Abstract
Recently the interest in the remediation of liquid effluents from industries such as paint manufacturing, leather tanning, etc. has increased, because the quality of the water used in these processes is highly compromised and is generally discarded without any process of purification, causing an inadequate use of water and contributing to the hydric stress of the planet. Therefore, it is necessary to find alternatives for the remediation of water used in industrial processes; one of the methods that has been widely accepted given its high efficiency, low cost, and versatility compared to others is the bioadsorption using materials derived from various processes used for the elimination of metals such as Cr, Co, Cu, Ni, etc. from liquid effluents. Among the materials used for this purpose are rice husk, orange, and wheat as well as apatite (hydroxyapatite and brushite), derived from animal bones, which have shown good capacity (>90%) to adsorb metals from aqueous solutions. Through the characterization by DRX, FTIR, and SEM, of the brushite and studies in equilibrium and kinetics of adsorption, it has been demonstrated that this material has a good capacity to remove metals present in water.
Keywords
- brushite
- removal
- isotherm
- kinetics
- metals
1. Introduction
The contamination of water bodies due to the presence of heavy metals is a serious problem, because every day this vital resource is scarce and because of the high toxicity of these compounds for the health of living beings. The metals present in water are a risk factor for the development of diseases such as cancer and dermatitis; in addition, they may be accumulated in the human body because they cannot be metabolized [1, 2, 3, 4, 5, 6, 7]. Solid-liquid removal processes such as chemical precipitation, filtration, and adsorption, among others, have been widely used for the removal of metals such as nickel (Ni), iron (Fe), copper (Cu), zinc (Zn), cobalt (Co), and chromium (Cr) of liquid effluents [8, 9, 10, 11]; however, some of these methods have disadvantages such as high operating cost and low efficiency; however, methods such as coagulation and precipitation are already used in various industrial processes for the removal of metals from industrial effluents [12]. In recent years, adsorption has been one of the most used metal ion removal techniques, since it is a simple, effective, and inexpensive process compared to other methods [13, 14, 15, 16, 17]. Adsorption processes have been experimented with an extensive amount of materials such as adsorbents, among which activated carbon stands out due to its high capacity for capturing metal ions; however, this material has the disadvantage of generating large quantities of sludge, since the removal of metals trapped in activated carbon can only be done with processes that are often expensive such as leaching [5, 9, 18, 19]. For this reason, the use of different materials that are economical, are easy to obtain, and have high efficiency in the removal of metal ions has been investigated. In recent decades, these studies have focused on the waste derived from the agricultural industry that produces large amounts of waste such as biomass, wheat husks, rice, orange, etc. [2, 4, 8, 9, 16, 18, 19, 20, 21, 22, 23, 24, 25, 26, 27, 28, 29, 30]; the use of residues from other industries has also been investigated, such as the case of apatites derived from the bone tissue of animals, which have been used for removal of dyes and metal ions obtaining promising results. The use of apatites in particular hydroxyapatite and brushite for the adsorption of heavy metals such as Cd, Cu, Ni, Pb, Co, Mn, and Fe, to name a few, has already been reported [31, 32, 33, 34, 35]; however, in most of the studies carried out, only the process of adsorption of metallic solutions of a single component has been analyzed, so the objective of the present work is to evaluate the capacity of brushite (nDCPD), obtained from bovine bone to remove Ni (II), Co (II), and Cu (II) of aqueous solutions, analyzing the selectivity of removal of metal ions in aqueous solutions with two or three different metals, determining the kinetic models and in equilibrium in which the removal of metals takes place and the structural changes suffered by nDCPD during the development of the different tests.
2. Experimental
2.1 Reagents
All the reagents that were used were of analytical grade. The water used for the preparation of solutions in the experiment was deionized. The solutions to be evaluated were prepared by dissolution of salts of nickel (Ni(NO3)2 6H2O), cobalt (Co(NO3)2⋅6H2O), and copper (Cu(NO3)2) in concentrations from 0 to 1,000 ppm.
2.2 Preparation of the adsorbent
Brushite natural (nDCPD) was obtained from bovine bone, which was washed with hot water several times to remove tissue debris, and then it was dried at 353 K for 24 h. Next, the bones were crushed and sieved to obtain a particle size of 150 mesh (104 μm). Then, the powder obtained was treated with HCl and NaOH solution, 10−2 M, respectively, using a ratio of 30% w/v. Finally nDCPD was stored until its use [1].
2.3 Characterization of natural brushite
The X-ray diffraction patterns (XRD) were obtained in a Rigaku diffractometer (Ultima IV). The Fourier transform infrared studies of the samples were performed in an IR 100 Analyzer spectrophotometer (PerkinElmer), in a range of 400–4000 cm−1. The scanning electron microscopy (SEM) images were obtained in a JOEL equipment (6510-Plus).
2.4 Co, Cu, and Ni adsorption isotherm
The different isotherm models used to describe the adsorption of Ni, Co, and Cu are concentrated in Table 1, for each one of the regression coefficients was calculated to evaluate the adjustment of each nonlinear model and the separation factor,
Model | Equation |
---|---|
SIPS |
|
Redlich-Peterson (R-P) |
|
Langmuir |
|
Temkin |
|
Freundlich |
|
where
where
For the study of the adsorption isotherms of the different metals in nDCPD, 1 g of sorbent was put in contact with 50 ml of the aqueous solution of the metal ions Co, Cu, and Ni, varying the concentration between 0 and 1000 ppm in a shaker (ZHWY-200D) with an agitation of 200 rpm at 25, 35, and 45°C for 24 h of contact time.
2.5 Batch removal kinetics
The experiments to establish the kinetics of metal ion removal in nDCPD and to know the evolution of the adsorption of Ni, Co, and Cu ions in the biomaterial were carried out in batches. They were carried out varying the concentration of nDCPD (Cads), from 0 to 40 g/L, during 24 h at a speed of 200 rpm and at 25, 35, and 45°C. At specific times aliquots of aqueous solution were taken to separate the adsorbent material and the liquid supernatant by centrifugation at 10,000 rpm. The supernatant was analyzed with the help of a spectrophotometer (JENWAY 6705) to know the concentration of the different ions present in the solution. The amount of ions removed (
where
The percentage of removal (%
3. Results and discussion
3.1 Adsorption isotherms
Adsorption data obtained at different temperatures help to understand the interaction between nDCPD and Ni, Co, and Cu ions; analyzing the data with different adsorption models, the model with better fit is obtained. In Table 1, the most used isotherm models are described according to the literature, and in Figures 1–3 for Ni, Co, and Cu, respectively, the behavior of the removal of metal ions at different temperatures is shown. The parameters derived from the adjustments together with the coefficient of determination, R2, are shown in Tables 2
Models | Parameters | ||
---|---|---|---|
15°C | 30°C | 45°C | |
0.005 | 0.016 | 0.0020 | |
18.2426 | 20.6152 | 22.4789 | |
1.1611 | 0.8644 | 1.3671 | |
R2 | 0.9969 | 0.9985 | 0.9974 |
0.0191 | 0.2423 | 0.2024 | |
0.007 | 0.0240 | 0.0078 | |
β | 1.0 | 0.9046 | 1.0 |
R2 | 0.9943 | 0.9990 | 0.9913 |
0.0007 | 0.0078 | 0.0105 | |
27.7198 | 18.9551 | 25.9445 | |
R2 | 0.9962 | 0.9975 | 0.9913 |
0.588–0.935 | 0.114–0.562 | 0.087–0.488 | |
0.0552 | 1.6384 | 1.5515 | |
1.2921 | 2.7263 | 2.3854 | |
R2 | 0.9923 | 0.9869 | 0.9980 |
1.873 × 10−8 | 2.683 × 10−8 | 2.3779 × 10−10 | |
1.0213 | 2.3617 | 2.8940 | |
R2 | 0.6402 | 0.9078 | 0.8337 |
Models | Parameters | ||
---|---|---|---|
15°C | 30°C | 45°C | |
0.0470 | 0.0208 | 0.0117 | |
23.8607 | 30.1446 | 41.8104 | |
1.1294 | 0.8178 | 0.9105 | |
R2 | 0.9895 | 0.9958 | 0.9895 |
0.1884 | 0.4259 | 0.3462 | |
0.0073 | 0.0326 | 0.0089 | |
β | 1.0 | 0.8886 | 1.0 |
R2 | 0.9980 | 0.9953 | 0.9891 |
0.0073 | 0.0089 | 0.0124 | |
25.6863 | 26.5263 | 39.0000 | |
R2 | 0.9980 | 0.9933 | 0.9891 |
0.121–0.578 | 0.101–0.529 | 0.075–0.447 | |
1.3457 | 2.2983 | 2.1685 | |
2.2770 | 2.6411 | 2.2291 | |
R2 | 0.9723 | 0.9773 | 0.9753 |
2.0398 × 10−8 | 1.8935 × 10−8 | 4.696 × 10−8 | |
2.8230 | 3.3781 | −6.3526 × 10−6 | |
R2 | 0.8390 | 0.9084 | 0.4984 |
Models | Parameters | ||
---|---|---|---|
15°C | 30°C | 45°C | |
1.396 × 10−5 | ND | 0.2080 | |
41.4493 | 41.3266 | ||
2.3971 | 1.1676 | ||
R2 | 0.9980 | 0.9200 | |
0.2036 | ND | 9.9421 | |
0.0013 | 0.2322 | ||
β | 1.0 | 1.0 | |
R2 | 0.9632 | 0.9170 | |
0.0013 | ND | 0.2322 | |
154.8825 | 42.8164 | ||
R2 | 0.9632 | 0.9170 | |
0.435–0.885 | 0.004–0.041 | ||
0.2914 | ND | 14.5249 | |
1.1274 | 4.7001 | ||
R2 | 0.9548 | 0.7741 | |
2.9527 × 10−8 | ND | 10.1004 | |
4.5983 | 6.7337 | ||
R2 | 0.5789 | 0.8472 |
3.2 Effect of temperature on the removal of metal ions
In the literature it has been widely reported that one of the most important variables in the process of solid-liquid removal is temperature, since it directly influences some thermodynamic parameters (Table 5) of great interest in the removal process. The negative values of Δ
Metal | T (K) | -Δ |
Δ |
Δ |
---|---|---|---|---|
Ni | 288.15 | 18.52 | 69.63 | 308.53 |
303.15 | 25.56 | |||
318.15 | 27.62 | |||
Co | 288.15 | 24.15 | 13.39 | 130.08 |
303.15 | 25.91 | |||
318.15 | 28.07 | |||
Cu | 288.15 | 20.20 | 131.74 | 572.27 |
303.15 | ND | |||
318.15 | 36.02 |
3.3 Effect of contact time and amount of adsorbent
In the process of solid-liquid adsorption, it is convenient to know the necessary contact time between the adsorbent and the adsorbate to achieve a maximum interaction between both and get removed as much metal ions as possible. Figures 4–6 show the adsorption curves of each metal ion, where it is observed that about 10 h after the start of the process, the adsorption speed is high and that after this time the rate of removal of the ions. It decays, probably, because the sites where the capture of the ions is carried out are saturated, and therefore the balance is reached regardless of the concentration of absorber that has been used. This type of behavior is common among various adsorbent materials [37]. Also, it is observed that the adsorption capacity of the adsorbent material decreases significantly with the increase in the concentration of absorbent independent of the temperature at which the removal process is carried out, so that the adsorption potential of the Ni ions decreases from 25.8 to 7.78 mg/g at 15°C, while at 30 and 45°C, it decreases from 20.6 to 7.78 and 20.6 to 8.6 mg/g, respectively. In the case of Co ions, the adsorption capacity decreases from 28.4 to 10.4 mg/g, from 31.04 to 11.97 mg/g, and from 31.04 to 10.4 mg/g at 15, 30, and 45°C, respectively. Finally, in the case of Cu ions, the decrease in the adsorption capacity at 15, 30, and 45°C was 49.9–11.0, 56.8–12.4, and 61.2–12 mg/g, respectively. This type of behavior is observed in the adsorption of metals [1, 26, 28, 29].
In the aqueous solutions with the three metal ions present, a behavior similar to that observed in the solutions prepared with a single metal compound was observed; however, the time necessary to reach equilibrium was around 5 h, and the adsorption capacity of the ions in solution was also significantly decreased by increasing the concentration of sorbent in the solution. The adsorption capacity achieved (Figure 7), for Ni ions, was from 32.4 to 6.2 mg/g, for Co ions from 41.9 to 10 mg/g, and for Cu ions from 59.9 to 12.1 mg/g at 45°C, which indicates that it is not necessary to saturate the solution with nDCPD to achieve greater metal uptake [32, 33, 34]. On the other hand, in the analysis of the Co-Cu binary solution, a behavior similar to the previous cases was observed, achieving a greater adsorption capacity with less amount of absorbent, so that at a temperature of 45°C (Figure 8), for Co ions, it was possible to adsorb 32–9.9 mg/g and for Cu ions from 57 to 11.8 mg/g.
In the removal of ions in solutions, it was observed that the percentage of removal increases with the increase in the amount of nDCPD used, achieving removal percentages close to 100% for Cu ions and 95% for Co ions; however, for Ni about 70% removal was only achieved (Figure 9), suggesting that sites available for nickel capture are quickly saturated due to the large amount of chromium in the effluent. The changes caused by the variation of the temperature depend on the metal ion, since the maximum removal of the Ni ions is between 15 and 30°C, while for the Cu and Co ions, it is given at 30°C. Similar observations have been reported in adsorption studies conducted with other biomaterials [29, 38]. The selectivity shown in the present study was the following: Cu > Co > Ni, with percentages of removal in solutions composed of the three ions of 96% (Cu), 83% (Co), and 59% (Ni). Additionally, in Figure 10, it is observed that in the solutions composed only by Co or Cu, the time necessary to reach the equilibrium decreases considerably; in addition, the selectivity is maintained toward the removal of Cu compared to the Co, having a percentage of removal of 95–79%, respectively. Finally, the changes caused by the variation of the temperature depend on the metal ion, since the maximum removal of the Ni ions is between 15 and 30°C, while for the Cu and Co ions, it was at 30°C (Figure 11).
3.4 Kinetic study
To understand the process of removal of the different metal ions in aqueous solution, as well as the relationship that occurs between the metals and the interaction of the metal ions with the adsorbent material, the data obtained in the experimentation was evaluated at different temperatures and with different concentrations of adsorbents with the adsorption models that are concentrated in Table 6 [6]. The kinetic parameters calculated with the different models (Table 1), were used to adjust the experimental adsorption values obtained for the three metal ions with the different concentrations of adsorbent and temperatures utilized, by using SigmaPlot software (Version 11®). Based on the obtained values, it is distinguished that the models that present the best adjustments to the obtained data are pseudo first order, Elovich and pseudo-second order, so it can be inferred that the removal mechanism is due to the ions being adsorbed in one or two sites on the surface that is heterogeneous since each site has different adsorption energy [1, 4, 5]. Similarly, it can be noticed that the models that do not adequately describe the process of metal removal in nDCPD are those that are related to the mass transfer both external and internal, independent of the temperature, the concentration of the adsorbent material, and the presence of another metal ion in the same solution; so it can be inferred that the removal process of these metals does not present problems of mass transfer.
3.5 Characterization of nDCPD
Figure 12 shows the SEM image of the nDCPD doped with the Ni, Co, and Cu ions, where the main characteristics of nDCPD (Figure 12a), monoclinic disk morphology [1, 15, 29, 39], which does not present significant changes in the presence of Ni (Figure 12b), Co (Figure 12c), and Cu (Figure 12d) ions can be observed, probably because the vast majority of metal ions are adsorbed on the surface of nDCPD. The XRD patterns of nDCPD doped with Ni, Co, and Cu are shown in Figure 13, and according to the International Center of Diffraction Data Chart (JCPDS) database, some changes are observed in the samples with metal ions compared to that of nDCPD without doping [1]. The peaks at ∽32° and 40° increase in intensity, while at ∽34°, the intensity of the peaks directly related to the presence of Ni, Co, and Cu ions decreases. While at 26, 29, and 53°, new peaks appear in the doped brushite samples, which also caused a decrease in the network parameter of 4.99 nm, a value lower than the 5.77 nm obtained for nDCPD, without doping, together with the particle size from 9.26 to 4.45, 4.08, and 4.35 Å, for Ni, Co, and Cu, respectively, which was determined with the Scherrer Equation [39, 40]. This may be due to the fact that the Ca ions of nDCPD without doping (1.12 Å) are replaced during the adsorption process by the ions of Ni (0.78 Å), Co (0.63 Å), and Cu (0.69 Å), which implies that part of the ions are retained inside the structure of nDCPD [40].
In Figure 14, the infrared spectra of nDCPD are presented, where the characteristic peaks of the groups that make up apatite are observed, among which the presence of a doublet stands out at 577 and 526 cm
4. Conclusion
Based on the thermodynamic parameters obtained at different temperatures and concentrations of brushite (nDCPD), used as an adsorbent material in the removal of different heavy metals (Ni, Co, and Cu), from aqueous solutions, it can be concluded that the adsorption of heavy metals with nDCPD is feasible and that the adsorption capacity of nDCPD increases at a higher temperature. The percentages of removal achieved show that nDCPD has a higher affinity for adsorbing Cu and Co compared to Ni. From the data obtained from the adsorption isotherms, it can be inferred that the process of removing the metal ions in solution on the surface of nDCPD is carried out, forming a heterogeneous monolayer since the model that best fits to the data obtained in the SIPS is a combination of the Langmuir and Freundlich models. The experimental data obtained also show that there are different models to describe the kinetic process of adsorption, such as the pseudo-first-order model, which suggests that only one surface site is needed for adsorption to take place, as well as the pseudo-second-order model which indicates that two sites are needed for each ion molecule and that each site requires different adsorption energies as described by the Elovich model, which confirms the heterogeneity of the nDCPD surface determined from of the adsorption isotherms generated. The surface changes of nDCPD, evidenced by the XRD and FTIR analyses, suggest that the HPO− and PO3−4 are directly involved in the Ni, Co, and Cu adsorption process, which allows us to conclude that nDCPD is an appropriate candidate to be used in the removal of heavy metals present in wastewater from different industries.
Acknowledgments
The authors thank the Interdisciplinary Professional Unit of Engineering Campus Guanajuato of the IPN, the Center for Nanoscience and Nanotechnology (CNyN) of the UNAM, and the Colombian Polytechnic “Jaime Isaza Cadavid” for the infrastructure provided for the realization of this project and the Research and Postgraduate Secretary for the financial support for this work (SIP: 20170577) and to the BIOCATEM Network.
References
- 1.
Hernández-Maldonado JA, Torres-Garcia FA, Salazar-Hernández MM, Hernández-Soto R. Removal of chromium from contaminated liquid effluents using natural brushite obtained from bovine bone. Desalination and Water Treatment. 2017; 95 :262-273. DOI: 10.5004/dwd.2017.21480 - 2.
Yildiz S. Kinetic and isotherm analysis of Cu(II) adsorption onto almond shell ( Prunus dulcis ). Ecological Chemistry and Engineering S. 2017;24 (1):87-106. DOI: 10.1515/eces-2017-0007 - 3.
Moreira VR, Lebron YAR, Freire SJ, Santos LVS, Palladino F, Jacob RS. Biosorption of copper ions from aqueous solution using Chlorella pyrenoidosa : Optimization, equilibrium and kinetics studies. Microchemical Journal. 2019;145 :119-129. DOI: 10.1016/j.microc.2018.10.027 - 4.
Giza S. Biosorption of heavy metal from aqueous waste solution using cellulosic orange peel. Ecological Engineering. 2017; 99 :134-140. DOI: 10.1016/j.ecoleng.2016.11.043 - 5.
Sudha R, Srinivasan K, Premkumar P. Removal of nickel(II) from aqueous solution using Citrus Limettioides peel and seed carbon. Ecotoxicology and Environmental Safety. 2015; 117 :115-123. DOI: 10.1016/j.ecoenv.2015.03.025 - 6.
Qiu Y, Yang L, Huang S, Ji Z, Li Y. The separation and recovery of copper(II), nickel(II), cobalt(II), zinc(II), and cadmium(II) in a sulfate-based solution using a mixture of Versatic 10 acid and Mextral 984H. Chinese Journal of Chemical Engineering. 2017; 25 :760-767. DOI: 10.1016/j.cjche.2016.10.013 - 7.
Guo Y, Zhao H, Han Y, Liu X, Guan S, Zhang Q , et al. Simultaneous spectrophotometric determination of trace copper, nickel, and cobalt ions in water samples using solid phase extraction coupled with partial least squares approaches. Spectrochimica Acta Part A: Molecular and Biomolecular Spectroscopy. 2017; 173 :532-536. DOI: 10.1016/j.saa.2016.10.003 - 8.
Huan-Ping C, Chung-Cheng C, Aileen N. Biosorption of heavy metals on Citrus maxima peel, passion fruit shell, and sugarcane bagasse in a fixed-bed column. Journal of Industrial and Engineering Chemistry. 2014;20 :3408-3414. DOI: 10.1016/j.jiec.2013.12.027 - 9.
Pedrosa Xavier AL, Herrera Adarme OF, Furtado LM, Dias Ferreira GM, Mendes da Silva LH, Alves Gurgel LV, et al. Modeling adsorption of copper(II), cobalt(II) and nickel(II) metal ions from aqueous solution onto a new carboxylated sugarcane bagasse. Part II: Optimization of monocomponent fixed-bed column adsorption. Journal of Colloid and Interface Science. 2018; 516 :431-445. DOI: 10.1016/j.jcis.2018.01.068 - 10.
Qiu X, Hu H, Yang J, Wang C, Cheng Z. Removal of trace copper from simulated nickel electrolytes using a new chelating resin. Hydrometallurgy. 2018; 180 :121-131. DOI: 10.1016/j.hydromet.2018.07.015 - 11.
Liu X, He Y, Zhao Z, Chen X. Study on removal of copper from nickel-copper mixed solution by membrane electrolysis. Hydrometallurgy. 2018; 180 :153-157. DOI: 10.1016/j.hydromet.2018.07.019 - 12.
Sikder T, Rahman M, Jakariya M, Hosokawa T, Kurasaki M, Saito T. Remediation of water pollution with native cyclodextrins and modified cyclodextrins: A comparative overview and perspectives. Chemical Engineering Journal. 2019; 355 :920-941. DOI: 10.1016/j.cej.2018.08.218 - 13.
Ivanets AI, Srivastava V, Kitikova NV, Shashkova IL, Sillanpää M. Kinetic and thermodynamic studies of the Co(II) and Ni(II) ions removal from aqueous solutions by Ca-Mg phosphates. Chemosphere. 2017; 171 :348-354. DOI: 10.1016/j.chemosphere.2016.12.062 - 14.
Vollprecht D, Mischitz R, Krois LM, Sedlazeck KP, Müller P, Olbrich T, et al. Removal of critical metals from waste water by zero-valent iron. Journal of Cleaner Production. 2019; 208 :1409-1420. DOI: 10.1016/j.jclepro.2018.10.180 - 15.
Martins JJ, Órfão JJM, Soares OGSP. Sorption of copper, nickel and cadmium on bone char. Protection of Metals and Physical Chemistry of Surfaces. 2017; 53 (4):618-627. DOI: 10.1134/S2070205117040153 - 16.
Moscatello NJ, Pfeifer BA. Yersiniabactin metal binding characterization and removal of nickel from industrial wastewater. Biotechnology Progress. 2017; 33 (6):1548-1554. DOI: 10.1002/btpr.2542 - 17.
Osińska M. Removal of lead(II), copper(II), cobalt(II) and nickel(II) ions from aqueous solutions using carbon gels. Journal of Sol-Gel Science and Technology. 2017; 81 :678-692. DOI: 10.1007/s10971-016-4256-0 - 18.
Bhatnagar A, Sillanpää M. Utilization of agro-industrial and municipal waste materials as potential adsorbents for water treatment: A review. Chemical Engineering Journal. 2010; 157 :277-296. DOI: 10.1016/j.cej.2010.01.007 - 19.
Bhatnagar A, Sillanpää M, Witek-Krowiak A. Agricultural waste peels as versatile biomass for water purification: A review. Chemical Engineering Journal. 2015; 270 :244-271. DOI: 10.1016/j.cej.2015.01.135 - 20.
Romero-Cano LA, García-Rosero H, Gonzalez-Gutierrez LV, Baldenegro-Pérez LA, Carrasco-Marín F. Functionalized adsorbents prepared from fruit peels: Equilibrium, kinetic and thermodynamic studies for copper adsorption in aqueous solution. Journal of Cleaner Production. 2017; 162 :195-204. DOI: 10.1016/j.jclepro.2017.06.032 - 21.
Femina Carolin C, Senthil Kumar P, Saravanan A, Janet Joshiba G, Naushad M. Efficient techniques for the removal of toxic heavy metals from aquatic environment: A review. Journal of Environmental Chemical Engineering. 2017; 5 :2782-2799. DOI: 10.1016/j.jece.2017.05.029 - 22.
Liang S, Guo X, Feng N, Tian Q. Adsorption of Cu2+ and Cd2+ from aqueous solution by mercapto-acetic acid modified orange peel. Colloids and Surfaces B: Biointerfaces. 2009; 73 :10-14. DOI: 10.1016/j.colsurfb.2009.04.021 - 23.
Annadurai G, Juang RS, Lee DJ. Adsorption of heavy metals from water using banana and orange peels. Water Science and Technology. 2002; 47 (1):185-190. DOI: 10.2166/wst.2003.0049 - 24.
De Gisi S, Lofrano G, Grassi M, Notarnicola M. Characteristics and adsorption capacities of low-cost sorbents for wastewater treatment: A review. Sustainable Materials and Technologies. 2016; 9 :10-40. DOI: 10.1016/j.susmat.2016.06.002 - 25.
Romero-Cano LA, Gonzalez-Gutierrez LV, Baldenegro-Perez LA. Biosorbents prepared from orange pressure peels using instant controlled drop for Cu(II) and phenol removal. Industrial Crops and Products. 2016; 84 :344-349. DOI: 10.1016/j.indcrop.2016.02.027 - 26.
Moreno-Piraján JC, Giraldo L. Heavy metal ions adsorption from wastewater using activated carbon from orange peel. E-Journal of Chemistry. 2012; 9 (2):926-937. DOI: 10.1155/2012/928073 - 27.
Farroq U, Kozinski JA, Ain Khan M, Athar M. Biosorption of heavy metal ions wheat based biosorbents—A review of the recent literature. Bioresource Technology. 2010; 101 :5043-5053. DOI: 10.1016/j.biortech.2010.02.030 - 28.
Habib A, Islam N, Islam A, Shafiqul Alam AM. Removal of copper from aqueous solution using orange peel, sawdust and bagasse. Pakistan Journal of Analytical & Environmental Chemistry. 2007; 8 (1-2):21-25. DOI: 10.21743/pjaec/2016.06.005 - 29.
Khalfaoui A, Meniai AH. Application of chemically modified orange peels for removal of copper(II) from aqueous solutions. Theoretical Foundations of Chemical Engineering. 2012; 46 (6):732-739. DOI: 10.1134/S0040579512060103 - 30.
Surovka D, Pertile E. Sorption of iron, manganese, and copper from aqueous solution using orange peel: Optimization, isothermic, kinetic, and thermodynamic studies. Polish Journal of Environmental Studies. 2017; 26 (2):795-800. DOI: 10.15244/pjoes/60499 - 31.
Hamidi E, Arsalane S, Halim M. Kinetics and isotherm studies of copper removal by brushite calcium phosphate: Linear and non-linear regression comparison. E-Journal of Chemistry. 2012; 9 (3):1532-1542. DOI: 10.1155/2012/928073 - 32.
Mobasherpour I, Salahi E, Pazouki M. Comparative of the removal of Pb2+, Cd2+ and Ni2+ by nano crystallite hydroxyapatite from aqueous solutions: Adsorption isotherm study. Arabian Journal of Chemistry. 2012; 5 :439-446. DOI: 10.1016/j.arabjc.2010.12.022 - 33.
El Hamidi A, Mulongo Masamba R, Khachani M, Halim M, Arsalane S. Kinetics modeling in liquid phase, sorption of copper ions on brushite di-calcium phosphate dihydrate CaHPO4·2H2O (DCPD). Desalination and Water Treatment. 2016; 56 :779-791. DOI: 10.1080/19443994.2014.940391 - 34.
Huang Y, Chen L, Wang H. Removal of Co(II) from aqueous solution by using hydroxyapatite. Journal of Radioanalytical and Nuclear Chemistry. 2012; 291 :777-785. DOI: 10.1007/s10967-011-1351-0 - 35.
Fernane F, Boudia S, Aiouache F. Removal Cu(II) and Ni(II) by natural and synthetic hydroxyapatites: A comparative study. Desalination and Water Treatment. 2014; 52 :2856-2862. DOI: 10.1080/19443994.2013.807084 - 36.
Singh KK, Hasan SH, Talat M, Singh VK, Gangwar SK. Removal of Cr(VI) from aqueous solutions using wheat bran. Chemical Engineering Journal. 2009; 151 :113-121. DOI: 10.1016/j.cej.2009.02.003 - 37.
Elabbas S, Mandi L, Berrekhis F, Pons MN, Leclerc JP, Ouazzani N. Removal of Cr(III) from chrome tanning wastewater by adsorption using two natural carbonaceous materials: Eggshell and powdered marble. Journal of Environmental Management. 2016; 166 :589-595. DOI: 10.1016/j.jenvman.2015.11.012 - 38.
Pehlivan E, Pehlivan E, Tutor-Kahraman H. Hexavalent chromium removal by Osage Orange. Food Chemistry. 2012; 133 :1478-1484. DOI: 10.1016/j.foodchem.2012.02.037 - 39.
Mirković MM, Lazarević-Pašti TD, Došen AM, Ćebela MŽ, Rosić AA, Matović BZ, et al. Adsorption of malathion on mesoporous monetite obtained by mechanochemical treatment of brushite. RSC Advances. 2016; 6 :12219-12225. DOI: 10.1039/c5ra27554g - 40.
Thangadurai V, Kopp P. Chemical synthesis of Ca-doped CeO3-intermediate temperature oxide ion electrolytes. Journal of Power Sources. 2007; 168 :178-183. DOI: 10.1016/j.jpowsour.2007.03.030 - 41.
Sopcak T, Medvecky L, Giretova M, Stulajterona R, Durisin J, Girman V, et al. Effect of phase composition of calcium silicate phosphate component on properties of brushite based composite cements. Materials Characterization. 2016; 117 :17-29. DOI: 10.1016/j.matchar.2016.04.011 - 42.
Arifuzzaman SM, Rohani S. Experimental study of brushite precipitation. Journal of Crystal Growth. 2004; 267 :624-634. DOI: 10.1016/j.crysgro.2004.04.024