Tunable Mn Oxidation State and Redox Potential of Birnessite Coexisting with Aqueous Mn(II) in Mildly Acidic Environments

Abstract

As the dominant manganese oxide mineral phase in terrestrial and aquatic environments, birnessite plays an important role in many biogeochemical processes. The coexistence of birnessite with aqueous Mn²⁺ is commonly found in the subsurface environments undergoing Mn redox cycling. This study investigates the change in Mn average oxidation state (AOS) of birnessite after reaction with 0.1–0.4 mM Mn²⁺ at pH 4.5–6.5, under conditions in which phase transformation of birnessite by Mn²⁺ was not detectable. The amount of Mn²⁺ uptake by birnessite and the equilibrium concentration of Mn(III) proportionally increased with the initial concentration of Mn²⁺. The Mn AOS of birnessite particles became 3.87, 3.75, 3.64, and 3.53, respectively, after reaction with 0.1, 0.2, 0.3, and 0.4 mM Mn²⁺ at pH 5.5. Oxidation potentials (E_h) of birnessite with different AOS values were estimated using the equilibrium concentrations of hydroquinone oxidized by the birnessite samples, indicating that E_h was linearly proportional to AOS. The oxidation kinetics of bisphenol A (BPA), a model organic pollutant, by birnessite suggest that the logarithms of surface area-normalized pseudo-first-order initial rate constants (log k_SA) for BPA degradation by birnessite were linearly correlated with the E_h or AOS values of birnessite with AOS greater than 3.64.

1. Introduction

Birnessite (δ-MnO₂) is a dominant Mn(III,IV)-oxide mineral, widely found in a variety of environmental settings, such as soils, sediments, marine Mn nodules, and desert varnishes [1]. The birnessite structure consists of stacked sheets of edge-sharing MnO₆ octahedra with water molecules or cations in the interlayer regions. The layers of naturally occurring birnessite commonly contain varying contents of Mn(IV) vacancies and/or Mn(III) substitutions, due to abiotic/biotic Mn(IV) reduction or Mn(II) oxidation [2,3,4]. Many studies have shown that Mn(III) on birnessite surface can be the active sites for metal sorption, contaminant oxidation, and topotactic structure transformation [2,5,6,7]. Average oxidation states (AOS) of Mn are extensively used to indicate the content of Mn(III) or vacancies in the birnessite structure. AOS of birnessite-group minerals is typically in the range of 3.0–4.0 [8,9], and can be affected by many factors, including growth conditions, solution pH, light, and redox reactions [10,11,12,13,14,15]. Moreover, naturally occurring birnessite is mainly formed via biotic oxidation of Mn(II) or from subsequent transformation of biogenic minerals, which is much faster than abiotic Mn(II) oxidation at circumneutral pH [3,16,17]. As a result, natural birnessite particles typically have poor crystallinity, large specific surface area, and varying AOS values. These unique structural and physiochemical properties endow birnessite with excellent performance and high reactivity in metal sequestration, degradation of organic pollutants, and microbial respiration in anaerobic environments.

Birnessite commonly coexists with aqueous Mn(II) as a result of various biogeochemical redox processes, such as biotic/abiotic reduction of birnessite or the biologically catalyzed oxidation of aqueous Mn(II)(Mn²⁺) [4,17,18]. Previous studies of interaction between birnessite and Mn²⁺ mainly focused on the effects of Mn²⁺ on the sorption capability of birnessite for heavy metals or on Mn(II)-induced phase transformation of birnessite under anoxic conditions [4,15,19,20]. However, the transformation studies of birnessite in the presence of Mn²⁺ were mostly conducted at pH ≥ 7, because no detectable secondary phases have been observed at lower pH values [15,20] or within a couple of days [21]. Nevertheless, it is likely that electron transfer between birnessite and sorbed Mn²⁺ impacts Mn AOS and oxidative reactivity of birnessite under mildly acidic conditions. Our recent studies showed that electron injection from sorbed Fe(II) to magnetite (Fe₃O₄) can change the structural Fe(II)/Fe(III) ratio and the reduction potential of magnetite without the formation of secondary mineral phases, the extent of which depends on solution pH, magnetite loading, and initial concentrations of aqueous Fe(II) and redox-active organic molecules [22,23]. Similarly, the interfacial electron transfer between birnessite and Mn²⁺ may induce electron injection and delocalization in Mn octahedral layers of birnessite, even though no detectable secondary phases are formed. However, how the Mn(II)-birnessite interaction impacts the AOS and redox potential of birnessite, without mineral phase transformation, under mildly acidic conditions remains unclear.

Although oxidative reactivity of birnessite-group minerals has been extensively studied using many model organic compounds or contaminants, such as phenols, anilines, and low molecular weight organic acids, most of these studies focused on how the chemical properties of the organic compounds or products, as well as solution conditions, affect the oxidation rates [8,24,25]. Relatively few studies have investigated the relationship between mineralogical properties of birnessite minerals and the oxidation rates of organic compounds. Several attempts have been made to study the effect of Mn AOS or the redox potential of manganese oxides on their oxidative reactivities with model organic compounds, such as phenolic compounds and sulfadiazine, but different manganese oxide phases (including birnessite, buserite, manganite, feitnkechtite, and cryptomelane) with different AOS values were used [7,26,27,28]. Although increasing oxidation rates of organic compounds with the increase in Mn AOS and redox potential were observed in some of these studies, the different mineral phases or synthesis methods may also affect many other properties of the manganese oxides, such as crystallinity and specific surface area, resulting in different oxidative reactivities for organic compounds. Moreover, Mn(III) center availability has been considered as an important factor controlling the oxidation rates of many organic compounds by birnessite, so birnessite with a lower Mn AOS may have more surface Mn(III) sites and correspondingly present the higher oxidative reactivities [2,7,28]. Mn AOS values of birnessite minerals can dynamically change in response to redox potential fluctuations in surrounding environments or induced by redox biogeochemical processes. It is important to study how Mn²⁺-birnessite interaction affects Mn AOS and oxidative reactivity for understanding the role of birnessite in a variety of biogeochemical processes and for developing the applications of birnessite in environmental remediation.

Here, the quantitative relationship among Mn AOS, redox potential, and oxidative reactivity of birnessite after reaction with Mn²⁺ at different concentrations under mildly acidic conditions were investigated. Under the experimental conditions of this study, the interaction of Mn²⁺ with birnessite only changed Mn AOS, without inducing phase transformation of birnessite. Hydroquinone (HQ) has been used as a chemical redox probe (CRP) to estimate the oxidation potential (E_h) of birnessite minerals after reaction with Mn²⁺ of different concentrations. The results reveal a linear relationship between AOS values of birnessite and the logarithms of the surface-area-normalized rate constants and extents of HQ oxidation. The enhanced E_h or oxidation reactivity of birnessite with the increase in AOS was tested using the oxidation experiments with a model organic pollutant, bisphenol A (BPA). The findings of this study show the tunable AOS and redox potential of birnessite by reaction with Mn²⁺ at different concentrations, as well as the quantitative correlation between oxidation rates and extents of organic compounds and AOS/E_h of birnessite. 2. Materials and Methods 2.1. Synthesis and Characterization of Birnessite

Hexagonal birnessite, i.e., c-disordered H⁺-birnessite, was synthesized according to the method previously reported by Mckenzie [29]. In brief, 32.7 mL of concentrated HCl was added dropwise to 500 mL 0.4 M boiling KMnO₄ solution using a peristaltic pump at a flow rate of 0.7 mL/min, while the suspension was vigorously stirred and heated at ~100 ℃. After the HCl solution was completely added, the suspension was heated at ~100 ℃ for 30 more minutes and then cooled to room temperature. The solid products in the suspension were collected by centrifugation and then washed with Milli-Q water three times. The resulting suspension was stored at 4 °C in the dark.

The crystal phase of the synthesized particles was identified by a PANalytical X-ray powder diffractometer (XRD, PANalytical, Almelo, The Netherlands) equipped a Cu Kα radiation (λ = 0.15406 nm). Particles after freeze-drying of the stock suspension were amounted on zero-background quartz sample holders. Diffraction patterns were scanned in the 2θ range of 5°–75° at a step rate of 0.02° 2θ·s⁻¹. The morphology and particle size of the synthesized particles were observed using a JSM-IT300 scanning electron microscope (SEM, JEOL, Tokyo, Japan) operated at an accelerating voltage of 5 kV in secondary electron mode. Specific surface area (SSA) of the synthetic particles was determined via the Brunauer-Emmett-Teller (BET) method. Measurements were carried out on an ASAP 2020 Surface Area and Porosity Analyzer (Micromeritics, Norcross, GA, USA) from Micrometer by determining the nitrogen adsorption-desorption isotherms at 77 K. X-ray photoelectron spectroscopy (XPS) measurements were carried out with the AXIS Supra X-ray photoelectron spectrometer (Kratos Analytical Ltd., Manchester, UK) to determine the Mn oxidation states in the synthesized birnessite before and after reaction with Mn²⁺ by fitting the Mn3s lines, according to the previously reported method [11,30]. All XPS spectra were analyzed using CasaXPS (Casa Software Ltd., Teignmouth, UK).

2.2. Mn(II)-Birnessite Interaction Experiments

Batch experiments were conducted to measure the time-dependent concentrations of aqueous Mn(II) and Mn(III) produced during the reactions between 200 mg/L birnessite, i.e., 1.86 mM according to the formula of Na_0.5Mn₂O₄·1.5H₂O reported in previous studies [31,32], and 0.1–0.4 mM Mn²⁺ at pH 4.5, 5.5, and 6.5, respectively. The buffer solution at pH 4.5 or 5.5 was 200 mM acetate buffer solution (NaAc-HAc) with 10 mM NaCl, and that at pH 6.5 was 20 mM MES (2-(N-morpholino) ethanesulfonic acid) buffer solution with 10 mM NaCl. All experiments were conducted in sealed containers with continuous shaking on a rotating mixer. To measure the uptake of Mn²⁺ by birnessite, a certain volume of 10 mM MnCl₂·4H₂O stock solution into 1.86 mM birnessite suspension (50 mL), resulting in the initial Mn²⁺ concentration at 0.1, 0.2, 0.3, and 0.4 mM, respectively Two-milliliter aliquots were taken out at designated time intervals using 5 mL syringes and immediately filtered through 0.22 μm syringe filters. After acidification with 2% HNO₃ (high purity-grade), the concentrations of Mn²⁺ in the filtrates were determined using inductively coupled plasma optical emission spectrometer (ICP-OES, Prodigy 7, Teledyne Leeman Labs, Mason, OH, USA). The time-dependent concentration of produced Mn(III) from the Mn(II)-birnessite interaction was measured under similar conditions, except that 50 mM sodium pyrophosphate (PP) was initially added together with MnCl₂·4H₂O to trap Mn(III). After sample aliquots (2 mL each) were taken and filtered through the 0.22 μm syringe filters, the concentration of PP-complexed Mn(III) (Mn(III)-PP) in the filtrate was calculated from the absorbance at λ = 254 nm (ε = 6562 L·mol⁻¹·cm⁻¹) [13] that was measured using a UV-vis spectrophotometer (UV-1800, Shimadzu, Kyoto, Japan). At the end of 24 h reactions, particles in the suspensions were collected by centrifugation and washed with Milli-Q water three times. After freeze-drying, the resulting particles were analyzed by XPS to determine Mn AOS.

2.3. Redox Potential Determination of Birnessite with Different AOS Values

To study the relationship between Mn AOS of birnessite and oxidation rates/extents of the chemical redox probe, hydroquinone (HQ), batch experiments were performed in 100 mL closed serum bottles with 1.82 mM HQ and 1.86 mM birnessite particles after reaction with Mn²⁺ at different concentrations under the conditions described above. In this process, 200 mM NaAc-HAc buffer solution with 10 mM NaCl was used to maintain the pH at 5.5. After the birnessite suspension was sonicated for 5 min, 5 mL of 9.08 mM HQ stock solution was spiked into the suspension to initiate the oxidation experiment. Sample aliquots (3 mL) were taken and filtered through 0.22 μm syringe filters. In the experimental suspensions, HQ was oxidized to benzoquinone (BQ) by birnessite according to the following Equations [24]:

≡MnOH+HQ_k1⇔_k−1≡MnOH+_H2O

≡MnQ→_k2Mnaq2++BQ

The concentrations of HQ and BQ in the filtrates were determined using the UV-vis spectrophotometer according to the previously reported method [33]. Redox potential of the suspension at equilibrium (E_h) was estimated from the extent of HQ oxidation according to the following equation [34]:

_Eh=_Eh0+RT2Fln([BQ]^[H+]2[HQ])

where_Eh0 is the standard redox potential of HQ (−0.699 V) [34]; R is the gas constant; T is the temperature; F is the Faraday constant; [BQ], [HQ], and [H⁺] are the concentrations of benzoquinone, hydroquinone and H⁺, respectively. All experiments were performed at least in triplicate.

2.4. Oxidation of Model Organic Molecules by Birnessite with Different AOS Values

To further study the oxidation activity of birnessite particles with different AOS values for the degradation of organic pollutants, oxidation experiments of 131.4 μM BPA by 2.80 mM birnessite at pH 5.5 were conducted under the similar conditions of HQ oxidation. BPA concentrations were measured over the course of the reaction by sampling an aliquot (3 mL) of the suspension and filtering it through a 0.22 μm syringe filter. The absorbance at λ = 276 nm was measured using the UV-vis spectrophotometer [35,36].

3. Results 3.1. Characteristics of Synthetic Birnessite

The XRD pattern (Figure 1a) of the synthetic sample shows that only birnessite phase is present. The four diffraction peaks at 2θ = 12.4°, 24.9°, 37°, and 65.5° confirm the formation of birnessite with hexagonal layer symmetry. The representative SEM image (Figure 1b) shows that the synthetic birnessite particles present platelet morphology with a diameter of ~300–400 nm and assemble to form flower-like aggregates. The BET specific surface area of the synthetic birnessite is 45.5 m²/g, which is consistent with the small thickness of birnessite platelets. These characteristics agree well with the previously reported properties of birnessite synthesized via reductive precipitation of KMnO₄ by HCl [37].

3.2. Effect of Mn²⁺–Birnessite Interaction on AOS of Birnessite

3.2.1. Mn²⁺ Uptake and Mn(III) Formation

Figure 2a shows the uptake profiles of 0–0.4 mM aqueous Mn²⁺ on 1.86 mM birnessite at pH 5.5. Similar trends were observed in the profiles with different concentrations of added Mn²⁺, which contain spontaneous adsorption at the initial stage, followed by gradual decrease in adsorption rates, until a plateau is reached. As shown in Figure S1, the uptake profiles of 0–0.4 mM Mn²⁺ on 1.86 mM birnessite at pH 4.5 and pH 6.5, respectively, present the similar trend in the change in Mn²⁺ concentration versus time. Nearly complete uptake of 0–0.4 mM Mn²⁺ by birnessite was observed at pH 4.5–6.5, except that the extent of Mn²⁺ uptake in the experiments with 0.4 mM Mn²⁺ was slightly lower at the elevated solution pH (Figure 2c). Because >95% of the added Mn²⁺ can be rapidly sorbed onto the birnessite surface within ~2 h, it is feasible to adjust the amount of surface-associated Mn²⁺ and electrons injection from sorbed Mn²⁺ to structural Mn(IV) in birnessite via changing the initial concentration of Mn²⁺ in solution.

The rapid uptake of Mn²⁺ by birnessite has been attributed to the high adsorption capability of the Mn(IV) vacancies in birnessite structure to divalent metals [38], autocatalytic oxidation of surface-associated Mn(II) by O₂ [39], or electron injection from sorbed Mn(II) to structural Mn(IV) [4]. The extent of structural changes in birnessite from the Mn²⁺–birnessite interaction is highly dependent on experimental conditions, such as solution pH, initial Mn²⁺ concentration, and reaction time. We measured the time-dependent concentration of Mn(III) throughout the reaction of 1.86 mM birnessite with 0–0.4 mM aqueous Mn²⁺ at pH 4.5–6.5 using the Mn(III)-pyrophosphate colorimetric method. As shown in Figure 2b and S1, Mn(III) rapidly formed upon spiking the Mn²⁺ stock solution into the birnessite suspension, and the Mn(III) concentration gradually increased over time until reaching a steady plateau state. The trend in the profiles of Mn(III) production was very similar to that of Mn(II) uptake, indicating that the formation of Mn(III) over time was closely related to Mn(II) uptake by birnessite. Moreover, the equilibrium Mn(III) concentration linearly increased as the initial Mn²⁺ concentration increased (Figure 2d). Pyrophosphate can complex with both structural Mn(III) in birnessite and Mn(III) released from birnessite or associated with birnessite surface. In order to check whether the increase in measured Mn(III) concentration was due to the increased content of structural Mn(III), Mn AOS values of end-products after 24 h interaction between birnessite and aqueous Mn²⁺ were measured using the XPS Mn 3s peak separation values. The XPS results will be presented and discussed in detail below.

It is worth mentioning that, although the amounts of Mn²⁺ uptake by birnessite at pH 4.5–6.5 were similar at a fixed initial Mn²⁺ concentration, the concentration of Mn(III) produced at pH 6.5 was obviously lower than the corresponding values at pH 4.5 and 5.5. The results suggest that the change in solution pH within the range of this study would not significantly affect Mn²⁺ uptake by birnessite but probably influence the formation of Mn(III) from electron injection from sorbed Mn²⁺ to structural Mn(IV) in birnessite. Moreover, when pH (pH = 4.5 or 5.5) and initial Mn²⁺ concentration were fixed, the concentration of produced Mn(III) was about two times that of Mn²⁺ uptake by birnessite at steady state. The ratio is consistent with the theoretical expectation of charge balance, i.e., one mole of Mn(II) reacting with one mole of Mn(IV) leads to the production of two moles of Mn(III).

3.2.2. AOS of Birnessite after Reaction with Aqueous Mn(II)

Although Mn AOS of birnessite has been extensively measured using redox titration or X-ray absorption near-edge spectroscopy (XANES) [40], XPS can provide information about AOS changes specifically on the surface or in the near-surface region of birnessite after reaction with aqueous Mn²⁺ at a lower concentration range. Figure 3a shows the survey scan of the as-synthesized birnessite. In addition to the strong signals of Mn and O, the weak signals of C and K can be assigned to very small amounts of surface contaminants, probably resulting from the exposure to ambient air and residual KMnO₄. Compared to the intensities of Mn and O peaks, the signals of C and K are much weaker, so the interference of the surface contaminants on the Mn²⁺–birnessite interaction is negligible.

The Mn 3s peaks of birnessite before and after reaction with 0–0.4 mM Mn²⁺ at pH 5.5 are compared in Figure 3b. This peak consists of two, multiplet split components that are caused by the coupling of non-ionized 3s electron with 3d valence-band electrons. Due to the relatively low proportions of Mn(II) and Mn(III) in birnessite, deconvolution of Mn 3s curve was not employed to determine Mn AOS in this study. According to the previously reported linear correlation between the Mn AOS of birnessite and the multiplet splitting of the Mn 3s line [30,41], the Mn AOS of birnessite can be estimated from the magnitude of the peak splitting according to the following Equation [42,43]:

AOS = 8.95 − 1.13ΔE_s(eV)

where ΔE_s represents the multiplet spitting of the Mn 3s line, which is the energy difference between the main peak and its satellite.

As shown in Figure 3c, the birnessite particles after reaction with 0.1, 0.2, 0.3, and 0.4 mM Mn²⁺, respectively, have the corresponding AOS = 3.87, 3.75, 3.64, and 3.53. The more Mn²⁺ added leads to a lower AOS value in birnessite. The results confirm that Mn²⁺ sorbed on the birnessite surface injected electrons into structural Mn(IV) and decreased Mn AOS. Moreover, the linear correlation between the concentration of added Mn²⁺ and AOS value or the concentration of produced Mn(III) suggests that the AOS or Mn(III) content of birnessite can be adjusted via the reaction with aqueous Mn²⁺ at different concentrations under mildly acidic conditions.

3.3. E_h of Birnessite with Different AOS Values Determined from HQ Oxidation

To explore the quantitative correlation between AOS values and oxidation rates of organic compounds by birnessite, we conducted the oxidation experiments of 1.82 mM HQ with 1.86 mM birnessite with different AOS values at pH 5.5. Figure 4 shows that, in all experiments, the HQ concentration exponentially decreased over time, whereas the corresponding BQ concentration rapidly increased as a function of time. After about 20 h, the concentration of both HQ and BQ reached a plateau. Moreover, the spontaneous formation of BQ was observed along with the rapid decrease in HQ. The nearly synchronous changes in the concentrations of HQ and BQ with time indicate that HQ adsorption on birnessite surface could not significantly contribute to the removal of HQ by birnessite under the conditions of this study. Moreover, the negligible sorption of HQ to birnessite and the rapid redox reaction between them make HQ an appropriate thermodynamic and kinetic chemical reactivity probes (CRPs) for birnessite with different AOS values [44].

In order to quantify the correlation between AOS values and redox potentials of birnessite, the oxidation experiments of 2.73 mM HQ by 1.86 mM birnessite with different AOS values were conducted at pH 5.5. As shown in Figure S2, the extent of HQ oxidation highly depends on Mn AOS of birnessite at the same initial HQ concentration and birnessite loading. At pH 5.5, as the Mn AOS of birnessite decreased from 3.98 to 3.53, the concentration of HQ at equilibrium increased from 1.25 ± 0.01 to 1.39 ± 0.03 mM, but that of BQ decreased from 1.88 ± 0.01 to 1.73 ± 0.00 (Figure S2). A similar trend was observed at pH 4.5 and 6.5 (Figure S2). Moreover, with the increase in pH from 4.5 to 6.5, the extents of HQ oxidation and BQ production decreased significantly. The black color of particle suspension at equilibrium suggests that birnessite was not completely reduced by HQ at equilibrium, and thus the oxidation potential (E_h) of birnessite can be estimated from the concentrations of HQ and BQ at equilibrium, according to the method described in Section 2.3. As shown in Figure 5a and Figure S3, the calculated E_h of birnessite is linearly proportional to its Mn AOS at pH 4.5–6.5. Moreover, the E_h value of birnessite at pH 5.5 determined from the thermodynamic data of HQ oxidation in this study was 376–379 mV, which falls into the E_h range of birnessite previously reported [45]. For birnessite with a fixed AOS value, the observed E_h value obviously increased with the decrease in pH, suggesting an increasing oxidative reactivity of birnessite under acidic conditions. This pH dependence has been widely observed in oxidation of nearly all model compounds by manganese oxides, which can be attributed to the promoted sorption and electron injection of organic molecule to the birnessite surface [46,47].

The oxidation rates for HQ follow pseudo-first order kinetics at the initial stage of the reactions, when the properties of birnessite surface dominates reaction rates. As the reaction proceeds, accumulation of products on birnessite surface or changes in the structure or reactive site density of the birnessite surface would lead to different reaction orders or decreasing oxidation rates. To study the relationship between Mn AOS of birnessite and rates of HQ oxidation, we fitted the kinetic data during the first 13.3% of the reaction using a pseudo-first-order kinetic model to obtain surface-area normalized oxidation rate constants (k_SA) of HQ by birnessite with different AOS values (Figure 5b). As AOS increased from 3.53 to 3.98, k_SA proportionally increased from 0.011 to 0.016 min⁻¹ L m⁻² (Figure S4). Moreover, a linear relationship between the logarithms of k_SA and E_h values has been observed (Figure 5b), suggesting that the rate-limiting step is electron transfer from HQ to birnessite. The decreased AOS by Mn²⁺–birnessite interaction can significantly lower E_h and interfacial electron transfer capability of birnessite, leading to the decreased extent and reaction rates of HQ oxidation by birnessite.

3.4. Degredation of BPA by Birnessite with Different AOS Values

One promising application of birnessite is to remove organic contaminants in natural environments [8]. Understanding how the Mn²⁺–birnessite interactions affect the oxidative reactivity of birnessite for contaminant degradation is critical to predict the long-term efficiency of birnessite for contaminants. Here, BPA was selected as a model contaminant to investigate the relationship between Mn AOS of birnessite and its capability in BPA attenuation. Figure 6a shows the kinetic profiles of BPA degradation (the initial BPA concentration = 131.4 μM) by 2.80 mM birnessite with different AOS values at pH 5.5. In all experiments, the BPA concentration rapidly decreased at the initial stage, and then the removal rate gradually decreased with time. A good linear correlation between the logarithm of the surface area-normalized pseudo-first-order initial rate constants (log k_SA) of BPA oxidation and birnessite AOS was observed (Figure 6b). As AOS decreased from 3.98 to 3.53, the corresponding log k_SA decreased from −1.845 to −2.973 min⁻¹ L m⁻².

Different from HQ, BPA can be oxidized by birnessite into multiple intermediates and products [48], so the estimation of E_h from thermodynamic data is not applicable for the oxidation experiments with BPA. Instead, we compared removal efficiency of BPA at the end of two-hour reactions with different birnessite samples (Figure 6c). As the AOS value of birnessite decreased from 3.98 to 3.53, the percentage of BPA removal by birnessite decreased from 98% to 56%, suggesting that the efficiency of BPA removal also highly depends on Mn AOS of birnessite. The similar inhibited capacity of birnessite for BPA removal was observed in the previous study of BPA oxidation by birnessite with Mn²⁺ as a coexisting metal ion [48]. However, in the experiments with both Mn²⁺ and birnessite, the competitive binding of Mn²⁺ onto birnessite surface could also suppress complexation of BPA with reactive surface sites on birnessite, in addition to the decreased E_h of birnessite. In this study, after the reactions with Mn²⁺ at different concentrations, birnessite particles were collected and repeatedly washed to remove excess Mn²⁺ sorbed on the mineral surface. The observed changes in k_SA and efficiency of BPA removal are mainly related to the inhibited oxidative reactivity of birnessite, not the competitive binding effect of Mn²⁺.

4. Discussion 4.1. Tunable Mn AOS and E_h of Birnessite by Reaction with Aqueous Mn²⁺

It has been well recognized that Mn²⁺–birnessite interaction may induce birnessite transformation into different secondary mineral phases, but the kinetics and extent of the transformation highly depend on pH and the ratio of Mn²⁺ to birnessite [4,49]. In this study, no peaks of secondary mineral phases were observed in the XRD pattern of 1.86 mM birnessite after the 24 h-reaction with 0.4 mM Mn²⁺ at pH 5.5 (data not shown). The representative SEM images of birnessite after reactions with 0.1–0.4 mM Mn²⁺ at pH 5.5 (Figure S5) show that the particle size and morphology remain similar under all experimental conditions. These results imply that no mineralogical transformation of birnessite after reaction with aqueous Mn²⁺ under the conditions of this study occurs. It agrees well with the results previously reported by Lefkowitz et al. and Hinkle et al. that no phase transformation of birnessite was induced by aqueous Mn²⁺ at pH < 7 [21,41]. Generally, high ratios of aqueous Mn(II) to structural Mn(IV) in birnessite are needed to induce extensive Mn(IV) reduction and phase transformation of birnessite [4]. As the concentration of aqueous Mn(II) decreased, the time required to form new mineral phases from Mn(II)–birnessite interaction significantly increased [4,49]. The added Mn²⁺ in this study was at a low concentration range, which might only increase the content of structural Mn(III) to a certain extent and disrupt the stacking order of birnessite. Correspondingly, the bulk birnessite structure probably remained intact during the course of the reactions [19].

Although no detectable secondary mineral phases were formed, the interaction of 1.86 mM birnessite with 0.1–0.4 mM Mn²⁺ at pH 4.5–6.5 obviously decreased Mn AOS of birnessite. It can be attributed to Mn(II) incorporation into vacant sites or electron transfer between sorbed Mn(II) and structural Mn(IV) in birnessite, resulting in increased contents of Mn(III) and decreased Mn AOS [21]. The increasing concentration of Mn(III) upon exposure of birnessite to Mn²⁺ (Figure 2b) also confirmed the production of Mn(III) from Mn(II)-Mn(IV) comproportionation reaction. Moreover, the equilibrium concentration of Mn(III) and AOS value proportional increased with the increase in the initial Mn²⁺ concentration (Figure 2). Adding more Mn²⁺ resulted in more sorbed Mn(II) on birnessite surface (Figure 2c) and promoted the reduction of structural Mn(IV). On the other hand, increasing the initial concentration of aqueous Mn²⁺ lowered reduction potential of the solution and promoted electron injection from the solution to the solid. These results indicate that the Mn AOS of birnessite can be changed as the concentration of coexisting Mn²⁺ increases in surrounding environments.

However, it is worth mentioning that the AOS values tuned by the Mn²⁺–birnessite interaction is within a range. Mn²⁺ at high concentrations may induce phase transformation of birnessite. In that case, the change in Mn AOS is dependent not only on electron transfer at the Mn²⁺–birnessite interface but also on the crystal structure of secondary mineral phases. Moreover, as AOS decreased, redox potential of birnessite correspondingly decreased. When the AOS value is sufficiently low, the difference in the redox potentials across the solid–solution interface can be not enough to drive electron injection from sorbed Mn(II) to birnessite, leading to the limited AOS range adjusted by aqueous Mn²⁺. 4.2. A Linear Correlation between Rate Constants/E_h and AOS of Birnessite

Figure 5b shows that the E_h values of birnessite estimated from the equilibrium concentrations of HQ/BQ are linearly proportional to the Mn AOS values of birnessite. Although many attempts have been made to investigate how the Mn AOS values of manganese oxide minerals impact their oxidative reactivity or adsorption capability to heavy metals, different MnO₂ mineral phases or the particles prepared via different synthetic methods were used to obtain MnO₂ particles with a range of AOS values [27]. In addition to different AOS values, these minerals may also have distinct physicochemical properties that are likely to affect their oxidative reactivity. Thus, no quantitative correlations between AOS and E_h have been reported in the previous studies. In this study, only the AOS values were changed by the reactions of birnessite with aqueous Mn²⁺ of different concentrations at pH 4.5–6.5, and the particle size and morphology remained similar (Figure S5). Based on the thermodynamic data of HQ oxidation by birnessite samples with different AOS values, we developed a linear correlation between AOS and E_h, which provides a facile way to estimate E_h of birnessite via measuring its Mn AOS. On the other hand, coexistence of birnessite with aqueous Mn²⁺ in low concentrations is ubiquitous in various environmental settings with active manganese cycling [4,21,50]. The linear correlation between the concentration of coexisting Mn²⁺ and AOS/E_h of birnessite allows us to estimate E_h or oxidative reactivity of birnessite from the Mn²⁺ concentration in natural environment.

Figure 5 and Figure 6b show that logk_SA is linearly proportional to E_h/AOS in the oxidation experiments of either HQ or BPA by the birnessite samples with AOS = 3.64–3.98. The linear correlation between logk_SA and E_h/AOS suggests that the rate-determining step of HQ or BPA oxidation by birnessite is electron transfer from organic cmpounds to birnssite, not the diffusion of organic compounds into the boundary layer to form a surface complex. At the initial stage, the E_h/AOS value of birnessite controls the rate of interfacial electron transfer between sorbed Mn(II) and birnessite, so logk_SA was positively proportional to the E_h/AOS value of birnessite. This observed trend agrees well with the results that the presence of aqueous Mn²⁺ suppresses the efficiency of manganese oxide in removing BPA [48]. However, Huang et al. reported that the pseudo-first-order rate constants (k) for BPA oxidation by a range of manganese oxide, including δ-MnO₂, hollandite (α-MnO₂), pyrolusite (β-MnO₂), ramsdellite (γ-MnO₂), and manganite (γ-MnOOH), is proportional to surface Mn(III) content but negatively correlated with Mn AOS values [7]. The opposite trend of k vs. AOS, compared to our findings, might be attributed to the different specific surface area, crystal structure, or surface Mn(III) density of the different manganese oxide mineral phases. It is worth mentioning that logk_SA of birnessite with the lowest AOS (3.53) and E_h (376.4 mV) was similar to that of the sample with AOS = 3.64 in the experiments with either HQ or BPA, suggesting logk_SA did not decrease further with the decrease in AOS or E_h in this case (Figure 5b and Figure 6b). The non-linear correlation at the lowest AOS/E_h can be attributed to a change in the rate-limiting step or reaching a minimal rate constant. These findings quantitatively describe the range of AOS and E_h of birnessite adjusted by the Mn²⁺–birnessite interaction, as well as the correlation between the AOS/E_h values of birnessite and oxidation rate constants of model organic compounds by birnessite.

5. Conclusions

This study presents that the average Mn oxidation state (AOS) of birnessite can be tuned by changing the concentration of coexisting Mn²⁺, without detectable mineral phase transformation, under mildly acidic environments. The higher Mn²⁺ concentration and lower solution pH facilitates to lower the Mn AOS of birnessite. Using the well-defined chemical redox probe, HQ, we revealed that the oxidation potential (E_h) of birnessite is proportion to its Mn AOS. A good linear correlation between the logarithms of the surface area-normalized pseudo-first-order initial rate constants (log k_SA) of BPA oxidation and AOS values of birnessite suggests that the degradation rate of BPA at the initial stage is determined by the capability of birnessite to transfer electrons with surface-complexed organic compounds. The findings of this study suggest that the AOS and oxidative reactivity of birnessite in natural environments may vary in a range, when it is exposed to aqueous Mn²⁺ resulting from many geochemical processes, such as upward diffusion of Mn(II) across oxic/anoxic interfaces in sediments and water columns [51,52]. The quantitative correlations among Mn²⁺/birnessite ratio, Mn AOS, E_h of birnessite, and oxidation rates/extents of organic contaminants by birnessite that are developed in this study can be helpful to predict the efficiency of manganese oxide for contaminant degradation and to develop its applications for environmental treatments.

Figure 1.(a) The XRD pattern of synthetic particles show the characteristic peaks of hexagonal birnessite (JCPDS No.43-1456); (b) representative SEM image of the synthetic birnessite.

Figure 2. Concentration changes in Mn2+ (ΔMn2+) (a) and Mn(III) production (b) as a function of time in the uptake experiments of 0-0.4 mM aqueous Mn2+ onto 1.86 mM birnessite at pH 5.5; The extent of Mn2+ uptake (c) and Mn(III) production (d) as a function of initial Mn2+ concentrations at pH 4.5-6.5. Error bars indicate standard deviation from three independent experiments.

Figure 3.(a) XPS survey scan for the as-synthesized birnessite particles; (b) Mn 3s spectra of birnessite before (black) and after reaction with 0.1 mM (red), 0.2 mM (blue), 0.3 mM (green), and 0.4 mM (purple) Mn2+, respectively, at pH 5.5; (c) Mn average oxidation state (AOS) of birnessite after reaction with 0-0.4 mM Mn2+ at pH 5.5.

Figure 4. Time-dependent concentrations of hydroquinone (HQ) (a) and benzoquinone (BQ) (b) in the oxidation experiments of 1.82 mM HQ by 1.86 mM birnessite with AOS = 3.98 (black), 3.87 (red), 3.75 (blue), 3.64 (purple), and 3.53 (green), respectively, at pH 5.5. Error bars indicate standard deviation from three independent experiments.

Figure 5.(a) Oxidation potentials (Eh) of birnessite, determined from the concentrations of HQ and BQ at equilibrium, as a function of Mn AOS of birnessite; (b) logarithms of surface area-normalized pseudo-first-order initial rate constants (log kSA) for HQ oxidation by birnessite versus the calculated Eh values shown in Figure 5a. Error bars indicate standard deviation from three independent experiments.

Figure 6.(a) Time-dependent concentrations of BPA in the oxidation experiments of 131.4 μM BPA by 2.80 mM birnessite with different AOS values at pH 5.5; (b) surface area-normalized pseudo-first-order initial rate constants (log kSA) of BPA oxidation as a function of Mn AOS of birnessite; (c) percentages of BPA removal by birnessite versus its Mn AOS at the end of the 2 h reactions.

Supplementary Materials

The following are available online at https://www.mdpi.com/2075-163X/10/8/690/s1. Figure S1: Concentration of Mn2+ uptake and Mn(III) production; Figure S2: Concentrations of HQ and BQ at equilibrium; Figure S3: Relationship between Eh and Mn AOS; Figure S4: Relationship between kSA and Mn AOS; Figure S5: SEM images of birnessite particles.

Author Contributions

Conceptualization, J.L.; methodology, Q.G. and A.S.; validation, J.L., B.Z. and Q.G.; formal analysis, Q.G., Y.Z. and A.S.; investigation, Q.G. and A.S.; resources, J.L. and B.Z.; data curation, Q.G.; writing-original draft preparation, J.L., Y.Z. and A.S.; writing-review and editing, J.L. and A.S.; supervision, J.L. and B.Z.; project administration, J.L. and B.Z.; funding acquisition, J.L. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by National Natural Science Foundation of China, grant number 91751105, 41820104003, and 41972318.

Acknowledgments

We acknowledge the support from National Natural Science Foundation of China (91751105, 41820104003, and 41972318) and the use of facilities within Beijing Key Laboratory of Mineral Environmental Function and The Key Laboratory of Water and Sediment Sciences at Peking University.

Conflicts of Interest

The authors declare no conflict of interest.

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