- Research article
- Open Access
Interaction mechanisms and kinetics of ferrous ion and hexagonal birnessite in aqueous systems
© Gao et al. 2015
- Received: 28 November 2014
- Accepted: 17 September 2015
- Published: 22 September 2015
In soils and sediments, manganese oxides and oxygen usually participate in the oxidation of ferrous ions. There is limited information concerning the interaction process and mechanisms of ferrous ions and manganese oxides. The influence of air (oxygen) on reaction process and kinetics has been seldom studied. Because redox reactions usually occur in open systems, the participation of air needs to be further investigated.
To simulate this process, hexagonal birnessite was prepared and used to oxidize ferrous ions in anoxic and aerobic aqueous systems. The influence of pH, concentration, temperature, and presence of air (oxygen) on the redox rate was studied. The redox reaction of birnessite and ferrous ions was accompanied by the release of Mn2+ and K+ ions, a significant decrease in Fe2+ concentration, and the formation of mixed lepidocrocite and goethite during the initial stage. Lepidocrocite did not completely transform into goethite under anoxic condition with pH about 5.5 within 30 days. Fe2+ exhibited much higher catalytic activity than Mn2+ during the transformation from amorphous Fe(III)-hydroxide to lepidocrocite and goethite under anoxic conditions. The release rates of Mn2+ were compared to estimate the redox rates of birnessite and Fe2+ under different conditions.
Redox rate was found to be controlled by chemical reaction, and increased with increasing Fe2+ concentration, pH, and temperature. The formation of ferric (hydr)oxides precipitate inhibited the further reduction of birnessite. The presence of air accelerated the oxidation of Fe2+ to ferric oxides and facilitated the chemical stability of birnessite, which was not completely reduced and dissolved after 18 days. As for the oxidation of aqueous ferrous ions by oxygen in air, low and high pHs facilitated the formation of goethite and lepidocrocite, respectively. The experimental results illustrated the single and combined effects of manganese oxide and air on the transformation of Fe2+ to ferric oxides.
- Ferrous ion
The iron redox cycling, particularly FeII–FeIII (FeIII and FeIII (hydr)oxides), in soils and sediments has obtained a growing concern in the field of soil science, environmental science, and biology, as the redox of FeII–FeIII− occurs through either abiotic or biotic pathway in soluble, adsorbed, and solid states . The redox reaction of FeII–FeIII− affects the geochemical behavior of minerals and nutrient elements. New experimental evidence shows that Fe2+ induced the release of structural manganese from manganese-doped goethite due to iron oxide recrystallization . Fe(II) can also catalyze the phase transformation from ferrihydrite to goethite and hematite by electron transfer through a dissolution-reprecipitation process [3, 4]. NO3 − can be reduced by Fe(II) to form NH4 + and magnetite with nitrogen cycle in soils and groundwaters . The migration and transformation of pollutants are usually coupled with the redox of FeII–FeIII−. For example, nitrate strongly influenced arsenic cycling by oxidizing ferrous iron to produce As-adsorbing particulate hydrous ferric oxides under anoxic conditions . The reduction of U(VI) and the oxidation of ferrous sulfides including pyrrhotite and pyrite are usually catalyzed by Fe2+ as FeII–FeIII− cycling works as electron transporter [7–9]. Fe-oxide formation and further transformation affect the uptake and release of cerium and uranium in Fe(II/III) aqueous solutions, and it is also found that trivalent actinides and lanthanides are released when dissimilatory iron reduction of Fe(III)-oxides leads to the formation of green rust. However, under oxidizing conditions, green rust may influence radionuclide mobility by catalyzing their transformation to a higher oxidation state . These redox cycles of FeII–FeIII− were sometimes derived by biogeochemical pathway [1, 11]. Therefore, a comprehensive attention has been given for the oxidation of Fe(II) in environment system.
As one of the most important natural constituents in soils and sediments, manganese oxide minerals with various crystal structures exhibit excellent oxidation and adsorption capacity for organic pollutants and toxic metallic ions [6, 9, 12–16]. Manganese oxides are determined to participate in the oxidation of ferrous ions and the formation of ferric oxides [6, 13, 17]. Fe(II) usually works as catalyst and electron transfer mediator in the oxidation of ferrous sulfides and others [6, 9]. However, there are few researches on the interaction process and mechanisms of ferrous ions and manganese oxides, particularly birnessite.
Manganese oxides participated in the oxidation of ferrous ions to form ferric oxides. The oxidation rates of ferrous ions by pyrolusite and γ-MnO2 were compared in sulfate solution, and the influence factors of acidity and particle size were considered, indicating that oxidation rate increased about 2 times when pyrolusite was substituted by γ-MnO2 . Birnessite, formed from microbial oxidation of Mn(II), is often enriched with heavy metals and alkaline and alkali earth metals, and generally exhibits the highest oxidation activity and largest adsorption capacity [2, 12, 13, 16, 19]. The oxidation of Fe(II), such as ferrocyanide and Fe2+, by birnessite was also studied, and the influence of pH and temperature on the release rate of Mn2+ was considered [20, 21]. Column experiment was conducted to study the reduction of Mn-oxides by ferrous ions in a flow system, and reactive transport modeling was used to analyze, quantify, and elucidate the different reaction controls and their interaction, and it was found that the release of newly formed Fe3+ and Mn2+ would be retarded as they would be first adsorbed on the surface of manganese oxides . During the redox process, initial reduction rates were much faster than long-term rates because of the inhibition by Fe(III) precipitates in the later stage at higher pH . The above researches focus on reaction kinetics, which is usually based on the deduced reaction process. However, limited information is available for the interaction process and mechanisms of ferrous ions and manganese oxides, especially for the transformation processes of ferric oxides.
Transition metal ions affected the transformation of ferric oxides with different crystal structures. The presence of Ni(II) and Pb(II) inhibited the transformation of amorphous iron oxide into a more crystalline form [24, 25]. Mn(II) participates in the transformation of ferric oxides, because Mn(II) substitution would increase the cell volumes and decrease the degree of crystallinity of goethite; in addition, dissolution and recrystallization subsequently occurred . During the oxidation of ferrous ions by birnessite, Mn(II) would be released and affect the formation process of ferric oxides. The further transformation of ferric oxides and manganese oxides needs to be intensively studied in detail, especially with regard to the influence of the released Mn(II) and Fe(II) on the formation of ferric oxides.
In the supergene environment, oxygen usually participates in the redox behaviors of active substances. The adsorbed Mn(II) could also catalyze the oxidation of Cr(OH)3(s) to toxic Cr(VI) in air . The presence of oxygen improves the chemical stability of manganese oxides during the reduction process . Sometimes, this redox reaction was only tested in acidic environment with anoxic conditions. The influence of air (oxygen) on reaction process and kinetics of birnessite and ferrous ions was seldom investigated. Because the redox reactions usually occur in open systems, the participation of air also needs to be further studied.
This work aims for the better understanding of the interaction mechanisms and kinetics of ferrous ion and hexagonal birnessite in aqueous systems. The transformation of synthesized birnessite and ferrous ions during the reaction process and the influences pH, temperature, and concentration on reaction rate were studied. The admission of air into reaction solution is to simulate the aerobic environment in open system. The catalysis of Fe2+ and Mn2+ in the transformation from amorphous Fe(III)-hydroxide to lepidocrocite and goethite were also investigated in nitrogen atmosphere.
The synthesis of birnessite
Birnessite was synthesized through the reduction of potassium permanganate by concentrated hydrochloric acid . KMnO4 of 31.61 g was dissolved in 300 mL deionized water in a conical flask and boiled with an oil-bath heated at 100 °C, and then 60 mL of 6 mol L−1 hydrochloric acid was added dropwisely to the boiling solution at 0.7 mL min−1 with vigorous stirring. The reaction lasted for 30 min, and then the suspension was aged for 12 h at 60 °C. The as-obtained mineral was washed with deionized water until filtrate conductivity was below 20.0 μS cm−1, and subsequently dried in an oven at 60 °C, and birnessite was prepared and used in the subsequent redox experiments.
The redox of birnessite and ferrous ions
FeSO4·7H2O of 0.5561, 1.1121 and 2.2242 g was dissolved into 200 mL distilled deionized water, and the concentration of Fe2+ was about 10, 20, and 40 mmol L−1 (mM), respectively. The reactor was continuously purged with high purity nitrogen gas (99.999 %, Wuhan Iron and Steel (Group) Corp., China). Nitrogen pressure inside the reactor was maintained to be slightly higher than atmospheric pressure to further prevent air ingress. The as-prepared birnessite of 0.2 g was then added to FeSO4 solution with stirring. The pHs of reaction systems were controlled at 4.0, 5.5 and 7.0, respectively, using NaOH and H2SO4 of 1.0 mol L−1. After a period of reaction, about 3.0 mL solution was filtered through a 0.22-μm microporous membrane filter. The solid products and dissolved components in filtrate were respectively characterized to analyze reaction mechanism. To simulate the open system, air was admitted into the reaction solution instead of nitrogen.
To study the influence of Fe2+ and Mn2+ on the formation and further transformation of ferric oxides, Fe2(SO4)3 of 8.0 g was dissolved into 200 mL distilled deionized water in nitrogen atmosphere, and MnSO4 or FeSO4 was then added at a concentration of 10 mmol L−1, respectively, and pH was controlled at 5.5. To investigate the oxidation process of ferrous ions in the presence of air, air was admitted into 200 mL FeSO4 solution of 20 mmol L−1 at pH 5.5 and pH 7.0, respectively. After filtration, the filtrates and precipitates were respectively characterized at different times.
The concentration of ferrous ions in filtrate was directly determined by ultraviolet–visible spectrophotometry (UV-1800, Shanghai Mapada Instruments Co., Ltd., China). The filtrate could be first reduced by oxammonium hydrochloride, and then Fe2+ concentration was measured as the total concentration of Fe2+ and Fe3+, and Fe3+ concentration could be obtained by subtraction. The total concentration of Fe2+ and Fe3+ in reaction system and manganese content in samples were also quantified by atomic absorption spectroscopy (Varian AAS240FS). The average oxidation state (AOS) of manganese was measured by an oxalic method . The content of K in samples and released K+ concentration in filtrate was determined by flame photometer (HG-3 blaze photometer). BET surface area of as-obtained birnessite was analyzed by Micromeritics ASAP2020 using nitrogen adsorption measurements. All chemical analysis for each sample was repeated three times.
After a period of reaction time, about 3.0 mL solution in reaction system was drawn off and filtered through a 0.45-μm microporous membrane filter. The wet solid products were soon identified by X-ray diffraction spectrometry (XRD, Bruker D8 Advance diffractometer with Cu Kα) at a scan rate of 4° min−1. Before and after redox reactions, their morphologies were characterized by scanning electron microscopy (SEM, JEOL, JSM-6700F Field Emission) and transmission electron microscopy (TEM, Hitachi, H-7650). Fourier transform infrared spectroscopy (FTIR, Nicolet 8700) was used to characterize the functional group of redox products with a DTGS detector by making pellets with KBr powder. The contents of crystal water in birnessite were calculated from the mass balance using thermo-gravimetric analysis (TGA) with NETZSCH TG 209 thermal analysis system.
The oxidation of Fe2+ by birnessite under anoxic condition
The oxidation of Fe2+ by birnessite in air
The oxidation kinetics of Fe2+ by birnessite
As reported, the generation of FeOOH could not be confirmed by XRD , however, the transformation process of ferric (hydr)oxides was characterized and illustrated in this work. According to reaction (1), the molar ratio of the concentration of oxidized Fe2+ to that of the released Mn2+ would be 1.83 (mass ratio: 1.86). In this experiment, the removal Fe2+ in reaction solution was all treated as the oxidized Fe(III), which existed as adsorption states on the surface of manganese oxides and the precipitate of ferric (hydr)oxides including goethite and lepidocrocite. The interrelation of the concentration of oxidized Fe2+ and the released Mn2+ was compared and the influence of reaction conditions was studied.
Figure 10b shows the concentration of released Mn2+ as the reaction proceeded. In the initial stage, the release rate of Mn2+ was similar when Fe2+ of 10 and 20 mmol L−1 was oxidized by birnessite of 1.0 g L−1, and it significantly increased when Fe2+ of 40 mmol L−1 was used instead. The concentration of released Mn2+ could reach 208, 420, and 463 mg L−1, respectively, after reaction of 12 h. The amount of the released Mn2+ increased with an increase in the concentration of ferrous ions, suggesting that high concentration of Fe2+ accelerated the reduction of birnessite. The mass ratios of Fe2+ consumption to Mn2+ production (ΔFe/ΔMn slopes) were 2.04, 1.84, and 1.61 when ferrous ion concentration was controlled at 10, 20, and 40 mmol L−1, respectively (Fig. 10c).
During the reduction process of birnessite, active adsorption sites would first be quickly occupied by Fe2+, and then redox reactions occurred. Subsequently, the newly formed Mn2+ from the reduction of birnessite would be paritially released into aqueous system, because some Mn2+ ions would be readsorbed on the surface of newly exposed birnessite if incomplete redox occurred. We have compared the theoretical and experimental concentrations of consumed Fe2+ and released Mn2+ for the reactions of Fe2+ of 10, 20 and 40 mmol L−1 and birnessite of 1 g L−1, respectively. When Fe2+ of 10 mmol L−1 participated in the reaction, 5.46 mmol L−1 Mn2+ should be released for the complete oxidation of Fe2+ by excessive birnessite. When Fe2+ concentrations were 20 and 40 mmol L−1, excessive Fe2+ was used and about 9.32 mmol L−1 Mn2+ should be released. However, the concentration of released Mn2+ was determined to be 3.58, 6.03 and 8.12 mmol L−1 after 30 min for the reactions of birnessite of 1 g L−1 and Fe2+ of 10, 20 and 40 mmol L−1, respectively. All the released Mn2+ concentrations were lower than the theoretical values. Therefore, all the reductions of birnessite by Fe2+ were incomplete when Fe2+ ions were controlled at 10, 20 and 40 mmol L−1, and the formation of the precipitate of ferric (hydr)oxides including goethite and lepidocrocite possibly inhibited the further reduction of birnessite [20, 22, 23, 43]. Another possibility should be considered for the low concentration of released Mn2+, the formed Mn2+ would be partially readsorbed on the surface of newly exposed birnessites, resulting in a decrease in released Mn2+ concentration. The similar concentrations of released Mn2+ were determined as Fe2+ concentration was controlled at 10 and 20 mmol L−1, suggesting that Mn2+ could be readsorbed because new active adsorption sites would be exposed with the partial reduction and dissolution of birnessite.
As shown in Fig. 5, released K+ was determined to be 1.34 mmol L−1 within 5 min, and K+ concentrations increased to 1.46 and 1.79 mmol L−1 after reaction of 60 and 360 min, respectively. However, complete reduction of birnessite would result in the concentration of released K+ about 2.15 mmol L−1, which further suggested that rapid adsorption in the initial stage and the incomplete reduction of birnessite occurred in this process.
Figure 10a shows the concentration of Fe2+ at different times as the initial concentrations of Fe2+ were changed from 10 to 40 mmol L−1 in reaction systems. The consumed Fe2+ concentration reached 4.0, 4.4 and 7.5 mmol L−1 within 2 min, and they approached to 6.6, 8.4 and 12.0 mmol L−1 after 30 min, respectively. However, the concentrations of released Mn2+ were almost zero within 2 min, and they approached to 1.1, 1.0 and 2.6 mmol L−1 when Fe2+ of 10, 20, and 40 mmol L−1 participated in the reaction, respectively. These results further indicated that the adsorption of Fe2+ on birnessite surface might be the major reaction, and high concentration of Fe2+ facilitated the reduction of birnessite and the corresponding release rate of Mn2+, which proved the redox kinetics of birnessite and ferrous ions [20, 22].
As reported, for the oxidation of Fe2+ and Cr3+ by manganese oxides, reaction rate was controlled by chemical reaction and not dependent upon diffusion from the bulk solution or transport of dissolved species from birnessite at pH > 4, and initial reduction rates can be significantly faster than long-term rates because of the inhibition by Fe(III) precipitates [20, 22, 23, 43]. In this work, the adsorption of Fe2+ on the surface of birnessite was extremely fast, and it could be proved by the release rate and concentration variation of K+. In the initial stage, almost the similar amount of Fe2+ would be quickly adsorbed on the surface of birnessite although the different concentrations of Fe2+ were applied because of the fixed concentration of oxidant birnessite. Therefore, the adsorption of Fe2+ played an important role in the decrease of Fe2+ in the initial stage, and they have the similar concentration changing trend due to the same amount of birnessite. The decrease in Fe2+ concentration was mainly attributed to the adsorption reaction in the initial stage. The incomplete redox reactions occurred, and redox reaction worked as the rate-determining step. The redox rate and the corresponding release rate of Mn2+ increased with an increase in the concentration of Fe2+ . The change amplitude of the concentration of Fe2+ was not as significant as that of Mn2+. Therefore, the decrease of ΔFe/ΔMn values with an increase in Fe2+ concentration was owing to the increase redox rate as Fe2+ concentration increased.
Reaction rate increased with an increase in temperature (Fig. 11b), suggesting a corresponding increase in oxidation activity of birnessite . Another possibility might be attributed to the increase of adsorption capacity as reaction temperature increased. Enhancement of adsorption capacity of birnessite at higher temperatures may be ascribed to the enlargement of pore size and/or activation of the adsorbent surface (Han et al., 2006). When air was bubbled into the aqueous system, compared with the reaction under anoxic condition, reaction rate was increased (Fig. 11a, c) due to the participation of oxygen. The amount of released Mn2+ increased within 12 h because of the incomplete redox as shown in Fig. 2. It was also noted that the release rate of Mn2+ increased with increasing pH within 4 h, and then it would keep increasing and stable when pH values were controlled at 4.0, 5.5 and 7.0, respectively (Fig. 11c). The redox reaction between birnessite and ferrous ions might be intensified in the late stage likely owing to the higher oxidation activity of birnessite at lower pH. These results further indicated that the presence of oxygen facilitated the chemical stability of birnessite in the initial stage, because Mn(II/III) would be oxidized to Mn(IV) oxide in air atmosphere (Schippers et al., 2005; [28, 41].
It was noted that this slope significantly increased from 2.95, 1.84, and 1.77 to 19.43, 8.86, and 6.02 in the presence of air when pH was controlled at 4.0, 5.5, and 7.0, respectively (Fig. 12c). These results indicated the rapid oxidation/adsorption of Fe2+ and slow reduction/dissolution of birnessite. Other characterization results indicated that the decrease rate of Fe2+ concentration significantly improved (Fig. 5b), and birnessite could be determined after 18 days (Figs. 7b, 4d), and the concentration of released Mn2+ dramatically decreased after bubbling air. High pH accelerated the oxidation of Fe2+ by birnessite through surface adsorption, and improved the chemical stability, and these factors affected the redox rate at the same time. Combining with these results, it could be safely concluded that the presence of air (oxygen) facilitated the fast oxidation of Fe2+ and the improvement of chemical stability of birnessite. These results about the relationship between the oxidized Fe2+ and released Mn2+ concentration were consistent with the change trend of released Mn2+ concentration during the reaction process. Temperature, pH, and oxygen significantly affected the adsorption and oxidation rate with different reaction mechanism.
The stimulated redox behaviors of ferrous ions and birnessite were studied, and the influence of Fe3+, Mn2+, temperature, and the presence of air on the transformation process of ferric oxides was investigated with pH 4-7. A mixture of goethite and lepidocrocite was formed with the redox reaction of ferrous ion and birnessite, and lepidocrocite transformed into goethite at the final stage. The transformation from amorphous ferric (hydr)oxide to lepidocrocite and goethite was accelerated by adding Fe2+ and Mn2+ into Fe2(SO4)3 aqueous solution at pH 5.5, and Fe2+ showed better catalytic activity compared with Mn2+. A mixed phase of goethite and lepidocrocite was formed within a day. The presence of air (oxygen) improved the chemical stability of birnessite, and significantly accelerated the oxidation rate of ferrous ions. In the oxidation reaction of ferrous ions by oxygen in air, low and high pH values facilitated the formation of goethite and lepidocrocite, respectively. Amorphous ferric (hydr)oxide was formed during the initial stage, and a mixture of poorly crystallized goethite and lepidocrocite was formed after 7 days when pH was controlled at 5.5. A mixture of lepidocrocite and goethite was formed, and the latter was the main product with high crystallinity at pH 7.0. The redox rate was indicated by the disappearing rate of Fe2+ and the appearing rate of Mn2+ in reaction system. The oxidation rate increased with an increase in the initial concentration of Fe2+, pH, and temperature, and the rate was controlled by the redox reaction of adsorbed Fe2+ with birnessite, and accelerated in the presence of air.
TYG carried out redox experiments and SEM analysis, ZHJ and YGS conducted FTIR, TEM, and ion chromatography measurements and analysis. FL, YSZ, XHF, and CFC helped with the analysis of results. GHQ had the idea for the project. All authors read and approved the manuscript.
The authors would like to thank the National Natural Science Foundation of China (Grant Nos: 41171375 and 41571228), the Program for New Century Excellent Talents in University of China (No. NCET-12-0862), the Fok Ying-Tong Education Foundation (No. 141024), the Natural Science Foundation of Hubei Province of China (Grant Nos: 2012FFA031, 2014CFA016), and the Fundamental Research Funds for the Central Universities (Program Nos.: 2662015JQ002, 2013PY029, 2013PY030 and 2010QC036) for financial support. The authors also gratefully acknowledge Dr. Wenfeng Tan and Qiang Lv at Huazhong Agricultural University for insightful suggestions.
Compliance with ethical guidelines
Competing interests The authors declare that they have no competing interests.
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