Development of New Effective Sorbents Based on Nanomagnetite
© Kołodyńska et al. 2016
Received: 30 November 2015
Accepted: 14 March 2016
Published: 21 March 2016
Magnetic hybrid nanocomposite material based on the kraft lignin was prepared by the co-precipitating method. Kraft lignin was modified by iron nanooxide in order to enhance its sorption properties towards heavy metal ions. The composite material was characterized by physicochemical methods such as BET N2, ATR-FTIR, TGA, DSC, pHpzc, XRD and SEM. Its adsorption behaviour was studied using the batch mode by varying different parameters like pH, initial concentration of metal ions and shaking time as well as the presence of interfering ions. Adsorption of Cu(II), Cd(II) and Pb(II) ions from the aqueous solutions was studied in comparison with the commercial kraft lignin. The adsorption capacity and kinetic sorption characteristics of the composite material were determined.
Due to heavy metal environmental persistence and intense utilization in several applications, development of cost-effective removal strategies is required for treating metal containing waters and wastewaters. A variety of well-known treatment methods exists for metal removal including precipitation, coagulation and co-precipitation, electrochemical treatment, ion exchange and membrane separation [1, 2]. However, high capital costs of the above mentioned processes led to explore more cost-effective options including the use of sorption media developed from such natural materials as biosorbents. Many low-cost adsorbents such as chitosan, clay, saw dust, lignin, pectin, seaweed, zeolite, bark materials and iron oxide-coated sand were previously investigated for metal ion removal. Lignin, the by-product of paper industry and emerging cellulose ethanol industry, is a potential metal sorbent.
Most research related to lignin deals with the kraft lignin or black liquor of paper industry. Many other types of lignin were also designated as having dark black appearance. This is solely due to the self condensation of various functional groups of lignin macromolecules during separation from the lignocellulosic matrix. However, compared with polysaccharides, cellulose and hemicellulose, the effective use of lignin has not been progressed owing to the difficult separation of lignin from the other components of wood without their denaturation. The limited use of lignin compared to cellulose is attributable to its molecular structure; i.e. the lignin molecule lacks stereo-regularity and the repeating units of the polymer chain are heterogeneous. Also, lignin in wood forms interpenetrating polymer units with cellulose. Hence, using conventional methods, strong reagents are necessary to separate hydrophobic lignin from hydrophilic cellulose which results in the condensation of lignin on itself giving complicated molecular networks.
Recent industrial applications of lignin are mainly based on modified lignins. Their aromatic three-dimensional structure involving a large number of functional groups, such as methoxy groups, hydroxyl groups, carboxylic acid groups and sulfonate groups, suggests that these groups can play an important role in the formation of macromolecular materials. Therefore, the main aim of this study was to compare the relative ability of kraft lignin and modify by magnetite lignin to sorb Cu(II), Cd(II) and Pb(II) ions from aqueous solution in the batch technique. The batch method is mainly used for determination of physical and chemical properties of sorption: selectivity coefficients, stability of complexes in the phase of a sorbent, and its capacities. A secondary aim was to find the correlation between the sorption mechanisms and such important parameters as the surface properties (i.e., particle size, surface area, functional group composition/content) of selected lignin sorbents.
Modification of lignin by iron nanooxides was provided in order to enhance its sorption properties. Iron oxides have a relatively high surface area and effective adsorption groups. Various forms of iron oxides, e.g. magnetite Fe3O4, hematite α-Fe2O3 and maghemite γ-Fe2O3 are widely described in literature .
Materials and Apparatus
Aqueous solutions of Cu(II), Cd(II) and Pb(II) ions were prepared by dissolving corresponding analytical grade individual metal chlorides or nitrates. pH of the solutions was adjusted by dilute sodium hydroxide solution. The pH of the sample solution was measured by using a pH meter model M 85 Precision (Radiometer).
Batch experiments were carried out in triplicate in the pH range from 2–6, sorbent dose 0.01–0.5 g and the initial metal concentration 100 mg/dm3. A series of initial metal concentrations (c 0) ranging from 25 to 100 mg/dm3 for kinetic analysis and from 25 to 500 mg/dm3 for isotherms, respectively, were prepared from metal stock solutions of Cu(II), Cd(II) and Pb(II). The initial suspension pH value was adjusted by adding 0.01 M HCl or 0.01 M NaOH.
The flasks were equilibrated at room temperature on a mechanical shaker (ELPIN+ 358 type, Elpin) with constant shaking at 180 rpm. Based on the preliminary tests, a 3-h equilibration time was chosen. After equilibration, the samples were filtered through 0.45-μm membrane filters (Millipore) and then analyzed for metal concentration by atomic absorption spectroscopy (AAS) using Spectr AA240 FS (Varian). All experiments were carried out in triplicate, and the deviation from the mean value was less than 5 % in all cases.
Thermal behaviour of kraft lignin was determined by thermogravimetric analysis (TGA) using Q50 TGA instrument. TGA measurements of 4–25 mg samples were carried out at 10 °C/min heating rate in the range of 25–1000 °C under nitrogen atmosphere with a flow rate of 50 cm3/min.
The differential scanning calorimetry (DSC) analysis was made using DSC TA Instruments Q20 equipped with a cooling system up to a temperature −90 °C; 2–10 mg samples were placed in the air-tight aluminum crucible and heated at the rate 10 °C/min in the range 25–450 °C under nitrogen atmosphere with a flow rate of 50 cm3/min. Measurements were made in the N2 atmosphere. DSC measures the exothermic and endothermic responses of the samples, while the FTIR analysis observes their changes in chemical and physical composition.
The Fourier transform infrared spectra of kraft lignin-based sorbents before and after the sorption process were registered using a Cary 630 ATR-FTIR instrument (Agilent Technologies) by the attenuated total reflectance technique.
The X-ray phase analysis (XRD) was made by the powder method using an X-ray diffractometer Philips X’pert APD (Panalytical) with a goniometer PW 3020 and Cu lamp a well as a graphite monochromator. The analyses were made at an angle 5–65 2θ.
The pH of the point of zero charge pHzpc was measured using the pH drift method. The pH of the sorbent in the 0.01 M NaCl solution was adjusted between 2 and 12 by adding 0.01 M NaOH and 0.01 M HCl; 0.2 g of the adsorbent was added to 50 cm3 of the solution, and after 24 h, the final pH was measured.
All reagents were analytical grade and used without further purification. Demineralized water was used in preparation of all sample solutions (Hydrolab).
where q t is the adsorption amount of heavy metal ion at time t (mg/g), m is the weight of sorbent (g), V is the volume of solution (dm3) and c 0 and c t are the initial and at time t concentrations of heavy metal ion in solution, respectively (mg/dm3).
where c 0 and c t are the initial and at time t concentrations of heavy metal ion in solution, respectively (mg/dm3), V is the volume of the solution (cm3) and m is the amount (g) of the sorbent.
When t is equal to the equilibrium contact time, c t = c e, q t = q e, and the amount of heavy metal ions adsorbed at equilibrium, q e, is calculated using Eq. (1).
where q e is the amount of metal ion sorbed at equilibrium (also denoted as q 1 and q 2 for the PFO and PSO models, respectively) (mg/g), q t is the amount of metal ion sorbed at time t (mg/g) and k 1 and k 2 are the equilibrium rate constants (1/min).
where k i is the rate constant of diffusion (mg/g min−1/2) and C is the intercept.
where A (mg/g min) is the initial sorption rate and B (g/mg) is related to the extent of surface coverage and activation energy for chemisorption (desorption constant).
Based on the linear plots of q t versus ln t, the Elovich parameters can be calculated.
where c e is the equilibrium concentration of the metal ion (mg/dm3), q e is the adsorption capacity at equilibrium (mg/g), and the constants q 0 (mg/g) and K L are the characteristics of the Langmuir equation (dm3/mg) which can be determined from its linearized form (plots of c e /q e versus c e ).
where K F is the Freundlich adsorption capacity (mg/g) and 1/n is the Freundlich constant related to the surface heterogeneity. The above equation can be linearized to calculate the parameters K F and n.
Results and Discussion
Specific Surface Area
The measurement of specific surface area and average pore diameter was made using ASAP 2405 (Micrometrics Inc.). The specific surface area (S BET) was determined based on the Brunauer-Emmett-Teller (BET) multilayer adsorption. The total pore volume (V t ) was determined from the adsorbed nitrogen volume at p/p 0 = 0.99. The average pore diameter (D p ) is estimated from the pore volume, assuming a cylindrical pore geometry and using the equation 4V t /S BET. The mesopore distribution curve was obtained from the adsorption branch of the N2 isotherm by the BJH method. The micropore distribution is calculated from the gas adsorption using the Horvath-Kawazoe equation, with relative pressure (p/p 0) below 0.01.
However, it is well known that lignin is characterized by the high carbon content 65 %, hydrogen content 4.2 % and low nitrogen content 0.01 %. Also, the high sulfur content 2 % originated from both the Kraft or sulfate process, based on the action of NaOH and Na2S for separating cellulose from the other wood constituents, can be also a great attribute for the lignin application in heavy metal ions removal even in the case of its low surface area . In addition to the sulphur groups, the carbon containing carboxyl and hydroxyl groups of magnetic hybrid nanocomposite material can also be responsible for the sorption of M(II) ions. On the other hand, its sorptive properties can be improved by obtaining the hybrid material based on lignin and containing the iron oxide particles. There have been many methods of the synthesis of magnetite nanoparticles reported, such as reduction of hematite, co-precipitation of iron salts by ammonia solution, oxidation of iron gels, X-ray radiation, synthesis assisted by microwave radiation, and microemulsion . The common way of magnetite synthesis is the alkaline hydrolysis of iron(II) and iron(III) salts. The size of formed particles depends on the relative oversaturation of solution, and the formation of nanoparticles is expected at very low and very high concentration.
In solutions, magnetite can be in the cationic (FeOH2 +) and anionic (FeO−) forms under acidic and alkaline conditions, respectively. For them, there have been the two protonation constants reported [13, 14]: FeOH2 + ⇄ H+ + FeOH, pK a,1 = 5.3 and FeOH ⇄ H+ + FeO−, pK a,2 = 8.8. The sorption of heavy metal ions on HFO could be explained by the formation of both monodentate and bidendate complexes between the heavy metal cations and the negatively charged species of iron oxide nanoparticles [14–17] as well as the reaction between the cation metal ions and the functional groups of kraft lignin. Therefore, the most important factor is determination of pHzpc (point of zero charge) of the obtained composite.
It was found that pHpzc of kraft lignin (L) is equal to 6.39. However, after modification by magnetite (LM), it is equal to 7.45. It can be assumed that the negative charge of active sites on the surface of the magnetic hybrid nanocomposite material allows metal ions or eventually metal hydroxides to be adsorbed on the surface.
Effect of pH
The removal of Cu(II) using the magnetic hybrid nanocomposite material at different pH values in the range from 2 to 6 was studied using Cu(II) solutions at the concentration of 100 mg/dm3. It was found that the maximum removal (S%) was obtained at pH 6.0. With the increasing pH from 2 to 6, the residual concentration of Cu(II) decreases from 88 to 6.25 mg/dm3. Therefore, pH 6 was chosen as the more adequate value for the metal ion removal on the kraft lignin-based sorbents. For the metal ions, a similar variation of increase in S% with the increasing pH was observed. As the metal ions exist as cationic species at pH values less than 5.0, the removal takes place according to the mechanism of cation exchange. However, it should be mentioned that the most metal ions at pH higher than 6 can exist in the form of hydroxides. For example, for M(II) ions in the system, the dominant species is M(OH)2 and M(OH)+. At low pH particularly below pHzpc, the positively charged M2+ and M(OH)+ species present in the solution may exchange with H+ from –COOH or hydroxyl groups of carbon. It was found that the final pH of the solution is always less than the initial pH at pH range between 2.0 and pH of zero point charge.
It was found that after the sorption process, the broad and strong peak at 3344 cm−1 was due to the bound hydroxyl (–OH) groups. The peaks observed at 2933 cm−1 can be assigned to C–H stretching vibration, the CH2 stretching bands at 2919 and 2849 cm−1 are assigned to asymmetric and symmetric stretching of CH2 groups. The band at 1701 cm−1 of unmodified lignin can be attributed to the carbonyl group conjugated to the aromatic ring of lignin. The bands at 1590, 1455 and 1263 cm−1 are attributed to the C–O stretching of COOH groups, coupled OH in-plane deformation vibration and C(–O)–O stretching vibrations, respectively. The region between 1200 and 1000 cm−1 represented C–O stretching of alcohols and ethers. The bands at 1512 and 1117 cm−1 for unmodified lignin can be assigned to aromatic ring and C–O stretching of secondary alcohols, respectively . In addition, common functional groups in lignin include methoxyl, phenolic hydroxyl, aliphatic hydroxyl and other carbonyl groups [20, 21]. After the sorption of Cu(II) ions, a strong band appears at 1628 cm−1.
TGA and DSC Analysis
Effect of Shaking Time
Effect of Initial Concentration of Metal Ions
In Fig. 2a–f, plots of the sorption of Cu(II), Cd(II) and Pb(II) ions on the kraft lignin and the magnetic hybrid nanocomposite material at initial concentration 25, 50, 75 and 100 mg/dm3 at different time intervals were presented. The pH of the systems was maintained at 6.0.
Kinetic parameters of Cu(II) ions removal on kraft lignin for the initial concentrations 25, 50, 75 and 100 mg/dm3
Cu(II) ions concentration
R i,1 2
R i,3 2
R i,3 2
Kinetic parameters of Pb(II) ions removal on magnetic hybrid nanocomposite material for the initial concentrations 25, 50, 75 and 100 mg/dm3
Pb(II) ions concentration
R i,1 2
R i,3 2
R i,3 2
Moreover, the values of k 2 are greater than k 1 values and decrease with the increasing initial concentration. According to the Weber and Morris model, it is possible to establish whether the sorption is the intraparticle diffusion or not. It was found that the plots of q t versus t 1/2 do not pass through the origin. The multilinearity in the shape of the intraparticle diffusion plots has also been observed. The results indicate that the intraparticle diffusion rate decreased with the increase of the initial concentration from 25 to 100 mg/dm3. As for the Elovich model, it was found that it is more suitable for lower concentrations.
As for sorption parameters, the values of q o and K L were calculated from the intercept and slope of the linear plots of c e /q e versus c e . The monolayer capacities for the kraft lignin are as follows: 56.11 mg/g for Cu(II), 63.98 mg/g for Cd(II) and 101.33 mg/g for the Pb(III). Therefore, the determined affinity series of metal ions for lignin is as follows: Pb(II) > Cd(II) > Cu(II). The same tendency was observed in the case of magnetic hybrid nanocomposite.
The process efficiency is also affected by the presence of NO3 − and SO4 2− ions at the initial concentration 100 mg/dm3; practically 87 % of the Cu(II), Cd(II) and Pb(II) ions is removed.
Magnetite lignin-based composites are quite a new type of sorption materials despite the fact that the literature describes application of this type of materials as catalysts. Lignin has also been recently used for the production of activated carbons by thermal treatment in the presence of alkali metal hydroxides such as NaOH and KOH [22–24]. The sorbent preparation procedure involves phosphorylation of lignin with phosphoric acid in the presence of urea as described by Bykov and Ershov . The sorbent has a maximum possible phosphorus content and exhibits high sorption activity for Cu(II) and U(VI). The total exchange capacity was 0.86 mmol/g for Cu(II) ions and 0.23 mmol/g for UO2 2+. In the paper by Li et al. , biochars from lignin, cellulose and wood were prepared at 400 and 600 °C. Authors suggest that due to excellent sorption capacities, lignin biochars exhibited a sorption capacity >180,000 mg/kg comparable to both cellulose and wood biochars. They are good candidates for uptake of aromatic pollutants. A magnetic lignin composite was prepared and modified with diethylenetriamine and described in . Its sorptive properties were tested towards Cr(VI). Based on the Langmuir isotherm model, the calculated maximum Cr(VI) capacity q m was equal to 123 mg/g. Regeneration of the magnetic lignin composite was achieved by 0.4 M NaCl and 0.2 M NaOH solution, and more than 87 % efficiency of desorption was obtained after 5 cycles.
Moreover, in the paper by Mostashari et al. , the use of Fe3O4 magnetic nanoparticles as a recoverable adsorbent for lignin removal from aqueous solutions has been investigated. They tested several sorbents for magnetite particles regeneration. Desorption of lignin from Fe3O4 was studied using deionized water and different kinds of organic solvents, including acetonitrile, ethanol and methanol. According to the results, the desorption ability of acetonitrile was found to be the highest of all the solvents. The results showed that a desorption efficiency above 80 % can be achieved in a short time of 10 min and in a one-step elution using 5 mL of acetonitrile. The recovery for deionized water, EtOH and MeOH was lower than 40, 50 and 65 %, respectively. However, it should be mentioned that acetonitrile is quite expensive and not used in the wastewater treatment.
Based on the results obtained, both lignin and modified lignin can find use in the removal of heavy metal ions such as Cu(II), Cd(II) and Pb(II). The pH dependence of used sorbents may suggest that the metal ions are adsorbed according to ion exchange and chelating mechanisms. The main parameters affecting sorption are initial concentration of the solution, pH and phase contact time. Temperature has only a slight influence. With respect to effectiveness of removal of Cu(II), Cd(II) and Pb(II) on the obtained hybrid sorbents, it can be arranged as follows: modified lignin by nanoiron oxides > lignin without modification.
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.
- Harmita H, Karthikeyan KG, Pan XJ (2009) Copper and cadmium sorption onto kraft and organosolv lignins. Bioresource Technol 100:6183View ArticleGoogle Scholar
- Calvo-Flores FG, Dobado JA (2010) Lignin as renewable raw material. Chemsuschem 3:1227View ArticleGoogle Scholar
- Chung H, Washburn NR (2012) Chemistry of lignin-based materials. Green Mater 1:137View ArticleGoogle Scholar
- Sheha RR, Metwally E (2007) Equilibrium isotherm modeling of cesium adsorption onto magnetic materials. J Hazard Mater 143:354View ArticleGoogle Scholar
- Tsibranska I, Hristova E (2011) Comparison of different kinetic models for adsorption of heavy metals onto activated carbon from apricot stones. Bulgarian Chem Commun 43:370Google Scholar
- Ozacar M, Sengil IA (2005) A kinetic study of metal complex dye sorption onto pine sawdust. Process Biochem 40:565View ArticleGoogle Scholar
- Weber WC, Morris JC (1963) Kinetics of adsorption on carbon from solution, J. Sanit. Eng Div Proc Am Soc Civil Eng 89:31Google Scholar
- Goh KH, Lim TT, Dong Z (2008) Application of layered double hydroxides for removal of oxyanions: A review. Water Res 42:1343View ArticleGoogle Scholar
- Langmuir I (1916) The constitution and fundamental properties of solids and liquids. J Am Chem Soc 38:2221View ArticleGoogle Scholar
- Freundlich HFM (1906) Über die adsorption in lösungen. Z Phys Chem 57:385Google Scholar
- Fierro V, Torné-Fernández a V, Celzard A (2006) Kraft lignin as a precursor for microporous activated carbons prepared by impregnation with ortho-phosphoric acid: Synthesis and textural characterization. Microporous Mesoporous Mater 92:243View ArticleGoogle Scholar
- Tombácz E, Majzik A, Horvát ZS, Illés E (2006) Magnetite in aqueous medium: coating its surface and surface coated with it. Rom Reports Phys 58:281Google Scholar
- Chou S, Huang C, Huang Y (2001) Heterogeneous and homogeneous catalytic oxidation by supported g-FeOOH in a fluidized-bed reactor: kinetic approach. Environ Sci Technol 35:1247View ArticleGoogle Scholar
- Kołodyńska D, Kowalczyk M, Hubicki Z, Shvets V, Pavlovich BI (2015) Effect of accompaning ions and ethylenediaminedisuccinic acid on heavy metals sorption using hybride materials Lewatit FO 36 and Purolite Arsen Xnp. Chem Eng J 276:376View ArticleGoogle Scholar
- Lee SM, Laldawngliana C, Tiwari D (2012) Iron oxide nano-particles-immobilized-sand material in the treatment of Cu(II), Cd(II) and Pb(II) contaminated waste waters. Chem Eng J 195–196:103View ArticleGoogle Scholar
- Xu P, Zeng GM, Huang DL, Feng CL, Hu S, Zhao MH, Lai C, Wei Z, Huang C, Xie GX, Liu ZF (2012) Use of iron oxide nanomaterials in wastewater treatment: A review. Sci Total Environ 424:1View ArticleGoogle Scholar
- Zhang YB, Li P, Zhou YL, Pan GH, Li GH, Xu B, Jiang T (2012) Adsorption of lignite humic acid onto magnetite particle surface. J Central South Univ 19:1967View ArticleGoogle Scholar
- Boeriu CG, Bravo D, Gosselink RJA, van Dam JEG (2004) Characterisation of structure-dependent functional properties of lignin with infrared spectroscopy. Ind Crop Product 20:205View ArticleGoogle Scholar
- Smith B (1999) Infrared spectral interpretation. A Systematic Approach. CRC Press, Boca RatonGoogle Scholar
- Zuman P, Ainso S, Paden C, Pethic BA (1988) Sorptions on lignin, wood and celluloses. I. Bile salts. Colloid Surface 33:121View ArticleGoogle Scholar
- Wieber J, Kulik F, Pethic BA, Zuman P (1988) Sorptions on lignin, wood and celluloses. III. copper(II) and zine(II) ions. P Colloid Surface 33:141View ArticleGoogle Scholar
- Zhai Y, Dou Y, Zhao D, Fulvio PF, Mayes RT, Dai S (2011) Carbon materials for chemical capacitive energy storage. Adv Mater 23:4828View ArticleGoogle Scholar
- Zhang LL, Zhao XS (2009) Carbon-based materials as supercapacitor electrodes. Chem Soc Rev 38:2520View ArticleGoogle Scholar
- Fierro V, Torné-Fernández V, Celzard A (2007) Methodical study of the chemical activation of Kraft lignin with KOH and NaOH. Microporous Mesoporous Mater 101:419View ArticleGoogle Scholar
- Bykov GL, Ershov BG, Russ J (2010) A sorbent based on phosphorylated lignin. App Chem 83:316Google Scholar
- Li J, Li Y, Wu Y, Zheng M (2014) A comparison of biochars from lignin, cellulose and wood as the sorbent to an aromatic pollutant. J Hazard Mater 280:450View ArticleGoogle Scholar
- Song Z, Li W, Liu W, Yang Y, Wang N, Wang H, Gao H (2015) Novel magnetic lignin composite sorbent for chromium(VI) adsorption. RSC Adv 5:13028View ArticleGoogle Scholar
- Mostashari SM, Shariati S, Manoochehri M (2013) Lignin removal from aqueous solutions using Fe3O4 magnetic nanoparticles as recoverable adsorbent. Cellul Chem Technol 47:727Google Scholar