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Journal of Nanomaterials
Volume 2015 (2015), Article ID 895837, 8 pages
Research Article

Dispersion of Iron Nanoparticles by Polymer-Based Hybrid Material for Reduction of Hexavalent Chromium

1Department of Chemistry, Islamia University of Bahawalpur, Bahawalpur, Pakistan
2Chemistry Division, Pakistan Institute of Nuclear Science and Technology (PINSTECH), P.O. Nilore, Islamabad 45650, Pakistan
3Department of Chemistry, University of Sargodha, Pakistan
4Department of Chemical Engineering, Pakistan Institute of Engineering and Applied Sciences (PIEAS), P.O. Nilore, Islamabad 45650, Pakistan
5Central Analytical Facility Division, Pakistan Institute of Nuclear Science and Technology (PINSTECH), P.O. Nilore, Islamabad 45650, Pakistan
6Institute of Chemistry, University of the Punjab, Lahore, Pakistan

Received 23 June 2015; Accepted 30 August 2015

Academic Editor: John Zhanhu Guo

Copyright © 2015 Syed Wasim Ali et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.


A gel type acrylic acid resin, based on ethyl acrylate-co-1,7-octadiene, has been synthesized by suspension polymerization at 20% cross-linking and subsequent hydrolysis by H2SO4. Capacity of the resin was observed to be 8.90 meq/g or 3.28 meq/mL. The iron nanoparticles used in this study were synthesized by ferrous sulphate method by using LiBH4 as a reductant and characterized by SEM, TEM, XRD, surface area, and electrical properties. Later, the resin was applied for the dispersion of iron nanoparticles over its surface for the reduction of Cr(VI) and subsequent adsorption of Fe(III) and Cr(III) as byproducts. In the column studies the reduction of Cr(VI) and the adsorption of Cr(III) and Fe(III) have been observed up to 240 μmole/L.

1. Introduction

Cation-exchange resins have wide spread applications in water softening, removal of toxic metals from water in the environment, wastewater treatment, hydrometallurgy, sensors, chromatography, and biomolecular separations [1]. In the environment applications, the use of cation-exchange resins has advantage over the other techniques due to better selectivity of the resins for metals, production of less sludge volume, compliance with strict discharge specifications, and easy regeneration for the next applications [2]. A large number of classes of cation-exchange resins have been synthesized so far of different strengths and selectivity, but the use of appropriate resin for particular applications depends upon the attached functional groups. Among the different cation-exchange resins, the carboxylic acid resins are of considerably weaker acid strength ( values in the range of 4–6) than their sulphonic acid counterpart [3]. Some of the features of weak acid resins are the following: these can work in neutral and basic solutions [4], have higher selectivity towards heavy metal ions, are easier to regenerate compared to -SO3H groups [5], have high capacity; twice that of strong-cation resins and 3-4 times that of chelating resins, low cost and have faster kinetics compared to chelating resins [6]. Despite these good features, still weak acid cation exchange resins are considered to be unfamiliar in scientist community and thus less literature is available, in either its synthesis or its applications.

In the present study 1,7-octadiene was used as a cross-linker in the synthesis of acrylic acid resin, which gives the whole structure more flexible as reported in our previous study where n-heptane was used as a diluent and later the resin was applied for picking metal ions from aqueous media [7]. In the present study, the synthesized resin was applied as a polymer support material for the removal of chromium(VI) from water which is based on oxidation reduction process by using iron nanoparticles in two processes. In the first process the iron nanoparticles were dispersed over the surface of the resin, which act as a polymer support. When chromium(VI) comes under the potential of Fe0, the net result is the reduction of chromium(VI) to chromium(III) onto the surface of the support material which is a cation exchanger [8]. The dispersion of iron nanoparticles onto the surface of support material is necessary because the iron nanoparticles have high tendency to undergo oxidation, hydrolysis, and agglomeration into microparticles that have become low reactive [9]. Most commonly used support material for the dispersion of iron nanoparticles is Poly-Flo resin [9] which is neutral in character but the resin with ionic moiety has extra advantages as this enriches the cationic byproduct from the same aqueous media [8, 1012]. Use of polymer support to disperse iron oxide nanoparticles like iron nanoparticles has also been reported by many authors [1214]. So in our present study, the use of weak acid cationic support material is also helpful for the capturing of produced ions, that is, Cr(III) and Fe(III) from the reaction mixture in a single step. Cr(VI) is considered to be a potential toxic and carcinogenic material and the maximum permissible dose level of Cr(VI) is 0.05 mg/L; on the other hand Cr(III) species are not toxic and necessary to mammalian system except at elevated dose and their allowed dose in the drinking water is 5 mg/L [15]. Thus second process is the capturing of newly produced Cr(III) and Fe(III) ions by weak acid resin which is equally important. For the removal of Cr(III) from water, Zeolite 3A [16], Zeolite 5A [17], sphagnum moss peat [18], carbon [19], and so forth, and for the Fe(III) ions from water, bamboo charcoals [20], vermiculite [21], and so forth, are some of the examples that have been reported in the past few years, but the methods based on ion exchange for the capturing of the metal ions from aqueous media have some extra advantages including its repeated use after regeneration [1]. Thus the present utility of the weak acid resin as a polymer support and the degradation of Cr(VI) and finally removal of degraded products from water is a new era in the field of weak acid cation exchanger.

2. Experimental

2.1. Chemicals

The reagents used for polymerization, ethyl acrylate from Merck, 1,7-octadiene, benzyl peroxide (97% purity moisture with 25% water) from Fluka. Other reagents like LiBH4 was obtained from Merck. FeSO4·7H2O and K2Cr2O7 was obtained from Fluka. Demineralized water was distilled and the product water having conductivity ~1.5 μS/cm were used in all the experiments. All other reagents for characterization were of analytical grade.

2.2. Synthesis of Copolymer

The copolymer in the form of beads was prepared by suspension polymerization as reported recently [7]. Briefly the polymerization mixture consisting of ethyl acrylate and 1,7-octadiene was 4 : 1 ratio. Benzoyl peroxide was added in each polymerization mixture 1% by weight. Aqueous phase was prepared by dissolving gum-Arabic and gelatin by 1% w/v each in distilled water. One part by volume of the polymerization mixture was suspended in five parts of the aqueous phase under mechanical stirring. The suspension was left under stirring for half an hour at room temperature. The temperature was then raised to 80°C in ~20 min and maintained at 80°C for 20 hours while mechanical stirring was continued. The copolymer beads were then filtered out in a Buckner funnel and washed with hot water to get free from gelatin and gum-Arabic and then washed with acetone to get free from diluents and unreacted homopolymers. The excessive acetone was removed by centrifugation and the volume of the swelled beads () was recorded. The beads were dried at 110°C until constant weight and the product was kept for acid hydrolysis.

2.3. Hydrolysis of Ethyl-Acrylate-1,7-Octadiene Copolymer

Acid hydrolysis of dried copolymer was carried out in 100 mL round bottom flask fitted with reflux and thermometer. 5 g of oven dried copolymer beads was mixed with 40 mL of 98% H2SO4 at 96°C for 2 hours under constant stirring. After completion of reaction, flask was poured into 1 L of cold demineralized water and the beads were filtered out and washed with demineralized distilled water till the effluent was free of acid. The beads then segregated in the desired fraction with sieve. The colorless beads changed to black.

2.4. Density

The density () of the dried hydrolyzed beads was calculated by , where is the weight of the dried beads and is the volume of died beads at 110°C for 24 hours.

2.5. Capacity

The known amount of resin loaded in a column of 1 cm diameter and passed 100 mL of 2 M HCl which was neutralized by passing approximately 200 mL demineralized distilled water. Then 200 mL of 0.2 M NaOH was passed through the column followed by 50 mL demineralized distilled water. The 250 mL of the effluent was titrated to analyze the NaOH concentration. Milli moles of NaOH consumed in the resin are equal to the milli moles of –COOH groups in the resin [7] as given in the following equation:where P is the polymer chain. The resins containing carboxylic acid groups are effective in neutral and alkaline solution, and furthermore the reverse reaction is very effective by hydrogen ion; thus the regeneration can be accomplished readily at efficiencies approaching 100% [4].

2.6. FTIR Analysis

The FTIR spectra of this synthesized resin were recorded after minimizing the moisture present in the sample by NICOLET 6700 FTIR spectrophotometer.

2.7. Particle Analysis

The average particle size, surface area, and dispersal coefficient of the dried hydrolyzed resin was determined by BT 2002 laser particle size analyzer.

2.8. Synthesis of Iron Nanoparticles

The method of synthesis of iron nanoparticles was similar as reported earlier [22]. Briefly, first 6.15 g of FeSO4·7H2O was dissolved in 50 mL demineralized water having conductivity nearly 1.5 μS/cm. pH of this solution was adjusted to ~7.00 by adding 3.8 M NaOH solution. The color of the solution changed to orange. The FeSO4·7H2O solution was transferred to 1000 mL vacuum flask and nitrogen gas was supplied to create inert atmosphere in the reaction flask. The contents were kept under fast and constant stirring at ambient temperature. Then 1.72 g of LiBH4 was added slowly to the mixture. Reaction proceeded very fast with large foaming and effervescence. The color of the reaction mixture finally changed to black. Stirring was continued for another 30–40 minutes. The black precipitates were filtered and washed with demineralized water followed by washing with excess acetone. The filtrate after washing was collected and analyzed by atomic absorption spectroscopy to estimate the percentage conversion of FeSO4·7H2O to nano-Fe0. Final product (iron nanoparticles) was stored in acetone for further studies.

2.9. Dispersion of Iron Nanoparticles on Polymer Support

In the ethanol-acetone mixture (1 : 4), the nano-Zero Valent Iron (n-ZVI) was dispersed in a 1 : 10 w/w ratio. Then this dispersed mixture was combined with the known weight of weak acid resin. The slurry of the mixture was sonicated for about 10 minutes and continuously shaken for another 2 hours [23]. Later the composite of iron nanoparticles and weak acid polymer was centrifuged to remove excessive acetone and then dried in vacuum oven at 50°C and stored in desiccators for further studies.

2.10. Estimation of Iron in the Composite

Freshly prepared polymer-based hybrid materiel in a dried form was immersed in 30 mL of 0.1 M HCl solution and left under constant agitation for 8 hours. Then composite/hybrid material was further washed with distilled water three times. The effluents were combined and analyzed for iron contents by atomic adsorption spectroscopy using Hitachi Z 8000 atomic absorption spectrometer [22].

2.11. Characterization of Iron Nanoparticles (INPs)

Analytical scanning electron microscope was used to determine the morphology of INPs. The samples were coated with gold with JFC-1500 ion sputtering device prior to taking images. Size assessment of the synthesized INPs was carried out by using JEOL transmission electron microscope (JEM-1010) with acceleration voltage range of 40–100 KV. The samples were dispersed with methanol in a sonicator. For the electrical characterization, the current voltage measurements were taken at room temperature using the agilent E4980 LCR meter. Prior to analysis the sample of iron nanoparticles was converted to pellets of 10 mm size at the pressure of 3 tons by STENHØJ 25 hydraulic press. BET surface area of the synthesized iron nanoparticles was measured (5-point isotherm) by using nitrogen adsorption method with a Micromeritics Instrument Co., Surface Area Analyzer. The sample was dried/degassed automatically overnight under the flow of nitrogen, prior to the analysis. XRD analysis was performed using a Rigaku Diffractometer with a high power Cu Kα radioactive source (λ = 1.5406 Å). The sample was scanned from 5° to 90° 2θ at a scanning rate of 0.3 2θ/min.

2.12. Reduction of Cr(VI) and Enrichment of Cr(III) and Fe(III)
2.12.1. Column Method

Polymer supported iron nanoparticles in a dried form loaded in a glass column of 1 cm diameter. Then K2Cr2O7 solution of different concentrations and known volumes were passed through it with a flow rate of 2 mL/min. The residues obtained were analyzed by diphenyl carbazide method for Cr(VI) concentration and for total Cr and Fe by atomic adsorption method. The reduction and simultaneous enrichment into weak acid polymer supported were calculated by the following relationship [22]: where adsorption capacity in (μmol/g), , are the initial and residual concentrations, respectively, in μmol/L, is total volume of solution in liter, and is the weight of Fe0 in the supported resin in grams. In a similar way the adsorption of Cr(III) and Fe(III) ion produced as a result of reduction of Cr(VI) and subsequently captured by cationic support can be calculated on the basis of the total weight of the weak acid polymer support. The distribution coefficient () can be calculated by the following equation:

2.12.2. Batch Method

Batch equilibrium adsorption isotherm studies were performed with aqueous solution of Cr(VI) at 96.1 μmol/L at pH 5.2. The iron nanoparticles dosage varies 40 to 78 mg/g of the resin in all the experiments. 1 g supported composite material and 25 mL solution were mixed in an Erlenmeyer flask for 150 minutes of shaking at 120 rpm to reach equilibrium. The solutions were periodically pipette out for the analysis. Parameters like effect of amount of n-ZVI towards the fixed concentration of Cr(VI) and effect of amount of Cr(VI) towards the fixed amount of reacting n-ZVI have been calculated by using (2).

The equilibrium data has been applied to Freundlich isotherm model to describe the interaction of Cr(VI) with n-ZVI and the adsorption of the newly generated ions towards the polymer support material. The linear form of Freundlich adsorption isotherm is [24]

The kinetics parameters were studied with respect to the degradation of Cr(VI) to Cr(III) and the absorption of Cr(III) and Fe(III) by ion exchange support material at constant temperature. The degradation rate of Cr(VI) to Cr(III) by the reaction of n-ZVI and ion exchange kinetics of Cr(III) and Fe(III) towards cation resin support material were tested by using pseudo-first-order and pseudo-second-order sorption equations. The pseudo-first-order equation is given as follows:where is adsorption capacity at equilibrium in (μmol/g), is adsorption capacity at time “” in (μmol/g), (min−1) is the rate constant of the pseudo-first order degradation rate of Cr(VI) to Cr(III), and pseudo-first-order rate can be calculated by plotting versus time “”.

The linear form of pseudo-second-order equation is [25] as follows: where (μmol/g·min) is the rate constant of the degradation rate of Cr(VI) by n-ZVI and pseudo-second-order sorption of Cr(III) and Fe(III) ions to the porous support material. Slope of the plots versus was used to calculate the pseudo-second-order rate constant.

3. Results and Discussion

The copolymer beads obtained by the chain reaction of two monomers, that is, ethyl acrylate and 1,7-octadiene, are soft, gelatinous, hydrophobic and semitransparent, and not settled in separate state as the dry volumes are not possible. In the absence of solvent, the microstructure obtained of the resin is gel type even at 20% cross-linking. But after hydrolysis with H2SO4 and drying, the particles are in the form of free flowing. There were no signs of cracks or breakages in optical microscopic picture as shown in Figure 1.

Figure 1: Optical microscopic picture of the resin. (One small division in the inserted scale is 30 μm.)

This means that the particles are supposed to be physically stable because the resins are strong enough to stand osmotic shock where the medium was suddenly changed from acid to neutral. Long chain in this polymer imparts good flexibility as reported earlier in our study [7]. The general characteristics of the copolymer ethyl acrylate-co-1,7-octadiene and the acrylic acid resin derived from it are given in Table 1. Table 1 shows the better results of volume capacity, that is, 3.28 meq/mL (without diluents) as compared to our previous reported capacity which was 3.05 meq/mL (diluents n-heptane, 20%) [7]. The variation of capacity results may be due to the main structure of the polymer and deduced that the gel type of the resin may perform better.

Table 1: Characteristics of ethyl-acrylate-co-1,7-octadiene and acrylic acid derived from it.

FTIR Characterization. FTIR characterization of the copolymer and the resin derived from ethyl acrylate-co-1,7-octadiene was reported and interpreted in detail in our early study [7]. In Figure 2 curve 1 related with the copolymer and shows that the signal at 2800–3000 cm−1 is due to C–H bond of the monomer and cross-linking agent, that is, long chain of 1,7-octadiene which after copolymerization has been converted to saturated hydrocarbon.

Figure 2: IR spectra of the base copolymer and acrylic acid resin derived after acid hydrolysis.

Strong peak in spectra at 1700–1800 cm−1 with maximum at 1730 cm−1 is due to C=O group, which is also seen in curve 2 but at 1700 cm−1. In Figure 2 curve 2 relates to the acrylic acid derived from the base copolymer of 1,7-octadiene and shows the signal at 2800–3000 cm−1 corresponding to C–H bond. A strong peak at around 1700 cm−1 is due to the presence of C=O group in the resin and the peak at 3000–3600 cm−1 is due to the moisture contents in the resin. The peak at around 117 cm−1 is due to the coupling between plane OH bending and CO stretching vibrations of neighboring carbonyl groups [26].

3.1. Characterization of INPs

Figure 3 shows the SEM image of the synthesized n-ZVI in two different magnifications and it is indicated in the figure that the iron nanoparticles are spherical and have chain-like conformation.

Figure 3: Scanning electron microscope image of synthesized iron nanoparticles (a) at 10 μm and (b) at 0.5 μm.

This chain-like morphology is because of magnetostatic attraction between the iron nanoparticles [27]. TEM image of the nanoparticles is shown in Figure 4 and shows that the particles size of the synthesized n-ZVI is in the range of 25–75 nm but some overlapped and small particles are also shown in the image.

Figure 4: Transmission electron microscope image of the synthesized iron nanoparticles.

Figure 5 is related to electrical properties and shows that the current and voltage drawn each parallel at room temperature in the range of −0.1 to 1.0 V. The linear behaviour of the curve with respect to each other shows that with the increase of voltage the current also increases which reveals good conduction behaviour of the iron nanoparticles. So the synthesized iron nanoparticles in present study imparted good conduction and have sufficiently high metallic behaviour. A similar behaviour was also observed at milli-voltage range and also shows the linear behaviour with respect to current.

Figure 5: It shows the relationship of voltage and currents of the iron naoparticles.

XRD profile as shown in Figure 6 indicates the basic reflection peak at 2θ of 44.8° which corresponds with the zero valent iron. The peak intensity at 2θ = 44.8° is very close to the previously reported work [27, 28]. All other peaks correspond to the iron oxides or other impurities. However, it is difficult to evaluate all the peaks except the peaks corresponding with the zero valent iron because the intensity of the peaks is very low and the XRD profile is poorly ordered and exhibits amorphous structure.

Figure 6: XRD pattern of synthesized iron nanoparticles.

Such amorphous nature of zero valent iron has been reported in some previous literature with FeCl3 as a precursor and KBH4 as a reducing agent in the preparation of iron nanoparticles [10]. Low intensity profile of XRD obtained in this study and like the previous studies may be linked due to the smaller size of INPs [29] and the presence of the smaller sizes of the iron nanoparticles has been verified in TEM images as shown in Figure 3. Surface area (BET) of synthesized n-ZVI particles is obtained, the average 28.92 m2/g, which is very close to the reported values in the literature [22, 30, 31].

3.2. Reduction of Cr(VI) and Enrichment of Fe(III) and Cr(III) onto the Polymer Surface

Cr(VI) reduces itself immediately and efficiently in contact with the potential applied by the zero valent iron in a very simply stoichiometric ratio [32] as given in (7). Figure 7 also illustrates the reduction capacity of Cr(VI) as a function of initial Cr(VI) concentration up to 240 μmol/L, and also given in the following equation:The use of support material prevents agglomeration, which produces greater hydraulic surface conductivity and high specific surface area [9]. Thus the reduction capacities were obtained profoundly high as compared to the iron nanoparticles applied without support material for the reduction of Cr(VI) as in Figure 7. When comparing these results with the previous study, where we use porous strong acid support, it can be seen that the reduction capacity of Cr(VI) with the iron nanoparticles is slightly less for the weak acid support as compared to porous strong acid support. Therefore, we can conclude that the porous support has some advantages, but the weak acid support possesses higher capacity as compared to the strong acid capacity which plays key role for the picking of trivalent cations.

Figure 7: Reduction capacity of Cr(IV) with iron nanoparticles: ◆ = loaded onto gel type weak acid resin of diameter ranging 45–150 μm, ■ = powder, without support.

As a result of reduction of Cr(VI) by iron nanoparticles the formation of two trivalent ion of chromium and iron was absorbed by the weak acid cationic supported as given in Figure 8 and illustrated in (6), (7), and (9). So it is proved from the results that the gel type functional polymer support not only disperses the INPs for the enhancement of reduction rates of Cr(VI) to Cr(III) but also enriches the cations from the aqueous media. Adsorption capacities of Fe(III) are higher than for the adsorption capacities for Cr(III).

Figure 8: Absorption capacity of ◆ = Cr(III) and ■ = Fe(III) onto gel type weak acid support.

It shows that selectivity of Fe(III) towards the gel type weak acid cation exchange resin is higher. This observation is in agreement with results reported in literature where Fe(III) and Cr(III) ions were removed by using a chelating ion exchange resin “Diaion CR11” from aqueous media [33]: where P is polymer chain in the above equations. When comparing these results with the strong acid resin support with the same particle size, that is, 45–150 μ [22], the results revealed that the absorption capacity for the trivalent cations is higher, that is, 2.9 and 1.414 μmol/L for Fe+3 and Cr+3, respectively, as compared to 1.85 and 0.901 μmol/L for the strong acid support at the dose level of 240 μmol/L.

3.3. Kinetics Studies

The kinetic reduction of Cr(VI) to Cr(III) has been carried out with different amount of iron nanoparticles in the polymer support as shown in Figure 9. With increase of time the reduction capacity increases and settled at the maximum equilibrium position after about 120 minutes for all the dose levels (Table 2).

Table 2: Kinetics of reduction of Cr(VI) by varying amount of n-ZVI.
Figure 9: The kinetics curve of degradation of Cr(VI) by INPs ◆ = 78 mg/g of support material; ■ = 55 mg/g of support material; ▲ = 40 mg/g of the support material.

Table 3 showed that the equilibrium data having 4% of n-ZVI having value 0.951 followed Freundlich adsorption isotherm model and explained the interaction of Cr(VI) and the adsorption of the newly generated ions towards the polymer support material.

Table 3: Freundlich constant measurements. [ = 298K, Co = 96.1 μmole/L, vol. 30 mL, pH = 5.2].

4. Conclusions

(1)The cross-linked acrylic acid resin based on ethyl-acrylate-1,7-octadiene can be synthesized in beads form by different amount of diluents and cross linking percentages to get distinct characteristics of resin for desirable applications.(2)The synthesized acrylic acid resin is good enough to disperse iron nanoparticles onto its surface for the reduction of Cr(VI) to Cr(III) and subsequent enrichment of its byproducts, that is, Fe(III) and Cr(III), by the same resin in a single step is a new era in the world of weak acid resin.(3)So in our present study, the use of weak acid cationic support material is helpful for capturing of produced ions, that is, Fe(III) and Cr(III) from the reaction mixture.(4)Results showed that the equilibrium data having 4% of n-ZVI having value 0.951 followed Freundlich isotherm model.

Conflict of Interests

The authors declare that there is no conflict of interests regarding the publication of this paper.


The authors thank Dr. Jamshed Hussain Zaidi (PINSTECH) for XRD analysis, Mr. Javed Iqbal (NIBGE) for TEM analysis, Dr. Tariq Yasin for IR and BET surface area analysis, and Dr. Tanvir Ahmad for composing and drawing the figure in this paper. This work is a part of Ph.D thesis of Syed Wasim Ali.


  1. K. Dofner, Ion Exchangers, Walter de Gruyter, New York, NY, USA, 1991.
  2. A. Dąbrowski, Z. Hubicki, P. Podkościelny, and E. Robens, “Selective removal of the heavy metal ions from waters and industrial wastewaters by ion-exchange method,” Chemosphere, vol. 56, no. 2, pp. 91–106, 2004. View at Publisher · View at Google Scholar · View at Scopus
  3. C. E. Harland, Ion Exchange: Theory and Practice, Royal Society of Chemistry, London, UK, 1994.
  4. F. C. Nachod and J. Schubert, Ion Exchange Technology, Academic Press, New York, NY, USA, 1956.
  5. R. Kunin and R. E. Barry, “Carboxylic, weak acid type, cation exchange resin,” Industrial & Engineering Chemistry, vol. 41, no. 6, pp. 1269–1272, 1949. View at Publisher · View at Google Scholar
  6. P. Meyers, “Applications of weak acid cation resin in waste treatment,” in Proceedings of the Annual International Technical Conference (AESF SUR/FIN '99), pp. 609–618, American Electroplaters and Surface Finishers Society, Cincinnati, Ohio, USA, June 1999.
  7. S. Wasim Ali, M. A. Malik, S. Jan, and K. Naeem, “Comparison of rigid divinylbenzene with flexible 1,7-octadiene crosslinks in acrylic acid resins—effects on kinetics of swelling and loading of heavy metal ions from water,” Journal of Applied Polymer Science, vol. 131, no. 21, Article ID 41038, 2014. View at Publisher · View at Google Scholar · View at Scopus
  8. F. Fu, J. Ma, L. Xie, B. Tang, W. Han, and S. Lin, “Chromium removal using resin supported nanoscale zero-valent iron,” Journal of Environmental Management, vol. 128, pp. 822–827, 2013. View at Publisher · View at Google Scholar · View at Scopus
  9. S. M. Ponder, J. G. Darab, J. Bucher et al., “Surface chemistry and electrochemistry of supported zerovalent iron nanoparticles in the remediation of aqueous metal contaminants,” Chemistry of Materials, vol. 13, no. 2, pp. 479–486, 2001. View at Publisher · View at Google Scholar · View at Scopus
  10. Y. Li, Z. Jin, T. Li, and S. Li, “Removal of hexavalent chromium in soil and groundwater by supported nano zero-valent iron on silica fume,” Water Science and Technology, vol. 63, no. 12, pp. 2781–2787, 2011. View at Publisher · View at Google Scholar · View at Scopus
  11. C. J. Lin, S.-L. Lo, and Y. H. Liou, “Degradation of aqueous carbon tetrachloride by nanoscale zerovalent copper on a cation resin,” Chemosphere, vol. 59, no. 9, pp. 1299–1307, 2005. View at Publisher · View at Google Scholar · View at Scopus
  12. H. Gu, S. B. Rapole, J. Sharma et al., “Magnetic polyaniline nanocomposites toward toxic hexavalent chromium removal,” RSC Advances, vol. 2, no. 29, pp. 11007–11018, 2012. View at Publisher · View at Google Scholar · View at Scopus
  13. B. Qiu, H. Gu, X. Yan et al., “Cellulose derived magnetic mesoporous carbon nanocomposites with enhanced hexavalent chromium removal,” Journal of Materials Chemistry A, vol. 2, no. 41, pp. 17454–17462, 2014. View at Publisher · View at Google Scholar · View at Scopus
  14. F. Gao, H. Gu, H. Wang, X. Wang, B. Xiang, and Z. Guo, “Magnetic amine-functionalized polyacrylic acid-nanomagnetite for hexavalent chromium removal from polluted water,” RSC Advances, vol. 5, no. 74, pp. 60208–60219, 2015. View at Publisher · View at Google Scholar
  15. E. Pehlivan and S. Cetin, “Sorption of Cr(VI) ions on two Lewatit-anion exchange resins and their quantitative determination using UV–visible spectrophotometer,” Journal of Hazardous Materials, vol. 163, no. 1, pp. 448–453, 2009. View at Publisher · View at Google Scholar · View at Scopus
  16. H. Tahir, M. Saleem, M. Afzal, H. Ahmad, S. T. Hussain, and J. Afzal, “Estimation and removal of chromium ions from tannery wastes using zeolite-3A,” Adsorption Science & Technology, vol. 16, no. 3, pp. 153–161, 1998. View at Google Scholar · View at Scopus
  17. H. Tahir, “Comparative trace metal contents in sediments and liquid wastes from tanneries and the removal of chromium using Zeolite-5A,” Electronic Journal of Environmental, Agricultural and Food Chemistry, vol. 4, no. 4, pp. 1021–1032, 2005. View at Google Scholar
  18. C. Balan, D. Bilba, and M. Macoveanu, “Studies on chromium(III) removal from aqueous solutions by sorption on Sphagnum moss peat,” Journal of the Serbian Chemical Society, vol. 74, no. 8-9, pp. 953–964, 2009. View at Publisher · View at Google Scholar · View at Scopus
  19. S. Heydari, H. Sharififard, M. Nabavinia, H. Kiani, and M. Parvizi, “Adsorption of chromium ions from aqueous solution by carbon adsorbent,” International Journal of Environmental, Chemical, Ecological, Geological and Geophysical Engineering, vol. 7, no. 12, pp. 649–652, 2013. View at Google Scholar
  20. B. K. Baruah, B. Das, A. Haque, K. Misra, and A. K. Misra, “Iron removal efficiency of different bamboo charcoals: a study on modified indigenous water filtration technique in rural areas of Assam,” Journal of Chemical and Pharmaceutical Research, vol. 3, no. 2, pp. 454–459, 2011. View at Google Scholar
  21. W. Agnieszka, C. Lucjan, Z. Pawal et al., “Adsorbents for iron removal obtained from vermiculite,” Acta Geodynamica et Geomaterialia, vol. 10, no. 3, pp. 353–361, 2013. View at Publisher · View at Google Scholar
  22. S. W. Ali, M. L. Mirza, and T. M. Bhatti, “Removal of Cr(VI) using iron nanoparticles supported on porous cation-exchange resin,” Hydrometallurgy, vol. 157, pp. 82–89, 2015. View at Publisher · View at Google Scholar
  23. L. Wu, M. Shamsuzzoha, and S. M. C. Ritchie, “Preparation of cellulose acetate supported zero-valent iron nanoparticles for the dechlorination of trichloroethylene in water,” Journal of Nanoparticle Research, vol. 7, no. 4-5, pp. 469–476, 2005. View at Publisher · View at Google Scholar · View at Scopus
  24. M. I. Din, M. L. Mirza, S. Ata, M. Athar, and I. U. Mohsin, “Thermodynamics of biosorption for removal of Co(II) ions by an efficient and ecofriendly biosorbent (Saccharum bengalense): kinetics and isotherm modeling,” Journal of Chemistry, vol. 2013, Article ID 528542, 11 pages, 2013. View at Publisher · View at Google Scholar · View at Scopus
  25. Y.-S. Ho, “Review of second-order models for adsorption systems,” Journal of Hazardous Materials, vol. 136, no. 3, pp. 681–689, 2006. View at Publisher · View at Google Scholar · View at Scopus
  26. M. A. Moharram, S. M. Rabie, and H. M. El-Gendy, “Infrared spectra of γ-irradiated poly(acrylic acid)-polyacrylamide complex,” Journal of Applied Polymer Science, vol. 85, no. 8, pp. 1619–1623, 2002. View at Publisher · View at Google Scholar · View at Scopus
  27. Y. Xi, M. Megharaj, and R. Naidu, “Dispersion of zerovalent iron nanoparticles onto bentonites and use of these catalysts for orange II decolourisation,” Applied Clay Science, vol. 53, no. 4, pp. 716–722, 2011. View at Publisher · View at Google Scholar · View at Scopus
  28. C. J. Choi, O. Tolochko, and B. K. Kim, “Preparation of iron nanoparticles by chemical vapor condensation,” Materials Letters, vol. 56, no. 3, pp. 289–294, 2002. View at Publisher · View at Google Scholar · View at Scopus
  29. Y.-H. Lin, H.-H. Tseng, M.-Y. Wey, and M.-D. Lin, “Characteristics of two types of stabilized nano zero-valent iron and transport in porous media,” Science of the Total Environment, vol. 408, no. 10, pp. 2260–2267, 2010. View at Publisher · View at Google Scholar · View at Scopus
  30. T.-T. Lim, J. Feng, and B.-W. Zhu, “Kinetic and mechanistic examinations of reductive transformation pathways of brominated methanes with nano-scale Fe and Ni/Fe particles,” Water Research, vol. 41, no. 4, pp. 875–883, 2007. View at Publisher · View at Google Scholar · View at Scopus
  31. R. J. Barnes, C. J. van der Gast, O. Riba et al., “The impact of zero-valent iron nanoparticles on a river water bacterial community,” Journal of Hazardous Materials, vol. 184, no. 1–3, pp. 73–80, 2010. View at Publisher · View at Google Scholar · View at Scopus
  32. P. V. V. V. Prasad, C. Das, and A. K. Golder, “Reduction of Cr(VI) to Cr(III) and removal of total chromium from wastewater using scrap iron in the form of zerovalent iron(ZVI): batch and column studies,” Canadian Journal of Chemical Engineering, vol. 89, no. 6, pp. 1575–1582, 2011. View at Publisher · View at Google Scholar · View at Scopus
  33. S. Fernandes, I. S. Romão, C. M. R. Abreu, M. J. Quina, and L. M. Gando-Ferreira, “Selective separation of Cr(III) and Fe(III) from liquid effluents using a chelating resin,” Water Science and Technology, vol. 66, no. 9, pp. 1968–1976, 2012. View at Publisher · View at Google Scholar · View at Scopus