Adsorption-Oxidation Mechanism of <i>δ</i>-MnO<sub>2</sub> to Remove Methylene Blue

Yan, Ge; Wang, Pu; Li, Yuqian; Qin, Zhangjie; Lan, Shuai; Yan, Yupeng; Zhang, Qin; Cheng, Xiaodi

doi:https://doi.org/10.1155/2021/3069392

Adsorption Science & Technology

On this page

Abstract Introduction Materials and Methods Results Discussion Conclusions Data Availability Conflicts of Interest Acknowledgments References Copyright Related Articles

Special Issue

Biogeochemical Processes, Interactions, and Control of Pollutants in Soil-Plant Systems

View this Special Issue

Research Article | Open Access

Volume 2021 | Article ID 3069392 | https://doi.org/10.1155/2021/3069392

Adsorption-Oxidation Mechanism of δ-MnO₂ to Remove Methylene Blue

Ge Yan,¹Pu Wang,²Yuqian Li,¹Zhangjie Qin,¹Shuai Lan,¹Yupeng Yan,¹Qin Zhang,¹and Xiaodi Cheng¹

Academic Editor: Xue Tao Guo

Received19 Aug 2021

Accepted08 Oct 2021

Published26 Oct 2021

Abstract

The material, δ-MnO₂, has exhibited superior performance on the removal of methylene blue (MB), but the process is significantly impacted by pH, and the impacting mechanism is still unclear. In this study, the effects of pH on the removal mechanism of MB using synthesized δ-MnO₂ were investigated by distinguishing the adsorption and oxidation of MB by δ-MnO₂ during the removal process in the dark. The results show that the total removal efficiency of MB by δ-MnO₂ decreased significantly with an increase in the pH. MB could be removed by δ-MnO₂ via an adsorption mechanism and oxidation mechanism, and the proportion of adsorptive removal and oxidative removal was different under different pH conditions. With an increase in the initial pH from 2.00 to 8.05, the redox potential of δ-MnO₂ decreased, and its oxidation ability for the removal of MB also gradually decreased. In contrast, the surface negative charges of δ-MnO₂ increased with an increase in the pH, and the adsorption ability towards positively charged MB also gradually increased. This indicates that the effects of pH on the removal of MB by δ-MnO₂ are primarily dominated by its influence on the oxidation ability of δ-MnO₂. In addition, it is further proved that the pH value has a significant effect on the oxidation and adsorption of MB on δ-MnO₂. Moreover, the significant effects of pH on the oxidation of MB by δ-MnO₂ are further demonstrated by observing the changes in Mn²⁺ and the UV-Vis spectra of intermediate products during the reaction, as well as the changes in the FTIR and XPS characterizations of δ-MnO₂ after the reaction.

1. Introduction

Manganese oxides widely exist in the earth’s surface and water environments, and they are important components of soil and sediment [1]. In the microstructures of manganese oxides, manganese atoms coordinate with oxygen atoms in the form of [MnO₆] octahedra, and the [MnO₆] octahedra form single chains through coedge connections. These single chains are connected by sharing edges or corner oxygen atoms forming manganese oxides with different crystal structures [2]. The surface of manganese oxides belongs to hydrated oxide types with variable surface charges [3]. Because the zero point of charge (ZPC) of manganese oxides is very low, they are usually negatively charged within the normal pH range, which can adsorb charged heavy metal ions or organic pollutants [4–6]. Manganese oxides are primarily composed of high valent Mn(III) and Mn(IV) [7], which have high redox potentials. Hence, the removal towards organic pollutants can be achieved via oxidation reactions [8–10]. As a semiconductor, manganese oxides also exhibit photocatalytic activity, which can photocatalytically remove organic pollutants by irradiation [11]. Manganese oxides are often used to remove organic pollutants due to their multiple environmental properties, such as adsorption, oxidation, and photocatalysis [12, 13].

More than tons of dyes and pigments widely used in many industries are produced every year, of which more than 10% are found in wastewater [14]. MB has a high chroma, and it is difficult to remove biologically [15]. It has been widely studied as a representative dye because it is a serious environmental pollutant [16]. A large number of studies have shown that manganese oxides can effectively remove MB, but the efficiency is significantly affected by pH [17–19]. A study by Kuan et al. in 2011 showed that the removal capacity of γ-MnO₂ towards MB at pH 7.2 was lower than that at pH 4.8. By measuring the total organic carbon (TOC) of the reactants, it was speculated that there was an oxidative removal mechanism in the removal process of MB by γ-MnO₂ [20]. Kuan et al. subsequently found that pyrolusite could oxidatively remove MB when the pH was lower than its pH_iep (4.70), while when the pH was higher than its pH_iep (4.70), cationic MB was more easily adsorbed on pyrolusite electrostatically [21]. In 2017, Peng et al. used MnO₂ nanosheets to remove MB, and it was found that the removal efficiency gradually decreased with an increase in pH from 2 to pH_zpc3.69, while the removal efficiency gradually increased when the pH increased from pH_zpc3.69 to 12. They speculated that the effective removal observed at was due to the oxidation of MB by MnO₂ nanosheets, while at , the removal was due to the electrostatic adsorption of MB by MnO₂ nanosheets [22]. Wang et al. found that with an increase in pH from 3.0 to 9.0, the total removal efficiency of MB decreased from 99.3% to 84.7%, and the oxidative removal efficiency decreased from 98.7% to 43.0%, while the adsorptive removal efficiency increased from 0.6% to 41.7% [18]. The above studies indicated that there existed two possible mechanisms for the removal of MB by manganese oxides: (1) MB with positive charges can be adsorbed on the surface of manganese oxides due to the large number of negative charges on the surface and (2) manganese oxides can remove MB via oxidation reactions due to their high redox potential. The surface charges and redox potentials of manganese oxide are impacted by pH. It is unclear how such an impact affects the adsorption or oxidation of MB by manganese oxides and whether there is a coupling mechanism between the two degradation mechanisms. In addition, all the above studies were conducted under light, and the photocatalytic degradation of MB by manganese oxides was not considered.

Therefore, in this study, the common manganese oxide, δ-MnO₂, was selected as a representative for manganese oxides. The effects of pH on the removal mechanism of MB by δ-MnO₂ were studied by analyzing the adsorption amount and oxidation amount of MB by δ-MnO₂, as well as the changes in pH, Mn²⁺, and products during the reaction process. The reaction was conducted in the dark in order to avoid the photocatalytic effect of δ-MnO₂.

2. Materials and Methods

2.1. Synthesis and Characterization

The used δ-MnO₂ were prepared with KMnO₄ and HCl, typically in a triangular flask with 300-400 mL of deionized water boiled in a constant temperature oil bath (110°C). Then, 120 mL of 6 mol/L HCl was added dropwise at a rate of 0.7 mL/min under strong stirring. After the addition was completed, the reaction was continued for 30 min, and the obtained product was aged at 60°C for 12 h [23]. After washing with deionized water to conductivity of <15 μs/cm, the final product was dried in a 40°C oven, ground and passed through a 60-mesh sieve, and then placed in a desiccator for later use. Methylene blue () was purchased from Beijing Guangcheng Chemical Reagent Co. Ltd., China, and used without further purification. All other employed chemicals are of analytical reagent grade. The chemical structure of MB was given previously.

2.2. Characterization

The crystal structure of the sample was determined by the Bruker Advance D8 X-ray powder diffraction (XRD) with CuKα radiation at 40 kV tube voltage, 40 mA tube current, 1°/min scanning speed, scanning interval of 5°-85°, and step size of 0.02°. The morphology of δ-MnO₂ was observed under the scanning electron microscope (SEM) of FEI Nova NanoSEM450. Transmission electron microscope (TEM) analysis was used to analyze the morphology and particle size characteristics by JEOL JEM-2100. The specific surface area (SSA) was determined using Quantachrome Autosorb-1. The zero point of charge (ZPC) was measured by the rapid potentiometric titration method. The average oxidation state (AOS) of Mn was measured by the oxalic acid-permanganate back-titration method [24].

2.3. Dye Removal

2.3.1. Kinetic

100 mL 160 μmol/L dye solution (pH 3.99) was added into 100 mL 400 mg/L δ-MnO₂ suspension (pH 4.00) in a 250 mL triangle bottle under magnetic stirring, and the tin paper was wrapped in a triangular bottle to avoid light. The pH of dye and δ-MnO₂ was adjusted with HCl or NaOH solution until the pH value is stable in ±0.05 in 12 h. 10 mL of the supernatant was sampled using a syringe and immediately filtered through a 0.45 μm membrane filter at 0 min, 1 min, 3 min, 5 min, 9 min, 15 min, 20 min, 30 min, 60 min, 90 min, 180 min, and 240 min, respectively. In addition, two parallel experiments were set. The liquid under test was ally determined by the UV spectrophotometer (UV). The removal rate of dye was calculated by where (μmol/L), (μmol/L), and (μmol/L) are the initial concentrations, dye concentration at contact time (), and dye concentration at equilibrium, respectively. It is used to evaluate the degree of removal. and represent adsorbent dosage (mg) and dye solution volume (L), respectively. Then, fitting was obtained using the experimental kinetic data with the linear forms of the two kinetic models: the pseudo-first-order (PFO) and pseudo-second-order (PSO) models [25]; the specific formula is as follows: where (mg/g) are adsorption capacity at equilibrium, (mg/g) are adsorption amount at contact time (min), and and (min^-1) are first-order and second-order rate constants.

2.3.2. Removal Mechanism

For the investigation of the mechanism, 50 mL of an 80 μmol/L MB solution was added into 50 mL of 200 mg/L δ-MnO₂ suspension in a 150 mL triangle bottle using tin foil to avoid light under magnetic stirring. The pH of the dye and the δ-MnO₂ was adjusted to the desired value (pH of 2.00, 4.01, 5.92, and 8.05) with the HCl or NaOH solution. The sampling times were 0.5 h, 1 h, and 3 h. At the specified time, 10 mL of the solution was filtered through a 0.45 μm membrane filter, and the removal efficiency was measured using the dye (Equation (1)) of the filter membrane as the total removal efficiency (). Concurrently, another 10 mL solution was added using 2 mL of 20 g/L hydroxylamine hydrochloride (HONH₃Cl) and adding HONH₃Cl to dissolve the δ-MnO₂, releasing the dye adsorbed on the surface of the δ-MnO₂. The removal ratio obtained by adding HONH₃Cl was the oxidative removal efficiency (). The adsorptive removal efficiency () was the difference between and . Each group was divided into two parallel groups.

The δ-MnO₂ that passed through the filter in the experiment was collected and repeatedly rinsed with ultrapure water and drying. The reacted δ-MnO₂ was subjected to FTIR and XPS measurement and compared with the initial δ-MnO₂ [26, 27]. UV-visible spectroscopy was utilized to determine dye removal efficiency and adsorption capacity. pH and the contents of Mn²⁺ of the solution after filtering the solution were also measured using atomic absorption spectrometry (AAS, PerkinElmer AA900). All the experiments were run in duplicate, and the data presented are averages of this duplicate analysis.

3. Results

3.1. Characterization of δ-MnO₂

Table 1 shows the physicochemical properties of the as-synthesized δ-MnO₂. The powder XRD pattern of the as-synthesized sample is shown in Figure 1(a). The values of the diffraction peaks of the as-synthesized sample were 0.719 nm, 0.362 nm, 0.244 nm, and 0.142 nm, which were consistent with the characteristic diffraction peaks of δ-MnO₂ (JCPDS 86-0666). Therefore, it was concluded that the as-synthesized sample was δ-MnO₂. Figure 1(b) shows the N₂ isothermal adsorption-desorption curve of δ-MnO₂ and the pore size distribution found using the Saito-Foley (SF) method. The measured N₂ isothermal adsorption-desorption curve was fitted using the Brunauer-Emmett-Teller (BET) method. The specific surface area of δ-MnO₂ was 89.8 m²/g. The diameter of the micropores (Figure 1(c)) of δ-MnO₂ primarily distributed near 8.1 Å was fitted using the SF method. In addition, the micropore volume was 0.042 cm³/g as analyzed using the total pore volume method. The micropore area and the external surface area of δ-MnO₂ were 13.9 m²/g and 75.9 m²/g (Table 1), respectively, as analyzed using the -method. This indicates that the mesoporous specific surface area was much larger than the microporous specific surface area, meaning the mesoporous structure was dominant, although there existed a microporous structure in the as-synthesized δ-MnO₂. The SEM and TEM images of the as-synthesized δ-MnO₂ are shown in Figures 1(d)–1(g). Thin sheets of δ-MnO₂ were observed in the SEM images, and the TEM images further proved that the sample was composed of many thin sheet crystals aggregated to form flower-like aggregates between one hundred and several hundreds of nanometers.

3.2. Kinetics of the Removal of MB by δ-MnO₂

The kinetics of the removal of MB by δ-MnO₂ are shown in Figure 2. The removal rate of MB was high within the initial 60 min, and the removal efficiency reached 50.93% at 1 min and 79.66% at 60 min. With an increase in the reaction time, the removal rate gradually decreased reaching equilibrium, and the removal efficiency was 85.74% (Figure 2(a)) after 6 h of reaction. The obtained kinetic data were linearly fitted using the pseudo-first-order (PFO) and the pseudo-second-order (PSO) kinetic models (Figures 2(b) and 2(c)). The fitting results are shown in Table 2. The correlation coefficients, , of the PFO kinetics and PSO kinetics were 0.9269 and 0.9999, respectively, which indicated that the removal process of MB by δ-MnO₂ was more consistent with the second-order kinetics (Table 2). Figure 2(d) presents the UV-Vis wavelength scan of the reaction solution in the kinetic experiment. A blue shift was observed for the maximum absorption peak of MB in the full-band scan spectrum after reacting with δ-MnO₂.

(a)

(b)

(c)

(d)

3.3. The Effect of pH on Removal of MB

The changes in of the MB by δ-MnO₂ at different pH are shown in Figure 3. With an increase in the initial pH, of MB by δ-MnO₂ decreased gradually. After 0.5 h of reaction, of MB by δ-MnO₂ was 98.38%, 66.66%, 47.22%, and 30.66% at pH of 2.00, 4.01, 5.92, and 8.05, respectively (Figure 3(a)). Thereafter, the reaction rate decreased, and the corresponding total removal efficiencies were 98.85%, 81.03%, 62.15%, and 41.91%, respectively, at 3 h of reaction (Figure 3(a)). For further analysis of the oxidation removal rate and adsorption removal rate of MB by δ-MnO₂, the law is as follows: the oxidation removal of MB by δ-MnO₂ has a similar change trend with the total removal rate, which gradually decreases from 98.85% to 27.29% as the pH increases. However, the adsorption removal rate of δ-MnO₂ on MB increased with the increase of the initial pH. When the pH increased from 2.00 to 4.01, 5.92, and 8.05, after 3 hours of reaction, the adsorption and removal rates of δ-MnO₂ on MB were 0%, 6.24%, 14.72%, and 14.62%, respectively.

(a)

(b)

(c)

(d)

(e)

The above results indicate that there was almost no adsorption of MB on the surface of δ-MnO₂ when the pH was 2.00 (Figure 3(b)), at which time, the removal of MB on the surface of δ-MnO₂ was primarily dominated by oxidation reactions. In addition, there was almost no MB in the reaction system. At a , the adsorption of MB by δ-MnO₂ increased to equilibrium, while the oxidative removal efficiency decreased (Figures 3(c)–3(e)).

4. Discussion

The above results show that the removal of MB by δ-MnO₂ includes oxidation removal and adsorption removal. In order to further explore the oxidation removal mechanism, the UV-visible spectra of the MB solution after reaction with δ-MnO₂ under different pH conditions are compared (Figure 4). The change of Mn²⁺ in the solution (Figure 5), FTIR spectrum (Figure 6), and XPS (Figure 7).

(a)

(b)

(c)

(d)

(e)

4.1. Oxidating MB by δ-MnO₂

In order to prove that the oxidation-reduction reaction occurred when δ-MnO₂ removes MB, the intermediate and final products of the oxidation reaction can be analyzed. First of all, it can be seen from Figure 4 that under the reaction conditions of different pH, the absorption peaks of the UV-Vis of the solution after the reaction are significantly different. With the decrease of pH, the absorption peak of the solution after the reaction changes significantly and accompanied by the appearance of new absorption peaks, such as absorption peaks at 451, 557, 608, 632, and 657 nm. And similar to the trend reported by Zaied et al., the MB removal process will produce intermediate products such as Azure B, Azure A, Azure C, and Thionin [28], and the absorption peak gradually shifts to the left. Therefore, it can be inferred that the oxidation-reduction reaction of MB occurred during the removal of δ-MnO₂, and as the pH of the reaction system gradually decreased, the oxidation capacity of δ-MnO₂ gradually increased, and the degradation degree of MB also increased, and intermediate products were formed. The maximum absorption peak also gradually shifted to the left.

By detecting the change of Mn²⁺ in the solution after the reaction, it can also be proved that the process of removing MB by δ-MnO₂ has undergone an oxidation-reduction reaction. As shown in Figure 5, at pH 2.00 and 4.01, δ-MnO₂ is accompanied by the release of Mn²⁺ in the process of removing MB. At pH 2.00, the release of Mn²⁺ reaches 13.3 mmol/L. When the pH was 4.01, the release of Mn²⁺ was only 0.76 mmol/L, and the lower the pH, the greater the release of Mn²⁺. When the pH was 5.92 and 8.05, Mn²⁺ was not detected in the solution after the reaction. However, it can be seen from Figure 3 that the redox reaction still occurs at pH 5.92 and 8.05. It can be inferred that the negative charge on the surface of δ-MnO₂ will increase with the pH under weakly acidic, neutral, and alkaline conditions. However, the corresponding adsorption sites that can adsorb positively charged Mn²⁺ increase accordingly; that is, the Mn²⁺ released during the reaction is readsorbed to the surface of δ-MnO₂, so Mn²⁺ is not detected in the solution.

4.2. The Mechanism of Adsorption

By comparing the changes of the FTIR spectra of δ-MnO₂ before and after the reaction (Figure 6), it was explored whether δ-MnO₂ had an adsorption and removal effect on organic matter in the solution. As shown in Figure 6, for the FTIR spectrum of the reacted δ-MnO₂, compared with the δ-MnO₂ that has not reacted with MB, a new chemical bond vibration is obviously detected. The absorption bands of δ-MnO₂ before the reaction are located at 1619, 920, 449, and 512 cm^-1, of which 449 and 512 cm^-1 are the characteristic absorption of δ-MnO₂, respectively. The lattice vibration of the layered Mn-O bond has a slight blue shift [29]; 920 cm^-1 is the bending vibration of manganese-oxygen octahedron-OH [30], and 1619 cm^-1 is the bending vibration of H₂O. After reacting with MB, δ-MnO₂ still retains the characteristic peak of δ-MnO₂. The layered structure of Mn-O bond lattice vibrates, but the bending vibration of the manganese oxide octahedral cavity -OH at 920 cm^-1 disappears. At the same time, many new chemical bond vibrations have appeared. For example, 1395 cm^-1 was assigned to the stretching vibrations of CN bonds in the heterocycle of MB; the band at about 1491 cm^-1 was ascribed to the CH₂ deformation vibration. In addition, the wave bands at 1252 and 1224 cm^-1 are due to the Ar-N deformation vibration. For the tensile vibration of C=S and CS, the wave band is about 1142 and 887 cm^-1. In the band of 820 cm^-1, new chemical bonds appear, which are attributed to the rocking vibration of C-H in the benzene ring of MB [31]. In addition, no bending vibration of -OH at 920 cm^-1 was detected on the surface of δ-MnO₂ after reacting with MB. It can be presumed that the adsorbed material occupied the -OH site of δ-MnO₂ and disappeared. It can be seen from Figure 4 that δ-MnO₂ is accompanied by the production of intermediate products in the process of removing MB, and the structure of the intermediate product is similar to that of MB. This can prove that the surface of δ-MnO₂ adsorbs MB or organic matter similar to MB.

It can also be found from Figure 6 that the adsorbed substances on δ-MnO₂ increase with the increase of pH, which is contrary to the result that the adsorption removal rate of δ-MnO₂ on MB gradually increases with the increase of pH of the reaction system in Figure 3. Therefore, XPS was used to further quantitatively analyze the content of adsorbed substances on δ-MnO₂.

The N element is a characteristic element in the molecular structure of MB and an element that does not exist in the δ-MnO₂ structure; for the N element, the δ-MnO₂ before and after the reaction is analyzed by XPS (X-ray photoelectron spectroscopy); as shown in Figure 7, XPS analysis found that N element was detected on the reacted δ-MnO₂, indicating that the δ-MnO₂ had adsorbed the material with N element, and the peak fitting of the N 1s peak of the mineral powder after the reaction was performed (N atoms are not directly bonded to the surface of δ-MnO₂, and the binding energy of N 1s is 399.2 eV; N atoms are directly bonded to the surface of δ-MnO₂, and the binding energy of N 1s is 401.0 eV) [32].

The results are shown in Figure 7(a) and Table 3. As the pH increases, the N content on δ-MnO₂ gradually decreases. Under the conditions of pH 2.00, 4.01, 5.92, and 8.05, the ratio of N directly adsorbed on δ-MnO₂ to N not directly adsorbed on δ-MnO₂ is roughly 1 : 2. It is known that both the structure of MB and its intermediate product contain 3 nitrogen atoms, and the hole -OH on the manganese oxygen octahedron of δ-MnO₂ has disappeared. It can be speculated that one N atom in the molecule of the adsorbed substance is adsorbed on the -OH site on the δ-MnO₂ hole, while the remaining two N atoms in the molecule do not directly contact the δ-MnO₂. Therefore, the δ-MnO₂ decolorization MB has an adsorption decolorization process, and the content of adsorbed substances gradually decreases with the increase of pH.

4.3. Removal Mechanism

Based on the above results, it is reasonable to speculate that the removal process of MB by δ-MnO₂ is as follows: Under low pH conditions, the δ-MnO₂ with a small amount of positive charge on the surface has a high redox potential, so it is strongly oxidizing, and the positively charged MB will be adsorbed on its surface, and then, oxidation reaction occurs. With the consumption of H⁺ and the release of Mn²⁺, part of MB is completely degraded into CO₂, H₂O, and other inorganic substances, and part of it has not been completely degraded. It is accompanied by the generation of intermediate products, including MB parent ion and an MB-analogous compound in which one methyl group is replaced by a proton, Azure B, Azure A, Azure C, Thionin, and other substances.

As the pH of the reaction system increases, the oxidation-reduction potential of δ-MnO₂ decreases [17, 33]; the oxidation removal rate of MB decreases significantly with the increase of pH. After the reaction, the UV-Vis band scanning spectrum of the solution can confirm that the oxidation degree of MB gradually decreases with the increase of the pH value. The oxidation of MB by δ-MnO₂ is a process that consumes H⁺, is accompanied by the conversion of high-valence manganese to Mn²⁺, and is accompanied by the formation of intermediate products. When the initial pH is 2.00, the oxidation removal rate of δ-MnO₂ to MB is as high as 98.85%. The more H⁺ consumed and Mn²⁺ released, the amount of H⁺ consumed is less than the original system.

As the initial pH increases to 4.01 and 5.53, the oxidation removal rate of MB decreases to 74.49% and 47.43%, and the H⁺ consumption and Mn²⁺ release in the reaction system gradually decrease. Then, when the initial pH is 7.35, the surface of δ-MnO₂ has a large number of negative charges, and the added positively charged dye MB quickly replaces the H⁺ in the hydroxyl group on δ-MnO₂, H⁺ is released into the solution, so that the H⁺ in the system increases rapidly, and the pH shows a downward trend. As the oxidation dye reaction progresses, after H⁺ is gradually consumed, the pH gradually increases, due to the change of pH 7.35 to H⁺. As the pH of the system increases, the surface of δ-MnO₂ becomes electronegative. Through the interaction between charges, Mn²⁺ can be adsorbed to the surface of δ-MnO₂, causing the released Mn²⁺ to be readsorbed on the surface of minerals [18, 34], so at high pH, Mn²⁺ is not detected in the system.

The results of FTIR (Figure 6) can prove the adsorption effect of δ-MnO₂ on MB. In the experiment, the concentration of the dye after the reaction is measured by using the UV spectrophotometer to measure the absorbance at 664 nm to calculate the concentration of MB. The experiment measured the adsorption and removal of MB by δ-MnO₂ as the pH increases. The rate gradually increases, but XPS (Figure 7) shows that under low pH conditions, the number of adsorbed substances is greater. From this, it can be inferred that the adsorbed substances of δ-MnO₂ are not only MB. It can be judged by the results of UV-Vis band scanning that MB produced certain intermediate products during the decolorization process, namely, Azure A, Azure B, Azure C, and Thionin. These four intermediate products are obtained by the gradual demethylation of MB. The heterocyclic ring and benzene ring in the MB structure are still undamaged, so the adsorbed substances detected by FTIR and XPS may also include intermediate products in the reaction process, and the molecular weight of these oxidized intermediate products is less than that of MB, which is easier adsorbed on the surface of δ-MnO₂. It can be inferred that as the pH of the reaction system increases, the amount of MB adsorbed on the surface of δ-MnO₂ gradually increases, but the adsorbed intermediate product decreases.

5. Conclusions

The removal of MB by δ-MnO₂ has both oxidation and adsorption mechanisms, and the change of pH significantly affects the oxidation and adsorption of MB by δ-MnO₂. We believe that the removal of MB by δ-MnO₂ should be divided into two stages: first adsorption and then oxidation. First of all, MB molecules migrate to the vicinity of the mineral surface and then diffuse to the surface of δ-MnO₂ through the boundary layer, and adsorbed on the hydroxyl active sites on the surface of δ-MnO₂ to replace the H⁺ in the hydroxyl group, and continue to diffuse into the micropores inside the adsorbent. Secondly, the adsorbed MB reacts with the high-valence manganese in δ-MnO₂, and the high-valence manganese (Mn⁴⁺/Mn³⁺) is reduced to Mn²⁺. Part of Mn²⁺ is adsorbed by manganese oxide again due to the Coulomb effect. After the adsorption is saturated, the remaining Mn²⁺ is free in the solution. At the same time, the MB oxidation reaction produces organic intermediate products and some inorganic compounds, and some intermediate products after the MB reaction can also be adsorbed on the surface of δ-MnO₂. Therefore, the research results show that δ-MnO₂ is a combined effect of oxidation and adsorption on the removal of MB.

Data Availability

The data used to support the findings of this study are included within the article.

Conflicts of Interest

The authors declared no potential conflicts of interest with respect to the research, authorship, and/or publication of this article.

Acknowledgments

The authors disclosed receipt of the following financial support for the research, authorship, and/or publication of this article: this work is financially supported by the National Natural Science Foundation of China (41867004) and Scientific Research Project of Jiangxi Provincial Education Department (GJJ160408).

References

J. E. Post, “Manganese oxide minerals: crystal structures and economic and environmental significance,” Proceedings of the National Academy of Sciences of the United States of America, vol. 96, pp. 3447–3454, 1999.
View at: Google Scholar
S. W. Donne, A. F. Hollenkamp, and B. C. Jones, “Structure, morphology and electrochemical behaviour of manganese oxides prepared by controlled decomposition of permanganate,” Journal of Power Sources, vol. 195, pp. 367–373, 2010.
View at: Google Scholar
T. W. Healy, A. P. Herring, and D. W. Fuerstenau, “The effect of crystal structure on the surface properties of a series of manganese dioxides,” Journal of Colloid & Interface Science, vol. 21, pp. 435–444, 1966.
View at: Google Scholar
J. W. Murray, “The surface chemistry of hydrous manganese dioxide,” Journal of Colloid & Interface Science, vol. 46, pp. 357–371, 1974.
View at: Google Scholar
N. Caliskan, A. R. Kul, S. Alkan, E. G. Sogut, and İ. Alacabey, “Adsorption of zinc(II) on diatomite and manganese-oxide-modified diatomite: a kinetic and equilibrium study,” Journal of Hazardous Materials, vol. 193, pp. 27–36, 2011.
View at: Google Scholar
F. X. Han, Z. L. Mei, T. W. Feng, L. Fan, and H. J. Zheng, “Adsorption and redox reactions of heavy metals on synthesized Mn oxide minerals,” Environmental Pollution, vol. 147, pp. 366–373, 2007.
View at: Google Scholar
W. Tan, F. Liu, X. Feng, Q. Huang, and X. Li, “Adsorption and redox reactions of heavy metals on Fe–Mn nodules from Chinese soils,” Journal of Colloid & Interface Science, vol. 284, pp. 600–605, 2005.
View at: Google Scholar
G. Landrot, M. Ginder-Vogel, K. Livi, J. P. Fitts, and D. L. Sparks, “Chromium(III) oxidation by three poorly crystalline manganese(IV) oxides. 2. Solid phase analyses,” Environmental Science & Technology, vol. 46, pp. 11601–11609, 2012.
View at: Google Scholar
S. Chen, S. Zhang, T. Wang et al., “Structure and properties of vanadium-doped α-MnO₂ and enhanced Pb²⁺ adsorption phenol/photocatalytic degradation,” Materials Chemistry & Physics, vol. 208, pp. 258–267, 2018.
View at: Google Scholar
Y. Wang, B. Q. Han, N. Chen et al., “Beta-MnO₂ microrods for the degradation of methyl orange under acid condition from aqueous solutions,” Research on Chemical Intermediates, vol. 43, pp. 3975–3987, 2017.
View at: Google Scholar
J. Villasenor, P. Reyes, and G. Pecchi, “Catalytic and photocatalytic ozonation of phenol on MnO₂ supported catalysts,” Catalysis Today, vol. 76, pp. 121–131, 2002.
View at: Google Scholar
M. O. Omorogie, J. O. Babalola, E. I. Unuabonah, and J. R. Gong, “Clean technology approach for the competitive binding of toxic metal ions onto MnO₂ nano-bioextractant,” Clean Technologies & Environmental Policy, vol. 18, pp. 171–184, 2016.
View at: Google Scholar
E. J. Elzinga, “Reductive transformation of birnessite by aqueous Mn(II),” Environmental Science & Technology, vol. 45, pp. 6366–6372, 2011.
View at: Google Scholar
X. Yu, C. Wei, L. Ke, Y. Hu, X. Xie, and H. Wu, “Development of organovermiculite-based adsorbent for removing anionic dye from aqueous solution,” Journal of Hazardous Materials, vol. 180, pp. 499–507, 2010.
View at: Google Scholar
J. Mei and L. Zhang, “Ultrasonic-assisted self-assembly synthesis of highly dispersed b-MnO₂ nano-branches interwoven with graphene flakes for catalytic oxidation of aromatic compounds,” RSC Advances, vol. 5, pp. 14843–14850, 2015.
View at: Google Scholar
P. C. C. Faria, J. J. M. OrfO, and M. F. R. Pereira, “Adsorption of anionic and cationic dyes on activated carbons with different surface chemistries,” Water Research, vol. 38, pp. 2043–2052, 2004.
View at: Google Scholar
M. X. Zhu, Z. Wang, S. H. Xu, and T. Li, “Decolorization of methylene blue by delta-MnO₂-coated montmorillonite complexes: emphasizing redox reactivity of Mn-oxide coatings,” Journal of Hazardous Materials, vol. 181, pp. 57–64, 2010.
View at: Google Scholar
M. X. Wang, P. Pang, L. K. Koopal, G. H. Qiu, Y. Wang, and F. Liu, “One-step synthesis of delta-MnO₂ nanoparticles using ascorbic acid and their scavenging properties to Pb(II), Zn(II) and methylene blue,” Materials Chemistry and Physics, vol. 148, pp. 1149–1156, 2014.
View at: Google Scholar
Y. X. Zhang, X. L. Guo, M. Huang, X. D. Hao, Y. Yuan, and C. Hua, “Engineering birnessite-type MnO₂ nanosheets on fiberglass for pH-dependent degradation of methylene blue,” Journal of Physics and Chemistry of Solids, vol. 83, pp. 40–46, 2015.
View at: Google Scholar
W. H. Kuan, C. Y. Chen, and C. Y. Hu, “Removal of methylene blue from water by gamma-MnO₂,” Water Science and Technology, vol. 64, pp. 899–903, 2011.
View at: Google Scholar
W. H. Kuan and Y. C. Chan, “pH-dependent mechanisms of methylene blue reacting with tunneled manganese oxide pyrolusite,” Journal of Hazardous Materials, vol. 239, pp. 152–159, 2012.
View at: Google Scholar
L. Peng, B. Liu, Q. R. Zeng et al., “Highly efficient removal of methylene blue from aqueous solution by a novel fishing-net effect of manganese oxide nano-sheets,” Clean Technologies and Environmental Policy, vol. 19, pp. 269–277, 2017.
View at: Google Scholar
R. M. Mckenzie, “The synthesis of birnessite, cryptomelane, and some other oxides and hydroxides of manganese,” Mineralogical Magazine, vol. 38, pp. 493–502, 1971.
View at: Google Scholar
R. M. Mckenzie, “The surface charge on manganese dioxides,” Soil Research, vol. 19, pp. 41–50, 1981.
View at: Google Scholar
H. Kim and N. Saito, “One-pot synthesis of purple benzene-derived MnO₂-carbon hybrids and synergistic enhancement for the removal of cationic dyes,” Scientific Reports, vol. 8, no. 4342, 2018.
View at: Google Scholar
Y. F. Wei, P. Yuan, D. Liu et al., “Activation of natural halloysite nanotubes by introducing lanthanum oxycarbonate nanoparticles via co-calcination for outstanding phosphate removal,” Chemical communications, vol. 55, pp. 2110–2113, 2019.
View at: Google Scholar
Y. F. Wei, X. J. Liang, H. H. Wu, J. M. Cen, and Y. M. Ji, “Efficient phosphate removal by dendrite-like halloysite-zinc oxide nanocomposites prepared via noncovalent hybridization,” Applied Clay Science, vol. 213, p. 106232, 2021.
View at: Google Scholar
M. Zaied, S. Peulon, N. Bellakhal, B. Desmazieres, and A. Chausse, “Studies of N-demethylation oxidative and degradation of methylene blue by thin layers of birnessite electrodeposited onto SnO₂,” Applied Catalysis B-Environmental, vol. 101, pp. 441–450, 2011.
View at: Google Scholar
R. M. Potter and G. R. Rossman, “The manganese-and iron-oxide mineralogy of desert varnish,” Nature, vol. 25, no. 1-2, pp. 79–94, 1979.
View at: Google Scholar
G. Zhao, J. Li, and X. Ren, “Highly active MnO₂ nanosheet synthesis from graphene oxide templates and their application in efficient oxidative degradation of methylene blue,” Rsc Advance, vol. 3, 2013.
View at: Google Scholar
J. Gong, J. Liu, and Z. Jiang, “A facile approach to prepare porous cup-stacked carbon nanotube with high performance in adsorption of methylene blue,” Journal of Colloid and Interface Science, vol. 445, pp. 195–204, 2015.
View at: Google Scholar
L. Y. Zhao, X. K. Wang, Y. G. Guo, N. Z. Wu, and Y. C. Xie, “Adsorption of methylene blue on the muscovite,” Acta Physico-Chimica Sinica, vol. 10, pp. 896–901, 2003.
View at: Google Scholar
H. J. Cui, H. Z. Huang, B. Yuan, and M. L. Fu, “Decolorization of RhB dye by manganese oxides: effect of crystal type and solution pH,” Geochemical Transactions, vol. 16, p. 10, 2015.
View at: Google Scholar
A. Gürses, Ç. Doğar, M. Yalçın, M. Açıkyıldız, R. Bayrak, and S. Karaca, “The adsorption kinetics of the cationic dye, methylene blue, onto clay,” Journal of Hazardous Materials, vol. 131, pp. 217–228, 2016.
View at: Google Scholar

Copyright

Copyright © 2021 Ge Yan 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.

PDF Download Citation

Download other formats

Order printed copies

Views

1320

Downloads

742

Citations

Adsorption Science & Technology

Biogeochemical Processes, Interactions, and Control of Pollutants in Soil-Plant Systems

Adsorption-Oxidation Mechanism of δ-MnO2 to Remove Methylene Blue

Abstract

1. Introduction

2. Materials and Methods

2.1. Synthesis and Characterization

2.2. Characterization

2.3. Dye Removal

2.3.1. Kinetic

2.3.2. Removal Mechanism

3. Results

3.1. Characterization of δ-MnO2

3.2. Kinetics of the Removal of MB by δ-MnO2

3.3. The Effect of pH on Removal of MB

4. Discussion

4.1. Oxidating MB by δ-MnO2

4.2. The Mechanism of Adsorption

4.3. Removal Mechanism

5. Conclusions

Data Availability

Conflicts of Interest

Acknowledgments

References

Copyright

Adsorption-Oxidation Mechanism of δ-MnO₂ to Remove Methylene Blue

3.1. Characterization of δ-MnO₂

3.2. Kinetics of the Removal of MB by δ-MnO₂

4.1. Oxidating MB by δ-MnO₂