| Home | E-Submission | Sitemap | Contact Us |  
Environ Eng Res > Volume 25(6); 2020 > Article
Choi, Kim, Ryu, Oh, and Choi: Three-dimensional double-network hydrogels of graphene oxide, alginate, and polyacrylonitrile for copper removal from aqueous solution


Three-dimensional (3D) double-network graphene oxide/alginate-polyacrylonitrile (GO/Ca-Alg2-PAN) composite hydrogels were synthesized via surface functionalization of GO to activate adsorption sites. The morphology and structure of the GO/Ca-Alg2-PAN were analyzed by scanning electron microscopy (SEM), Brunauer-Emmett-Teller (BET), Fourier transform infrared spectroscopy (FT-IR), and thermogravimetric analysis (TGA-DSC). The results of the physicochemical analyses indicated that GO/Ca-Alg2-PAN was successfully synthesized by the combination of a 2D-structured graphene oxide with the alginate which was functionalized with the PAN polymer to generate the 3D double network composites. This functionalization approach contributed to an increase in Cu2+ ion adsorption capacity. The maximum adsorption capacity of the GO/Ca-Alg2-PAN for Cu2+ was 5.99 mmol/g. The results of adsorption kinetic experiments indicated that the GO/Ca-Alg2-PAN reached adsorption equilibrium within 147 mins at 2 mM Cu2+ in accordance with a pseudo-second-order model.

1. Introduction

As the industry develops, vast quantities of wastewater effluents are generated. These wastewaters contain a variety of heavy metal contaminants that need to be removed. Among these heavy metals, Cu2+ is an essential main target for removal, since it stimulates the central nervous system and causes cancer in human beings as well as affecting many ecosystems such as animals and plants in numerous adverse ways [1, 2]. Up to now, there have been many studies on the removal of Cu2+ ions by various methods, including ion-exchange, extraction, precipitation, filtration etc. [36]. In contrast to adsorption, however, these methods are complex and relatively expensive.
Carbon-based materials are used as adsorbents in the field of water-treatment technology because of their abundance on earth and their high surface areas [7]. In particular, graphene has a two-dimensional (2D) structure with a high specific area and good stability [7, 8]. Moreover, graphene oxide (GO) functionalized with many oxygen-containing groups has a high adsorption capacity for metal ions due to the binding of such ions to the surface; e.g. by crosslinking reactions with divalent cations such as calcium [9, 10]. However, GO is difficult to recover and separate from aqueous solution after treatment because of its high dispersibility, leading to environmental toxicity in aqueous solution.
Sodium alginate (Na-alginate) has been utilized for the encapsulation of GO. By encapsulating GO with Na-alginate, a single 2D GO network was combined with a single three-dimensional (3D) alginate network. Alginate consists of a linear chain of (1–4)-linked β-d-mannuronic acid and α-l-guluronic acid [11]. Alginate can be transformed into a hydrogel by an ionic crosslinking method. The carboxyl group of α-l-guluronic acid ionically bonds with divalent cations to form an “egg-box” structure [12]. In this study, calcium chloride was used as a divalent cation to transform the sodium alginate into calcium alginate (Ca-Alg2). When this alginate is combined with GO, the Ca cations are simultaneously linked with the alginate chains and the GO by a double crosslinking reaction to produce a 3D hydrogel double network [1316]. The developed hydrogels are excellent materials for separating and recovering ions from aqueous solution.
For the enhanced adsorption of Cu2+ ions, the surface of GO/Ca-Alg2 has been functionalized with a polymer that displays selectivity for Cu2+. Thiol-, amine- and nitrogen-containing functional groups are known to have strong binding properties to metal ions [1719]. Among these functional groups, the amine group was selected for introduction onto the surface of the composites via functionalization with poly(acrylonitrile) (PAN) to faciliate removal of Cu2+ ions [20].
In the present study, adsorbents were synthesized using GO and alginate functionalized with polyacrylonitrile (namely, GO/Ca-Alg2-PAN) for the removal of Cu2+ from wastewater. The GO/Ca-Alg2-PAN adsorbents were characterized by field emission scanning electron microscopy (FE-SEM) with energy dispersive spectroscopy (EDS), specific surface area analysis, Fourier transform-infrared (FT-IR) spectroscopy, and thermogravimetric analysis (TGA). The batch adsorption and conditions such as the contact time were varied as parameters of adsorption experiments. Finally, we investigated whether these data were well-fitted to adsorption equilibrium isotherms and the pseudo-second-order kinetic models.

2. Material and Methods

2.1. Materials and Reagents

All of the chemicals were analytical-grade reagents and were used without further purification.
The graphene oxide (GO) sheets and copper(II) chloride dihydrate (CuCl2·2H2O, 99.0%, average M.W. = 170.48 g/mol) were purchased from Sigma-Aldrich Chemical Co. The N,N-dimethylformamide (DMF) (C3H7NO, M.W. = 73.09 g/mol), calcium chloride (CaCl2, 85%), and sodium alginate (C6H9NaO7, M.W. = 216.121 g/mol) were purchased from Daejung Chemicals & Metals Co. (South Korea). The DMF was used for the polymerization of the acrylonitrile monomer to PAN. All of the solutions were prepared with ultra-pure water (18.2 MW×cm), which was obtained from Vivagen co. Ltd. (EXL5 Analysis 16, South Korea).

2.2. Synthesis of the Sorbents

The GO (0.02 g) was added to 20 mL of ultrapure water and dispersed completely using sonication (JAC-4020P, KODO Technical Research Co.) for 2 h. Sodium alginate (0.10 g) was added into the ultrasonicated GO solution and completely dissolved by stirring, followed by ultrasonic irradiation. For functionalization with PAN, the acrylonitrile monomer was added and stirred for 2 h under an N2 atmosphere. After stirring, methanol was added in order to precipitate the slurry. To obtain a perfect solution by removing the homopolymer, the solution was washed several times with DMF. When a homogeneous solution was obtained, this was dropped into a CaCl2·2H2O solution (10 g/L, 200 mL) using a syringe pump (NE1000, 4science Co., USA) at 2 mL/min under continuous magnetic stirring to encapsulate the alginate beads. The hydrogels were kept in CaCl2·2H2O solution for stabilization, washed 2–3 times with ultrapure water, then placed in an oven and allowed to dry for 24 h for subsequent use as adsorbents.

2.3. Characterization of the Sorbents

The morphology of the sorbents was analyzed by FE-SEM (SU8220, Hitachi, Japan). The specific surface area, pore size, and pore volume were measured using a surface area and pore size analyzer (BET, Autosorb-IQ & Quadrasorb SI, Quantachrome). The functional groups were analyzed to identify the chemical combination of sorbents by FT-IR (Frontier, PerkinElmer, USA). The thermal properties of the sorbents were identified via TGA (Q600, TA-Instrument, Japan) under an N2 atmosphere at a heating rate of 10°C/min.

2.4. Cu2+ ion Adsorption Experiments

As simulated wastewater, Cu2+ solutions were prepared with varying concentrations from 0.1 to 60 mM. All experiments were performed in a 50 mL conical tube (PE, SPL Korea) using a duplicate batch system. To carry out the adsorption isotherm experiments, 0.05 g of adsorbent was added into 55 mL of the Cu2+ solutions (0.1, 0.5, 1.0, 2.0, 5.0, 10, 20, 30, 40, 50 and 60 mM) and was mixed at 250 rpm for 24 h at room temperature. The samples were then centrifuged at 4,000 rpm for 10 min to separate the sorbent from the solution. The solution was filtered using 0.20 mm nitrocellulose membrane filters (Whatman) before analysis.
Adsorption kinetic experiments were conducted by sampling at various time intervals after mixing the solutions containing 0.05 g of adsorbent and 55 mL of 2mM Cu2+ in the tubes.
The supernatants were analyzed by inductively coupled plasma optical emission spectroscopy (ICP-OES, Optima 2100DV, PerkinElmer Co., USA) to measure the adsorption capacities. The equilibrium (qe) value is given by Eq. (1):
where qe is the Cu2+ adsorption capacity in milligrams per gram (mg/g) of adsorbent, Co is the initial concentration of Cu2+ solution, Ce is the concentration of Cu2+ in the effluent solution after adsorption, V is the solution contact volume (mL), and m is the mass of the adsorbent (g).

3. Results and Discussion

3.1. Characterization of the Sorbents

The FT-IR spectra of the GO, GO/Ca-Alg2, and GO/Ca-Alg2-PAN in the 4000–400 cm−1 region are presented in Fig. 1. Comparison of the spectra of GO (Fig. 1(a)) and GO/Ca-Alg2 (Fig. 1(b)) reveals the appearance of four new bands at 1453 cm−1, 1358 cm−1, 1249 cm−1, and 1074 cm−1, which indicate that the graphene oxide was fully reacted with the calcium alginate during the preparation of the double-network composite [21]. The presence of the –COO stretching vibrations and the C–H stretching bands located at 1453 and 1074 cm−1, the C–OH bending band at 1357 cm −1, the C–O–C asymmetric stretching band at 1249 cm−1 was observed [22]. An additional new band in the spectrum of GO/Ca-Alg2-PAN (Fig. 1(c)) indicates the successful combination of poly(acrylonitrile). Normally, nitrile-containing compounds have a sharp adsorption in the region of 2260–2200 cm−1 [23, 24]. The results of the spectral analysis of functional groups thus confirmed that the double-network 3D complex GO/Ca-Alg2-PAN was successfully synthesized.
The qualitative EDS results for the GO/Ca-Alg2-PAN showed the presence of C, N, O, Ca and Cl, as anticipated (Fig. 2). The presence of Ca and Cl in the Ca-Alg2 beads, along with C and O in the GO and PAN, demonstrate that the synthesized GO/Ca-Alg2-PAN beads have sufficient adsorption sites. In addition, the transformation of Na-Alg to Ca-Alg2 was achieved by cation-exchange as the beads formed the “egg-box” structure [13].
The surface structures of the GO/Ca-Alg2-PAN were investigated by analysis of the physical properties and FE-SEM images presented in Fig. 3. The FE-SEM image in Fig. 3(a) indicates that the GO consists of 2D plates, while Fig. 3(b) indicates the 3D structure of the GO/Ca-Alg2 beads after transformation of the GO/Na-Alg solution. The GO/Ca-Alg2-PAN composites are imaged in Fig. 3(c–d), which shows a group of spheres onto which the 3D-structured polymer was functionalized. The surface area of GO is much greater than those of GO/Ca-Alg2 and GO/Ca-Alg2-PAN; hence, the surface area of the GO/Ca-Alg2 is dramatically reduced to 2.466 m2 per gram of alginate. However, the functionalization of GO/Ca-Alg2 with PAN to form GO/Ca-Alg2-PAN with the double interpenetrating polymer network (IPN) structure led to an increase in surface area. The pore-sizes were similar, while the pore volume of GO was the largest. The final composition, GO/Ca-Alg2-PAN, had a pore volume of 0.034 cm3/g. The smaller surface area and pore volume relative to GO were due to the presence of alginate, but the resulting beads are easily separated from aqueous solution and have the advantage of high efficiency for a low surface area. [25]. As shown in Fig. 3, the PAN polymer was successfully functionalized onto the GO/Ca-Alg2 hydrogel-forming 3D structure.

3.2. Adsorption Isotherm and Kinetics

The data obtained from the Cu2+ adsorption experiment were fitted using two equilibrium models to confirm the adsorption behavior. The Langmuir isotherm model represents the monolayer adsorption of metal ions in accordance with Eq. (2):
where qm (mmol/g) is the maximum sorption capacity, b (L/mmol) is the Langmuir adsorption constant related to the free energy of the sorption, and Ce is the equilibrium concentration of Cu2+ aqueous solution.
Alternatively, multiple-layer adsorption can be analyzed according to the Freundlich adsorption model given by Eq. (3):
where Kf [(mmol/g) (L/mmol)1/n] and n are constants of the Freundlich model.
The kinetic behavior of Cu2+ adsorption was fitted using Lagergren’s pseudo first-order and pseudo second-order models, Eqs. (4) and (5), respectively:
ln(qe-qt)=ln qe-k1t
where qt is the concentration of Cu2+ ions (mmol/g) at time (t), qe is the equilibrium concentration, k1 is the pseudo-first-order constant (min−1) and k2 is the pseudo-second-order constant (g/mmol/min).
From the pseudo second-order model, the initial adsorption rate (h) could be calculated according to Eq. (6):
Fig. 4 shows the equilibrium isotherm nonlinear models and kinetic models for the removal of Cu2+ at room temperature. In the Langmuir isotherm model, the maximum adsorption capacity (qm) value of the GO/Ca-Alg2-PAN is 5.99 mmol/g. In the Freundlich model, however, the maximum adsorption amount increased with increasing concentration in solution. In Fig. 4(a), both kinetic models were well-fitted to the experimental data.
The constants and correlation coefficients of the isotherm and kinetic models are indicated in Table 1. When fitting the two adsorption models with the experimental data, the Freundlich isotherm model gave a better fit than the Langmuir isotherm model. In the Freundlich isotherm model, the determination coefficient (r2) was 0.980, which is closer to 1. Since the Freundlich model is well-suited to modeling Cu2+ removal using GO/Ca-Alg2-PAN, we conclude that the synthesized GO/Ca-Alg2-PAN is a double-network capable of adsorbing multiple layers of Cu2+ at multiple adsorption sites. In the absorption kinetics results, the kinetic behavior of the GO/Ca-Alg2-PAN depended on the second-order model better than the first-order model through the r2 value of two kinetic models for the absorption of 1 mM and 2mM of Cu2+. According to the pseudo first-order model, the equilibrium of adsorption was achieved within about 120 mins. Normally, powdered adsorbents reach equilibrium in a minimum of 10 mins [26]. However, the beads require time to swell in aqueous solution, so stirring for extra time was considered in order to reach equilibrium. As a result, the isotherm adsorption experiments in the present study confirmed that a stirring-time of 24 h allowed sufficient contact time for equilibrium to be reached. In addition, for the pseudo second-order model, the h value and the qe value increase as the concentration of Cu2+ increases. Hence, as the concentration increases, the time to reach the adsorption equilibrium decreases and the amount absorbed increases.
Generally, the mechanism of adsorption consists of three steps, namely: (i) external mass transfer, (ii) particle pore diffusion, and (ii) adsorption reaction at a surface site [27]. It can be interpreted according to two equations relating to the intraparticle diffusion [28] and the external mass transfer rate [29]. The rate of intraparticle diffusion equation is given by Eq. (7):
where ki is an intraparticle diffusion rate constant (mmol/g·min0.5), t is the contact time (min) and qt is the intraparticle diffusion rate.
From this, the diffusion coefficient (D, m2/s) is calculated using Eq. (8):
where t1/2 is the time when the adsorption reaches one half of the equilibrium value and d is the diameter of the adsorbents (m).
The external mass transfer rate can be represented by Eq. (9):
where A is the surface area of adsorbents (m2), V is the volume of solution (m3), and the mass transfer coefficient ks (m2/min) can be determined experimentally from a plot of −ln(C(t)/Co) against t.
As indicated in Fig. 5, multilinearities were observed in the plots of qt versus t0.5 for 1 and 2 mM Cu2+. The graph is divided into two linear lines, indicating that the Cu2+ adsorption takes place in a complex process involving external mass transfer and intraparticle diffusion. The steep slope in the first step indicates the external mass transfer to the external surface, and the second shallower slope is due to the intraparticle diffusion [30, 31]. The parameters from the Figures are presented in Table 2. The ki,1 and ki,2 values were calculated from the two straight lines in Fig. 5, each of which has a high correlation value (r2) of 0.9 or more. Although the adsorption rate was higher for a Cu2+ concentration of 2 mM than for 1 mM, the values of D and ks of the external material were decreased. This is because the adsorption rate is fast but takes a relatively long time to reach the adsorption equilibrium. These results confirm that the adsorption occurs by both internal diffusion and external mass transfer. With 1 mM Cu2+, the D value of the intraparticle diffusion is 3.8034 × 109 and the ks value of the external mass transfer is 12.2478. For 2 mM Cu2+, the corresponding values are 2.5563 ×109 m2/s and 9.0247×108 m/s, respectively. Therefore, intraparticle diffusion relatively dominates the total adsorption process.

4. Conclusions

In this study, the 3D structured double-network composites GO/Ca-Alg2-PAN were developed for removing Cu2+ ions from aqueous solution. The successful synthesis of GO/Ca-Alg2-PAN was confirmed by various physicochemical analyses. The synthesized GO/Ca-Alg2-PAN is robust and has a 3D double-network structure with many adsorption sites for Cu2+ ions. The GO/Ca-Alg2-PAN adsorbed Cu2+ ions with a maximum sorption capacity of 5.998 mmol/g. The adsorption behavior of the GO/Ca-Alg2-PAN was well-fitted to the Freundlich isotherm model in the batch experiments. The adsorption equilibrium of GO/Ca-Alg2-PAN was reached within 147 mins. Therefore, the GO/Ca-Alg2-PAN is judged to be an efficient adsorbent for Cu2+ ion removal from wastewater.


This research was supported by the Nuclear Energy Development Program through the National Research Foundation of Korea (NRF), funded by the Ministry of Science and ICT (2018M2B2B1065631).


Author Contributions

J.W.C. (ph.D. student) conducted all the experiments. H.J.K. (Doctor) wrote most of the manuscipts. H.R. (Master) did a little analysis. S.w.O. (Professor) helped revised the manuscript. S.-J.C. (Professor) led the overall study as a corresponding author.


1. Li N, Bai R. Copper adsorption on chitosan-cellulose hydrogel beads: behaviors and mechanisms. Sep Purif Technol. 2005;42:237–247.

2. Larous S, Meniai A-H, Lehocine MB. Experimental study of the removal of copper from aqueous solutions by adsorption using sawdust. Desalination. 2005;185:483–490.

3. Barros GKGC, Melo RPF, de Barros Neto EL. Removal of copper ions using sodium hexadecanoate by ionic flocculation. Sep Purif Technol. 2018;200:294–299.

4. Larsson M, Nosrati A, Kaur S, Wagner J, Baus U, Nydén M. Copper removal from acid mine drainage-polluted water using glutaraldehyde-polyethyleneimine modified diatomaceous earth particles. Heliyon. 2018;4:e00520

5. Thanh DN, Novák P, Vejpravova J, Vu HN, Lederer J, Munshi T. Removal of copper and nickel from water using nanocomposite of magnetic hydroxyapatite nanorods. J Magn Magn Mater. 2018;456:451–460.

6. Jang J, Lee DS. Magnetic Prussian blue nanocomposites for effective cesium removal from aqueous solution. Ind Eng Chem Res. 2016;55:3852–3860.

7. Vu HC, Dwivedi AD, Le TT, Seo S-H, Kim E-J, Chang Y-S. Magnetite graphene oxide encapsulated in alginate beads for enhanced adsorption of Cr (VI) and As (V) from aqueous solutions: Role of crosslinking metal cations in pH control. Chem Eng J. 2017;307:220–229.

8. Hosseinzadeh H, Ramin S. Effective removal of copper from aqueous solutions by modified magnetic chitosan/graphene oxide nanocomposites. Int J Biol Macromol. 2018;113:859–868.

9. Serrano-Aroca A, Deb S. Synthesis of irregular graphene oxide tubes using green chemistry and their potential use as reinforcement materials for biomedical applications. PloS one. 2017;12:e0185235

10. Zhu Y, Murali S, Cai W. , et alGraphene and graphene oxide: synthesis, properties, and applications. J Adv Mater. 2010;22:3906–3924.

11. Zhuang Y, Yu F, Chen J, Ma J. Batch and column adsorption of methylene blue by graphene/alginate nanocomposite: Comparison of single-network and double-network hydrogels. Journal of environmental chemical engineering. 2016;4:147–156.

12. Sikorski P, Mo F, Skjåk-Bræk G, Stokke BT. Evidence for egg-box-compatible interactions in calcium-alginate gels from fiber X-ray diffraction. Biomacromolecules. 2007;8:2098–2103.

13. Gong JP, Katsuyama Y, Kurokawa T, Osada Y. Double-network hydrogels with extremely high mechanical strength. Advanced materials. 2003;15:1155–1158.

14. Haque MA, Kurokawa T, Gong JP. Super tough double network hydrogels and their application as biomaterials. Polymer. 2012;53:1805–1822.

15. Serrano-Aroca Á, Ruiz-Pividal J-F, Llorens-Gámez M. Enhancement of water diffusion and compression performance of crosslinked alginate films with a minuscule amount of graphene oxide. Sci Rep. 2017;7:11684
crossref pdf

16. Llorens-Gámez M, Serrano-Aroca Á. Low-cost advanced hydrogels of calcium alginate/carbon nanofibers with enhanced water diffusion and compression properties. Polymers. 2018;10:405

17. Yoshitake H, Yokoi T, Tatsumi T. Adsorption of chromate and arsenate by amino-functionalized MCM-41 and SBA-1. Chem Mater. 2002;14:4603–4610.

18. Nastasović A, Jovanović S, Đorđević D, Onjia A, Jakovljević D, Novaković T. Metal sorption on macroporous poly (GMA-co-EGDMA) modified with ethylenediamine. React Func Polymer. 2004;58:139–147.

19. Deng S, Bai R. Removal of trivalent and hexavalent chromium with aminated polyacrylonitrile fibers: performance and mechanisms. Water Res. 2004;38:2424–2432.

20. Deng S, Bai R, Chen JP. Aminated polyacrylonitrile fibers for lead and copper removal. Langmuir. 2003;19:5058–5064.

21. Platero E, Fernandez ME, Bonelli PR, Cukierman AL. Graphene oxide/alginate beads as adsorbents: Influence of the load and the drying method on their physicochemical-mechanical properties and adsorptive performance. J Colloid Interface Sci. 2017;491:1–12.

22. Gupta A, Paliwal D, Bajaj P. Effect of an acidic comonomer on thermooxidative stabilization of polyacrylonitrile. J Appl Polymer Sci. 1995;58:1161–1174.

23. Usami T, Itoh T, Ohtani H, Tsuge S. Structural study of polyacrylonitrile fibers during oxidative thermal degradation by pyrolysis-gas chromatography, solid-state carbon-13 NMR, and Fourier-transform infrared spectroscopy. Macromol. 1990;23:2460–2465.

24. Uddin ME, Layek RK, Kim NH, Hui D, Lee JH. Preparation and properties of reduced graphene oxide/polyacrylonitrile nanocomposites using polyvinyl phenol. Composit B: Eng. 2015;80:238–245.

25. Ngah WSW, Fatinathan S. Adsorption of Cu(II) ions in aqueous solution using chitosan beads, chitosan–GLA beads and chitosan–alginate beads. Chem Eng J. 2008;143:62–72.

26. Lee HK, Yang DS, Oh W, Choi S-J. Copper Ferrocyanide Functionalized Core-Shell Magnetic Silica Composites for the Selective Removal of Cesium Ions from Radioactive Liquid Waste. J Nanosci Nanotechnol. 2016;16:6223–6230.

27. Cheung WH, Szeto YS, McKay G. Intraparticle diffusion processes during acid dye adsorption onto chitosan. Bioresour Technol. 2007;98:2897–2904.

28. Krishna R. A unified approach to the modelling of intraparticle diffusion in adsorption processes. Gas Sep Purif. 1993;7:91–104.

29. Mathews A, Weber W, editorsEffects of external mass transfer and intraparticle diffusion on adsorption rates in slurry reactors. AIChE Symposium Series1977.

30. Chen D, Zhang J, Chen J. Adsorption of methyl tert-butyl ether using granular activated carbon: Equilibrium and kinetic analysis. Int J Environ Sci Technol. 2010;7:235–242.
crossref pdf

31. Depci T, Kul AR, Önal Y. Competitive adsorption of lead and zinc from aqueous solution on activated carbon prepared from Van apple pulp: Study in single-and multi-solute systems. Chem Eng J. 2012;200:224–236.

Fig. 1
FT-IR spectra of (a) GO, (b) GO/Ca-Alg2, and (c) GO/Ca-Alg2-PAN.
Fig. 2
SEM-EDS spectra of GO/Ca-Alg2-PAN beads.
Fig. 3
FE-SEM images and physical properties of (a) GO, (b) GO/Ca-Alg2 and (c–d) GO/Ca-Alg2-PAN beads.
Fig. 4
Adsorption (a) Isotherms and (b) Kinetic models of Cu2+ using GO/Ca-Alg2-PAN.
Fig. 5
Intraparticle diffusion plot for Cu2+ adsorption by GO/Ca-Alg2-PAN.
Table 1
Constants and Correlation Coefficients of Isotherm Models for Cu2+ Removal at 0.1–60 mM and Kinetic Models at 1 and 2 mM Cu2+
Models Parameters
Isotherm Langmiur qm = 5.99 mmol/g, b =9.308 L/mg, r2 = 0.962
Freundlich Kf = 1.08 ((mg/g)(L/mg)1/n), n = 2.373, r2 = 0.980

Kinetics Pseudo first-order 1 mM Cu2+ k1 = 0.013 min−1, qe = 0.40 mmol/g, r2 = 0.988
2 mM Cu2+ k1 = 0.014 min−1, qe = 0.60 mmol/g, r2 = 0.969

Pseudo-second-order 1 mM Cu2+ k2 = 0.027 min−1, h = 0.0068 mmol/g·min, qe = 0.50 mmol/g, r2 = 0.995
2 mM Cu2+ k2 = 0.021 min−1, h = 0.0112 mmol/g·min, qe = 0.73 mmol/g, r2 = 0.984
Table 2
Kinetic Data Calculated for the Adsorption of 1 mM and 2 mM Cu2+ by GO/Ca-Alg2-PAN
Cu2+ (mM) Intraparticle External

ki,1 (mmol/g·min0.5) ki,2 (mmol/g·min0.5) D × 109 (m2/s) r12 r22 ks×108 (m/s) r2
1 0.026 0.013 3.8034 0.977 0.973 12.2478 0.759
2 0.039 0.016 2.5563 0.969 0.912 9.0247 0.691
Editorial Office
464 Cheongpa-ro, #726, Jung-gu, Seoul 04510, Republic of Korea
TEL : +82-2-383-9697   FAX : +82-2-383-9654   E-mail : eer@kosenv.or.kr

Copyright© Korean Society of Environmental Engineers. All rights reserved.        Developed in M2community
About |  Browse Articles |  Current Issue |  For Authors and Reviewers