could be concluded that the outer electron of oxygen atom transferred and the density of electrons changed during the adsorption process demonstrating that redox reaction occurred during the adsorption process.

3.6. Adsorbent Reuse

Reusability is a key factor in the investigation of adsorbent performance. A 0.1 mol/L of ethylene diamine tetraacetic acid (EDTA) solution was utilized in this experiment as a useful chelating agent to enhance removal of strongly adsorbed Sb and test reusability of the sorbent. The results showed Fe₃O₄/GO lost 50% of its efficiency after five continuous adsorption-regeneration-adsorption cycles as an adsorbent. This degradation may be due to decomposition of the sorbent or blocking of exchange sites by the EDTA.

4. Conclusions

The magnetic adsorbent Fe₃O₄/GO was synthesized and was studied in the removal of antimony from solution. The rate of removal rate of antimony was greatest in the pH range of 3.0–9.0. Reaction kinetics indicated that the adsorption of antimony onto Fe₃O₄/GO followed a pseudo-first-order kinetic model. The adsorption of Sb(III) onto synthesized Fe₃O₄/GO matched a Langmuir isothermal adsorption model according to reaction thermodynamics and the maximum adsorption capacity was found to be 9.59 mg/g. The thermodynamic parameters of the adsorption proved that the adsorption of Sb(III) onto Fe₃O₄/GO was a spontaneous and endothermic process. The XPS before and after adsorption and the relation between the binding energy displacement of O(1s) and surface charge indicated that the adsorption process was accompanied by a redox reaction. In addition, the regeneration test demonstrated that Fe₃O₄/GO composite has good reuse potential.

Conflicts of Interest

The authors declare that they have no conflicts of interest.

Acknowledgments

This work was financially supported by the National Natural Science Fund Project of Hunan Province (2016JJ6040) and the National Natural Science Foundation of China (51604113). The authors deeply appreciate this support.

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Copyright © 2017 Xiuzhen Yang et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

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