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. 2022 Mar 15;7(12):10187–10195. doi: 10.1021/acsomega.1c06606

A Novel Coordination Polymer as Adsorbent Used to Remove Hg(II) and Pb(II) from Water with Different Adsorption Mechanisms

Rui-Dong Wang †, Mei He †, Zhihao Li †, Zongling Niu †, Rong-Rong Zhu †, Wen-Qian Zhang §, Suoshu Zhang †, Lin Du †,‡,*, Qi-Hua Zhao †,‡,*
PMCID: PMC8973041  PMID: 35382326

Abstract

graphic file with name ao1c06606_0008.jpg

Under the hydrothermal condition, a new type of two-dimensional coordination polymer ([Cd(D-Cam)(3-bpdb)]n, Cd-CP) has been constructed. It is composed of D-(+)-Camphoric-Cd(II) (D-cam-Cd(II)) one-dimensional chain and bridging 1,4-bis(3-pyridyl)-2,3-diaza-1,3-butadiene (3-bpdb) ligands. Cd-CP has a good removal effect for Hg(II) and Pb(II), and the maximum adsorption capacity is 545 and 450 mg/g, respectively. Interestingly, thermodynamic studies have shown that the adsorption processes of Hg(II) and Pb(II) on Cd-CP use completely different thermodynamic mechanisms, in which the adsorption of Hg(II) is due to a strong electrostatic interaction with Cd-CP, while that of Pb(II) is through a weak coordination with Cd-CP. Moreover, Cd-CP has a higher affinity for Hg(II), and when Hg(II) and Pb(II) coexist, Cd-CP preferentially adsorbs Hg(II).

Introduction

In recent years, the concentrations of heavy metal ions in water have increased at an unimaginable rate because of the continuous development of industry.1−3 These excessive heavy metal ions in water have seriously threatened human health and the safety of the ecosystem.4−6 Among various heavy metal ions, Hg(II) and Pb(II) are not only highly toxic but also the most common heavy metal ions’ pollutants in the water environment.7,8 Therefore, the removal of Hg(II) and Pb(II) pollution from water is currently the most urgent thing.1,9,10 Moreover, wastewater is a complex system with a large number of ions, so it is very meaningful to design and synthesize novel stable and selective adsorbents.11,12

Coordination polymers (CPs), which are inorganic–organic hybrid materials prepared from metal ions and organic ligands, have emerged as excellent materials because of their availability in various applications.12−14 By selecting ligands with functional groups or postsynthetic modification, it is possible to design and synthesize CPs with specific structures and properties.15,16 With the continuous development of CPs, scientists have obtained a variety of CPs for the removal of heavy metal ions in water through presynthesis design or postsynthesis modification.17,18 The Morsali group chose H2BDC and nitrogen-containing ligand N1, N2-bis(pyridin-4-ylmethylene) ethane-1,2-diamine to construct a CP (TMU-40) that can efficiently remove Hg(II) (qe = 269 mg/g), and the O-TMU-40 by postsynthesis modification can remove Pb(II) (qe = 215 mg/g).19

In this article, a new type 2D Cd-CP has been constructed using the D-(+)-Camphoric (D-H2Cam) and nitrogen-containing bridging ligand 1,4-bis(3-pyridyl)-2,3-diaza-1,3-butadiene (3-bpdb), which can effectively remove Hg(II) and Pb(II) in water. We have studied the effects of pH, treatment time, temperature, and other conditions on the adsorption. It is worth noting that Cd-CP adsorption processes of Hg(II) and Pb(II) have completely different thermodynamics, which has not been reported to our knowledge. The different thermodynamic processes also caused the difference in the adsorption behavior of Cd-CP for Hg(II) and Pb(II).

Results

Synthesis of Cd(D-Cam)(3-bpdb) (Cd-CP)

Initially, D-H2Cam (0.025 mmol, 5.0 mg) and 100 μL of NaOH (1 M) were added to a 5 mL Pyrex glass tube with ultrasound for 15 min, and then Cd(NO3)2·4H2O (0.05 mmol, 15.4 mg), 3-bpdb (0.015 mmol, 3.2 mg, dissolved in 100 μL ethanol), and methanol (1 mL) were added in sequence. The tube was sealed and heated in an oven to 100 °C for 48 h and then naturally cooled to room temperature. Afterward, yellow block crystals were obtained with 75% yield based on 3-bpdb. The calculated elemental analysis values (%) for CdC22H24N4O4 were C, 50.77%; H, 4.62%; N, 10.77% (measured: C, 50.25%; H, 4.73%; N, 10.54%).

Crystal Structures of Cd-CP

X-ray diffraction indicates that Cd-CP crystallizes in the P21/c space group of monoclinic system. The asymmetric unit consists of a Cd(II), a deprotonated D-H2Cam ligand and two different half of 3-bpdb ligands. Cd(II) ion is six-coordinated with four O atoms (O1, O3, O2i, O4i) from two different D-Cam ligands and two N atoms (N3, N4) from two different 3-bpdb ligands (Figure 1a). From the a axis, Cd(II) is linked by D-Cam ligands in chelated coordination mode to form a 1D [Cd(D-Cam)]n chain (Figure 1b). In the ab plane, the 2D structure is formed by bridging adjacent 1D chains of [Cd(D-Cam)]n through 3-bpdb ligands (Figure 1c). The chiral D-H2Cam molecule has a phenomenon similar to racemization in the coordination policy, and thus, Cd-CP is achiral (Figure 1d). Except for the C atoms (C13, C14, C13i, C14i) on the two carboxylic acids, the C atoms from the D-H2Cam molecule are disordered, and the space occupation rate of all disordered C atoms are 50%.

Figure 1.

Figure 1

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(a) Coordination environment of the Cd(II) ions in Cd-CP. (b) The 1D [Cd(D-Cam)]n chains. (c) 2D structure of Cd-CP. (d) Coordination environment of disordered D-Cam ligands and Cd(II) ions, considering only C or C′. Symmetry codes: (i) x+1, y, z; (ii) −x, −y, −z+1; (iii) −x+2, −y+1, −z+1; (iv) x–1, y, z. Ellipsoid probability: 50%. In order to make the structure clear, all H and C′ atoms are omitted.

Characteristic of Cd-CP

The powder profile of the synthesized Cd-CP is consistent with the fitted data, demonstrating its high purity (Figure S2). Cd-CP has excellent thermal stability and remains stable up to 316 °C, and its structure begins to collapse when the temperature exceeds 316 °C (Figure S4).

Effect of pH

The pH of the solution will affect the form of heavy metal ions and thus the adsorption performance of the adsorbent.20 The experiment to determine the influence of pH is carried out in the range of 2–7. First, the stability of Cd-CP is studied. After immersing Cd-CP in a solution with different pH value for 3 days, the concentration of Cd2+ ions in the solution does not increase, indicating that Cd-CP has good stability.10,21 As shown in Figure 2, when the pH range is 2–4, as the pH value increases, and the adsorption capacity of Cd-CP on Hg(II) and Pb(II) also increases rapidly. After that, with the increase of pH, the adsorption capacity of Cd-CP remains stable (pH = 4–7). Considering that the industrial wastewater after simple treatment is weakly acidic or weakly alkaline, the subsequent series of experiments are carried out in ultrapure aqueous solutions without adjusting pH.8

Figure 2.

Figure 2

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Effect of pH on the adsorption performance and removal rate of Cd-CP on Hg(II) (a) and Pb(II) (b) (298 K, 24 h).

Adsorption Kinetics

The changes in the amount of adsorption of Hg(II) and Pb(II) over time are studied.22 The experimental results show that Pb(II) has a faster adsorption efficiency than Hg(II)29 (Figure 3). Hg(II) needs 60 h to reach the adsorption equilibrium (545 mg/g), while Pb(II) only takes 16 h (450 mg/g). In order to better evaluate the adsorption efficiency of Cd-CP on Hg(II) and Pb(II),23−25 the pseudo-first-order model and the pseudo-second-order model are used to fit the adsorption kinetic data.26,27 The pseudo-second-order kinetic model is more in line with the actual adsorption data.28 The data are listed in Table 1. In order to save energy and obtain the highest adsorption efficiency, the subsequent series of adsorption experiments are maintained at 24 h.29

Figure 3.

Figure 3

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Adsorption kinetics of Hg(II) (a) and Pb(II) (b) by Cd-CP. Insets: Pseudo-second-order kinetic model (298 K, 72 h).

Table 1. Fitted Date of Pseudo-First-Order and Pseudo-Second-Order Models (298 K, 72 h).

  pseudo-first-order model
 pseudo-second-order model
parameter qe (mg/g) K1 (min–1) R2 qe (mg/g) K2 (g mg–1 min–1) R2
Hg(II) 537 0.00145 0.939 609 3.32 × 10–6 0.953
Pb(II) 443 0.0300 0.778 458 1.26 × 10–4 0.949
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It can be seen from Table 2 that the adsorption capacity of Cd-CP is comparable to or even better than other CPs. It is worth noting that Cd-CP has a relatively high adsorption capacity for both Hg(II) and Pb(II), which is relatively rare. Although the adsorption capacity of Cd-CP is still lower than that of the derivatives of CPs (Fe3O4@TMU-32), it shows that we can obtain adsorbents with better adsorption properties by modifying Cd-CP.

Table 2. Comparison of Adsorption Capacity of Different Adsorbents.

adsorbent qe of Hg(II) (mg/g) qe of Pb(II) (mg/g) ref
Zn-MOF 32 1097 (1)
Fe3O4@TMU-32 905 1600 (8)
UiO-66-DMTD 670 – (25)
MOF-808/AO 388 – (26)
MOF-2 (Cd) – 434 (30)
EDTA-SBA-15 – 273 (31)
SBA-15/DZ 25 – (32)
Cd-CP 545 450 this work
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Effect of Initial Concentration

In order to explore the actual maximum adsorption capacity, adsorption experiments of Hg(II) and Pb(II) are carried out at different concentrations4 (15–300 mg/L). As shown in Figure 4a,b, with the increasing concentration of ions, the adsorption capacity of Hg(II) and Pb(II) gradually increases to the maximum.33 The maximum adsorption capacity of Hg(II) is 407 mg/g, and the maximum adsorption capacity of Pb(II) is 420 mg/g. Langmuir and Freundlich models are used to analyze the adsorption isotherms of Hg(II) and Pb(II) on Cd-CP.34

Figure 4.

Figure 4

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Nonlinear isotherm plots for the adsorption of Hg(II) (a) and Pb(II) (b). Insets: Fitted Langmuir model linear isotherm (298 K, 24 h). Linear fitting graph of lnK0 and 1/T for adsorbed Hg(II) (c) and Pb(II) (d) (298–318 K, 24 h).

Comparing the R2 of the Langmuir and Freundlich models and the calculated theoretical maximum adsorption value, the Langmuir model is more suitable for fitting the adsorption isotherm than the Freundlich model29 (Table 3). It shows that the adsorption of Hg(II) and Pb(II) by Cd-CP could be considered as a single-layer adsorption process that conforms to the Langmuir model.35 The theoretical maximum adsorption capacity values of Hg(II) and Pb(II) calculated by the Langmuir model are 448 and 436 mg/g, respectively, which are relatively close to the experimental results.36

Table 3. Adsorption Isotherm Model Parameters of Langmuir and Freundlich Models (298 K, 24 h).

  Langmuir
 Freundlich
parameter a (mg/g) b (1/mg) R2 (nonlinear) R2 (linear) k n R2 (nonlinear) R2 (linear)
Hg(II) 448 0.061 0.975 0.999 73.58 2.7 0.896 0.933
Pb(II) 436 0.084 0.960 0.999 137.98 4.8 0.858 0.933
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An interesting result is obtained by thermodynamic research (Figure 4c,d). The results show that the adsorption of Hg(II) of Cd-CP (ΔHHg > 0) is an endothermic process, but that of Pb(II) (ΔHPb < 0) is an exothermic process37 (Table S3). What is more surprising is that the adsorption of Pb(II) (ΔGPb > 0) by Cd-CP is a rare nonspontaneous process, while that of Hg(II) (ΔGHg < 0) is a common spontaneous process.1,38 The positive ΔSHg value indicates the random increase of the solid–liquid interface and the adsorption affinity of Cd-CP toward Hg(II)1. It is worth noting that the adsorption capacity of Cd-CP for both Hg(II) and Pb(II) increase with the increase of temperature, which indicates that temperature is one of driving force for Cd-CP to adsorb Pb(II). Such different thermodynamic data indicate that the adsorption of Hg(II) and Pb(II) is likely to be different adsorption mechanisms.

Adsorption Selectivity

We studied the removal efficiency of Cd-CP for different metal ions, and the study showed that Cd-CP has a good removal rate for both Hg(II) than Pb(II) (Figure 5a). Moreover, the preferential selectivity of Cd-CP to Hg(II) and Pb(II) and the change of the adsorption capacity of Cd-CP to Hg(II) and Pb(II) in the presence of other ions are studied (Figure 5b). Amazingly, in water system where multiple ions coexist (Mn+ = 300 mg/L, Cl– > 100 mg/L and NO3– > 100 mg/L), Cd-CP basically does not adsorb Pb(II), but the adsorption capacity for Hg(II) is still as high as 400 mg/g. This may be that Cd-CP has much greater affinity for Hg(II) than Pb(II)1.

Figure 5.

Figure 5

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(a) Removal efficiency of Cd-CP for different metal ions [Mn+ = 90 mg/L] (298 K, 24 h). (b) The adsorption capacity of Cd-CP for heavy metal ions in a complex system with multiple ions (298 K, 24 h).

Discussion

Figure 6a–i shows the scanning electron microscope (SEM) images of Cd-CP before and after the adsorption of heavy metal ions. The microstructure of Cd-CP presents a regular block structure, while the morphology of Cd-CP has changed significantly after adsorbing heavy metal ions.39 After the adsorption of Hg(II), the surface of Cd-CP appears to have flake accumulation, which may be caused by the deposition of HgCl2.26 EDS analysis also shows the appearance of Hg(II) and Cl(I), which indicate that Hg(II) may be removed by deposition (Figure S5). After the adsorption of Pb(II), the regular structure of Cd-CP is destroyed, but it is different from the morphology of a flake accumulation after adsorption of Hg(II), which indicates that the adsorption mechanism of Hg(II) and Pb(II) may be different.40

Figure 6.

Figure 6

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SEM images of Cd-CP (a–c), Hg@Cd-CP (d–f), and Pb@Cd-CP (g–i).

PXRD, FT-IR, and XPS

In order to further verify the adsorption mechanism of Cd-CP, we have conducted PXRD, FT-IR, and XPS studies.40 As shown in Figure 7a, the PXRD data of Cd-CP and Hg@Cd-CP are the same, indicating that the structure of Cd-CP has not changed after adsorbing Hg(II).41 However, after the adsorption of Pb(II), the PXRD data of Cd-CP has changed. Pb@Cd-CP has new strong diffraction peaks at 9.4° and 17.7°, while the strong diffraction peaks at 9°, 11.1°, 11.5°, and 16.9° have disappeared. These data confirm the structural transformation of Pb@Cd-CP, indicating that Pb(II) may be removed by coordination.

Figure 7.

Figure 7

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(a) PXRD patterns of Cd-CP, Hg@Cd-CP, and Pb@Cd-CP. (b) FT-IR spectrum of Cd-CP, Hg@Cd-CP and Pb@Cd-CP. (c) XPS survey of the Cd-CP, Hg@Cd-CP, and Pb@Cd-CP. (d) XPS Hg 4f of Hg@Cd-CP and HgCl2. (e) XPS Pb 4f of Pb@Cd-CP. (f) XPS N 1s of Cd-CP, Hg@Cd-CP, and Pb@Cd-CP.

In Figure 7b, the FT-IR spectrum of Hg@Cd-CP does not change significantly compared with that of Cd-CP, but the FT-IR spectrum of Pb@Cd-CP is significantly different.42 Compared with Cd-CP, some sharp peaks in the FT-IR spectrum of Pb@Cd-CP are obviously weakened or even disappeared.43 The peak at 1630 cm–1 should be attributed to the C=N, and the decrease in its intensity is probably caused by the coordination of Pb(II) with the uncoordinated N atom in the 3-bpdb ligand, which limits the stretching and vibration of C=N and lead to the disappearance of some peaks in the range of 640–700 cm–1 and 870–1060 cm–1.44

XPS further verified the different adsorption mechanisms of Hg(II) and Pb(II) (Figure 7c–f). Figure 7c shows the XPS spectra of Cd-CP before and after the adsorption of Hg(II) and Pb(II). The absorption spectrum clearly shows Hg 4f, Pb 4d, and Pb 4f peaks, which confirm the successful adsorption of Hg(II) and Pb(II).35,45 Compared with the binding energy of Hg(II) (104.38 and 100.33 eV) of HgCl2, that of Hg(II) (103.47 and 99.48 eV) of Hg@Cd-CP is low, which indicates that there is a strong electrostatic interaction between Hg(II) and Cd-CP (Figure 7d).1,46,47 After adsorption of Pb(II), the binding energy of the lower N 1s peak increases from 397.69 to 397.87 eV (Figure 7f),31,48 which indicates that the adsorption mechanism of Cd-CP for Pb(II) is the coordination between Pb(II) and the N on 3-bpdb ligand. XPS proves that Cd-CP has greater affinity for Hg(II) than Pb(II)1. This explains that the adsorption capacity of Hg(II) is greater than that of Pb(II),42,49 and when Hg(II) and Pb(II) exists together in the solution, the adsorption capacity of Cd-CP on Hg(II) is basically not reduced, but Pb(II) is hardly adsorbed.

Desorption Repeat Experiment

Desorption is one of the methods to verify the adsorption mechanism.50 When Hg@Cd-CP and Pb@Cd-CP are washed by the d 0.03 M HCl and 0.3 M thiourea solution, the Cd-CP after the adsorption of Pb(II) can be reused, but the Hg(II) adsorbed by Cd-CP cannot be washed away and cannot be reused. Even after being recycled for 5 times, Cd-CP can still maintain about 70% of the adsorption capacity of Pb(II) (Figure S7).

Conclusions

In this article, a new type of 2D Cd-CP has been successfully synthesized. Cd-CP exhibit a good removal effect for both Hg(II) and Pb(II), and the maximum adsorption capacity is 545 mg/g and 450 mg/g, respectively. Unexpectedly, thermodynamic studies have shown that the adsorption of Hg(II) and Pb(II) are completely different thermodynamic process, that the adsorption of Pb(II) by Cd-CP is a rare nonspontaneous process, while the adsorption of Hg(II) by Cd-CP is a common spontaneous process. Further research shows that the adsorption processes of Hg(II) and Pb(II) by Cd-CP use different adsorption mechanisms, and the affinity of Cd-CP to Hg(II) is much greater than that of Pb(II). This work provides an idea for the removal and separation of heavy metal ions in water.

Methods

Materials and Methods

All reagents and solvents used in the experiments were commercially available and used without further purification (Innochem, China). The FT-IR absorption spectra for Cd-CP, Hg@Cd-CP and Pb@Cd-CP were collected from KBr pellets using a Thermo Scientific FTIR-Nicolet iS10 spectrometer in the range of 4000–400 cm–1 (Thermo Scientific, U.S.A.). Powder X-ray diffraction (PXRD) was performed in the 2θ range of 5–50° on a Rigaku X-ray diffractometer with Cu Kα radiation (λ = 1.5418 Å) (Rigaku, Japan). Elemental analyses were carried out on a PerkinElmer 2400C elemental analyzer (Elementar, Germany). TGA data were acquired using a Mettler-Toledo simultaneous thermal analyzer from room temperature to 800 °C under an N2 atmosphere at a heating rate of 10 °C min–1 (Netzsch, Germany). XPS was performed using a K-Alpha X-ray photoelectron spectrometer (Thermo Scientific, USA). The morphology and energy-dispersive spectroscopy (EDS) data of Cd-CP, Hg@Cd-CP, and Pb@Cd-CP were obtained using a Nova NanoSEM 450 field-emission scanning electron microscope (SEM) at 10 Kv (Thermo Scientific, U.S.A.). The concentration of metal ions was determined with an iCAP6300 ICP-AES (Thermo Scientific, U.S.A.).

X-ray Crystallography

The selected single crystal with suitable dimensions was mounted on a glass capillary for X-ray diffraction analyses. Crystallographic data were collected on a Bruker Smart AXS CCD diffractometer with graphite-monochromated Mo Kα radiation (λ = 0.71073 Å) using the ω-scan technique (Bruker, Germany). Empirical absorption corrections were applied using the SADABS program. The structure was solved in each case by using the SHELXL package and refined by the full matrix least-squares method based on F2 using the SHELX-2014 program.51−53 All nonhydrogen atoms were located in different Fourier syntheses and finally refined with anisotropic thermal parameters. Crystallographic data and the details of data collection and structural refinements of Cd-CP are given in Table S1. The selected bond lengths and angles of Cd-CP are listed in Table S2. CCDC: 2101129 for Cd-CP

Adsorption Experimental System

First, 10 mg of Cd-CP and 30 mL of a heavy metal ions’ (HgCl2 and others are nitrate) aqueous solution are placed into a glass sample bottle of 40 mL in a shaker and shaken at 180 rpm for 24 h. Subsequently, the solution is then filtered with a 0.45-μm filter. The adsorbed filtrate is collected in a 10 mL centrifuge tube and analyzed for concentration of ions by ICP-AES.

The pH value of the solution is adjusted with 1 M HCl and 0.1 M NaOH solutions. The adsorption time of the kinetic research is extended to 72 h, at 298 K. The thermodynamic experiment is carried out in the range of 298–318 K.

Acknowledgments

This work was financially supported by the National Natural Science Foundation of China (No.22061047), the key Project of Scientific and Technological in Henan Province (No. 212102310343), the Foundation of Central Laboratory of Xinyang Agriculture and Forestry University (No. FCL202008), the Yunnan University’s Research Innovation Fund for Graduate Students (No. 2020205), and the Scientific Research Foundation Project of Yunnan Provincial Department of Education (No. 2021Y032). Authors thank Advanced Analysis and Measurement Center of Yunnan University for the sample testing service.

Supporting Information Available

The Supporting Information is available free of charge at https://pubs.acs.org/doi/10.1021/acsomega.1c06606.

  • Crystallographic data (ZIP)

  • Synthesis of 3-bpdb, BET data, PXRD data, TGA, EDS spectrum, thermodynamic parameter, crystal data, and selected bond lengths and angles (PDF)

Author Contributions

⊥ (R.-D.W., M.H.) These authors contributed equally to this work.

The authors declare no competing financial interest.

Supplementary Material

ao1c06606_si_001.zip (233.3KB, zip)
ao1c06606_si_002.pdf (450KB, pdf)

References

  1. Huang Z.; Zhao M.; Wang C.; Wang S.; Dai L.; Zhang L. Preparation of a Novel Zn(II)-Imidazole Framework as an Efficient and Regenerative Adsorbent for Pb, Hg, and As Ion Removal From Water. ACS Appl. Mater. Interfaces 2020, 12 (37), 41294–41302. 10.1021/acsami.0c10298. [DOI] [PubMed] [Google Scholar]
  2. Efome J. E.; Rana D.; Matsuura T.; Lan C. Q. Insight Studies on Metal-Organic Framework Nanofibrous Membrane Adsorption and Activation for Heavy Metal Ions Removal from Aqueous Solution. ACS Appl. Mater. Interfaces 2018, 10 (22), 18619–18629. 10.1021/acsami.8b01454. [DOI] [PubMed] [Google Scholar]
  3. Kumar P.; Bansal V.; Kim K.-H.; Kwon E. E. Metal-organic frameworks (MOFs) as futuristic options for wastewater treatment. J. Ind. Eng. Chem. 2018, 62, 130–145. 10.1016/j.jiec.2017.12.051. [DOI] [Google Scholar]
  4. Zhang P.; Xiang M.; He T.; Liu H.; Yu S.; Pan X.; Qiu F.; Zhu Z.; Zou Y.; Chen Y. High-efficiency water purification for methyl orange and lead(II) by eco-friendly magnetic sulfur-doped graphene-like carbon-supported layered double oxide. J. Hazard. Mater. 2021, 419, 126406. 10.1016/j.jhazmat.2021.126406. [DOI] [PubMed] [Google Scholar]
  5. Esrafili L.; Firuzabadi F. D.; Morsali A.; Hu M. L. Reuse of Predesigned Dual-Functional Metal Organic Frameworks (DF-MOFs) after Heavy Metal Removal. J. Hazard. Mater. 2021, 403, 123696. 10.1016/j.jhazmat.2020.123696. [DOI] [PubMed] [Google Scholar]
  6. Rego R. M.; Kuriya G.; Kurkuri M. D.; Kigga M. MOF based engineered materials in water remediation: Recent trends. J. Hazard. Mater. 2021, 403, 123605. 10.1016/j.jhazmat.2020.123605. [DOI] [PubMed] [Google Scholar]
  7. Peng Q.; Guo J.; Zhang Q.; Xiang J.; Liu B.; Zhou A.; Liu R.; Tian Y. Unique lead adsorption behavior of activated hydroxyl group in two-dimensional titanium carbide. J. Am. Chem. Soc. 2014, 136 (11), 4113–6. 10.1021/ja500506k. [DOI] [PubMed] [Google Scholar]
  8. Abdollahi N.; Akbar Razavi S. A.; Morsali A.; Hu M. L. High capacity Hg(II) and Pb(II) removal using MOF-based nanocomposite: Cooperative effects of pore functionalization and surface-charge modulation. J. Hazard. Mater. 2020, 387, 121667. 10.1016/j.jhazmat.2019.121667. [DOI] [PubMed] [Google Scholar]
  9. Liu F.; Xiong W.; Feng X.; Shi L.; Chen D.; Zhang Y. A novel monolith ZnS-ZIF-8 adsorption material for ultraeffective Hg (II) capture from wastewater. J. Hazard. Mater. 2019, 367, 381–389. 10.1016/j.jhazmat.2018.12.098. [DOI] [PubMed] [Google Scholar]
  10. Mehdinia A.; Jahedi Vaighan D.; Jabbari A. Cation Exchange Superparamagnetic Al-Based Metal Organic Framework (Fe3O4/MIL-96(Al)) for High Efficient Removal of Pb(II) from Aqueous Solutions. ACS Sustainable Chem. Eng. 2018, 6 (3), 3176–3186. 10.1021/acssuschemeng.7b03301. [DOI] [Google Scholar]
  11. Zare-Dorabei R.; Ferdowsi S. M.; Barzin A.; Tadjarodi A. Highly efficient simultaneous ultrasonic-assisted adsorption of Pb(II), Cd(II), Ni(II) and Cu(II) ions from aqueous solutions by graphene oxide modified with 2,2′-dipyridylamine: Central composite design optimization. Ultrason. Sonochem. 2016, 32, 265–276. 10.1016/j.ultsonch.2016.03.020. [DOI] [PubMed] [Google Scholar]
  12. Wang R.-D.; He L.; Zhu R.-R.; Jia M.; Zhou S.; Tang J.; Zhang W.-Q.; Du L.; Zhao Q.-H. Highly efficient and selective capture Pb(II) through a novel metal-organic framework containing bifunctional groups. J. Hazard. Mater. 2022, 427, 127852. 10.1016/j.jhazmat.2021.127852. [DOI] [PubMed] [Google Scholar]
  13. Zhang P.; Xu Y.; Guo K.; Yin Y.; Wang J.; Zeng Y. Hierarchical-pore UiO-66 modified with Ag(+) for pi-complexation adsorption desulfurization. J. Hazard. Mater. 2021, 418, 126247. 10.1016/j.jhazmat.2021.126247. [DOI] [PubMed] [Google Scholar]
  14. Li B.; Wen H. M.; Cui Y.; Zhou W.; Qian G.; Chen B. Emerging Multifunctional Metal-Organic Framework Materials. Adv. Mater. 2016, 28 (40), 8819–8860. 10.1002/adma.201601133. [DOI] [PubMed] [Google Scholar]
  15. Yang C.; Tian J.; Jiang F.; Chen Q.; Hong M. Functionalized Metal-Organic Frameworks for Hg(II) and Cd(II) Capture: Progresses and Challenges. Chem. Rec. 2021, 21 (6), 1455–1472. 10.1002/tcr.202000187. [DOI] [PubMed] [Google Scholar]
  16. Yan X.; Li P.; Song X.; Li J.; Ren B.; Gao S.; Cao R. Recent progress in the removal of mercury ions from water based MOFs materials. Coord. Chem. Rev. 2021, 443, 214034. 10.1016/j.ccr.2021.214034. [DOI] [Google Scholar]
  17. Shayegan H.; Ali G. A. M.; Safarifard V. Recent Progress in the Removal of Heavy Metal Ions from Water Using Metal-Organic Frameworks. ChemistrySelect 2020, 5 (1), 124–146. 10.1002/slct.201904107. [DOI] [Google Scholar]
  18. Zare-Dorabei R.; Darbandsari M. S.; Moghimi A.; Tehrani M. S.; Nazerdeylami S. Synthesis, characterization and application of cyclam-modified magnetic SBA-15 as a novel sorbent and its optimization by central composite design for adsorption and determination of trace amounts of lead ions. RSC Adv. 2016, 6 (110), 108477–108487. 10.1039/C6RA21895D. [DOI] [Google Scholar]
  19. Rouhani F.; Morsali A. Fast and Selective Heavy Metal Removal by a Novel Metal-Organic Framework Designed with In-Situ Ligand Building Block Fabrication Bearing Free Nitrogen. Chemistry 2018, 24 (21), 5529–5537. 10.1002/chem.201706016. [DOI] [PubMed] [Google Scholar]
  20. Sreejalekshmi K. G.; Krishnan K. A.; Anirudhan T. S. Adsorption of Pb(II) and Pb(II)-citric acid on sawdust activated carbon: Kinetic and equilibrium isotherm studies. J. Hazard. Mater. 2009, 161 (2–3), 1506–13. 10.1016/j.jhazmat.2008.05.002. [DOI] [PubMed] [Google Scholar]
  21. Tahmasebi E.; Masoomi M. Y.; Yamini Y.; Morsali A. Application of mechanosynthesized azine-decorated zinc(II) metal-organic frameworks for highly efficient removal and extraction of some heavy-metal ions from aqueous samples: a comparative study. Inorg. Chem. 2015, 54 (2), 425–33. 10.1021/ic5015384. [DOI] [PubMed] [Google Scholar]
  22. Bao S.; Li K.; Ning P.; Peng J.; Jin X.; Tang L. Highly effective removal of mercury and lead ions from wastewater by mercaptoamine-functionalised silica-coated magnetic nano-adsorbents: Behaviours and mechanisms. Appl. Surf. Sci. 2017, 393, 457–466. 10.1016/j.apsusc.2016.09.098. [DOI] [Google Scholar]
  23. Xiong C.; Wang S.; Hu P.; Huang L.; Xue C.; Yang Z.; Zhou X.; Wang Y.; Ji H. Efficient Selective Removal of Pb(II) by Using 6-Aminothiouracil-Modified Zr-Based Organic Frameworks: From Experiments to Mechanisms. ACS Appl. Mater. Interfaces 2020, 12 (6), 7162–7178. 10.1021/acsami.9b19516. [DOI] [PubMed] [Google Scholar]
  24. Yu C.; Han X.; Shao Z.; Liu L.; Hou H. High Efficiency and Fast Removal of Trace Pb(II) from Aqueous Solution by Carbomethoxy-Functionalized Metal–Organic Framework. Cryst. Growth Des. 2018, 18 (3), 1474–1482. 10.1021/acs.cgd.7b01427. [DOI] [Google Scholar]
  25. Fu L.; Wang S.; Lin G.; Zhang L.; Liu Q.; Fang J.; Wei C.; Liu G. Post-functionalization of UiO-66-NH2 by 2,5-Dimercapto-1,3,4-thiadiazole for the high efficient removal of Hg(II) in water. J. Hazard. Mater. 2019, 368, 42–51. 10.1016/j.jhazmat.2019.01.025. [DOI] [PubMed] [Google Scholar]
  26. Liu Q.; Zhang Q.; Liu B.; Ma J. A new synthesis and adsorption mechanism of ZrO2 based metal-organic frames for efficient removal of mercury ions from aqueous solution. Ceram. Int. 2019, 45 (12), 15720–15724. 10.1016/j.ceramint.2019.04.246. [DOI] [Google Scholar]
  27. Xin X.; Wei Q.; Yang J.; Yan L.; Feng R.; Chen G.; Du B.; Li H. Highly efficient removal of heavy metal ions by amine-functionalized mesoporous Fe3O4 nanoparticles. Chem. Eng. J. 2012, 184, 132–140. 10.1016/j.cej.2012.01.016. [DOI] [Google Scholar]
  28. Venkateswarlu S.; Yoon M. Surfactant-free green synthesis of Fe3O4 nanoparticles capped with 3,4-dihydroxyphenethylcarbamodithioate: stable recyclable magnetic nanoparticles for the rapid and efficient removal of Hg(II) ions from water. Dalton Trans. 2015, 44 (42), 18427–37. 10.1039/C5DT03155A. [DOI] [PubMed] [Google Scholar]
  29. Liu T.; Yang M.; Wang T.; Yuan Q. Prediction Strategy of Adsorption Equilibrium Time Based on Equilibrium and Kinetic Results To Isolate Taxifolin. Ind. Eng. Chem. Res. 2012, 51 (1), 454–463. 10.1021/ie201197r. [DOI] [Google Scholar]
  30. Ghaedi A. M.; Panahimehr M.; Nejad A. R. S.; Hosseini S. J.; Vafaei A.; Baneshi M. M. Factorial experimental design for the optimization of highly selective adsorption removal of lead and copper ions using metal organic framework MOF-2 (Cd). J. Mol. Liq. 2018, 272, 15–26. 10.1016/j.molliq.2018.09.051. [DOI] [Google Scholar]
  31. Huang J.; Ye M.; Qu Y.; Chu L.; Chen R.; He Q.; Xu D. Pb (II) removal from aqueous media by EDTA-modified mesoporous silica SBA-15. J. Colloid Interface Sci. 2012, 385 (1), 137–46. 10.1016/j.jcis.2012.06.054. [DOI] [PubMed] [Google Scholar]
  32. Nazerdeylami S.; Zare-Dorabei R. Simultaneous adsorption of Hg2+, Cd2+ and Cu2+ ions from aqueous solution with mesoporous silica/DZ and conditions optimize with experimental design: kinetic and isothermal studies. Micro Nano Lett. 2019, 14 (8), 823–827. 10.1049/mnl.2018.5775. [DOI] [Google Scholar]
  33. Xu G.; Zhao Y.; Hou L.; Cao J.; Tao M.; Zhang W. A recyclable phosphinic acid functionalized polyacrylonitrile fiber for selective and efficient removal of Hg2+. Chem. Eng. J. 2017, 325, 533–543. 10.1016/j.cej.2017.04.135. [DOI] [Google Scholar]
  34. Jeon C.; Höll W. H. Chemical modification of chitosan and equilibrium study for mercury ion removal. Water Res. 2003, 37 (19), 4770–4780. 10.1016/S0043-1354(03)00431-7. [DOI] [PubMed] [Google Scholar]
  35. Fu L.; Wang S.; Lin G.; Zhang L.; Liu Q.; Zhou H.; Kang C.; Wan S.; Li H.; Wen S. Post-modification of UiO-66-NH2 by resorcyl aldehyde for selective removal of Pb(II) in aqueous media. J. Cleaner Prod. 2019, 229, 470–479. 10.1016/j.jclepro.2019.05.043. [DOI] [Google Scholar]
  36. Huang L.; He M.; Chen B.; Hu B. A mercapto functionalized magnetic Zr-MOF by solvent-assisted ligand exchange for Hg2+ removal from water. J. Mater. Chem. A 2016, 4 (14), 5159–5166. 10.1039/C6TA00343E. [DOI] [Google Scholar]
  37. Zhu H.; Yuan J.; Tan X.; Zhang W.; Fang M.; Wang X. Efficient removal of Pb2+ by Tb-MOFs: identifying the adsorption mechanism through experimental and theoretical investigations. Environ. Sci.: Nano 2019, 6 (1), 261–272. 10.1039/C8EN01066H. [DOI] [Google Scholar]
  38. Ru J.; Wang X.; Wang F.; Cui X.; Du X.; Lu X. UiO series of metal-organic frameworks composites as advanced sorbents for the removal of heavy metal ions: Synthesis, applications and adsorption mechanism. Ecotoxicol. Environ. Saf.. 2021, 208, 111577. 10.1016/j.ecoenv.2020.111577. [DOI] [PubMed] [Google Scholar]
  39. Shayegan H.; Ali G. A. M.; Safarifard V. Amide-Functionalized Metal–Organic Framework for High Efficiency and Fast Removal of Pb(II) from Aqueous Solution. J. Inorg. Organomet. Polym. Mater. 2020, 30 (8), 3170–3178. 10.1007/s10904-020-01474-0. [DOI] [Google Scholar]
  40. Zhang J.; Xiong Z.; Li C.; Wu C. Exploring a thiol-functionalized MOF for elimination of lead and cadmium from aqueous solution. J. Mol. Liq. 2016, 221, 43–50. 10.1016/j.molliq.2016.05.054. [DOI] [Google Scholar]
  41. Zhang L.; Zhang W.; Shi J.; Hua Z.; Li Y.; Yan J. A new thioether functionalized organic-inorganic mesoporous composite as a highly selective and capacious Hg2+ adsorbent. Chem. Commun. (Camb) 2003, (2), 210–1. 10.1039/b210457a. [DOI] [PubMed] [Google Scholar]
  42. Deng M.; Huang Y.; Zhang X.; Feng Z.; Gou J.; Sun B. Preparation of a novel chelating resin bearing amidinothiourea moieties and its removal properties for Hg(II) ions in aqueous solution. Sep. Sci. Technol. 2016, 1–10. 10.1080/01496395.2016.1166135. [DOI] [Google Scholar]
  43. Ke F.; Qiu L. G.; Yuan Y. P.; Peng F. M.; Jiang X.; Xie A. J.; Shen Y. H.; Zhu J. F. Thiol-functionalization of metal-organic framework by a facile coordination-based postsynthetic strategy and enhanced removal of Hg2+ from water. J. Hazard. Mater. 2011, 196, 36–43. 10.1016/j.jhazmat.2011.08.069. [DOI] [PubMed] [Google Scholar]
  44. Xiong C.; Jia Q.; Chen X.; Wang G.; Yao C. Optimization of Polyacrylonitrile-2-aminothiazole Resin Synthesis, Characterization, and Its Adsorption Performance and Mechanism for Removal of Hg(II) from Aqueous Solutions. Ind. Eng. Chem. Res. 2013, 52 (14), 4978–4986. 10.1021/ie3033312. [DOI] [Google Scholar]
  45. Lin D.; Liu X.; Huang R.; Qi W.; Su R.; He Z. One-pot synthesis of mercapto functionalized Zr-MOFs for the enhanced removal of Hg(2+) ions from water. Chem. Commun. (Camb) 2019, 55 (47), 6775–6778. 10.1039/C9CC03481A. [DOI] [PubMed] [Google Scholar]
  46. Tian J.; Shi C.; Xiao C.; Jiang F.; Yuan D.; Chen Q.; Hong M. Introduction of Flexibility into a Metal-Organic Framework to Promote Hg(II) Capture through Adaptive Deformation. Inorg. Chem. 2020, 59 (24), 18264–18275. 10.1021/acs.inorgchem.0c02781. [DOI] [PubMed] [Google Scholar]
  47. Wang C.; He C.; Luo Y.-H.; Su S.; Wang J.-Y.; Hong D.-L.; He X.-T.; Chen C.; Sun B.-W. Efficient mercury chloride capture by ultrathin 2D metal-organic framework nanosheets. Chem. Eng. J. 2020, 379, 122337. 10.1016/j.cej.2019.122337. [DOI] [Google Scholar]
  48. Chen D.; Shen W.; Wu S.; Chen C.; Luo X.; Guo L. Ion exchange induced removal of Pb(ii) by MOF-derived magnetic inorganic sorbents. Nanoscale 2016, 8 (13), 7172–9. 10.1039/C6NR00695G. [DOI] [PubMed] [Google Scholar]
  49. Walcarius A.; Delacôte C. Mercury(II) binding to thiol-functionalized mesoporous silicas: critical effect of pH and sorbent properties on capacity and selectivity. Anal. Chim. Acta 2005, 547 (1), 3–13. 10.1016/j.aca.2004.11.047. [DOI] [Google Scholar]
  50. Amiri-Yazani T.; Zare-Dorabei R.; Rabbani M.; Mollahosseini A. Highly efficient ultrasonic-assisted pre-concentration and simultaneous determination of trace amounts of Pb (II) and Cd (II) ions using modified magnetic natural clinoptilolite zeolite: Response surface methodology. Microchem. J. 2019, 146, 498–508. 10.1016/j.microc.2019.01.050. [DOI] [Google Scholar]
  51. Burla M. C.; Caliandro R.; Camalli M.; Carrozzini B.; Cascarano G. L.; De Caro L.; Giacovazzo C.; Polidori G.; Siliqi D.; Spagna R. IL MILIONE: a suite of computer programs for crystal structure solution of proteins. J. Appl. Crystallogr. 2007, 40 (3), 609–613. 10.1107/S0021889807010941. [DOI] [Google Scholar]
  52. Hubschle C. ShelXle: a Qt graphical user interface for SHELXL. Acta Crystallogr., Sect. A 2019, 75 (a1), a187. 10.1107/S0108767319098143. [DOI] [PMC free article] [PubMed] [Google Scholar]
  53. Hubschle C. B.; Sheldrick G. M.; Dittrich B. ShelXle: a Qt graphical user interface for SHELXL. J. Appl. Crystallogr. 2011, 44 (6), 1281–1284. 10.1107/S0021889811043202. [DOI] [PMC free article] [PubMed] [Google Scholar]

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