- Research Article
- Open Access
Catalytic oxidation of arsenite and reaction pathways on the surface of CuO nanoparticles at a wide range of pHs
Geochemical Transactions volume 19, Article number: 12 (2018)
Recently, the wide application of CuO nanoparticles (NPs) in engineering field inevitably leads to its release into various geologic settings, which has aroused great concern about the geochemical behaviors of CuO NPs due to its high surface reactivity and impact on the fate of co-existing contaminants. However, the redox transformation of pollutants mediated by CuO NPs and the underlying mechanism still remain poorly understood. Here, we studied the interaction of CuO NPs with As(III), and explored the reaction pathways using batch experiments and multiple spectroscopic techniques. The results of in situ quick scanning X-ray absorption spectroscopy (Q-XAS) analysis verified that CuO NPs is capable of catalytically oxidize As(III) under dark conditions efficiently at a wide range of pHs. As(III) was firstly adsorbed on CuO NPs surface and then gradually oxidized to As(V) with dissolved O2 as the terminal electron acceptor. As(III) adsorption increased to the maximum at a pH close to PZC of CuO NPs (~ pH 9.2), and then sharply decreased with increasing pH, while the oxidation capacity monotonically increased with pH. X-ray photoelectron spectroscopy and electron paramagnetic resonance characterization of samples from batch experiments indicated that two pathways may be involved in As(III) catalytic oxidation: (1) direct electron transfer from As(III) to Cu(II), followed by concomitant re-oxidation of the produced Cu(I) by dissolved O2 back to Cu(II) on CuO NPs surface, and (2) As(III) oxidation by reactive oxygen species (ROS) produced from the above Cu(I) oxygenation process. These observations facilitate a better understanding of the surface catalytic property of CuO NPs and its interaction with As(III) and other elements with variable valence in geochemical environments.
Compared with its micro or bulk counterparts, CuO nanoparticles (NPs) possesses better optical, semiconductive and surface reactive properties, and is thus widely used for the production of ceramics, glass and pigments, catalysts, battery anodes, and antimicrobial agents [1,2,3,4,5]. Due to the increasing application of CuO NPs in industrial fields, its release and geochemical behaviors in the environment have aroused great concern [6,7,8,9]. Its potential toxicity to the organisms has been studied in detail [10,11,12,13,14]. Apart from the direct biotic effects, CuO NPs might also impact the mobility, transformation and toxicity of the co-existing contaminants through (de)sorption, redox and catalytic reactions [15,16,17]. However, little is known about the interaction of CuO NPs with redox-sensitive contaminants and the underlying reaction mechanism.
Arsenic (As) is the most common heavy metal in natural waters primarily in the forms of inorganic arsenate [As(V)] and arsenite [As(III)] . Redox processes on the surface of oxide minerals largely determine the speciation of As [19,20,21]. Compared with As(V), As(III) has higher toxicity, solubility and mobility .
CuO NPs is an excellent adsorbent to remove As(III) from water due to its large specific surface area and high point of zero charge (PZC) [17, 23,24,25]. In addition, X-ray photoelectron spectroscopy (XPS) analysis suggested that As(III) could be oxidized on CuO NPs surface, which remarkably enhances the immobility of As in the form of As(V) [17, 24]. A previous study has proposed the direct electron transfer from CuO NPs to As(III), which leads to As(III) oxidation . Given that XPS measurement is performed under a high vacuum condition, more solid evidences are needed to verify As(III) oxidation on the surface of CuO NPs.
Furthermore, it has been reported that reactive oxygen species (ROS) is involved in the oxidation pathway of organic matter [26,27,28]. For example, remarkable amounts of Cu+/Cu2+ and H2O2 were formed in zero-valent copper (ZVC) acidic system due to the corrosive dissolution of ZVC and the concurrent reduction of oxygen, which lead to highly efficient oxidation of diethyl phthalate under aerobic atmosphere condition . In addition, a synergistic effect of Fe(II) and copper oxide (CuO) was observed on the degradation of acetaminophen in the presence of O2, and the resulting Cu(I) significantly accelerated the destruction of acetaminophen by serving as an electron-mediator between the adsorbed Fe(II) and O2 to produce ROS . Therefore, it is possible that ROS might be produced through the activation of O2 on the surface of CuO NPs, which leads to the catalytic oxidation of As(III).
Thus, the objectives of this study are to (i) in situ confirm whether As(III) oxidation occurs on the surface of CuO NPs under dark condition; (ii) determine the effects of geochemical parameters [such as pH, As(III) concentration and O2] on As(III) adsorption and oxidation by CuO NPs; (iii) elucidate the adsorption and oxidation pathways of As(III) on the surface of CuO NPs at a wide range of pH values under dark condition. To achieve these objectives, batch experiments and spectroscopic analysis were performed. Time-resolved quick scanning X-ray absorption spectroscopy (Q-XAS) and electron paramagnetic resonance (EPR) spectroscopy were used to in situ measure the species of As and ROS, respectively. XPS spectroscopy was also used to determine the changes in oxidation state of Cu and As on the surface of CuO NPs after the reaction.
Preparation and characterization of CuO NPs
CuO NPs was prepared via a previously reported method [5, 29]. The synthesized CuO NPs contained no impurity phases as examined by powder X-ray diffraction (PXRD), Fourier-transformed infrared (FTIR) spectroscopy and transmission electron microscopy (TEM) analyses. The specific surface area was determined by Brunauer–Emmett–Teller (BET) N2 adsorption method. Additional details of analytical procedures and characterization results are provided in Additional file 1: Figures S1, S2, S5.
As(III) adsorption and oxidation kinetics
The adsorption-oxidation experiments were conducted by the reaction of 0.2 g CuO NPs with 200 mL 10 mg L−1 As(III) at pH 6, 9, and 11, respectively. The background electrolyte was 0.01 M NaCl solution. The CuO NPs suspensions were agitated by magnetic stirring at 10 Hz. Solution pH was measured using a pH meter (FE20, Mettler-Toledo) and manually adjusted to desired pH values ± 0.1 using 0.1 M HCl and 0.1 M NaOH. To examine the effect of dissolved oxygen (O2) on the oxidation of As(III), the reaction solution was purged by N2 before and during the reaction. At the selected reaction time, 5 mL suspension was filtered through 0.22 μm Millipore membrane to analyze the concentrations of As(III) and As(V) in the supernatant. The wet solids on the membrane were dissolved by 1 mL 1 M HCl to analyze the amount of As(III) and As(V) adsorbed onto CuO NPs surface. Another 5 mL suspension was directly dissolved by 1 M HCl (1 mL) to analyze the total amount of As(III) and As(V) in the suspension. All experiments were performed in triplicates. The As(V) concentration was measured by the molybdene blue method . The total As was determined by hydrate generation atomic fluorescence spectrometry (HG-AFS) (AFS-230E) . Additionally, the volume of 0.1 M NaOH consumed in open system and N2 system at pH 11 was recorded by automatic titrator (Metrohm 907 Titrando). All As(III) adsorption and oxidation experiments were carried out in reactors covered with aluminum foil to avoid the effect of light.
Effect of pH and initial As(III) concentration on As(III) adsorption and oxidation
To investigate the effect of pH values on the species distributions of As(III) and As(V) in solution and on CuO NPs surface, As(III) adsorption and oxidation were evaluated at pH 5, 6, 7, 8, 9, 10 and 11 by adjusting to the desired pH values ± 0.1 using 0.1 M HCl and 0.1 M NaOH. The experiments were carried out in 50-mL polyethylene centrifuge tubes by mixing 0.025 g of CuO NPs with 25 mL of 0.01 M NaCl containing fresh 10 mg L−1 As(III). To investigate the effect of initial As(III) concentration on As(III) adsorption and oxidation, the experiments were performed at initial As(III) concentrations ranging from 0.5 to 80 mg L−1 at pH 8 and 11. The reaction suspensions were equilibrated by shaking at 200 rpm and at 25 °C for 48 h. During the reaction, the pH of each batch sample was adjusted to the designed pH ± 0.05 at 1, 6, 12, 24, 36 and 48 h, respectively. After 48 h of reaction, the species distributions of As(III) and As(V) in solution and on CuO NPs surface were analyzed with the same procedures as described in “As(III) adsorption and oxidation kinetics”.
Quick Scanning K-edge X-ray absorption spectroscopy (Q-XAS) of As
Q-XAS was used to in situ investigate the changes in oxidation state of As with increasing reaction time. The Q-XAS spectra were measured at room temperature on the 1W2Bbeamline at the Beijing Synchrotron Radiation Facility(BSRF). Considering the detect limitations (≥ 100 mg L−1 for As) of Lytle prober, higher concentrations of AS(III) (150 mg L−1) and CuO NPs (5 g L−1) were used for the in situ Q-XAS measurement. The reaction was performed in 50-mL polypropylene reaction vessels (see Additional file 1: Scheme S1), into which a 1 × 3 cm slit was cut and sealed with Kapton tape, backed with Kapton film to prevent the interaction between the tape and suspension. The As K-edge XAS spectra was collected immediately when As(III) solution was added into the suspension. The measurement time for each XAS spectrum is 1 min and the total time for the in situ XAS experiment is 8 h. Additional experimental details are described in Additional file 1: S3.
X-ray photoelectron spectroscopic (XPS) analysis
To determine the oxidation state of As and Cu on the surface of CuO NPs, the samples prepared from the reaction of 0.05 g CuO with 50 mL of 10 mg L−1 As(III) for 12 h were measured with XPS using a monochromatic Al Kα X-ray source (VG Multilab 2000 X-ray photoelectron spectrometer). The scans were carried out in an energy range of 1100–5 eV to obtain XPS spectra for C1 s, Cu 2p, and As 3d. The position of binding energy was corrected by fixing the C1 s peak at 284.6 eV using the Advantage v6.5 software.
Electron paramagnetic resonance (EPR) spectroscopy
For the EPR experiment, 50 mL reaction suspension was prepared to contain 1 g L−1 CuO NPs and 10 mg L−1 As(III) at pH 11 over 2 h under stirring. At the selected time, 3 aliquots of 2 mL suspension were sampled for the detection of ROS speciation. The detection methods and procedures for different ROS species are described in Additional file 1: S4.
Results and discussion
As(III) adsorption and oxidation kinetics
Adsorption and oxidation of As(III) occurred while the rate of adsorption was relatively higher at the initial reaction stage (Fig. 1). The sum of surface-adsorbed As(III) and As(V) could indicate the adsorption capacity of CuO NPs, which was about 8.39 mg g−1 and 7.95 mg g−1 respectively at pH 6 and 9 and much lower at pH 11 (2.73 mg g−1). Surface adsorption of As(III) reached the maximum within 2 h at all three pHs, and then gradually decreased. In contrast, both surface-adsorbed and solution As(V) gradually increased at all pHs, except for solution As(V) at pH 6, which remained consistently low over time. Although the surface adsorption of As(V) was consistent among all three pHs, the amount of solution As(V) increased with increasing pH, suggesting a higher oxidation efficiency at high pH (please also refer to “Effect of pH and initial As(III) concentration on As(III) adsorption and oxidation”. In addition, both adsorbed and solution As(III) decreased as pH increased, revealing a high oxidation efficiency and low adsorption affinity of As(III) at high pH.
To determine the rate of As(III) oxidation by CuO NPs, the concentration of As(III) remaining in the system was fitted using first-order kinetic equation (Additional file 1: Fig. S2). The fitted rate constants were 0.013, 0.014, and 0.14 h−1 at pH 6, 9, and 11, respectively (Table 1). The oxidation rates at pH 6 and 9 were very close to each other, but were about an order of magnitude smaller than that at pH 11. The oxidation kinetics under N2 atmosphere at pH 11 were also measured to investigate the influence of O2 level. The oxidation rate (0.012 h−1) and oxidation extent were both lower under N2 than under O2 (Fig. 1d and Additional file 1: Fig. S2d), implying that O2 could be the terminal electron acceptor for As(III) oxidation (for details refer to “XPS analyses”). The lower rate and extent of As(III) oxidation under N2 condition could be ascribed to the direct electron transfer from a small amount of As(III) to surface Cu(II) sites on CuO NPs.
Effects of pH and initial As(III) concentration on As(III) adsorption and oxidation
The phase distributions of As(III) and As(V) at different pHs over 48 h are shown in Fig. 2. The total amount of As(III) oxidized by CuO NPs increased with increasing pH, particularly under alkaline condition. More specifically, the total amount of oxidized As(III) increased from 1.13 to 2.37 mg L−1 as pH increased from 5 to 8, and sharply rose from 3.94 to 9.98 mg L−1 with pH increasing from 9 to 11. In addition, most As(V) was partitioned on CuO NPs surface at pH below the PZC (9.2), but migrated into the aqueous phase at pH above the PZC, due to electrostatic repulsion between As(V) and negatively charged surface.
The effects of initial As(III) concentration on As(III) adsorption and oxidation were investigated at pH 8 and 11 over 24 h, and the results were shown in Fig. 3. Dramatic differences were observed between the two tested pHs: (1) at pH 8, although adsorption of As(III) increased almost linearly with initial As(III) (to 20 mg L−1), total oxidized As(III) plateaued rapidly (1.31 mg L−1), resulting in a rapid decrease in the percentage of oxidized As(III); and most of the formed As(V) remained on NPs surface; (2) at pH 11, much more As(III) was oxidized and plateaued only when the initial As(III) concentration was above 40 mg L−1, and the percentage of oxidized As(III) just decreased gradually; (3) although the oxidation amount increased with initial As(III) concentration, the total amount of adsorbed As(III) and As(V) was much smaller at pH 11 than at pH 8 under the same initial As(III) concentration. These results again suggest the remarkable oxidation capacity of CuO NPs at high pH.
The pH-dependent distribution of As species is most likely related to the species transformation of aqueous As(III) and As(V) and the surface charge of CuO NPs. At pH below 9, the main species of aqueous As(III) is H3AsO3, but As(V) mainly exists in the forms of H2AsO4−and HAsO42−. At pH above 9, As(III) exists in the forms of H2AsO3− and HAsO32−, and aqueous As(V) as HAsO42− and AsO43− . As(III) (in form of H3AsO3) is adsorbed on CuO NPs via Van der Waals force at pH 6–9 . The adsorption percentage of As(V) was observed to be obviously higher than that of As(III) under the same initial As concentration at pHs ranging from 6 to 11 . The aqueous As(V) in forms of H2AsO3− and HAsO32− may have a higher affinity than As(III) to the positively charged surface of CuO NPs and tend to form inner-sphere complexes. In this study, a large number of surface reactive sites were occupied by the formed As(V), resulting in the low oxidation rate of As(III) by CuO NPs at low pHs. Due to the strongly negative surface charge of CuO NPs at high pHs, the formed As(V) (mainly in the forms of HAsO42− and AsO43−) is electrostatically repulsed from CuO NPs surface. Furthermore, redox potential of As(V)/As(III) would increase with decreasing pH, indicating that As(III) is more readily oxidized at higher pH. For instance, in acid medium, the standard potential for the half reaction (H3AsO4+H+)/H3AsO3 is 0.56 V; but in alkaline medium, that of AsO43−/(AsO2−+OH−) is − 0.71 V . Therefore, CuO NPs surface remains highly reactive and can continuously oxidize As(III) at pH above the PZC.
Q-XAS test results
In situ Q-XAS was conducted to directly monitor the oxidation of As(III) . To obtain an optimal signal-to-noise ratio, we employed higher concentrations of AS(III) and CuO NPs for the in situ Q-XAS measurement than for batch experiments. The in situ As K-edge XANES spectra as a function of time and their LCF results are shown in Fig. 4 and Additional file 1: Fig. S7, respectively. Some data point truncations in Additional file 1: Fig. S7 were caused by the pause of synchrotron radiation facility for photon injection. In situ Q-XAS spectra over 8 h revealed that As(III) was oxidized to As(V) in CuO NPs suspension at pH 11, which is consistent with the results of batch experiments (Fig. 1c). With increasing reaction time, more As(III) was oxidized to As(V) and about 36% As(III) was oxidized after 470 min. The results of in situ Q-XAS measurement suggested that more than 10 mg As(III) could be oxidized by 1 g CuO NPs at pH 11. However, the rate constant (0.14 h−1) determined in batch experiments at this pH was much higher than that determined in Q-XAS experiment (0.03 h−1), which is probably due to the difference in the initial As(III) concentrations used in the two experiments. It is also possible that aggregation of CuO NPs at higher solute concentration may inhibit the oxidation of As(III) .
High-resolution Cu2p and As3d spectra of pure and reacted CuO NPs are shown in Fig. 5, Additional file 1: Figures S5, S6. The peak at 933.0 eV could be assigned to the binding energy of Cu(I) species, and the peaks at 934.8, 941.1, and 943.4 eV might belong to the binding energy of Cu(II) species [17, 36]. The surface Cu compositions of these selected samples determined by XPS fitting are presented in Additional file 1: Table S1. At higher pH, the proportion of Cu(I) tended to increase, implying that some Cu(II) was transformed to Cu(I) at the near-surface of CuO NPs. Given that CuO is likely reduced during XPS measurement [17, 36], the measured content of Cu(I) can only reflect its relative composition on the surface. Moreover, another reason for the presence of Cu(I) species might be the reduction of a small amount of Cu(II) by glacial acetic acid added during the synthesis of CuO NPs . A large amount of Cu(II) was present on the surface, indicating that Cu(I) might not be the final stable form during As(III) oxidation, but an intermediate phase involved in As(III) oxidation. Due to the relatively low initial As(III) concentration, the amount of As on CuO NPs surface was not sufficient for the collection of As3d spectra with a good noise-signal ratio Additional file 1: Fig. S6. However, the results showed that the intensity of As3d spectra at pH below PZC was higher than that at pH above PZC, which further confirms the negative effect of pH on As adsorption. The binding energy of As3d for As(V) was about 1 eV greater than that for As(III) [38, 39], which can help to distinguish As(III) and As(V). As3d spectra in the tested samples of pH 6, 7 and 8 showed no clear energy shift, and exhibited a slight energy shift at pH 9 (Additional file 1: Fig. S6). The spectral intensity was too weak for the observation of any change in energy shift in pH 10 and 11 samples, probably due to the small adsorption amounts of As at these pHs.
EPR analysis for ROS
In systems containing CuO NPs, ROS is commonly generated by Fenton-like heterogeneous reactions through the Cu(II)/Cu(I) redox couple at the interfaces . EPR experiments were conducted to reveal the production and speciation of ROS in both pure and reaction systems at the selected reaction intervals. As a spin trap, TEMP can specifically capture 1O2 to form TEMPONE, a nitroxide radical with a stable EPR signal . Figure 6a, b show the EPR spectra of TEMPONE in the absence and presence of As(III) for different reaction time periods. The EPR spectra clearly reveal that 1O2 was consistently produced in all pure CuO NPs suspensions (Fig. 6a). The EPR signal intensity of TEMPONE did not vary temporally (Fig. 6a), suggesting a stable generation and accumulation of 1O2 in the suspension during the whole process. The addition of 10 mM NaN3, a 1O2 quencher, substantially decreased the 1O2 EPR signal (Fig. 6c), further verifying the production of 1O2 species in CuO NPs suspensions at pH 11. After the addition of As(III) into CuO NPs suspension, the EPR signal intensity of TEMPONE was decreased at 10 min, and then restored to the normal level at 30 min. At 120 min, the EPR signal intensity dropped again (Fig. 6b). The instability of 1O2 EPR signal was possibly caused by the reaction between As(III) and 1O2 species, and continuous production of 1O2 in the reaction (which will be discussed below). No DMPO-OOH, DMPO-OH, BMPO-OOH and BMPO-OH adducts were detected in EPR measurements of the CuO NPs suspension (Fig. 6d). In combination with macroscopic analyses, 1O2 might play a crucial role in the oxidation of As(III) by CuO NPs. Additionally, the presence and impacts of other ROS species, such as ·OH and O2·−, could not be determined, though they may also be involved in the reaction.
As(III) oxidation mechanisms
Based on the first sharp increase and the subsequent slow decrease of As(III) on CuO NPs surface (Fig. 1), we propose that As(III) might be firstly adsorbed on the surface of CuO NPs and then slowly oxidized to As(V). Therefore, at pH below PZC, As(III) and the produced As(V) are mainly adsorbed on the surface of CuO NPs; at pH above PZC, the adsorbed As(III) can be rapidly oxidized to As(V) on the surface and then the produced As(V) is abruptly desorbed into the solution from CuO NPs surface, which ensures that an active surface is available for further oxidation of newly adsorbed As(III).
Our XPS data indicated that part of Cu(II) was converted to Cu(I) at the near-surface (Fig. 5). It could be inferred that the oxidation of some As(III) was triggered by the conversion of CuO to Cu2O (Eq. 1) at the electron donor active sites on CuO NPs . It has been suggested that the number of these active sites sharply rises when the particle size decreases down to nano-scale . The particle size of CuO NPs used in this study was around 15 nm in width and 60 nm in length, which could contribute to a high surface activity. Generally, Cu2O is not stable in open systems and is readily re-oxidized to CuO by dissolved O2 , resulting in the continuous catalytic oxidation of As(III) on the surface of CuO NPs (Eqs. 2 and 3), which can be regarded as the first pathway of As(III) oxidation (Fig. 7).
In addition, the Cu(I) in CuO NPs could be responsible for the production of ROS . O2·− could be produced on the reactive site with electron transfer from Cu(I) to O2. However, O2·− was not detected using EPR in our study. It is possible that O2·− was not a stable species under our experimental conditions, and its concentration was too low to be detected. In fact, O2·− is readily transformed to 1O2 via disproportionation reaction , which was detected in CuO NPs suspension at the absence or presence of As(III) (Fig. 6). The standard redox potential of 1O2/H2O is 2.204 eV , indicating that 1O2 is a strong oxidant similar to ·OH, which has a standard redox potential of 2.538 eV (·OH/H2O). Therefore, we suggest the second reaction pathway: As(III) is oxidized by ROS produced via the activation of O2 on Cu(I) sites of the CuO NPs surface (Fig. 7). CuO will be re-generated from Cu(I) after reaction with O2, and participates in the further oxidation of As(III) via the above-mentioned first reaction pathway. Figure 1d shows that dissolved O2 is an essential factor for the high rate of As(III) oxidation by CuO NPs. Formation of 1O2 from O2 in the presence of CuO NPs might also contribute to As(III) oxidation by CuO NPs (Eqs. 3 and 4). The observation of continuous 1O2 production in the experiments (Fig. 6) indicates a close coupling of these two pathways, which can explain the cycling of CuO NPs catalyst and efficient As(III) oxidation. That is to say, the oxidation of As(III) by the re-generated Cu(II) active sites via the first pathway yields Cu(I) sites again, which could trigger the continuous production of 1O2.
In addition, titration experiment was performed to compare the differences in the amount of consumed OH− between the N2 and open systems at pH 11. In the N2 system, only 0.022 mmol OH− was consumed at the very beginning, which might result from the surface hydrolysis of CuO NPs. However, in the open system, OH− consumption gradually increased from 0.022 mmol at 2 h to 0.080 mmol at 12 h as the reaction proceeded (Additional file 1: Fig. S8). These results suggest that H+ production or OH− consumption is associated with As(III) oxidation.
Taking the above results together, we propose the reaction pathways of As(III) oxidation at high pH as the following equations.
In general, ROS is mainly formed in acidic solution, and Cu2+ cations in solution play an important role in ROS production [26,27,28]. But the above XPS results indicate that the changes of Cu valence mainly occur at pH > 9, when Cu2+ could not be present in solution (Additional file 1: S4). Therefore, ROS is probably formed via electron transfer from Cu(I) to O2 on the surface of CuO NPs. Even when O2 is absent in the system, direct electron transfer from As(III) to Cu(II) can occur on the surface of CuO NPs. These findings can also facilitate a better understanding about the impact of CuO NPs on the mobility and transformation of some redox-sensitive substances in various geochemical settings.
Our results verify that CuO NPs is capable to catalytically oxidize As(III) efficiently with dissolved O2 as the terminal electron acceptor using in situ spectroscopic techniques (Fig. 4). Therefore, CuO NPs can be a potential catalyst and adsorbent to affect the geochemical behaviors of As, which can help researchers to predict the risk of CuO NPs before the application of it in some industrial and environmental fields. Also, this study provides a new perspective for investigation of As(III) oxidation process related to Cu-based NPs.
It can be indicated that the amount and rate of As(III) oxidation by CuO NPs are greatly enhanced by increasing pH to a high alkaline range (Fig. 3b). It should be noted that the adsorption of produced As(V) decreases to a certain degree in alkaline solution. Thus, other adsorbents with high As(V) retention ability at alkaline pHs could be applied simultaneously to enhance the removal of aqueous As to meet the environmental standard in As contaminated areas. Besides, it will be of great environmental significance to further improve the catalytic oxidation capacity of CuO NPs at around neutral pHs. Actually, our undergoing study has shown that the addition of aqueous Mn(II) could remarkably enhance the oxidation of As(III) and the adsorption of As(V) at near neutral pH (Additional file 1: Fig. S9).
Furthermore, two coupled reaction pathways, i.e. direction oxidation by CuO and oxidation by ROS produced via O2 activation on Cu(I) surface sites, are proposed for As(III) oxidation (Fig. 7). These findings further demonstrate the high catalytic activity of CuO NPs towards the oxidation reactions in water, implying the important role of CuO NPs to affect the fate and geochemical behaviors of some reducing pollutants and redox-sensitive organic substances in the environment. The stability and potential reusability of CuO NPs also make it an ideal candidate to be applied in permeable reactive barrier (PRB) in ground water purification. Actually, some developing countries (e.g., Bangladesh and West Bengal of India ) suffer from heavy As contamination in the groundwater, and usually there is a serious lack of water treatment facilities to purify the As-contaminated groundwater [47, 48]. Systematic studies of the adsorption–oxidation mechanisms of As(III) on CuO NPs surfaces are significant for a full understanding of the potential influence of CuO NPs on the reductive pollutants, and for the further development of reliable techniques to deal with As contamination efficiently.
Raimondi F, Scherer GG, Kotz R, Wokaun A (2005) Nanoparticles in energy technology: examples from electrochemistry and catalysis. Angew Chem Int Ed 44(15):2190–2209
Qiu G, Dharmarathna S, Zhang Y, Opembe N, Huang H, Suib SL (2011) Facile microwave-assisted hydrothermal synthesis of CuO nanomaterials and their catalytic and electrochemical properties. J Phys Chem C 116(1):468–477
Pandey P, Merwyn S, Agarwal GS, Tripathi BK, Pant SC (2012) Electrochemical synthesis of multi-armed CuO nanoparticles and their remarkable bactericidal potential against waterborne bacteria. J Nanopart Res 14(1):709–711
Ren G, Hu D, Cheng EW, Vargas-Reus MA, Reip P, Allaker RP (2009) Characterisation of copper oxide nanoparticles for antimicrobial applications. Int J Antimicrob Agents 33(6):587–590
Zhang Q, Zhang K, Xu D, Yang G, Huang H, Nie F, Liu C, Yang S (2014) CuO nanostructures: synthesis, characterization, growth mechanisms, fundamental properties, and applications. Prog Mater Sci 60:208–337
Blinova I, Ivask A, Heinlaan M, Mortimer M, Kahru A (2010) Ecotoxicity of nanoparticles of CuO and ZnO in natural water. Environ Pollut 158(1):41–47
Unsar EK, Ciggin AS, Erdem A, Perendeci NA (2016) Long and short term impacts of CuO, Ag and CeO2 nanoparticles on anaerobic digestion of municipal waste activated sludge. Environ Sci Process Impacts 18(2):277–288
Dimkpa CO, Latta DE, McLean JE, Britt DW, Boyanov MI, Anderson AJ (2013) Fate of CuO and ZnO nano- and microparticles in the plant environment. Environ Sci Technol 47(9):4734–4742
Klaine SJ, Alvarez PJ, Batley GE, Fernandes TF, Handy RD, Lyon DY, Mahendra S, Mclaughlin MJ, Lead JR (2008) Nanomaterials in the environment: behavior, fate, bioavailability, and effects. Environ Toxicol Chem 27(9):1825–1851
Nel A, Xia T, Mädler L, Li N (2006) Toxic potential of materials at the nanolevel. Science 311(5761):622–627
Wang Z, Xie X, Zhao J, Liu X, Feng W, White JC, Xing B (2012) Xylem- and phloem-based transport of CuO nanoparticles in maize (Zea mays L.). Environ Sci Technol 46(8):4434–4441
Chang YN, Zhang M, Xia L, Zhang J, Xing G (2012) The toxic effects and mechanisms of CuO and ZnO nanoparticles. Materials 5(12):2850–2871
Ivask A, Juganson K, Bondarenko O, Mortimer M, Aruoja V, Kasemets K, Blinova I, Heinlaan M, Slaveykova V, Kahru A (2014) Mechanisms of toxic action of Ag, ZnO and CuO nanoparticles to selected ecotoxicological test organisms and mammalian cells in vitro: a comparative review. Nanotoxicology 8(S1):57–71
Bondarenko O, Juganson K, Ivask A, Kasemets K, Mortimer M, Kahru A (2013) Toxicity of Ag, CuO and ZnO nanoparticles to selected environmentally relevant test organisms and mammalian cells in vitro: a critical review. Arch Toxicol 87(7):1181–1200
Zhang Y, Fan J, Yang B, Ma L (2017) Synergistic effect of ferrous ion and copper oxide on the oxidative degradation of aqueous acetaminophen at acid conditions: a mechanism investigation. Chem Eng J 326:612–619
Zhou K, Wang R, Xu B, Li Y (2006) Synthesis, characterization and catalytic properties of CuO nanocrystals with various shapes. Nanotechnology 17(15):3939
Yu XY, Xu RX, Gao C, Luo T, Jia Y, Liu JH, Huang XJ (2012) Novel 3D hierarchical cotton-candy-like CuO: surfactant-free solvothermal synthesis and application in As(III) removal. ACS Appl Mat Interfaces 4(4):1954–1962
Smedley PL, Kinniburgh DG (2002) A review of the source, behaviour and distribution of arsenic in natural waters. Appl Geochem 17(5):517–568
Lan S, Ying H, Wang X, Liu F, Tan W, Huang Q, Zhang J, Feng X (2018) Efficient catalytic As(III) oxidation on the surface of ferrihydrite in the presence of aqueous Mn(II). Water Res 128:92–101
Lafferty BJ, Ginder-Vogel M, Sparks DL (2010) Arsenite oxidation by a poorly crystalline manganese-oxide 1. stirred-flow experiments. Environ Sci Technol 44(22):8460–8466
Liu CH, Chuang YH, Chen TY, Tian Y, Li H, Wang MK, Zhang W (2015) Mechanism of arsenic adsorption on magnetite nanoparticles from water: thermodynamic and spectroscopic studies. Environ Sci Technol 49(13):7726–7734
Ferguson JF, Gavis J (1972) A review of the arsenic cycle in natural waters. Water Res 6(11):1259–1274
Cao AM, Monnell JD, Matranga C, Wu JM, Cao LL, Gao D (2007) Hierarchical nanostructured copper oxide and its application in arsenic removal. J Phys Chem C 111(50):18624–18628
Mcdonald KJ, Reynolds B, Reddy KJ (2015) Intrinsic properties of cupric oxide nanoparticles enable effective filtration of arsenic from water. Sci Rep 5:11110
Martinson CA, Reddy KJ (2009) Adsorption of arsenic(III) and arsenic(V) by cupric oxide nanoparticles. J Colloid Interface Sci 336(2):406–411
Wen G, Wang SJ, Ma J, Huang TL, Liu ZQ, Zhao L, Xu JL (2014) Oxidative degradation of organic pollutants in aqueous solution using zero valent copper under aerobic atmosphere condition. J Hazard Mater 275:193–199
Yuan X, Miller CJ, Pham AN, Waite TD (2014) Kinetics and mechanism of auto-and copper-catalyzed oxidation of 1,4-naphthohydroquinone. Free Radical Biol Med 71(6):291–302
Zhang Y, Fan J, Yang B, Huang W, Ma L (2017) Copper-catalyzed activation of molecular oxygen for oxidative destruction of acetaminophen: the mechanism and superoxide-mediated cycling of copper species. Chemosphere 166:89–95
Zhu J, Bi H, Wang Y, Wang X, Yang X, Lu L (2008) CuO nanocrystals with controllable shapes grown from solution without any surfactants. Mater Chem Phys 109(1):34–38
Lenoble V, Deluchat V, Serpaud B, Bollinger JC (2003) Arsenite oxidation and arsenate determination by the molybdene blue method. Talanta 61(3):267–276
Qin W, Wang Y, Fang G, Liu C, Sui Y, Zhou D (2016) Oxidation mechanism of As(III) in the presence of polyphenols: new insights into the reactive oxygen species. Chem Eng J 285:69–76
Kuriakose S, Singh TS, Pant KK (2004) Adsorption of As(III) from aqueous solution onto iron oxide impregnated activated alumina. Water Qual Res J Can 39(3):258–266
Feng X, Zu Y, Tan W, Liu F (2006) Arsenite oxidation by three types of manganese oxides. J Environ Sci 18(2):292–298
Ginder-Vogel M, Landrot G, Fischel JS, Sparks DL (2009) Quantification of rapid environmental redox processes with quick-scanning X-ray absorption spectroscopy (Q-XAS). Proc Nat Acad Sci USA 106(38):16124–16128
Feng X, Yan Y, Wan B, Li W, Jaisi DP, Zheng L, Zhang J, Liu F (2016) Enhanced dissolution and transformation of ZnO nanoparticles: the role of inositol hexakisphosphate. Environ Sci Technol 50(11):5651–5660
Klein JC, Li CP, Hercules DM, Black JF (1984) Decomposition of copper compounds in X-ray photoelectron spectrometers. Appl Spectrosc 38(5):729–734
Naseri A, Samadi M, Mahmoodi NM, Pourjavadi A, Mehdipour H, Moshfegh AZ (2017) Tuning composition of electrospun ZnO/CuO nanofibers: towards controllable and efficient solar photocatalytic degradation of organic pollutants. J Phys Chem C 121(6):3327–3338
Wu K, Liu T, Xue W, Wang X (2012) Arsenic(III) oxidation/adsorption behaviors on a new bimetal adsorbent of Mn-oxide-doped Al oxide. Chem Eng J 192:343–349
Tuček J, Prucek R, Kolařík J, Zoppellaro G, Petr M, Filip J, Zbořil R (2017) Zero-valent iron nanoparticles reduce arsenites and arsenates to As (0) firmly embedded in core–shell superstructure: challenging strategy of srsenic treatment under anoxic conditions. ACS Sustain Chem Eng 5(4):3027–3038
Wang Z, Bussche AVD, Kabadi PK, Kane AB, Hurt RH (2013) Biological and environmental transformations of copper-based nanomaterials. ACS Nano 7(10):8715–8727
Alia Mohanty P, Matysik J (2001) Effect of proline on the production of singlet oxygen. Amino Acids 21(2):195–200
Oberdörster G, Oberdörster E, Oberdörster J (2005) Nanotoxicology: an emerging discipline evolving from studies of ultrafine particles. Environ Health Perspect 113:823–839
Tromans D, Silva J (1997) Anodic behavior of copper in chloride/tolytriazole and chloride/benzotriazole solutions. Corrosion 53(1):16–25
Brunet LN, Lyon DY, Hotze EM, Alvarez PJ, Wiesner MR (2009) Comparative photoactivity and antibacterial properties of C60 fullerenes and titanium dioxide nanoparticles. Environ Sci Technol 43(12):4355–4360
Li Y, Zhang W, Niu J, Chen Y (2012) Mechanism of photogenerated reactive oxygen species and correlation with the antibacterial properties of engineered metal-oxide nanoparticles. ACS Nano 6(6):5164–5173
Nordstrom DK (2002) Worldwide occurrences of arsenic in ground water. Science 296(5576):2143–2145
Meharg AA, Rahman MM (2015) Arsenic contamination of Bangladesh paddy field soils: implications for rice contribution to arsenic consumption. Environ Sci Technol 37(37):229–234
Dittmar J, Voegelin A, Roberts LC, Hug SJ, Saha GC, Ali MA, Badruzzaman ABM, Kretzschmar R (2010) Arsenic accumulation in a paddy field in Bangladesh: seasonal dynamics and trends over a three-year monitoring period. Environ Sci Technol 44(8):2925–2931
XF lead project conceptualization and all authors contributed to the research design. LZ and BW collected data, all authors analyzed data and contributed to writing the manuscript. All authors read and approved the final manuscript.
The authors gratefully acknowledge National Natural Science Foundation of China (No. 41471194), the Strategic Priority Research Program of the Chinese Academy of Sciences (No. XDB15020402) and the Fundamental Research Funds for the Central Universities (No. 2662017PY070) for financial support for this research. We also thank Aiwen Lei from Wuhan University and Jing Zhang and Lirong Zheng from Beijing Synchrotron Radiation Facility for experimental help and Songhu Yuan from China University of Geosciences (Wuhan) for helpful suggestion on paper corrections.
The authors declare that they have no competing interests.
Availability of data and materials
This work was funded by National Natural Science Foundation of China (Grant Nos 41471194), and the Strategic Priority Research Program of the Chinese Academy of Sciences (Grant no XDB15020402).
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Zeng, L., Wan, B., Huang, R. et al. Catalytic oxidation of arsenite and reaction pathways on the surface of CuO nanoparticles at a wide range of pHs. Geochem Trans 19, 12 (2018) doi:10.1186/s12932-018-0058-3
- CuO NPs
- Surface catalysis