A millimeter-sized negatively charged polymer embedded with molybdenum disulfide nanosheets for efficient removal of Pb(Ⅱ) from aqueous solution

Guangze Nie Shijun Qiu Xiang Wang Yan Du Qingrui Zhang Yang Zhang Hengle Zhang

Citation:  Guangze Nie, Shijun Qiu, Xiang Wang, Yan Du, Qingrui Zhang, Yang Zhang, Hengle Zhang. A millimeter-sized negatively charged polymer embedded with molybdenum disulfide nanosheets for efficient removal of Pb(Ⅱ) from aqueous solution[J]. Chinese Chemical Letters, 2021, 32(7): 2342-2346. doi: 10.1016/j.cclet.2020.12.014 shu

A millimeter-sized negatively charged polymer embedded with molybdenum disulfide nanosheets for efficient removal of Pb(Ⅱ) from aqueous solution

English

  • Wastewater containing heavy metal ions, such as Pb(Ⅱ), Hg(Ⅱ), Cr(Ⅵ), and Cd(Ⅱ), discharged from various industries has caused a potential toxicological threat to human health [1, 2]. Lead, due to its high toxicity, bioaccumulation and non-degradability has received constant attention [3, 4]. The common methods for lead removal from wastewater include chemical precipitation [5], adsorption [6, 7], electrocoagulation [8], and membrane filtration [9]. Among them, adsorption is considered one of the most effective treatment methods for lead-containing wastewater due to the significant advantages including low cost, high efficiency and easy handling [10-12]. However, it is still urgent to develop an adsorbent with high adsorption capacity, fast adsorption kinetics, excellent selectivity and reusability.

    As a promising nanomaterial, molybdenum disulfide (MoS2), a two-dimensional transition metal dichalcogenide (TMD), is widely favored in the fields of energy [13, 14], optics [15] and electronics [16] due to its excellent electrical and mechanical properties. On the other hand, MoS2 also shows great potential as a heavy metal adsorbent in the environmental field because of numerous active S-functional groups (considered as a potential adsorption site) on its surface, excellent chemical stability, high selectivity, and its remarkable charge transfer potential [17-20]. It has been proved that the adsorption mechanism of MoS2 to heavy metal ions is mainly through chemical complexation to form metal-sulfur bonding [21, 22]; electrostatic attraction has also been demonstrated to be a mean of adsorption [23], although its role is much less than that of complexation.

    In previous studies, monolayer MoS2 prepared by chemical exfoliation is the most optimal adsorbent for removing heavy metal ions from wastewater. However, this method will change the structure of MoS2 [24], which need further annealing or laser to restore the original structure. In addition, there is still a bottleneck to separate and recover the monolayer MoS2 from the liquid phase, which limits its further practical application in fixed beds or other flow-through systems for water treatment. Compared with chemical exfoliation, the hydrothermal method is more preferred due to its advantages of simple operation, large yield, controllable morphologies and facile hybridization with other functional materials [25]. The regeneration ability of an adsorbent also plays an important role during the adsorption process, but the premise is that the adsorbent is facile to be separated and recovered from water. One of the most widely used strategy for nanomaterial separation and recycle is to anchor magnetic materials on the surface of molybdenum disulfide to realize the magnetic separation of MoS2 from the liquid phase [26-29]. Another potential strategy is to impregnate MoS2 nanoparticles onto other porous materials with large size [30]. The large-scale host materials with built-in nanostructures could achieve highly effective solid-liquid separation. Recently, millimeter-sized ion-exchange resins have been widely employed to support nanoparticles for in the fabrication of hybrid materials because of the special merits of their satisfactory hydrodynamic performance as well as the controllable pore space and surface chemistry [31]. Meanwhile, to our knowledge, such MoS2 hybrid material has not yet been reported.

    Herein, D-001, a commercially available cation exchanger with porous polystyrene structure tailored with sulfonic acid groups [RSO3·Na+] was selected as the host to load MoS2 nanosheets by simple hydrothermal method. The basic physicochemical properties of the resultant nanocomposite (named MoS2-001) were characterized and the effects of solution pH, reaction temperature, adsorption time and coexisting ions on lead removal were examined by batch adsorption experiments. Profit from the negatively charged sulfonic acid groups and millimeter-scale size of the host, the nanocomposite would have higher adsorption capacity and better hydraulic property compared to the bulk MoS2. Fixed-bed adsorption and regeneration experiments were conducted in a glass column to further elucidate the practical application potential of MoS2-001 in lead removal.

    The detailed synthesis, characterization and experiment sections of MoS2-001 were provided in Support information.

    Macroscopically, MoS2-001 is a spherical bead about 1 mm in diameter with no apparent difference from the host D-001 in appearance, while the color changed from white to black, as shown in Scheme 1. Further, the morphology and microstructure of the as-prepared material were characterized by scanning electron microscopy (SEM) and transmission electron microscopy (TEM) analysis. Figs. 1a and b show the SEM images of MoS2-001′s cross-section, as shown, the porous structure can be observed on the inner surface, which is conducive to providing more active sites and facilitating the diffusion of the target pollutant inside the adsorbent during the adsorption process [32]. Mo analysis of the MoS2-001 after acidic digestion showed the loading amount of MoS2 in nanocomposite was 6.2 wt% in Mo mass. The distribution of Mo and S element on the cross-section of the nanocomposite was characterized by energy-dispersive X-ray spectroscopy (EDS) mapping (Figs. 1c and d), the homogeneous distribution of molybdenum and sulfur also proved the successful loading of molybdenum sulfide on the host D-001. TEM analysis revealed that nanosized MoS2 particles are well-dispersed on the host (Fig. 1e). The high resolution TEM (HRTEM) image of the MoS2 nanosheet is shown in Fig. 1f, from where the (002) and (102) lattice fringes with a lattice spacing of 6.5 Å and 2.6 Å are observed. The X-ray diffraction spectra (XRD) of nanocomposite (Fig. 1g1) shows the typical diffraction peaks at 2θ=13.56°, 32.29°, 35.65°and 57.65° corresponding to the (002), (100), (102) and (110) planes of MoS2 [33, 34], and matched well with the standard 2H phase of MoS2. The layer spacing of the loaded MoS2 (~6.5 Å) was calculated by Bragg's Law (Eq. S2 in Support information), and the result is in good agreement with the HRTEM image. Particularly, due to the addition of excessive thiourea in the synthesis process, the (002) peak shift to a lower angle (Fig. 1g2), indicting the d-spacing of MoS2-001 is larger than the standard 2H phase of MoS2 (JCPDS No. 34-1942). It was reported that excessive sulfur element in the synthesis process can expand the layer spacing of MoS2 [35], which is conducive to the diffusion and capture of Pb(Ⅱ).

    Scheme 1

    Scheme 1.  The synthesis process of MoS2-001 and optical view of D-001 and MoS2-001.

    Figure 1

    Figure 1.  Characterization of the as-prepared MoS2-001. (a) SEM image of MoS2-001 at cross-section, (b) the enlarged view of (a), (c and d) corresponding EDS mapping of (b, e, f) TEM and HRTEM images of MoS2-001, (g1) XRD pattern, (g2) the (002) peak shift of MoS2-001.

    To investigate the adsorption performance of MoS2-001 toward Pb(Ⅱ), sorption experiments were conducted by the batch equilibrium method. As a pivotal factor, the solution pH has a great influence on the adsorption process. Generally speaking, the higher pH values would facilitate the Pb(Ⅱ) adsorption onto MoS2-001 (Fig. 2a). As shown, the uptake capacity increased dramatically from 201.81 mg/g to 388.10 mg/g with increasing pH from 1.0 to 3.0, then tends to be stable between pH from 3.0 to 7.0. Such pH-dependent adsorption could be explained by the specific structure of MoS2-001: The negatively charged sulfonic groups bound on the host D-001 could sequester lead ions through nonspecific electrostatic interaction [36], and the MoS2 nanosheets loaded on the host showed strong specific complexation with lead ions [35]. Generally, low pH value would enhance the surface protonation of MoS2, thus increasing the repulsive force between nanomaterials and lead ions. Besides, a high concentration of hydrogen ions can compete with lead ions for adsorption sites, which is not conducive to adsorption.

    Figure 2

    Figure 2.  (a) Effect of equilibrium pH (T=298 K). (b) Adsorption isotherm of Pb(Ⅱ) on MoS2-001 and D-001 (pH 4.8±0.2, T=298 K). (c) Effect of contact time on Pb(Ⅱ) adsorption on MoS2-001 and D-001 (pH 4.8, T=298 K, initial Pb(Ⅱ) concentration=200 mg/L). (d) Effect of competitive ions on Pb(Ⅱ) uptake onto MoS2-001 and D-001 (T=298 K, pH 4.8±0.2, initial Pb(Ⅱ) concentration=250 mg/L).

    Comparative study on the absorption capability of MoS2-001 and D-001 was investigated by adsorption isotherm experiments, and the results are shown in Fig. 2b. Notably, the adsorption capacity of the nanocomposite is significantly higher than that of the host D-001 under different lead concentrations. Langmuir and Freundlich models (Text S6 in Support information) were utilized to analyze the experiment data [37, 38]. As shown in Table S1 (Supporting information), the Langmuir model with a correlation coefficient as high as 0.99 can well describe the adsorption behavior of MoS2-001, and the adsorption process suggests being monolayer adsorption. The maximum adsorption capacities of Pb(Ⅱ) uptake by D-001 and nanocomposite MoS2-001 determined from the Langmuir model are 353.79 and 404.17 mg/g, respectively. It can be inferred that the higher adsorption capacity of MoS2-001 was attributed to the successful embedding of MoS2 provides more potential adsorption sites for Pb(Ⅱ) adsorption. In addition, we also evaluated the Pb(Ⅱ) adsorption on the bulk MoS2 under the same conditions (Fig. S1 and Table S1 in Supporting information). The maximum adsorption capacity (about 274.88 mg/g) is lower than other two samples, which may be due to the loss of active sites caused by agglomeration of MoS2 nanoparticles. The adsorption kinetics of lead on MoS2-001 and D-001 are depicted in Fig. 2c. The uptake of Pb(Ⅱ) from aqueous solution both by MoS2-001 and D-001 was very rapid within the initial 60 min and then slowed down considerably before gradually attaining equilibrium at 150 min. The pseudo-first order model and pseudo-second order model (Text S6) were employed to fit the adsorption kinetic data [39, 40]. The results of model calculations are shown in Fig. 2c and the fitted parameters are presented in Table S2 (Supporting information). The pseudo-first order model can better describe the process of lead removal on MoS2-001 and D-001 due to its higher correlation coefficients (R2=0.998), as well as the calculated Qe values closer to the experimental ones. The better description by the pseudo-first-order model indicated that the adsorption process is mainly controlled by the diffusion process [41]. The excellent adsorption property of MoS2-001 can be elucidated based on its specific dual structure, i.e., the sulfonic acid groups bonding to the host D-001 exerts a powerful electrostatic effect which can enhance preconcentration and permeation of lead ions before their effective sequestration by the MoS2 nanoparticles, known as the Donnan effect [42]. Under similar reaction conditions, adsorption on MoS2-001 was compared with other reported materials (Table 1) [29, 43-48] Apparently, MoS2-001 has an enormous advantage both in adsorption capacity and kinetics, which can be used in the treatment of lead-containing wastewater.

    Table 1

    Table 1.  Comparison of adsorption capacity for Pb(Ⅱ) by different adsorbents.
    DownLoad: CSV

    There are many other cations such as Ca(Ⅱ) and Mg(Ⅱ) ions, usually coexist with the target ions [49]. Therefore, it is necessary to evaluate the selectivity and anti-interference of the nanocomposite adsorbent for Pb(Ⅱ) removal. Here, Ca(Ⅱ) and Mg(Ⅱ) with different molar ratios to Pb(Ⅱ) were selected as competitive ions, and the results were illustrated in Fig. 2d. With the increase of competing ion concentration, the adsorption capacities of MoS2-001 and D-001 decreased significantly. However, it is worth noted that MoS2-001 still has a decent adsorption capacity even in the presence of calcium or magnesium ions with a molar ratio of 200, while D-001 has almost no adsorption capacity under such conditions. Compared to the host D-001, the adsorption selectivity of MoS2-001 for Pb(Ⅱ) was enhanced. This may be attributed to that D-001 host captures Pb(Ⅱ) ions only through the non-specific electrostatic interactions with its negatively charged sulfonic acid groups, and the common ions would compete for these adsorption sites, leading to a decrease in the adsorption capacity for Pb(Ⅱ) ions. Whereas the impregnated MoS2 in D-001 with the soft Lewis base nature from sulfide ions can selectively bond with the soft Lewis acid Pb(Ⅱ) ions to form metal-sulfur complex [35, 50]. To evaluate the reusability of MoS2-001, 5 cycles of Pb(Ⅱ) adsorption onto MoS2-001 followed by regeneration with a binary 10 wt% NaCl + 0.1 mol/L EDTA-2Na solution were conducted. As illustrated in Fig. 3a, the negligible capacity loss indicated its excellent stability and reusability for Pb(Ⅱ) removal.

    Figure 3

    Figure 3.  (a) Cyclic adsorption-regeneration experiments (pH=4.8, T=298 K, Pb(Ⅱ)=50 mg/L, Ca(Ⅱ) =Mg(Ⅱ)=Na(Ⅰ)=200 mg/L). (b) Continuous treatment capacity evaluation for application onto MoS2-001 during fixed-bed column runs at 298 K (Pb(Ⅱ)=10 mg/L, Ca(Ⅱ)=Mg(Ⅱ)=Na(Ⅰ)=200 mg/L, pH 4.8±0.3, T=298 K, EBCT=6 min), the inset is the column regeneration of the exhausted MoS2-001 (SLV=0.115 m/h, EBCT=24 min, T=298 K).

    MoS2-001 was available in fixed-bed owe to the millimeter size of the host D-001. Fig. 3b illustrates the effluent history of the separate fixed-bed columns fed with a synthetic solution containing Pb(Ⅱ) and other competing ions (Na(Ⅰ), Ca(Ⅱ), Mg(Ⅱ)). The column breakthrough point of the effluent is set at 1 mg/L, the Chinese industrial wastewater discharge standard. As expected, the effective treatable volume of MoS2-001 approached to ~1450 bed volume (BV). The exhausted MoS2-001 could be well regenerated with a binary 10% NaCl +0.1 mol/L EDTA-2Na solution (Fig. 3b inset) and still able to treat ~1350 BV of wastewater in the second run, suggesting its possible applicability in practice water treatment.

    In order to explore the preliminary adsorption mechanism, X-ray photoelectron spectroscopy (XPS) was employed to study the intrinsic interaction between MoS2-001 and Pb(Ⅱ). Fig. 4a shows the XPS spectra for MoS2-001 [12] before and after adsorption. A new peak of Pb 4f can be observed after lead removal further verifying the adsorption of Pb(Ⅱ) on MoS2-001. The low contents of Mo and S elements could be explained that the thickness of the polymer exceeds the detection limit of XPS which leads to the inner MoS2 is difficult to be detected [51]. As illustrated in Fig. 4b, the Pb 4f5/2 and Pb 4f7/2 spectrum could be divided into two peaks, respectively. The peaks around 144.2 eV and 139.3 eV are attributable to the Pb-S complex species, whereas the peaks around 144.85 eV and 139.95 eV are attributable to the (RSO3)2·Pb2+ species formed between Pb(Ⅱ) and sulfonic acid groups by electrostatic interaction [52, 53]. Thus, the adsorption preference of MoS2-001 toward Pb(Ⅱ) can be explained by its two distinct active sites for Pb(Ⅱ) uptake. One is the negatively charged sulfonic acid groups covalently binding the matrix of host D-001, and the other is MoS2 nanosheets impregnated inside D-001. Although the competitive cations would occupy the nonspecific adsorption sites of the sulfonic acid groups and result in reduced adsorption capacity, the MoS2 nanosheets capture Pb(Ⅱ) mainly through the metal-sulfur chemical complexation (the strong soft-soft interactions of Lewis acid and base) was not significantly influenced by coexisting competitive metal ions.

    Figure 4

    Figure 4.  (a) XPS survey spectrum of MoS2-001 before and after Pb(Ⅱ) adsorption. (b) Deconvoluted spectra of Pb 4f on the Pb(Ⅱ) loaded adsorbent.

    In summary, a millimeter-sized nanocomposite MoS2-001 was successfully fabricated by loading molybdenum disulfide into the cation exchanger D-001. MoS2-001 displayed high adsorption capacity, fast adsorption kinetics, and high availability in the wide range of pH 2–7 toward Pb(Ⅱ). The adsorption could be well described by the Langmuir model and the pseudo-first order kinetic model. Even better, MoS2-001 showed remarkable adsorption capacity even in the presence of an extremely high concentration of calcium and magnesium ions. This excellent performance of MoS2-001 could mainly be attributed to the Donnan membrane effect exerted by the sulfonic acid groups bonded to the D-001 as well as the specific complexation of MoS2 loaded inside the D-001. Fixed-bed runs and adsorption-regeneration experiments further verified its practical application potential. These properties make MoS2-001 an excellent candidate adsorbent for lead ions removal from wastewater.

    The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.

    We greatly acknowledge the financial support from the National Key Research and Development Program of China (No. 2017YFE0107200), Postgraduate Research & Practice Innovation Program of Jiangsu Province (No. KYCX20_1105), NSFC (No. 21876145), the Supporting Plan for 100 Excellent Innovative Talents in Colleges and Universities of Hebei Province (No. SLRC2019041), and Open Foundation of State Key Laboratory of Pollution Control and Resource Reuse (No. PCRRF18026, Nanjing University).


    1. [1]

      W. Liu, J. Tian, L. Chen, Y. Guo, Environ. Pollut. 220 (2017) 696-703. doi: 10.1016/j.envpol.2016.10.031

    2. [2]

      Y. Liu, T. Li, C. Ling, et al., Chin. Chem. Lett. 30 (2019) 2211-2215. doi: 10.1016/j.cclet.2019.05.020

    3. [3]

      Q. Yang, Z. Li, X. Lu, et al., Sci. Total. Environ. 642 (2018) 690-700. doi: 10.1016/j.scitotenv.2018.06.068

    4. [4]

      L.N. Hu, Z.G. Ren, Chin, Chem. Lett. 20 (2009) 334-338. doi: 10.1016/j.cclet.2008.12.006

    5. [5]

      P. Zhang, S. Ouyang, P. Li, et al., J. Clean. Prod. 246 (2020) 118728. doi: 10.1016/j.jclepro.2019.118728

    6. [6]

      S. Bao, K. Li, P. Ning, et al., Appl. Surf. Sci. 393 (2017) 457-466. doi: 10.1016/j.apsusc.2016.09.098

    7. [7]

      A. Shahat, H.M.A. Hassan, H.M.E. Azzazy, et al., Chem. Eng. J. 332 (2018) 377-386. doi: 10.1016/j.cej.2017.09.040

    8. [8]

      H.J. Mansoorian, A.H. Mahvi, A.J. Jafari., Sep. Purif. Technol. 135 (2014) 165-175. doi: 10.1016/j.seppur.2014.08.012

    9. [9]

      P. Yenphan, A. Chanachai, R. Jiraratananon, Desalination 253 (2010) 30-37. doi: 10.1016/j.desal.2009.11.040

    10. [10]

      Y. Li, M. Li, J. Zhang, X. Xu., Chin. Chem. Lett. 30 (2019) 762-766. doi: 10.1016/j.cclet.2018.11.005

    11. [11]

      M.I. Shariful, S.B. Sharif, J.J.L. Lee, et al., Carbohydr. Polym. 157 (2017) 57-64. doi: 10.1016/j.carbpol.2016.09.063

    12. [12]

      M. Zhang, F. Jia, M. Dai, S. Song, Appl. Surf. Sci. 455 (2018) 258-266. doi: 10.1016/j.apsusc.2018.05.207

    13. [13]

      X. Sun, Z. Wang. Appl. Surf. Sci. 455 (2018) 911-918. doi: 10.1016/j.apsusc.2018.06.032

    14. [14]

      F. Chen, L. Wu, Z. Zhou, et al., Chin. Chem. Lett. 30 (2019) 197-202. doi: 10.1016/j.cclet.2018.10.007

    15. [15]

      S. Ridene, Superlattice. Microst. 114 (2018) 379-385. doi: 10.1016/j.spmi.2017.12.060

    16. [16]

      U. Khan, T.H. Kim, M.A. Khan, et al., Nano Energy 75 (2020) 104936. doi: 10.1016/j.nanoen.2020.104936

    17. [17]

      Z. Wang, A. Sim, J.J. Urban, B. Mi, Environ. Sci. Technol. 52 (2018) 9741-9748. doi: 10.1021/acs.est.8b01705

    18. [18]

      C. Liu, Q. Wang, F. Jia, S. Song, J. Mol. Liq. 292 (2019) 111390. doi: 10.1016/j.molliq.2019.111390

    19. [19]

      Q. Wang, L. Yang, F. Jia, Y. Li, S. Song, J. Mol. Liq. 263 (2018) 526-533. doi: 10.1016/j.molliq.2018.04.149

    20. [20]

      H. Wang, F. Wen, X. Li, et al., Sep. Purif. Technol. 170 (2016) 190-198. doi: 10.1007/s10753-015-0238-6

    21. [21]

      H. Tian, J. He, M. Hu, J Colloid Interface Sci. 551 (2019) 251-260. doi: 10.1016/j.jcis.2019.05.027

    22. [22]

      C. Liu, S. Zeng, B. Yang, F. Jia, S. Song, J. Mol. Liq. 296 (2019) 111987. doi: 10.1016/j.molliq.2019.111987

    23. [23]

      M.J. Aghagoli, M. Hossein Beyki, F. Shemirani, Food Chem. 223 (2017) 8-15. doi: 10.1016/j.foodchem.2016.12.023

    24. [24]

      Z. Wang, B. Mi, Environ. Sci. Technol. 51 (2017) 8229-8244. doi: 10.1021/acs.est.7b01466

    25. [25]

      L. Luo, M. Shi, S. Zhao, et al., J. Saudi. Chem. Soc. 23 (2019) 762-773. doi: 10.1016/j.jscs.2019.01.005

    26. [26]

      R. Li, H. Deng, X. Zhang, et al., Bioresource. Technol. 273 (2019) 335-340. doi: 10.1016/j.biortech.2018.10.053

    27. [27]

      Y. Song, M. Lu, B. Huang, et al., J. Alloy. Compd. 737 (2018) 113-121. doi: 10.1016/j.jallcom.2017.12.087

    28. [28]

      J. Wang, W. Zhang, X. Yue, et al., J. Mater. Chem. A 4 (2016) 3893-3900. doi: 10.1039/C6TA00269B

    29. [29]

      Z. Wang, J. Zhang, T. Wen, et al., Sci. Total. Environ. 699 (2019) 134341. doi: 10.1016/j.scitotenv.2019.134341

    30. [30]

      J. Qian, X. Gao, B. Pan, Environ. Sci. Technol. 54 (2020) 8509-8526. doi: 10.1021/acs.est.0c01065

    31. [31]

      B. Pan, X. Zhang, Z. Jiang, et al., Polymer and Polymer-Based Nanocomposite Adsorbents for Water Treatment, in: Das R. (Eds. ), Polymeric Materials for Clean Water, Springer, Cham. 2019, pp. 93-119.

    32. [32]

      G. Nie, L. Wu, Y. Du, et al., Chem. Eng. J. 360 (2019) 1128-1136. doi: 10.1016/j.cej.2018.10.184

    33. [33]

      H. Cao, Z. Bai, Y. Li, et al., ACS Sustain. Chem. Eng. 8 (2020) 7343-7352. doi: 10.1021/acssuschemeng.0c00736

    34. [34]

      P. Afanasiev, C. Geantet, I. Llorens, O. Proux, J. Mater. Chem. 22 (2012) 9731– 9737. doi: 10.1039/c2jm30377a

    35. [35]

      K. Ai, C. Ruan, M. Shen, L. Lu, Adv. Funct. Mater. 26 (2016) 5542-5549. doi: 10.1002/adfm.201601338

    36. [36]

      R.S. Juang, S.H. Lin, T.Y. Wang, Chemosphere 53 (2003) 1221-1228. doi: 10.1016/S0045-6535(03)00578-2

    37. [37]

      Y. Du, S. Qiu, X. Zhang, G. Nie, Chem. Eng. J. 400 (2020) 125907. doi: 10.1016/j.cej.2020.125907

    38. [38]

      Y. Hu, Y. Du, G. Nie, et al., Sci. Total. Environ. 700 (2020) 134999. doi: 10.1016/j.scitotenv.2019.134999

    39. [39]

      Q. Zhang, J. Teng, Z. Zhang, et al., RSC Adv. 5 (2015) 55445-55452. doi: 10.1039/C5RA09628F

    40. [40]

      C.D. Shuang, F. Yang, F. Pan, et al. Chin. Chem. Lett. 22 (2011) 1091-1094. doi: 10.1016/j.cclet.2011.04.009

    41. [41]

      Y.S. Ho, G. McKay. Process Biochem. 34 (1999) 451-465. doi: 10.1016/S0032-9592(98)00112-5

    42. [42]

      S. Sarkar, P.K. Chatterjee, L.H. Cumbal, A.K. SenGupta, Chem. Eng. J. 166 (2011) 923-931. doi: 10.1016/j.cej.2010.11.075

    43. [43]

      X. Luo, Z. Huang, J. Lin, et al. J. Clean. Prod. 258 (2020) 120991. doi: 10.1016/j.jclepro.2020.120991

    44. [44]

      Y. Liu, J. Xu, Z. Cao, R. et al. J. Colloid. Inter. Sci. 559 (2020) 215-225. doi: 10.1016/j.jcis.2019.10.035

    45. [45]

      A.A. Alqadami, M. Naushad, Z.A. Alothman, M. Alsuhybani, M. Algamdi. J. Hazard. Mater. 389 (2020) 121896. doi: 10.1016/j.jhazmat.2019.121896

    46. [46]

      P.L. Yap, Y.L. Auyoong, K. Hassan, et al. Chem. Eng. J. 395 (2020) 124965. doi: 10.1016/j.cej.2020.124965

    47. [47]

      C. Chen, Q. Chen, J. Kang, et al. J. Mol. Liq. 298 (2020) 112031. doi: 10.1016/j.molliq.2019.112031

    48. [48]

      M. Dinari, S. Neamati. Colloid. Surface. A. 589 (2020) 124438. doi: 10.1016/j.colsurfa.2020.124438

    49. [49]

      C.X. Li, J.M. Pan, J. Gao, Y.S. Yan, G.Q. Zhao. Chin. Chem. Lett. 20 (2009) 985-989. doi: 10.1016/j.cclet.2009.03.020

    50. [50]

      F. Jia, Q. Wang, J. Wu, Y. Li, S. Song. ACS Sustain. Chem. Eng. 5 (2017) 7410-7419. doi: 10.1021/acssuschemeng.7b01880

    51. [51]

      Q. Huang, J. Zhao, M. Liu, et al. J. Taiwan. Inst. Chem. E., 86 (2018) 174-184. doi: 10.1016/j.jtice.2017.12.027

    52. [52]

      B. Pan, H. Qiu, B. Pan, G. et al. Water Res, 44 (2010) 815-824. doi: 10.1016/j.watres.2009.10.027

    53. [53]

      N. Kumar, E. Fosso-Kankeu, S.S. Ray. ACS Appl. Mater. Inter. 11 (2019) 19141-19155. doi: 10.1021/acsami.9b03853

  • Scheme 1  The synthesis process of MoS2-001 and optical view of D-001 and MoS2-001.

    Figure 1  Characterization of the as-prepared MoS2-001. (a) SEM image of MoS2-001 at cross-section, (b) the enlarged view of (a), (c and d) corresponding EDS mapping of (b, e, f) TEM and HRTEM images of MoS2-001, (g1) XRD pattern, (g2) the (002) peak shift of MoS2-001.

    Figure 2  (a) Effect of equilibrium pH (T=298 K). (b) Adsorption isotherm of Pb(Ⅱ) on MoS2-001 and D-001 (pH 4.8±0.2, T=298 K). (c) Effect of contact time on Pb(Ⅱ) adsorption on MoS2-001 and D-001 (pH 4.8, T=298 K, initial Pb(Ⅱ) concentration=200 mg/L). (d) Effect of competitive ions on Pb(Ⅱ) uptake onto MoS2-001 and D-001 (T=298 K, pH 4.8±0.2, initial Pb(Ⅱ) concentration=250 mg/L).

    Figure 3  (a) Cyclic adsorption-regeneration experiments (pH=4.8, T=298 K, Pb(Ⅱ)=50 mg/L, Ca(Ⅱ) =Mg(Ⅱ)=Na(Ⅰ)=200 mg/L). (b) Continuous treatment capacity evaluation for application onto MoS2-001 during fixed-bed column runs at 298 K (Pb(Ⅱ)=10 mg/L, Ca(Ⅱ)=Mg(Ⅱ)=Na(Ⅰ)=200 mg/L, pH 4.8±0.3, T=298 K, EBCT=6 min), the inset is the column regeneration of the exhausted MoS2-001 (SLV=0.115 m/h, EBCT=24 min, T=298 K).

    Figure 4  (a) XPS survey spectrum of MoS2-001 before and after Pb(Ⅱ) adsorption. (b) Deconvoluted spectra of Pb 4f on the Pb(Ⅱ) loaded adsorbent.

    Table 1.  Comparison of adsorption capacity for Pb(Ⅱ) by different adsorbents.

    下载: 导出CSV
  • 加载中
计量
  • PDF下载量:  1
  • 文章访问数:  400
  • HTML全文浏览量:  92
文章相关
  • 发布日期:  2021-07-15
  • 收稿日期:  2020-10-03
  • 接受日期:  2020-12-03
  • 修回日期:  2020-11-06
  • 网络出版日期:  2020-12-15
通讯作者: 陈斌, bchen63@163.com
  • 1. 

    沈阳化工大学材料科学与工程学院 沈阳 110142

  1. 本站搜索
  2. 百度学术搜索
  3. 万方数据库搜索
  4. CNKI搜索

/

返回文章