Next Article in Journal
Anti-Carcinogenic Glucosinolates in Cruciferous Vegetables and Their Antagonistic Effects on Prevention of Cancers
Next Article in Special Issue
Biobased Poly(ethylene furanoate) Polyester/TiO2 Supported Nanocomposites as Effective Photocatalysts for Anti-inflammatory/Analgesic Drugs
Previous Article in Journal
Can Adsorption on Graphene be Used for Isotopic Enrichment? A DFT Perspective
Previous Article in Special Issue
Effect of High Pressure Treatment on Poly(lactic acid)/Nano–TiO2 Composite Films
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Molecules
Volume 23
Issue 11
10.3390/molecules23112982
molecules-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Adsorption of Cu(II) and Zn(II) Ions from Aqueous Solution by Gel/PVA-Modified Super-Paramagnetic Iron Oxide Nanoparticles

by
Anudari Dolgormaa
1,
Chang-jiang Lv
1,
Yin Li
1,
Jian Yang
2,
Jun-xing Yang
3,
Peng Chen
1,
Hong-peng Wang
1,* and
Jun Huang
1,*
1
Zhejiang Provincial Key Lab for Chemical and Biological Processing Technology of Farm Product, School of Biological and Chemical Engineering, Zhejiang University of Science and Technology, Hangzhou 310023, China
2
State Key Laboratory Breeding Base of Dao-di Herbs, National Resource Center for Chinese Material Medical, China Academy of Chinese Medical Sciences, Beijing 100700, China
3
Institute of Geographical Sciences and Natural Resources Research, Chinese Academy of Sciences, Beijing 100101, China
*
Authors to whom correspondence should be addressed.
Molecules 2018, 23(11), 2982; https://doi.org/10.3390/molecules23112982
Submission received: 13 October 2018 / Revised: 9 November 2018 / Accepted: 12 November 2018 / Published: 15 November 2018
(This article belongs to the Special Issue Polymer Composites and Nanocomposites with Enhanched Properties)
Browse Figures
Review Reports Versions Notes

Abstract

:
Super-paramagnetic iron oxide nanoparticles (SPIONs)/gelatin (gel)/polyvinyl alcohol (PVA) nanoparticles were designed and synthesized by the co-precipitation method and further modified with gel and PVA. These nanoparticles were used for the removal of Cu(II) and Zn(II) from aqueous solutions. The adsorbents were rich in different functional groups for chemisorption and showed effective adsorption properties. The adsorption of Cu(II) and Zn(II) on the SPIONs/gel and SPIONs/gel/PVA materials were investigated with respect to pH, adsorption kinetics, and adsorption isotherms. The adsorption data was fitted to the Langmuir, Freundlich, and Sips models at the optimum pH 5.2 (±0.2) over 60 min; SPIONs/gel showed maximum adsorption capacities of 47.594 mg/g and 40.559 mg/g for Cu(II) and Zn(II); SPIONs/gel/PVA showed those of 56.051 mg/g and 40.865 mg/g, respectively. The experimental data fitted the pseudo-second-order model, indicating that the process followed chemical monolayer adsorption. In addition, the SPIONs/gel/PVA showed better stability and Cu(II) adsorption efficiency than SPIONs/gel.

Graphical Abstract

1. Introduction

In the past decade, toxic heavy metal ion pollution has had the harmful effects on the environment. Heavy metal ions such as Pb, Cu, Ni, Zn, Cd, and Cr are toxic to humans, animals, and plants even at low concentrations [1]. The accumulation of Cu(II) in living organisms can cause liver and brain damage, heart disease, skin conditions, and pancreas issues [2]. Zn(II) poisoning in humans causes nausea, dizziness, and dehydration [3]. Many technologies have been developed for the removal of heavy metal ions from water, such as chemical precipitation, electrochemical reduction, ion exchange, membrane separation, solvent extraction, coagulation, and adsorption [4]. However, the technologies have their own disadvantages as known as ineffective at lower heavy metal ions concentration, are not economical, and have specific working conditions [5]. Among these technologies, the adsorption process is attractive because of its low cost and high efficiency. Widely used adsorbents include carbonaceous materials, clays, zeolites, composite materials, biomass, nanomaterials, and polymeric materials [6,7,8]. The efficiency of adsorbents depends on their specific surface areas and their chemical stabilities [9]. Therefore, the choice of suitable materials for the adsorption of heavy metal ions from wastewater is very important.
The use of nanoparticle materials offers many advantages because of their small sizes and interesting physical properties. The use of magnetic nanoparticles is greatly interesting, especially in wastewater treatment. Magnetic sorbents could be easily separated by an external magnetic field from the liquid phase, which would assist in removing organic and inorganic pollutants using these materials [10]. The adsorptive removal of heavy metals, including those in aqueous solutions, by magnetic nanoparticles has been reported [8,11,12,13].
Gelatin is a natural water-soluble biopolymer with a variety of advantages such as environmental friendliness, biodegradability, biocompatibility, and low cost. It is feasible to use gelatin as an adsorbent material for various ionic species because of its abundant –OH, –NH2, and –COOH groups [14,15]. Therefore, gelatin coated on the surfaces of magnetic nanoparticles could enhance their adsorption capacity for heavy metal ions through the reactivity of its own functional groups [16,17,18]. Magnetic nanoparticles modified by gelatin have been reported in use for scavenging U(VI) under a series of environmental conditions [14]. However, the drawbacks of gelatin include its poor mechanical properties and rapid degradation in wet conditions [19,20,21]. The blending of gelatin with other polymers is one effective strategy to improve the physical performance [22], such as adsorption efficiency and reusability.
Poly (vinyl alcohol) (PVA) is a widely used polymer with good biocompatibility, non-toxicity, high mechanical strength, thermal stability, pH stability, and low cost. Composite materials of gelatin and PVA have good adsorption capacities for heavy metals [23,24]. Hui et al. [6] prepared PVA/gelatin hydrogel beads for Pb(II) removal, and the maximum adsorption capacity of Pb(II) was 211.86 mg/g and the adsorption capacity remained stable in four sequential adsorption–desorption cycles. Hence, coating PVA on the surface of gelatin-modified magnetic nanoparticles might reduce the aggregation of magnetic nanoparticles and provide good adsorption properties for heavy metals. A SPIONs/gelatin composite material has already been synthesized for drug delivery, chemotherapy, and the cleansing of radionuclide-bearing effluents, but not for the removal of Cu(II) and Zn(II). Moreover, SPIONs/gelatin and SPIONs/gelatin/PVA composite materials are reported for the first time here in the removal of heavy metal ions from aqueous solution.
In this work, gelatin/PVA-modified super-paramagnetic iron oxide nanoparticles (SPIONs) were prepared by the co-precipitation of Fe(II) and Fe(III) ions in an ammonia solution, and then treated with gelatin and PVA, characterized, and evaluated for adsorption of Cu(II) and Zn(II) from aqueous solutions. The objective of this work was to explore the feasibility of SPIONs/gelatin (SPIONs/gel) and SPIONs/gelatin/poly (vinyl alcohol) (SPIONs/gel/PVA) composites and to use them for removing Cu(II) and Zn(II) from aqueous solutions.

2. Results and Discussion

2.1. Characterization of the Adsorbents

The surface functional groups on the modified magnetic nanoparticles were determined by FTIR analysis; the spectra are shown in Figure 1. The Fe–O bond stretching at 566–575 cm−1 can be found in all samples [25,26]. Gelatin has functional groups such as –OH and –NH groups (between 3200–3500 cm−1), –CH2 group (asymmetric C–H stretching vibration 2946 cm−1 and symmetric C–H stretching vibration 2870 cm−1), amide group (1648 cm−1 and 1534 cm−1) [14,16,27]. PVA has functional groups such as –OH group (3200–3500 cm−1), –CH2 groups (2866 cm−1), C–O–C groups (1090 cm−1 stretching vibration) [6,7,28].
The FTIR results of gelatin, PVA, SPIONs/gel, and SPIONs/gel/PVA showed the carboxyl and amide groups at the range of 1632–1648 cm−1 and hydroxyl group at 1335–1396 cm−1. Moreover, as can be seen from FTIR results of SPIONs/gel and SPIONs/gel/PVA, the PVA and gelatin layers cannot be observed easily because the gelatin and PVA showed similar functional groups in their spectra, and small signals of the amide bands and C–O stretching vibrations were observed from the SPIONs/gel and SPIONs/gel/PVA. These functional groups are favorable for the adsorption of heavy metal ions.
The TEM images of SPIONs (a), SPIONs/gel (b), and SPIONs/gel/PVA (c) are shown in Figure 2. The TEM images showed that SPIONs, SPIONs/gel, and SPIONs/gel/PVA particles are quasi-spherical in shape with rough surfaces. The sizes of SPIONs, SPIONs/gel, and SPIONs/gel/PVA were measured to be approximately 14.02 nm, 22.63 nm, and 18.6 nm, respectively, from their TEM images. Furthermore, the DLS measurement showed the sizes of SPIONs, SPIONs/gel, and SPIONs/gel/PVA were with 15.2 nm, 22.47 nm, and 17.74 nm, respectively. The size of the magnetic nanoparticles results from TEM and DLS were identical.
Figure 3 showed XRD diffraction patterns of SPIONs, SPIONs/gel, and SPIONs/gel/PVA.
The diffraction pattern for SPIONs had eight broad peaks at 31.249°, 36.820°, 38.524°, 44.762°, 55.622°, 59.303°, 65.185°, and 77.249°, corresponding to the (220), (311), (222), (400), (422), (511), (440), and (533) planes, respectively [7,29]. All of the observed diffraction peaks were indexed by the structure of the Fe3O4. Meanwhile, the peaks of SPIONs/gel and SPIONs/gel/PVA showed a highly crystalline nature.
The magnetization values of the pure SPIONs/gel and SPIONs/gel/PVA were 56.382 and 57.765 emu/g, respectively. Figure 4 showed that the magnetization properties of these two materials were very similar, the modified layers should not influence the magnetization efficiency of the nanoparticles, since the SPIONs/gel and SPIONs/gel/PVA have very thin modified layers of gelatin and PVA. This results are consistent with the TGA results of the nanoparticles. It is clear that SPIONs/gel and SPIONs/gel/PVA samples can be easily separated from aqueous solution by applying an external magnetic field [14,30].
The TGA curves of SPIONs, SPIONs/gel, and SPIONs/gel/PVA at the temperature range 50–800 °C are shown in Figure 5. The samples were subjected to heating to 800 °C at a heating rate of 10 °C/min. The Figure 5 showed that the mass of the materials was reduced to some extent at the temperature range of 50–200 °C, indicating the removal of adsorbed water and some oxygen-containing functional groups at this temperature range. At the first stage, the mass losses of SPIONs/gel and SPIONs/gel/PVA at temperatures below 150 °C were 0.75% and 1.92%, respectively. In the second stage, when the temperature was between 150 and 250 °C, the mass losses of SPIONs/gel and SPIONs/gel/PVA were 0.87% and 2.58%, respectively. In the third stage, when the temperature was between 250 and 470 °C, the mass losses of the SPIONs/gel and SPIONs/gel/PVA were 9.85% and 9.42%, respectively. It was observed that the SPION/gel had a total weight loss of approximately 11.47% and SPIONs/gel/PVA had a total weight loss of approximately 13.92%. Therefore, the weight fraction of gelatin in the SPIONs/gel composite is approximately 10.72% and the weight fraction of PVA in the SPIONs/gel/PVA composite is approximately 1.25%, which suggested the thickness of organic layer of SPIONs/gel and SPIONs/gel/PVA are very thin, and both particles have similar thickness of organic layer.

2.2. Adsorption

2.2.1. Effect of pH

The effects of pH on the SPIONs/gel and SPIONs/gel/PVA are shown in Figure 6. As can be seen from Figure 6 with the increase of the pH of the aqueous solution, the adsorption capacity for Cu(II) and Zn(II) on both adsorbents is increased. At low pH, this may relate to the higher concentration and mobility of H+ ions. Meanwhile, minimal adsorption is favored by the high solubility and ionization of metallic salts in the acidic medium [31]. The suitable pH for Cu(II) and Zn(II) removal for all adsorbents is determined as 5–6, at which the maximum adsorption capacity occurs for both adsorbents. Moreover, the precipitation of heavy metal hydroxides occurs for a pH enhanced further [32]. If the pH is more than 6, the heavy metal ions will be precipitated from the aqueous solution [33]. Accordingly, the initial pH of the solutions was 5.2 (±0.2) for both solutions in the following adsorption experiments.

2.2.2. Adsorption Kinetics

The effects of contact time on the kinetics of Cu(II) and Zn(II) adsorption by the SPIONs/gel and SPIONs/gel/PVA adsorbents are displayed in Figure 7. As can be seen in Figure 7, the removal of Cu(II) and Zn(II) on the SPIONs/gel and SPIONs/gel/PVA is rapid in the initial 5 min, and the removal of Cu(II) increases sharply in the initial 30 min before continuing at a slower rate and finally reaching equilibrium at 60 min. Therefore, 60 min was chosen as the optimum contact time for the adsorption experiments. The adsorption rate is faster than those shown by some reported magnetic adsorbent materials [34,35,36]. Keochaiyom et al. [4] reported that the adsorption equilibrium time was 24 h for Zn(II), Cd(II), Pb(II) on magnetic chlorapatite nanoparticles. Ghasemi et al. [36] reported that the adsorption process reached equilibrium within 90 min for the removal of Zn(II) from an aqueous solution.
In order to investigate the mechanisms of adsorption of Cu(II) and Zn(II) on the SPIONs/gel and SPIONs/gel/PVA, fitting was determined according to the pseudo-first-order and pseudo-second-order kinetic models. The sorption kinetic parameters including K1, K2, Qt, and the correlation coefficients R2 are listed in Table 1. As can be seen, the correlation coefficients R2 for the pseudo-second-order model are higher than those for the pseudo-first-order model. The calculated Qt values are close to the experimental Qe values with the pseudo-second-order model for both adsorbents. These results suggest that the sorption kinetics of heavy metal ions on SPIONs/gel and SPIONs/gel/PVA can be described by the pseudo-second-order model, which means that the adsorption rate depends on chemical sorption [37]. For illustration, functional groups such as carboxyl, amino, and hydroxyl groups [27,28,38] on the surfaces of both adsorbents, as characterized by the FTIR results, were active in heavy metal ion binding on the SPIONs/gel and SPIONs/gel/PVA. Similar results have been reported by Vo et al. [28] and Wang et al. [38] for the removal of heavy metal ions by other magnetic adsorbents.

2.2.3. Adsorption Isotherms

The adsorption isotherms of Cu(II) and Zn(II) on SPIONs/gel and SPIONs/gel/PVA at pH 5 are presented Figure 8. It can be seen from Figure 8 that the adsorption capacities of Cu(II) and Zn(II) on both adsorbents are increased with increasing initial concentrations of the metal ions. The SPIONs/gel showed the equilibrium adsorption capacities of 20.1213 mg/g and 14.9092 mg/g for Cu(II) and Zn(II); SPIONs/gel/PVA showed those of 13.7879 mg/g and 9.7803 mg/g, respectively, at the equilibrium concentration of 0.1 mg/mL and 25 °C. The adsorption capacity of Cu(II) on bare iron oxide was just 0.15 mg/g, much less than that on another two adsorbents, so that the following adsorption experiments were carried on SPIONs/gel and SPIONs/gel/PVA. Moreover, the adsorption capacities of Cu(II) on SPIONs/gel and SPIONs/gel/PVA are much more than those of Zn(II); adsorption on SPIONs/gel in particular shows a higher adsorption capacity than SPIONs/gel/PVA.
The experimental data points were analyzed by the Langmuir, Freundlich, and Sips models.
The calculated parameters together with the correlation coefficients for the Langmuir, Freundlich, and Sips models are shown in Table 2. As seen in Table 2, the adsorption of Cu(II) and Zn(II) on both adsorbents is well correlated (R2 < 0.99) with the Langmuir model, Freundlich model, and Sips model. All models show good fits with the experimental data. The Langmuir model describes monolayer adsorption on the homogenous surface of the adsorbents [29]. The dimensionless separation parameter RL is the essential characteristic of the Langmuir isotherm model and expressed by:
R L = 1 / ( 1 + K L C 0 )
where C0 is initial concentration of the metal ions (mg/mL) and the definition of KL is as explained for Equation (4).
The RL value is classified as irreversible (RL = 0), linear (RL = 1), favorable (0 < RL < 1), and unfavorable (RL > 1) [39,40]. In this work, all the values of RL are between 0.1305 and 0.2274, indicating that the experimental data fall between zero and 1, which is an indication of the favorable adsorption of the two metal ions on the adsorbents.
The Freundlich model describes the surface heterogeneity of the sorbent, indicating multilayer adsorption. The 1/n value from the Freundlich model between 0.5 and 1.0, represents favorable adsorption; on the other hand, a value of 1/n > 1 suggests weak adsorption bonds between the adsorbent and adsorbate, indicating unfavorable adsorption [41]. The 1/n values from the Freundlich model for the adsorption of SPIONs/gel were 0.3164 and 0.3367 for Cu(II) and Zn(II); SPIONs/gel/PVA were those of 0.4373 and 0.4399, respectively. These values are lower than 1, indicating that the adsorption of Cu(II) and Zn(II) is favorable on the both adsorbents.
The Sips model is the combination of Langmuir and Freundlich model and explains adsorption on both homogeneous and heterogeneous surfaces. Its behavior is similar to Freundlich model; it reduces to the Freundlich isotherm at a low adsorbate concentration and to the Langmuir model at a high adsorbate concentration [42,43]. The adsorption of Cu(II) and Zn(II) on both adsorbents appears to be a monolayer adsorption process, because the Langmuir and Sips models both fit better than the Freundlich model. The correlation coefficients R2 from the Langmuir and Sips models are nearly 1, suggesting that the adsorption of Cu(II) and Zn(II) on both adsorbents appears to be a monolayer adsorption process. SPIONs/gel showed the maximum adsorption capacities of 47.594 mg/g and 40.559 mg/g for Cu(II) and Zn(II); SPIONs/gel/PVA showed those of 56.051 mg/g and 40.865 mg/g, respectively. Meanwhile, the interaction of carboxyl groups in both adsorbents with Cu(II) and Zn(II) formed bidentate chelates, a chemical sorption process [6].
The maximum adsorption capacities of both adsorbents were higher than the equilibrium adsorption capacities and SPIONs/gel/PVA showed a higher adsorption capacity than SPIONs/gel, indicating that the adsorption properties were improved significantly by PVA. These results suggest that the SPIONs/gel/PVA adsorbent showed monolayer adsorption for low concentrations of metal ions, while multilayer adsorption processes occur for increased concentrations. The SPIONs/gel/PVA has more hydroxyl groups on the surface than SPIONs/gel and greater rigidity, which increased the maximum adsorption capacities for both ions. The maximum adsorption capacity of Cu(II) is higher than that of Zn(II), meaning that the chelating effect is more suitable for Cu(II). Meanwhile, Cu(II) and Zn(II) have different characteristic properties, such as the difference in covalency index ( X m 2 r, where X m is electronegativity and r is ionic radius). Zhu et al. [44] recorded that the X m 2 r is a measure for a metal ions of the importance of covalent interactions relative to that of ionic interactions. The covalency index increased in the following order: Zn (2.04) < Cu (2.64), suggesting that Cu(II) has a stronger attraction that Zn(II), which agreed with the report by Nieboer et al. [45] in which metal ions preferentially interacted with functional groups in the following order: S- > N- > O-containing groups. This indicates that larger values of X m 2 r, correspond to more characteristics of soft acids (HSAB theory). The adsorption capacities of SPIONs/gel and SPIONs/gel/PVA for Cu(II) and (Zn) from aqueous solution were compared with those reported in previously published works. The adsorption capabilities of SPIONs/gel and SPIONs/gel/PVA for Cu(II) and Zn(II) from aqueous solution were higher than those of some magnetic nanomaterials such as poly(N-2-aminoethylacrylamide) magnetite nanoparticles and magnetic nanoparticle-decorated tea waste [46,47].

2.2.4. Regeneration

Repeated use of adsorbents and the recovery of the adsorbed metal ions are important parameters indicating economic efficiency. In this study, the regeneration of the SPIONs/gel and SPIONs/gel/PVA was tested by consecutive adsorption–desorption processes performed three times using the same adsorbents.
The adsorption capacity of Cu(II) on SPIONs/gel and SPIONs/gel/PVA were decreased by 5.05% and 7.28%. The adsorption capacity of Zn(II) on SPIONs/gel and SPIONs/gel/PVA were decreased by 7.87% and 12.57%, after three cycles, respectively. The reusability of these materials were compared with some magnetic adsorbent materials, which was used to similar preparation of iron oxide nanoparticles, initial concentration of heavy metal ions and cycling usage conditions. The adsorption capacity of Cu(II) on the Mg/Fe layered double hydroxide loaded with Magnetic (Fe3O4) carbon spheres [48], and the magnetic Fe3O4/carbon nanotube (CNT) [49] were decreased by 18.6%, and 17.6%, after three cycles of usage, respectively. The adsorption capacity of Cu(II) and Zn(II) on magnetic nanoparticles decorated tea waste (Fe3O4-tea) was decreased by 9.5% and 17.1% after six cycles [46]. As shown in Figure 9, after three cycles that the SPIONs/gel and SPIONs/gel/PVA exhibit good regeneration performance and can support long-term usage in the removal of Cu(II) and Zn(II).

3. Experimental

3.1. Materials

Ferric chloride (FeCl3), ferrous chloride (FeCl2·4H2O), ammonia solution (NH3·H2O), gelatin, polyvinyl alcohol (PVA), copper sulfate pentahydrate (CuSO4·5H2O), zinc sulfate heptahydrate (ZnSO4·7H2O), hydrogen chloride (HCl), nitric acid (HNO3), sodium hydroxide (NaOH), and all test solutions were prepared using deionized water. All chemicals were of were analytical grade and used without further purification.

3.2. Synthesis of SPIONs/Gel/PVA

Firstly, SPIONs were prepared by co-precipitating Fe(II) (FeCl2·4H2O) and Fe(III) (FeCl3) ions in ammonia solutions, as described in the literature [50,51]. 5.4066 g of FeCl3 and 3.3 g FeCl2·4H2O were dissolved in 100 mL deionized water and then heated to 80 °C under mechanical stirring in Ar atmospheric conditions. Afterwards, 15 mL of 29% NH3·H2O solution was added to the solution of iron salts, which formed a black precipitate. The mixture was continually stirred at 80 °C for 1 h, cooled to 70 °C, and stirred for 1 h. After that, 30 mL of gelatin solution (5% w/w) was added to the mixture and the synthesis was continued for 1 h. Then 30 mL of PVA solution (10% w/w) was added to the mixture. The synthesis was continued for another 1 h, and the solid phase was collected and washed several times with deionized water and ethanol. The resulting powder was dried at room temperature (25 °C) in vacuum (0.1 MPa) for 24 h. Pure SPIONs and SPIONs/gel were synthesized in a similar condition without the addition of the PVA solution.

3.3. Characterization of Adsorbent

The morphologies of SPIONs, SPIONs/gel, and SPIONs/gel/PVA were characterized using transmission electron microscopy (TEM, JEOL JEM-2100, Tokyo, Japan). The sizes of the SPIONs, SPIONs/gel, and SPIONs/gel/PVA were measured by Dynamic Light Scattering (DLS). All DLS measurements were performed with a Malvern Zetasizer Nano ZS particle analyzer (ZEN3600, Malvern, United Kingdom) at wavelength of 633 nm and He-Ne laser at scattering angle of 173° at 25 °C. In this analysis, 1 mL of particle suspension (each sample was diluted to approximately 0.1 mg/mL) was employed and placed in 10 mm × 10 mm quartz cuvette. The intensity and average diameters were calculated by the Zetasizer Nano Software 7.01 (Malvern, UK). The X-ray diffraction (XRD) patterns of SPIONs, SPIONs/gel, and SPIONs/gel/PVA were determined using an X-ray diffractometer using Cu Kα (λ = 1.54 Å, scanning rate of 5° min−1 in the range of 10–80° at 40 kV and 20 mA, Rigaku, RINT2000). The Fourier-transform infrared (FTIR) spectra of SPIONs, SPIONs/gel, and SPIONs/gel/PVA were recorded by using an FTIR spectrophotometer (Vertex 70, Brucker Optik GmbH, Karlsruhe, Germany) in the range 400–4500 cm−1. The fine powder of KBr was mixed with the sample (0.1–0.5%) and then ground to get a homogenous mixture. The homogenous mixture was compressed under 10 MPa pressure to a small disk for analysis (Transmission ~10%). The data of the sample from FTIR were plotted by Origin Pro 9.1 software. Thermogravimetric analysis (TGA) was performed by using a STA 449 F3 DSC/DTA-TG analyzer (Netzsch Germany, Wunsiedel, Germany), with the temperature heating range from 50 to 900 °C under N2 atmosphere, and the heating rate of 10 °C/min.

3.4. Adsorption

The adsorption experiments of Cu(II) and Zn(II) were performed via the batch adsorption method. Metal ion solutions used in the adsorption experiments were prepared by dissolving salts (CuSO4·6H2O and ZnSO4·7H2O) in deionized water. The initial and final heavy metal ion concentrations were measured by a flame atomic absorption spectrophotometer (AAS, AA6300, Shimadzu Corporation, Kyoto, Japan).

3.4.1. Effect of pH

25 mg of the adsorbents were added to 25 mL of 0.1 mg/mL Cu(II) and Zn(II) solution at a given initial concentration in a 50 mL flask. The pH of the contact solution was adjusted from 2 to 6 using 0.1 mol/L HCl and 0.1 mol/L NaOH solutions. The flask was then placed in an automatic shaker at 25 °C and shaken at 130 rpm for 60 min. The adsorbents were separated by an external magnetic field and the residual heavy metal concentrations were measured by AAS. All the experiments were conducted in duplicate and each data point was measured three times. The adsorption capacities of the SPIONs/gel and SPIONs/gel/PVA were calculated by the following equation [52]:
Q e = ( C 0 − C e ) × V / m
where Qe is the adsorption capacity of the SPIONs/gel or the SPIONs/gel/PVA (mg/g). C0 and Ce are the initial and final concentrations of the metal ions (mg/mL), respectively. V is the volume of the solution (mL), and m is the weight of the adsorbents (g).

3.4.2. Adsorption Kinetics

The effect of contact time on adsorption was determined at different time intervals from 5 to 240 min. 25 mL of Cu(II) and Zn(II) with the initial concentration of 0.1 mg/mL was mixed with 0.025 g of SPIONs/gel and SPIONs/gel/PVA adsorbents under shaking at 130 rpm and 25 °C for different contact times. The adsorbents were then separated and the solution concentrations were measured. The data obtained from these experiments were fitted to the pseudo-first-order and pseudo-second-order kinetic models [29,53].
The equations of these models are given by:
Pseudo-first-order model:
Q t = Q e ( 1 − e − K 1 t )
Pseudo-second-order model:
Q t = t Q e 2 K 2 / ( t K 2 Q e + 1 )
where Qt (mg/g) is the amount of metal ions adsorbed by SPIONs/gel or SPIONs/gel/PVA at time t, and K1 and K2 are the rate constants of the pseudo-first-order (min−1) and pseudo-second-order (min−1) models, respectively.

3.4.3. Adsorption Isotherms

25 mL of Cu(II) and Zn(II) metal ions solutions with different initial concentrations of 0.1, 0.2, 0.3, 0.4, 0.5, 0.75 and 1 mg/L was mixed with 0.025 g of adsorbents and shaken at 25 °C and 130 rpm for 60 min. After that, the adsorbents were separated by an external magnetic field and the residual concentrations of heavy metal ions were measured by AAS. The experimental data points were analyzed by the Langmuir, Freundlich, and Sips models.
Langmuir equation:
C e / Q e = 1 / ( K L Q m a x + C e / Q m a x )
Freundlich equation:
Q e = K F C e 1 / n
Sips equation:
Q e = Q m a x K s C e 1 / n / ( 1 + K s C e 1 / n )
where the definition of Qe is the same as that for equation 1, Qmax is the maximum adsorption capacity of the adsorbent (mg/g), KL is the Langmuir constant related to the adsorption strength or intensity (mg/g), KF is the Freundlich constant, KS is the Sips model constant (mL/mg)1/n, and 1/n is the heterogeneity factor.

3.4.4. Regeneration

25 mg of the SPIONs/gel and SPIONs/gel/PVA were added to 25 mL of 0.1 mg/L Cu(II) and Zn(II) and shaken at 130 rpm and 25 °C for 60 min. The SPIONs/gel and SPIONs/gel/PVA adsorbents were separated and the residual concentration was measured. The collected adsorbents were mixed with 0.1 mol/L HNO3 solution (25 mL) and shaken at 130 rpm and 25 °C for 60 min. After that, the adsorbents were collected and washed repeatedly with deionized water to neutralize the acidic condition and recycled three times.

4. Conclusions

In this work, magnetic nanoparticles were modified by gelatin and PVA for the removal of Cu(II) and Zn(II). Copper and Zinc are very important metals for industries, electroplating, paint, pigments, wood, metal plating, and so on. These enriched acidic solutions can be concentrated and continue used to produce their salts and materials. The SPIONs/gel and SPIONs/gel/PVA were used for the first time for the removal of heavy metal ions from aqueous solutions. SPIONs/gel and SPIONs/gel/PVA can adsorb the two metal ions effectively; SPIONs/gel showed equilibrium adsorption capacities of 18.067 mg/g and 14.143 mg/g for Cu(II) and Zn(II); SPIONs/gel/PVA showed those of 12.904 mg/g and 9.303 mg/g, respectively, at 0.1 mg/mL and 25 °C. The equilibrium data fitted very well with the pseudo-second-order model, indicating chemical adsorption by the chelating effect. The SPIONs/gel/PVA adsorbent is more stable than that of SPIONs/gel, with greater adsorption efficiency for Cu(II).

Author Contributions

The conceptualization and methodology, W.H.P. and J.H.; Validation, J.Y. and C.J.L.; Data curation, Y.L.; software, P.C. and J.X.Y.; formal analysis and writing-original draft preparation A.D.

Funding

This research was funded by the Zhejiang Provincial Natural Science Foundation of China (No. 2018C37052), the National Natural Science Foundation of China (No. 41771509), Zhejiang agricultural biological resources biochemical manufacturing collaborative innovation center (No. 2016KF0020 and 2016KF0025), The national college students’ science and technology innovation project (No. 201711057017), Zhejiang Science and Technology Project (No. 2016C37078) and SRF for ROCS, SEM.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Lingamdinne, L.P.; Chang, Y.Y.; Yang, J.K.; Singh, J.; Choi, E.H.; Shiratani, M.; Koduru, J.R.; Attri, P. Biogenic reductive preparation of magnetic inverse spinel iron oxide nanoparticles for the adsorption removal of heavy metals. Chem. Eng. J. 2017, 307, 74–84. [Google Scholar] [CrossRef]
  2. Ramavandi, B.; Asgari, G. Comparative study of sun-dried and oven-dried Malva sylvestris biomass for high-rate Cu(II) removal from wastewater. Process. Saf. Environ. Prot. 2018, 116, 61–73. [Google Scholar] [CrossRef]
  3. Turan, N.G.; Elevli, S.; Mesci, B. Adsorption of copper and zinc ions on illite: Determination of the optimal conditions by the statistical design of experiments. Appl. Clay Sci. 2011, 52, 392–399. [Google Scholar] [CrossRef]
  4. Keochaiyom, B.; Wan, J.; Zeng, G.; Huang, D.; Xue, W.; Hu, L.; Huang, C.; Zhang, C.; Cheng, M. Synthesis and application of magnetic chlorapatite nanoparticles for zinc (II), cadmium (II) and lead (II) removal from water solutions. J. Colloid Interface Sci. 2017, 505, 824–835. [Google Scholar] [CrossRef] [PubMed]
  5. Bilal, M.; Shah, J.A.; Ashfaq, T.; Gardazi, S.M.; Tahir, A.A.; Pervez, A.; Haroon, H.; Mahmood, Q. Waste biomass adsorbents for copper removal from industrial wastewater—A review. J. Hazard. Mater 2013, 263, 322–333. [Google Scholar] [CrossRef] [PubMed]
  6. Hui, B.; Zhang, Y.; Ye, L. Structure of PVA/gelatin hydrogel beads and adsorption mechanism for advanced Pb(II) removal. J. Ind. Eng. Chem. 2015, 21, 868–876. [Google Scholar] [CrossRef]
  7. Lv, L.; Chen, N.; Feng, C.; Gao, Y.; Li, M. Xanthate-modified magnetic chitosan/poly (vinyl alcohol) adsorbent: Preparation, characterization, and performance of Pb(II) removal from aqueous solution. J. Taiwan Inst. Chem. Eng. 2017, 78, 485–492. [Google Scholar] [CrossRef]
  8. Gaffer, A.; Al Kahlawy, A.A.; Aman, D. Magnetic zeolite-natural polymer composite for adsorption of chromium (VI). Egypt. J. Pet. 2017, 26, 995–999. [Google Scholar] [CrossRef]
  9. Zhu, F.; Li, L.; Xing, J. Selective adsorption behavior of Cd(II) ion imprinted polymers synthesized by microwave-assisted inverse emulsion polymerization: Adsorption performance and mechanism. J. Hazard. Mater. 2017, 321, 103–110. [Google Scholar] [CrossRef] [PubMed]
  10. Li, G.; Wang, X.; Row, K.H. Magnetic Solid-phase Extraction with Fe3O4/Molecularly Imprinted Polymers Modified by Deep Eutectic Solvents and Ionic Liquids for the Rapid Purification of Alkaloid Isomers (Theobromine and Theophylline) from Green Tea. Molecules 2017, 22, 1061. [Google Scholar] [CrossRef] [PubMed]
  11. Zhu, H.Y.; Fu, Y.Q.; Jiang, R.; Yao, J.; Xiao, L.; Zeng, G.M. Novel magnetic chitosan/poly(vinyl alcohol) hydrogel beads: Preparation, characterization and application for adsorption of dye from aqueous solution. Bioresour. Technol. 2012, 105, 24–30. [Google Scholar] [CrossRef] [PubMed]
  12. Duan, S.; Xu, X.; Liu, X.; Wang, Y.; Hayat, T.; Alsaedi, A.; Meng, Y.; Li, J. Highly enhanced adsorption performance of U(VI) by non-thermal plasma modified magnetic Fe3O4 nanoparticles. J. Colloid Interface Sci. 2018, 513, 92–103. [Google Scholar] [CrossRef] [PubMed]
  13. Li, M.F.; Liu, Y.G.; Liu, S.B.; Shu, D.; Zeng, G.M.; Hu, X.J.; Tan, X.F.; Jiang, L.H.; Yan, Z.L.; Cai, X.X. Cu(II)-influenced adsorption of ciprofloxacin from aqueous solutions by magnetic graphene oxide/nitrilotriacetic acid nanocomposite: Competition and enhancement mechanisms. Chem. Eng. J. 2017, 319, 219–228. [Google Scholar] [CrossRef]
  14. Tang, P.; Shen, J.; Hu, Z.; Bai, G.; Wang, M.; Peng, B.; Shen, R.; Linghu, W. High-efficient scavenging of U(VI) by magnetic Fe3O4@gelatin composite. J. Mol. Liq. 2016, 221, 497–506. [Google Scholar] [CrossRef]
  15. Saarai, A.; Kasparkova, V.; Sedlacek, T.; Saha, P. On the development and characterisation of crosslinked sodium alginate/gelatine hydrogels. J. Mech. Behav. Biomed. Mater. 2013, 18, 152–166. [Google Scholar] [CrossRef] [PubMed]
  16. Rajzer, I.; Menaszek, E.; Kwiatkowski, R.; Planell, J.A.; Castano, O. Electrospun gelatin/poly(epsilon-caprolactone) fibrous scaffold modified with calcium phosphate for bone tissue engineering. Mater. Sci. Eng. C Mater. Biol. Appl. 2014, 44, 183–190. [Google Scholar] [CrossRef] [PubMed]
  17. Rajan, M.; Raj, V.; Al-Arfaj, A.A.; Murugan, A.M. Hyaluronidase enzyme core-5-fluorouracil-loaded chitosan-PEG-gelatin polymer nanocomposites as targeted and controlled drug delivery vehicles. Int. J. Pharm. 2013, 453, 514–522. [Google Scholar] [CrossRef] [PubMed]
  18. Erden, P.E.; Kaçar, C.; Öztürk, F.; Kılıç, E. Amperometric uric acid biosensor based on poly(vinylferrocene)-gelatin-carboxylated multiwalled carbon nanotube modified glassy carbon electrode. Talanta 2015, 134, 488–495. [Google Scholar] [CrossRef] [PubMed]
  19. Hayeeye, F.; Sattar, M.; Chinpa, W.; Sirichote, O. Kinetics and thermodynamics of Rhodamine B adsorption by gelatin/activated carbon composite beads. Colloids Surf. A 2017, 513, 259–266. [Google Scholar] [CrossRef]
  20. Xing, Q.; Yates, K.; Vogt, C.; Qian, Z.; Frost, M.C.; Zhao, F. Increasing mechanical strength of gelatin hydrogels by divalent metal ion removal. Sci. Rep. 2014, 4, 4706. [Google Scholar] [CrossRef] [PubMed]
  21. Qiao, C.; Ma, X.; Zhang, J.; Yao, J. Molecular interactions in gelatin/chitosan composite films. Food Chem. 2017, 235, 45–50. [Google Scholar] [CrossRef] [PubMed]
  22. Zhou, Z.; Liu, Y.G.; Liu, S.B.; Liu, H.Y.; Zeng, G.M.; Tan, X.F.; Yang, C.P.; Ding, Y.; Yan, Z.L.; Cai, X.X. Sorption performance and mechanisms of arsenic(V) removal by magnetic gelatin-modified biochar. Chem. Eng. J. 2017, 314, 223–231. [Google Scholar] [CrossRef]
  23. Wong, E.T.; Chan, K.H.; Idris, A. Kinetic and equilibrium investigation of Cu(II) removal by Co(II)-doped iron oxide nanoparticle-immobilized in PVA–alginate recyclable adsorbent under dark and photo condition. Chem. Eng. J. 2015, 268, 311–324. [Google Scholar] [CrossRef]
  24. Zhu, Y.; Hu, J.; Wang, J. Removal of Co2+ from radioactive wastewater by polyvinyl alcohol (PVA)/chitosan magnetic composite. Prog. Nucl. Energy 2014, 71, 172–178. [Google Scholar] [CrossRef]
  25. Nithya, K.; Sathish, A.; Kumar, P.S.; Ramachandran, T. Fast kinetics and high adsorption capacity of green extract capped superparamagnetic iron oxide nanoparticles for the adsorption of Ni(II) ions. J. Ind. Eng. Chem. 2018, 59, 230–241. [Google Scholar] [CrossRef]
  26. Yang, L.; Tian, J.; Meng, J.; Zhao, R.; Ma, J.; Jin, T. Modification and Characterization of Fe3O4 Nanoparticles for Use in Adsorption of Alkaloids. Molecules 2018, 23, 562. [Google Scholar] [CrossRef] [PubMed]
  27. Dil, N.N.; Sadeghi, M. Free radical synthesis of nanosilver/gelatin-poly (acrylic acid) nanocomposite hydrogels employed for antibacterial activity and removal of Cu(II) metal ions. J. Hazard. Mater. 2018, 351, 38–53. [Google Scholar] [CrossRef] [PubMed]
  28. Vo, T.K.; Park, H.K.; Nam, C.W.; Kim, S.D.; Kim, J. Facile synthesis and characterization of γ-AlOOH/PVA composite granules for Cr(VI) adsorption. J. Ind. Eng. Chem. 2018, 60, 485–492. [Google Scholar] [CrossRef]
  29. Zhang, Y.; Bai, L.; Zhou, W.; Lu, R.; Gao, H.; Zhang, S. Superior adsorption capacity of Fe3O4@nSiO2@mSiO2 core-shell microspheres for removal of congo red from aqueous solution. J. Mol. Liq. 2016, 219, 88–94. [Google Scholar] [CrossRef]
  30. Yan, E.; Cao, M.; Jiang, J.; Gao, J.; Jiang, C.; Ba, X.; Yang, X.; Zhang, D. A novel adsorbent based on magnetic Fe3O4 contained polyvinyl alcohol/chitosan composite nanofibers for chromium (VI) removal. Solid State Sci. 2017, 72, 94–102. [Google Scholar] [CrossRef]
  31. Fakhre, N.A.; Ibrahim, B.M. The use of new chemically modified cellulose for heavy metal ion adsorption. J. Hazard. Mater. 2018, 343, 324–331. [Google Scholar] [CrossRef] [PubMed]
  32. Tan, P.; Wen, J.; Hu, Y.; Tan, X. Adsorption of Cu2+ and Cd2+ from aqueous solution by novel electrospun poly(vinyl alcohol)/graphene oxide nanofibers. RSC Adv. 2016, 6, 79641–79650. [Google Scholar] [CrossRef]
  33. Sutirman, Z.A.; Sanagi, M.M.; Karim, K.J.A.; Ibrahim, W.A.W.; Jume, B.H. Equilibrium, kinetic and mechanism studies of Cu(II) and Cd(II) ions adsorption by modified chitosan bead. Int. J. Biol. Macromol. 2018, 116, 255–263. [Google Scholar] [CrossRef] [PubMed]
  34. Ojemaye, M.O.; Okoh, O.O.; Okoh, A.I. Adsorption of Cu2+ from aqueous solution by a novel material; azomethine functionalized magnetic nanoparticles. Sep. Purif. Technol. 2017, 183, 204–215. [Google Scholar] [CrossRef]
  35. Mokadem, Z.; Mekki, S.; Saïdi-Besbes, S.; Agusti, G.; Elaissari, A.; Derdour, A. Triazole containing magnetic core-silica shell nanoparticles for Pb2+, Cu2+ and Zn2+ removal. Arab. J. Chem. 2017, 10, 1039–1051. [Google Scholar] [CrossRef]
  36. Ghasemi, N.; Ghasemi, M.; Moazeni, S.; Ghasemi, P.; Alharbi, N.S.; Gupta, V.K.; Agarwal, S.; Burakova, I.V.; Tkachew, A.G. Zn(II) removal by amino-functionalized magnetic nanoparticles: Kinetics, isotherm, and thermodynamic aspects of adsorption. J. Ind. Eng. Chem. 2018, 62, 302–310. [Google Scholar] [CrossRef]
  37. Li, L.; Wang, Z.; Ma, P.; Bai, H.; Dong, W.; Chen, M. Preparation of polyvinyl alcohol/chitosan hydrogel compounded with graphene oxide to enhance the adsorption properties for Cu(II) in aqueous solution. J. Polym. Res. 2015, 22, 150. [Google Scholar] [CrossRef]
  38. Wang, X.; Huang, K.; Chen, Y.; Liu, J.; Chen, S.; Cao, J.; Mei, S.; Zhou, Y.; Jing, T. Preparation of dumbbell manganese dioxide/gelatin composites and their application in the removal of lead and cadmium ions. J. Hazard. Mater. 2018, 350, 46–54. [Google Scholar] [CrossRef] [PubMed]
  39. Zhu, M.; Zhu, L.; Wang, J.; Yue, T.; Li, R.; Li, Z. Adsorption of Cd(II) and Pb(II) by in situ oxidized Fe3O4 membrane grafted on 316 L porous stainless steel filter tube and its potential application for drinking water treatment. J. Environ. Manag. 2017, 196, 127–136. [Google Scholar] [CrossRef] [PubMed]
  40. Silva, L.S.; Carvalho, J.O.; Bezerra, R.D.S.; Silva, M.S.; Ferreira, F.J.L.; Osajima, J.A.; Filho, E.C.S. Potential of Cellulose Functionalized with Carboxylic Acid as Biosorbent for the Removal of Cationic Dyes in Aqueous Solution. Molecules 2018, 23, 743. [Google Scholar] [CrossRef] [PubMed]
  41. Mirzabe, G.H.; Keshtkar, A.R. Application of response surface methodology for thorium adsorption on PVA/Fe3O4/SiO2/APTES nanohybrid adsorbent. J. Ind. Eng. Chem. 2015, 26, 277–285. [Google Scholar] [CrossRef]
  42. Hui, C.; Guo, X.; Sun, P.; Khan, R.A.; Zhang, Q.; Liang, Y.; Zhao, Y.H. Removal of nitrite from aqueous solution by Bacillus amyloliquefaciens biofilm adsorption. Bioresour. Technol. 2018, 248, 146–152. [Google Scholar] [CrossRef] [PubMed]
  43. Chatterjee, S.; Lee, D.S.; Lee, M.W.; Woo, S.H. Enhanced adsorption of congo red from aqueous solutions by chitosan hydrogel beads impregnated with cetyl trimethyl ammonium bromide. Bioresour. Technol. 2009, 100, 2803–2809. [Google Scholar] [CrossRef] [PubMed]
  44. Zhu, Y.; Hu, J.; Wang, J. Competitive adsorption of Pb(II), Cu(II) and Zn(II) onto xanthate-modified magnetic chitosan. J. Hazard. Mater. 2012, 221, 155–161. [Google Scholar] [CrossRef] [PubMed]
  45. Nieboer, E.; Richardson, D.H.S. The replacement of the bobdescript term heavy metals by a biologocally and chemically significant classification of metal ions. Environ. Pollut. 1980, 1, 3–26. [Google Scholar] [CrossRef]
  46. Wen, T.; Wang, J.; Li, X.; Huang, S.; Chen, Z.; Wang, S.; Hayat, T.; Alsaedi, A.; Wang, X. Production of a generic magnetic Fe3O4 nanoparticles decorated tea waste composites for highly efficient sorption of Cu(II) and Zn(II). JECE 2017, 5, 3656–3666. [Google Scholar] [CrossRef]
  47. Mirzaeinejad, M.; Mansoori, Y.; Amiri, M. Amino functionalized ATRP-prepared polyacrylamide-g-magnetite nanoparticles for the effective removal of Cu(II) ions: Kinetics investigations. Mater. Chem. Phys. 2018, 205, 195–205. [Google Scholar] [CrossRef]
  48. Xie, Y.; Yuan, X.; Wu, Z.; Zeng, G.; Jiang, L.; Peng, X.; Li, H. Adsorption behavior and mechanism of Mg/Fe layered double hydroxide with Fe3O4-carbon spheres on the removal of Pb(II) and Cu(II). J. Colloid Interface Sci. 2018, 536, 440–455. [Google Scholar] [CrossRef] [PubMed]
  49. Yang, Z.F.; Li, L.Y.; Hsieh, C.T.; Juang, R.S. Co-precipitation of magnetic Fe3O nanoparticles onto carbon nanotubes for removal of copper ions from aqueous solution. J. Taiwan Inst. Chem. Eng. 2018, 82, 56–63. [Google Scholar] [CrossRef]
  50. Wondracek, M.H.P.; Jorgetto, A.O.; Silva, A.C.P.; Ivassechen, J.D.R.; Schneider, J.F.; Saeki, M.J.; Pedrosa, V.A.; Yoshito, W.K.; Colauto, F.; Ortiz, W.A.; et al. Synthesis of mesoporous silica-coated magnetic nanoparticles modified with 4-amino-3-hydrazino-5-mercapto-1,2,4-triazole and its application as Cu(II) adsorbent from aqueous samples. Appl. Surf. Sci. 2016, 367, 533–541. [Google Scholar] [CrossRef]
  51. Vismara, E.; Bongio, C.; Coletti, A.; Edelman, R.; Serafini, A.; Mauri, M.; Simonutti, R.; Bertini, S.; Urso, E.; Assaraf, Y.G.; et al. Albumin and Hyaluronic Acid-Coated Superparamagnetic Iron Oxide Nanoparticles Loaded with Paclitaxel for Biomedical Applications. Molecules 2017, 22, 1030. [Google Scholar] [CrossRef] [PubMed]
  52. Habila, M.A.; Alothman, Z.A.; El-Toni, A.M.; Labis, J.P.; Khan, A.; Al-Matghany, A.; Elafifi, H.E. One-Step Carbon Coating and Polyacrylamide Functionalization of Fe3O4 Nanoparticles for Enhancing Magnetic Adsorptive-Remediation of Heavy Metals. Molecules 2017, 22, 2074. [Google Scholar] [CrossRef] [PubMed]
  53. Xu, L.; Chen, J.; Wen, Y.; Li, H.; Ma, J.; Fu, D. Fast and effective removal of cadmium ion from water using chitosan encapsulated magnetic Fe3O4 nanoparticles. Desalin. Water Treat. 2015, 57, 8540–8548. [Google Scholar] [CrossRef]
Sample Availability: Samples of the compounds SPIONs/gel and SPIONs/gel/PVA are available from the authors.
Molecules 23 02982 g001 550
Figure 1. The FTIR spectra of (a) poly vinyl acetate (PVA), gelatin (gel), (b) Super-paramagnetic iron oxide nanoparticles (SPIONs), SPIONs/gel and SPIONs/gel/PVA.
Figure 1. The FTIR spectra of (a) poly vinyl acetate (PVA), gelatin (gel), (b) Super-paramagnetic iron oxide nanoparticles (SPIONs), SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g001
Molecules 23 02982 g002a 550Molecules 23 02982 g002b 550
Figure 2. The TEM images and Dynamic Light Scattering (DLS) of (a) SPIONs, (b) SPIONs/gel, and (c) SPIONs/gel/PVA.
Figure 2. The TEM images and Dynamic Light Scattering (DLS) of (a) SPIONs, (b) SPIONs/gel, and (c) SPIONs/gel/PVA.
Molecules 23 02982 g002aMolecules 23 02982 g002b
Molecules 23 02982 g003 550
Figure 3. XRD spectra of SPIONs, SPIONs/gel and SPIONs/gel/PVA.
Figure 3. XRD spectra of SPIONs, SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g003
Molecules 23 02982 g004 550
Figure 4. Magnetization curve of SPIONs/gel and SPIONs/gel/PVA; the magnetization responds to the external magnetic field of magnetic adsorbents.
Figure 4. Magnetization curve of SPIONs/gel and SPIONs/gel/PVA; the magnetization responds to the external magnetic field of magnetic adsorbents.
Molecules 23 02982 g004
Molecules 23 02982 g005 550
Figure 5. Thermographs of SPIONs, SPIONs/gel and SPIONs/gel/PVA.
Figure 5. Thermographs of SPIONs, SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g005
Molecules 23 02982 g006 550
Figure 6. Effect of pH on Cu(II) (a) and Zn(II) (b) ions adsorption by SPIONs/gel and SPIONs/gel/PVA.
Figure 6. Effect of pH on Cu(II) (a) and Zn(II) (b) ions adsorption by SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g006
Molecules 23 02982 g007 550
Figure 7. Adsorption kinetics for the adsorption of Cu(II) (a) and Zn(II) (b) by SPIONs/gel and SPIONs/gel/PVA.
Figure 7. Adsorption kinetics for the adsorption of Cu(II) (a) and Zn(II) (b) by SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g007
Molecules 23 02982 g008 550
Figure 8. Equilibrium adsorption isotherm of Cu(II) (a) and Zn(II) (b) by the SPIONs/gel and SPIONs/gel/PVA.
Figure 8. Equilibrium adsorption isotherm of Cu(II) (a) and Zn(II) (b) by the SPIONs/gel and SPIONs/gel/PVA.
Molecules 23 02982 g008
Molecules 23 02982 g009 550
Figure 9. Regeneration of SPIONs/gel and SPIONs/gel/PVA for Cu(II) (a) and Zn(II) (b).
Figure 9. Regeneration of SPIONs/gel and SPIONs/gel/PVA for Cu(II) (a) and Zn(II) (b).
Molecules 23 02982 g009
Table
Table 1. Adsorption kinetic parameters for adsorption of Cu(II) and Zn(II) on SPIONs/gel and SPIONs/gel/PVA.
Table 1. Adsorption kinetic parameters for adsorption of Cu(II) and Zn(II) on SPIONs/gel and SPIONs/gel/PVA.
MetalAdsorbentsPseudo-First-OrderPseudo-Second-Order
Qt (mg/g)K1 (1/min)R2Qt (mg/g)K2 (g/(mg·min))R2
Cu(II)SPIONs/gel18.8340.0550.99220.7790.0040.991
SPIONs/gel/PVA13.8860.0430.99215.550.0030.994
Zn(II)SPIONs/gel14.1090.1370.98614.8880.0190.998
SPIONs/gel/PVA11.1010.0590.98312.1460.0080.986
Table
Table 2. Fitted result of the adsorption isotherms of the Cu(II) and Zn(II) by SPIONs/gel and SPIONs/gel/PVA.
Table 2. Fitted result of the adsorption isotherms of the Cu(II) and Zn(II) by SPIONs/gel and SPIONs/gel/PVA.
IsothermParametersCu(II)Zn(II)
SPIONs/GelSPIONs/Gel/PVASPIONs/GelSPIONs/Gel/PVA
Langmuir modelQmax (mg/g)47.59456.05140.55940.865
KL (mL/mg)6.663.3975.7273.267
R20.9950.9930.9970.999
Freundlich modelKF ((mg/g)(mL/mg)1/n)43.99145.65836.51532.866
1/n0.31640.43730.33670.4399
R20.9930.9760.9860.979
Sips modelQmax (mg/g)60.42254.82343.97438.976
KS (mL/mg)1/n2.3823.7133.8543.961
1/n0.68161.03190.86321.071
R20.9990.9910.9980.999

Share and Cite

MDPI and ACS Style

Dolgormaa, A.; Lv, C.-j.; Li, Y.; Yang, J.; Yang, J.-x.; Chen, P.; Wang, H.-p.; Huang, J. Adsorption of Cu(II) and Zn(II) Ions from Aqueous Solution by Gel/PVA-Modified Super-Paramagnetic Iron Oxide Nanoparticles. Molecules 2018, 23, 2982. https://doi.org/10.3390/molecules23112982

AMA Style

Dolgormaa A, Lv C-j, Li Y, Yang J, Yang J-x, Chen P, Wang H-p, Huang J. Adsorption of Cu(II) and Zn(II) Ions from Aqueous Solution by Gel/PVA-Modified Super-Paramagnetic Iron Oxide Nanoparticles. Molecules. 2018; 23(11):2982. https://doi.org/10.3390/molecules23112982

Chicago/Turabian Style

Dolgormaa, Anudari, Chang-jiang Lv, Yin Li, Jian Yang, Jun-xing Yang, Peng Chen, Hong-peng Wang, and Jun Huang. 2018. "Adsorption of Cu(II) and Zn(II) Ions from Aqueous Solution by Gel/PVA-Modified Super-Paramagnetic Iron Oxide Nanoparticles" Molecules 23, no. 11: 2982. https://doi.org/10.3390/molecules23112982

Article Metrics

Back to TopTop