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ChemEngineering 2019, 3(1), 22; https://doi.org/10.3390/chemengineering3010022
Reactivity and Heavy Metal Removal Capacity of Calcium Alginate Beads Loaded with Ca–Al Layered Double Hydroxides
INFIQC-CONICET, Departamento de Fisicoquímica, Facultad de Ciencias Químicas, Universidad Nacional de Córdoba, Ciudad Universitaria, 5000 Córdoba, Argentina
Author to whom correspondence should be addressed.
Received: 13 January 2019 / Accepted: 27 February 2019 / Published: 1 March 2019
Layered double hydroxides (LDHs) present multiple applications due to their versatility and reactivity. Thus, Ca–Al LDHs with Friedel’s salt structure (HC) have been proposed as heavy metal scavengers due to their buffering capacity at basic pHs. Nevertheless, the control of the reactivity of LDHs such as HC is necessary to optimize their applications. Here, the reactivity of an HC prepared by a coprecipitation method was modified by its inclusion in calcium alginate (CaAlg) beads prepared by ionic gelation. The obtained beads (CaAlg/HC) showed good dispersion of the HC particles in the alginate matrix and were used to test the acid base reactivity and heavy metal uptake capacity compared with pure CaAlg beads and HC powder separately. The pH buffering capacity of CaAlg beads was enriched by the inclusion of HC that, in turn, was modulated in its reactivity. Thus, the HC dissolution times changed from mere seconds for the powder to tens of minutes when enclosed in the beads in a kinetic profile determined by the diffusive step. On the other hand, Cu2+ uptake capacity of CaAlg/HC beads combined the Cu(OH)2 precipitation capacity of HC with the complexation capacity of alginate, reaching good affinity and capacity for the obtained beads. Nevertheless, the precipitation of the hydroxide was produced outside the bead, which would induce the addition of an additional separation step to produce an acceptable Cu2+ elimination.
Keywords:hydrocalumite; pH buffering; chelation; precipitation; ionic gelation
The combination of natural polymers and inorganic materials has drawn considerable attention due to the unique properties of the composite materials obtained, which makes them attractive in applications as packaging films, scaffolds, filters, etc. Thus, the combination of layered double hydroxides (LDHs) with hydrogels is a promising tool to enhance the properties of both components of the obtained composite, finding applications in the environmental and pharmaceutical areas, among others [1,2,3]. Among them, inclusion of LDHs in alginate beads has been extensively studied for environmental remediation, allowing an easy separation from the aquatic medium while providing a modulation of this solid reactivity .
Alginic acid is a natural, linear polymer that can be described as homopolymeric blocks formed of D-mannuronate and L-guluronate units. It portrays a large content of carboxylic groups, mainly deprotonated at neutral pH, and the interaction with Ca2+ ions leads to the crosslinking of the alginate chains and the formation of a water-entrapping calcium alginate network. This process is used to form calcium alginate beads by the simple dropping of a sodium alginate solution in a CaCl2 solution [5,6]. The presence of carboxylate groups also allows the uptake of heavy metal ions, such as Cu2+, Pb2+, or Cd2+, incorporated by chelation and ion exchange mechanisms [1,7,8].
Layered double hydroxides, on the other hand, have also demonstrated their capacity for heavy metal removal [9,10,11]. In some cases, polydentate ligands have been incorporated to provide heavy metal chelation capabilities to LDHs [12,13]. In others, the acid–base reactivity of LDHs , whose hydroxylated layers dissolve at a pH determined mainly by its composition, is used to produce the precipitation of the heavy metal hydroxides, either as a part of an LDH phase or not . Among them, Ca–Al LDHs present the highest removal capacity and efficiency [9,16,17]. Ca–Al LDHs, as a member of the Friedel’s salt group, present a structure similar to that of other LDHs, but their divalent cations are enclosed in a sevenfold coordination, the seventh position being occupied by a water molecule [9,16]. The most representative member of these Ca–Al LDHs with Friedel’s salt structure is the mineral hydrocalumite (Ca2Al(OH)6Cl·2H2O). These solids have not only been used for the removal of heavy metals, but also for the elimination of other pollutants, such as fluoride and arsenic [18,19].
The LDH application in heavy metal removal presents a drawback as LDHs are not easily separated from the polluted media due to their particle size . In the particular case of hydrocalumite, its extreme reactivity produces its complete dissolution in mildly acidic media, leading to its deactivation . A promising tool to overcome all these problems is the inclusion of LDHs in hydrogel beads of calcium alginate, which would allow an easy separation  while providing a protective environment to modulate the reactivity of the solids. Although the inclusion of LDHs in alginate beads for heavy metal removal applications has already been described [1,3], the effect on the reactivity of LDHs and the inclusion of Ca–Al LDHs has still not been explored.
In this work, a Ca–Al LDH with a Friedel’s salt structure (HC) was synthesized and enclosed in calcium alginate (CaAlg) hydrogel beads. After their structural characterization, the acid–base reactivity of the obtained beads was determined in comparison with that of pure CaAlg beads and pure HC. Finally, the uptake capacity of the beads was explored using Cu2+ ion as a probe and the results obtained were compared to those of CaAlg and HC.
2. Materials and Methods
CaCl2, AlCl3·6H2O and Cu(NO3)·3H2O (PA grade, Anedra®), NaOH granules and 37% w/w HCl solution (PA grade, Cicarelli®), and sodium alginate (Montreal, Argentina) were used. All solutions were prepared with purified water (18MΩ MilliQ, Millipore System) and all experiments, unless otherwise stated, were performed at room temperature.
2.1. Synthesis of Ca–Al Layered Double Hydroxides (HC)
A chloride intercalated Ca–Al layered double hydroxide with a Friedel’s salt structure was synthesized as follows. A 0.2 mol·L−1 CaCl2, 0.1 mol·L−1 AlCl3·6H2O solution (200 mL) was quickly added to a 200 mL solution containing 0.02 mol NaCl and 0.12 mol NaOH under vigorous agitation provided by a Ultraturrax T18 BASIC agitator at 25000 rpm. After the addition, the obtained solid (HC) was separated by centrifugation, washed three times with water, and finally dried at 60 °C.
2.2. Calcium Alginate Beads (CaAlg and CaAlg/HC) Preparation
A stock 2.50% (w/w) sodium alginate (NaAlg) solution was prepared under agitation and heating. Once the polymer was completely dissolved, pure alginate beads (AlgCa) were prepared by dropping a solution of 1.25% NaAlg, using a Pasteur pipette, in a 0.02 mol·L−1 CaCl2 solution under gentle magnetic stirring. The obtained beads were equilibrated for 1 hour and then separated and washed. To obtain the HC-containing calcium alginate beads (AlgCa/HC), 10 mL of the 2.50% NaAlg stock solution was added to 10 mL of a 10 g·L−1 HC dispersion under vigorous stirring with the Ultraturrax T25 apparatus described above. This dispersion was immediately dropped into the CaCl2 solution and the formed beads were equilibrated for 1 hour and then separated, washed with water, and stored. A portion of both CaAlg and CaAlg/HC beads were dried at 60 °C to perform the structural characterization.
2.3. Structural Characterization
Powder X-ray diffraction (PXRD) patterns were acquired at room temperature on an X-ray diffractometer (Phillips X’pert Pro instrument) equipped with a Pixcell 1D detector using Cu Kα radiation (λ = 1.5418 Å, tube operated at 40 kV, 40 mA). Data were collected over 2θ values from 5 to 70° in continuous scan mode. Fourier transform infrared (FT–IR) spectra were measured in a Bruker IFS28 instrument using KBr discs (1:100 sample to KBr ratio). The samples were measured from 4000 to 400 cm−1 at 4 cm−1 resolution and at an accumulation of 64 scans. Thermogravimetric and differential thermal analyses TGA/DTA were performed in a Shimadzu DTG 60 instrument from room temperature to 800 °C at 10 °C/min slope under flowing air (75 mL/min). Scanning electron microscopy (SEM) images were obtained using an FE–SEM Sigma instrument. For HC powder, 0.05 mL of 0.1 g·L−1 dispersion of the sample was placed on the holder, which was afterwards dried at 50 °C and covered with an Au layer. In the case of the beads, they were cut in sections, then were placed on the holder and covered directly with an Au layer without drying.
2.4. Proton Uptake Kinetics
Next, 100 mL solutions with increasing HCl concentration ([HCl] = 0.1–1 mmol·L−1) were prepared. Once the pH was equilibrated, 10 beads of either AlgCa or AlgCa/HC were added while the pH was measured at 10 s intervals up to 150 min using a Titrando 905 automatic titrator (Metrohm) controlled by Tiamo software and coupled to a Metrohm 9.0262.100 combined pH electrode. These experiments were also performed adding 1 mL of a 2.5 g·L−1 HC dispersion instead of the beads.
The pH values were converted into proton uptake (ΓH) values, calculated as:where pH0 and pH are the pH of the solution at t = 0, and at a given time t, V is the overall volume of the solution (the volume of the beads was neglected), while nb and m are the number of beads and the HC mass, respectively. The obtained ΓH vs t curves were fitted with the zero order and the Higuchi models [21,22]. The first model considers that the determining step of a given process is a reaction at the surface of a particle, while for the Higuchi model, it is the diffusion of reactive or products.where ΓH,0 is the origin of coordinates and kZ and kD are the kinetic constants of the corresponding models.
For CaAlg and CaAlg/HC beads: ΓH = (10−pH0–10pH)·V·nb−1
For HC: ΓH = (10−pH0–10−pH)·V·m−1
Zero order model: ΓH = ΓH,0 + kZ·t
Higuchi model: ΓH = ΓH,0 + kD·t1/2
2.5. Cu2+ Removal Tests
Cu2+ removal kinetics were studied as a function of Cu2+ concentration ([Cu2+]). Ten beads of either CaAlg or CaAlg/HC were added to 100 mL solutions with increasing Cu2+ concentrations ([Cu]0 = 0.4–17.6 ppm) while the pH was continuously measured as previously described. After 150 min, the solutions, together with the beads, were placed in sealed flasks and submitted to orbital agitation to complete 24 hours equilibration. A portion of the solution was separated and directly diluted 1:10 in 0.1 mol·L−1 HNO3. In the case of CaAlg/HC beads, turbidity was observed in the samples and, consequently, besides the portion directly diluted in HNO3, an additional portion was taken, filtered, and finally diluted 1:10 in HNO3. Finally, in the case of HC powder, 1 mL of a 2.5 g·L−1 was added to Cu2+ solutions of the same concentrations and, after equilibration, a portion of the obtained dispersions were filtered and diluted as previously described. The Cu2+ uptake (ΓCu) for beads and HC particles was calculated, respectively, aswhere [Cu]0 and [Cu]eq are the Cu2+ concentration at t = 0 and at equilibrium, respectively, mAlg and mHC the Alg and HC mass, respectively, while V is the solution volume.
ΓCu = ([Cu]0–[Cu]eq)·V·mAlg−1
ΓCu = ([Cu]0–[Cu]eq)·V·mHC−1
The Langmuir model was used to describe the curves and perform an estimation of the uptake capacity and affinity of the beads for Cu2+. The linearized form of the equation described for the model can be written as:where and are the uptake capacity at a considered concentration and the maximum uptake capacity, respectively, and (ppm−1) was the affinity constant. The model assumes that the uptake is produced as adsorption at the surface of a solid where a monolayer of the adsorbate is incorporated. Additionally, it is assumed that all the binding sites are of the same affinity for the adsorbate. This model, together with the Freundlich model, is commonly used to give an interpretation of the uptake behavior of alginate beads and LDHs against heavy metals [16,17,23,24]. Nevertheless, due to poor correspondence between the system characteristics and the basic assumptions of the Langmuir model, here it was used to allow comparison between CaAlg and CaAlg/HC beads. For the same reasons, the fitting with Freundlich model was avoided.
3.1. Structural and Morphological Characterization of CaAlg and CaAlg/HC
The above described bead preparation methods allowed the obtaining of pure CaAlg and Ca–Al LDH containing (CaAlg/HC) beads with regular sizes (Supporting Information, Figure S1): the former ones were more transparent than the latter, which showed a white shade compared to the yellowish-brown CaAlg beads. The CaAlg/HC beads were prepared right after the NaAlg/HC mixture was prepared, as a viscosity increase was observed with time. This effect was related to the instability of Ca–Al LDHs , enhanced by the high affinity of NaAlg for Ca2+ ions. Consequently, Ca2+ ions were released in the medium, which produced the ionic crosslinking of Alg chains and, therefore, its gelation.
The PXRD patterns of the dried beads and the HC sample are shown in Figure 1. CaAlg beads (Figure 1b) showed only small peaks corresponding to an NaCl phase (Joint Committee on Powder Diffraction Standards, JCPDS file 05-0628) and even the wide bands obtained for NaAlg (Figure 1a) were absent. The PXRD pattern of the HC sample (Figure 1c) showed that a single phase of a chloride intercalated LDH with a Friedel’s salt structure (JCPDS database, file 31-0105, with a rhombohedral unit cell with parameters c = 46.8 Å and a = 4.98 Å) was obtained. Contrarily to most LDH phases, the sample presented a high crystallinity, as reflected by the large number of thin, intense peaks obtained in the pattern. Upon their inclusion in CaAlg/HC beads (Figure 1d) the peaks corresponding to the HC phase diminished in intensity and, more importantly, presented a widening of the peaks. This result was indicative of an ordering loss upon incorporation with the beads and a strong interaction between the HC layers and the alginate chains.
The FT–IR spectra (Figure 2) confirmed the inclusion of HC in the CaAlg beads. Both NaAlg and CaAlg showed similar bands, such as the wide band obtained at 3416–3447 cm−1, corresponding to νOH of hydroxyl groups mannuronate and guluronate units as well as entrapped water. Bands obtained at 1610–1613 and 1419–1427 cm−1 were attributed to νCOO,sym and νCOO,asym, respectively, while the bands in the 1034–1100 cm−1 bands corresponded to νCOC,sym and νCOC,asym modes of the polysaccharide rings . Similarly, the HC sample showed typical bands of a Ca–Al LDHs with a Friedel’s salt structure, including bands at 3636 cm−1 corresponding to νOH of water molecules, 3475 cm−1 (νOH of hydroxyl groups of the layers), and 1610 cm−1 (bending νHOH of water), while the bands at wavenumber values below 1100 cm−1 were attributed to νMO and νMOM lattice modes of the layers [17,26]. Finally, the wide band at 1446 cm−1 was attributed to carbonate ions, incorporated as an impurity to the solid due to the basic pH conditions during the synthesis procedure . Finally, the FT–IR spectra of CaAlg/HC beads showed bands of both alginate (νCOO,sym and νCOO,asym as well as νCOC,sym and νCOC,asym modes at 1613, 1421, 1089, and 1033 cm−1, respectively) and HC (νOH at 3648 and 3489 cm−1, νMO and νMOM lattice modes below 1100 cm−1).
The TG/DTA curves (Figure 3) completed the study of CaAlg–HC interactions and allowed establishment of estimations on the chemical composition of the beads. The TGA curve of CaAlg beads showed a first weight loss up to a residual mass (%M) of 87.4%, associated with a wide endothermic effect in the DTA curve, centered at around 80 °C, which was attributed to dehydration of the CaAlg beads. Two main weight losses associated with exothermic effects centered at 280 and 650 °C, attributed to the oxidation of the alginate chains, were registered at larger T values. The % M at 800 °C was 22.9%, which was consistent with a (C6H8O6)2Ca·3.1 H2O formula, if CaO was considered the main residue of the thermal decomposition of the beads (the water content was estimated based on the dehydration mass loss).
On the other hand, HC showed a dehydration mass loss up to % M = 87.3%, associated with an endothermic peak centered at 130°. The mass loss was produced in a narrower T range than for CaAlg, as corresponds to the larger crystallinity of HC. The second weight loss was attributed to the dehydroxylation and interlayer anion loss , % M reaching 65.9% at 800 °C. The mass losses obtained were fitted well with the presence of a phase of a Ca2Al(OH)6Cl·2H2O like that proposed in the JCPDS file 31-0105, considering mayemite (Ca12Al14O33) and CaO as the main residues at 800 ℃ .
Finally, CaAlg/HC beads exhibited a dehydration step whose shape, both in the TGA and DTA curves, seemed to combine those of HC and CaAlg. The % M after this step was smaller (81.9%) than for HC and CaAlg, which indicated that HC inclusion in the beads produced a larger hydration of the polymer and/or the particles. At larger T values, the endothermic peak corresponding to the dihydroxylation and interlayer anion loss observed for HC was maintained for CaAlg/HC. However, the exothermic effects corresponding to the oxidation of the alginate chains observed for the CaAlg beads vanished and only a wide and weak endothermic band was observed in the 450–700 °C range. The % M value at 800 °C was 42.1%, intermediate between those of HC and CaAlg, which was concordant with the 1.25:1 NaAlg to HC ratio of the dispersion used for bead formation.
The SEM images of HC (Figure 4a) portrayed the typical lamellar morphology of the particles of Friedel’s salts  and a wide particle size distribution, although the particles mostly showed irregular borders, resembling the hexagonal symmetry of the unit cell. An EDS chemical analysis was performed for this sample, obtaining a Ca/Al ratio of 2.0 ± 0.1, quite concordant with the chemical composition of the Ca–Al LDH registered in JCPDS file 31-0105. On the other hand, the cross-sections of CaAlg beads showed only waves and wrinkles but neither particles or porosity were present [1,29]. Finally, the sections of the CaAlg/HC beads showed the presence of particles with a lamellar morphology, like those obtained for HC and, consequently, the cross-section of the beads presented a rougher surface than pure CaAlg beads.
3.2. Proton Uptake Kinetics
The pH buffering capacity of CaAlg and CaAlg/HC (Figure 5) were studied as a base to explain their heavy metal uptake capacity. pH plays a major role in heavy metal uptake by alginate beads, as the main uptake mechanism is the coordinate binding by carboxylate groups, whose deprotonation ratio is determined by the pH of the medium . Additionally, the removal capacity of HC is based on its acid base buffering capacity, which leads to an increase in the pH of the polluted medium, and the precipitation of the corresponding heavy metal hydroxides [9,17]. The pH vs t curves indicated that CaAlg beads (Figure 5a) presented buffering capacity at pH values lower than 5, which was in good accord with carboxylate as the main proton uptake agent. The final pH decreased with increasing [HCl] in all cases, which indicated that the carboxylate groups of alginate portrayed a wide range of pKa values. The AlgCa/HC beads (Figure 5c) presented larger final pH values than AlgCa for every [HCl], which was related to the acid base reactivity of HC. Previous works showed that Ca–Al LDHs are dissolved at pH values lower than 11 , and the dissolution kinetics of HC powder, performed in the same conditions as the beads (Supporting Information, Figure S2), led to final pH values of up to 9.5 for the lowest [HCl] value, which were reached in less than one minute. Then, HC inclusion in CaAlg beads allowed control of the proton release rate while increasing the buffering capacity of alginate.
The proton uptake (ΓH) vs t curves of both CaAlg and CaAlg/HC beads (Figure 5b, d, respectively) showed a proton uptake capacity at the end of the measured range (ΓH, 150) that increased with increasing [HCl]. ΓH, 150 values were similar for both at low [HCl] values but, at [HCl] larger than 0.5 mmol·L−1, ΓH, 150 values were larger for CaAlg/HC than for CaAlg. Proton uptake was exclusively due to protonation of carboxylate groups in the case of CaAlg beads. On the other hand, the proton uptake by CaAlg/HC beads at the lowest [HCl] values was exclusively due to HC dissolution, as the pH values in the experiment were considerably higher than the pKa values reported for this biopolymer . As [HCl] values increased and final pH values decreased, the contribution of carboxylate protonation processes increased. Consequently, HC dissolution and carboxylate protonation were additive at the two highest [HCl] values and the proton uptake by CaAlg/HC beads was higher than for CaAlg beads. The ΓH vs t curves were fitted with different kinetic models, including zero order and Higuchi models (see Section 2.4), but the best fits were obtained for the latter one in all cases. Consequently, only the fitting parameters of this model are included in Table 1, while the fitting parameters of the zero order model are included as supporting information (Table S1). The good fit obtained for this model indicated that the proton uptake rate was mainly controlled by the diffusion of protons or hydroxyls across the bead. The origin of coordinate (Γ0) values were near zero and even slightly negative, which indicated that there was no initial proton uptake due to fast processes that were not included in the main dissolution mechanism, contrary to that observed for LDHs in dispersion . The kD values were quite similar for AlgCa and CaAlg/HC beads at the same [HCl] value, which indicated that the kinetic behavior was mainly controlled by the CaAlg network. Both beads showed increasing kD values with increasing [HCl], which is a typical dependence for increasing concentration of one of the reactants in diffusion controlled reactions [21,31]. The only exception for these trends was the fitting of CaAlg beads at the lowest concentration, which showed a larger kD value than that of CaAlg. This effect was attributed to the high reactivity of HC, which was, as previously described, mainly responsible for the proton uptake at this [HCl].
3.3. Cu2+ Removal Tests
The Cu2+ uptake capacity (ΓCu) of the beads was evaluated as a function of the Cu2+ concentration at equilibrium ([Cu]eq, Figure 6). The pH kinetics of the solutions were also followed to obtain further information about the uptake mechanism. Both CaAlg beads and HC powder presented Cu2+ uptake capacity by themselves (Figure 6A), but the former presented a lower affinity for Cu2+ ions than the latter. Nevertheless, it was enough to produce a removal effectivity (% R = [Cu]eq/[Cu]ini) near 80% at [Cu]ini values around 3 ppm, which led to [Cu]eq values below those recommended by the US Environmental Protection Agency for tap water . The fitting of the curves using the Langmuir equation led to ΓCu, max and KL values similar (Table 2) to those found by other authors [1,7,8]. Heavy metal incorporation by CaAlg beads was produced by interaction with carboxylate and hydroxyl groups of the polymer chains, preferably to carboxylate groups of the mannuronate blocks, which do not participate in the binding of Ca2+ ions . The pH of the medium was maintained below 6.2 in all cases, which indicated that CaAlg beads were not producing a significant formation of Cu hydroxides.
On the other hand, HC showed a high capacity and affinity for Cu2+, which reduced the concentration of these anions below the detection limit until the plateau was abruptly reached. This high affinity allowed a % R = 99% at [Cu]ini = 3 ppm. This high affinity was related to the large buffering capacity of HC at high pH values, as reflected in the pH vs t curves (Figure 5c. Inset). These curves showed final pH values above 8, reached in less than 30 seconds, for points placed in the section where the [Cu]eq was nearly zero (points i–iii). Once the buffering capacity of HC was exhausted (point iv), the pH of the medium was equilibrated at values around 6 and the curve abruptly reached a plateau. These high ΓCu,max and KL values were similar to those obtained previously for Cu2+ ions removal by hydrocalumite [9,17]. This maximum capacity was consistent with the total substitution of Ca2+ ions by Cu2+ ions, obtaining a Cu–Al LDH as final product .
CaAlg/HC beads showed advantages and disadvantages compared to their separate components. The pH curves for these beads showed a great pH increase, which was slowed down by the inclusion in the alginate beads. This pH increase indicated that precipitation of Cu(OH)2 was produced. Regrettably, this precipitation was produced outside the CaAlg/HC beads, as deduced from the turbidity of the supernatants, which was detected visually. In order to confirm and quantify Cu(OH)2 precipitation outside the beads, [Cu]eq were determined before and after filtration of the equilibrated medium. The non-filtered medium contained the formed Cu(OH)2, which was dissolved after dilution on 0.1 mol·L−1, while with the filtered medium, only the remaining free Cu2+ ions were included.
The curve before filtration (filled squares) showed that negligible uptake was produced by the beads at low [Cu]eq, while the curve after filtration showed a drastic ΓCu increase at [Cu]eq near zero, similar to that found for HC. Cu2+ ions were then completely removed from the medium and precipitated as Cu(OH)2 outside the beads due to the HC buffering capacity. In good accord, the curves of points a) and b) showed equilibrium pH values above 7, although they were reached in longer times than for HC. At [Cu]eq larger than 3 ppm, the curves obtained for non-filtrated medium showed a significant ΓCu increase. This increase was parallel to a decreasing slope of the curves obtained after filtration, which, together with the diminution of the equilibrium pH below 6.5, indicated that the capacity of HC to buffer the pH of the medium was exhausted. Consequently, the mechanism of Cu2+ uptake by metal hydroxide precipitation was complemented by the metal ion complexation by carboxylate groups of alginate. This mechanism seemed not to be exhausted in the measurement range, but the fitting of the curve obtained after filtration indicated that the uptake capacity of CaAlg/HC beads was like that of CaAlg beads while the affinity increased. Nevertheless, the precipitation of Cu(OH)2 was a clear disadvantage for the usage of HC containing CaAlg beads as Cu2+ scavengers.
Calcium alginate (CaAlg) beads containing particles of a Ca–Al layered double hydroxide with hydrocalumite structures (HCs) were prepared. The obtained beads (CaAlg/HC) showed good dispersion of the HC particles, which interacted with the carboxylate groups of the alginate chains. Pure CaAlg beads showed proton uptake capacity due to the protonation capacity of carboxylate groups of alginate, which was complemented, in the case of CaAlg/HC beads, by the buffering capacity of HC particles. Conversely, the inclusion of these particles in the beads allowed the control of their reactivity, the equilibration times increasing from a few seconds for the HC powder to more than 60 min for the CaAlg/HC beads. These beads showed a diffusive proton uptake kinetics either for pure CaAlg or HC containing beads. Both CaAlg and HC presented Cu2+ uptake capacity by themselves, but their combination did not merge the easy separation of the former with the high affinity of the latter. Despite the fact that the buffering capacity of the HC included in CaAlg/HC beads produced an effective precipitation of Cu(OH)2 and CaAlg provided additional Cu2+ capacity, the heavy metal hydroxide was formed outside the beads, which hindered its separation. Nevertheless, inclusion of LDHs in CaAlg beads stands as an easy strategy to modify the reactivity of LDHs in environmental and pharmaceutical applications, among others.
The following are available online at https://www.mdpi.com/2305-7084/3/1/22/s1: Figure S1 Images of the calcium alginate beads, either pure or containing Ca–Al; Figure S2, pH vs t curves and proton uptake kinetics for HC; Table S1, Fitting constants of proton uptake kinetics according to the zero order model.
R.R. and A.B. conceived and designed the experiments; A.B. performed the experiments; R.R. and A.B. analyzed the data; R.R. contributed reagents/materials/analysis tools; R.R. wrote the paper.
This research was funded by SeCyT-UNC, project number 05/C585; FON-CyT, project numbers 12/0634; and CONICET, PIP 11220120100575.
SEM images were recorded at the Laboratorio de Microscopía Electrónica y Análisis porRayos X (LAMARX).
Conflicts of Interest
The authors declare no conflict of interest.
- Sun, J.; Chen, Y.; Yu, H.; Yan, L.; Du, B.; Pei, Z. Removal of Cu2+, Cd2+ and Pb2+ from aqueous solutions by magnetic alginate microsphere based on Fe3O4/MgAl-layered double hydroxide. J. Colloid Interface Sci. 2018, 532, 474–484. [Google Scholar] [CrossRef] [PubMed]
- Alcantara, A.C.S.; Aranda, P.; Darder, M.; Ruiz-Hitzky, E. Bionanocomposites based on alginate-zein/layered double hydroxide materials as drug delivery systems. J. Mater. Chem. 2010, 20, 9495–9504. [Google Scholar] [CrossRef]
- El Rouby, W.M.A. Efficient water decontamination using layered double hydroxide beads nanocomposites. Environ. Sci. Pollut. Res. 2018. Available online: https://doi.org/10.1007/s11356-018-3257-7 (accessed on 27 February 2019). [Google Scholar]
- Kim Phuong, N.T. Entrapment of Mg–Al layered double hydroxide into alginate/polyvinyl alcohol beads for water remediation. J. Environ. Chem. Eng. 2014, 2, 1082–1087. [Google Scholar] [CrossRef]
- Lee, K.Y.; Mooney, D.J. Alginate: Properties and biomedical applications. Prog. Polym. Sci. 2012, 37, 106–126. [Google Scholar] [CrossRef] [PubMed][Green Version]
- Rocher, V.; Siaugue, J.-M.; Cabuil, V.; Bee, A. Removal of organic dyes by magnetic alginate beads. Water Res. 2008, 42, 1290–1298. [Google Scholar] [CrossRef] [PubMed]
- Benettayeb, A.; Guibal, E.; Morsli, A.; Kessas, R. Chemical modification of alginate for enhanced sorption of Cd(II), Cu(II) and Pb(II). Chem. Eng. J. 2017, 316, 704–714. [Google Scholar] [CrossRef]
- Wang, F.; Lu, X.; Li, X.Y. Selective removals of heavy metals (Pb2+, Cu2+, and Cd2+) from wastewater by gelation with alginate for effective metal recovery. J. Hazard. Mater. 2016, 308, 75–83. [Google Scholar] [CrossRef] [PubMed]
- Rojas, R. Copper, lead and cadmium removal by Ca Al layered double hydroxides. Appl. Clay Sci. 2014, 87, 254–259. [Google Scholar] [CrossRef]
- Rojas, R. Effect of particle size on copper removal by layered double hydroxides. Chem. Eng. J. 2016, 303, 331–337. [Google Scholar] [CrossRef]
- Pérez, M.R.; Pavlovic, I.; Barriga, C.; Cornejo, J.; Hermosín, M.C.; Ulibarri, M.A. Uptake of Cu2+, Cd2+ and Pb2+ on Zn–Al layered double hydroxide intercalated with edta. Appl. Clay Sci. 2006, 32, 245–251. [Google Scholar] [CrossRef]
- Pavlovic, I.; Pérez, M.; Barriga, C.; Ulibarri, M.A. Adsorption of Cu2+, Cd2+ and Pb2+ ions by layered double hydroxides intercalated with the chelating agents diethylenetriaminepentaacetate and meso-2,3-dimercaptosuccinate. Appl. Clay Sci. 2009, 43, 125–129. [Google Scholar] [CrossRef]
- Kameda, T.; Hoshi, K.; Yoshioka, T. Uptake of Sc3+ and La3+ from aqueous solution using ethylenediaminetetraacetate-intercalated Cu–Al layered double hydroxide reconstructed from Cu–Al oxide. Solid State Sci. 2011, 13, 366–371. [Google Scholar] [CrossRef]
- Parello, M.L.; Rojas, R.; Giacomelli, C.E. Dissolution kinetics and mechanism of Mg-Al layered double hydroxides: a simple approach to describe drug release in acid media. J. Colloid Interf. Sci. 2010, 351, 134–139. [Google Scholar] [CrossRef] [PubMed]
- Liang, X.; Zang, Y.; Xu, Y.; Tan, X.; Hou, W.; Wang, L.; Sun, Y. Sorption of metal cations on layered double hydroxides. Colloids Surfaces A Physicochem. Eng. Asp. 2013, 433, 122–131. [Google Scholar] [CrossRef]
- Zhang, J.; Zhao, H.; Cao, H.; Li, H.; Li, Z. Removal of Cd2+ from water by Friedel’s salt (FS: 3CaO·A12O3·CaCl2·10H2O): Sorption characteristics and mechanisms. J. Environ. Sci. (China) 2013, 25, 1719–1725. [Google Scholar] [CrossRef]
- Milagres, J.L.; Bellato, C.R.; Vieira, R.S.; Ferreira, S.O.; Reis, C. Preparation and evaluation of the Ca-Al layered double hydroxide for removal of copper(II), nickel(II), zinc(II), chromium(VI) and phosphate from aqueous solutions. J. Environ. Chem. Eng. 2017, 5, 5469–5480. [Google Scholar] [CrossRef]
- Guo, Q.; Tian, J. Removal of fluoride and arsenate from aqueous solution by hydrocalumite via precipitation and anion exchange. Chem. Eng. J. 2013, 231, 121–131. [Google Scholar] [CrossRef]
- Li, D.; Guo, X.; Tian, Q.; Xu, R.; Xu, Z.; Zhang, J. Dearsenization of caustic solution by synthetic hydrocalumite. Hydrometallurgy 2016, 161, 1–6. [Google Scholar] [CrossRef]
- Rojas, R.; Jimenez-Kairuz, A.F.; Manzo, R.H.; Giacomelli, C.E. Release kinetics from LDH-drug hybrids: Effect of layers stacking and drug solubility and polarity. Colloids Surfaces A Physicochem. Eng. Asp. 2014, 463, 37–43. [Google Scholar] [CrossRef]
- Costa, P.; Sousa Lobo, J.M. Modeling and comparison of dissolution profiles. Eur. J. Pharm. Sci. 2001, 13, 123–133. [Google Scholar] [CrossRef]
- Li, L.; Qu, W.; Zhang, X.; Lu, J.; Chen, R.; Wu, F.; Amine, K. Succinic acid-based leaching system: A sustainable process for recovery of valuable metals from spent Li-ion batteries. J. Power Sources 2015, 282, 544–551. [Google Scholar] [CrossRef]
- Papageorgiou, S.K.; Katsaros, F.K.; Kouvelos, E.P.; Nolan, J.W.; Le Deit, H.; Kanellopoulos, N.K. Heavy metal sorption by calcium alginate beads from Laminaria digitata. J. Hazard. Mater. 2006, 137, 1765–1772. [Google Scholar] [CrossRef] [PubMed]
- Lalhmunsiama; Pawar, R.R.; Hong, S.M.; Jin, K.J.; Lee, S.M. Iron-oxide modified sericite alginate beads: A sustainable adsorbent for the removal of As(V) and Pb(II) from aqueous solutions. J. Mol. Liq. 2017, 240, 497–503. [Google Scholar] [CrossRef]
- Etcheverry, M.; Cappa, V.; Trelles, J.; Zanini, G. Montmorillonite-alginate beads: Natural mineral and biopolymers based sorbent of paraquat herbicides. J. Environ. Chem. Eng. 2017, 5, 5868–5875. [Google Scholar] [CrossRef]
- Kloprogge, J.T.; Frost, R.L. Infrared and Raman Spectroscopic Studies of Layered Double Hydroxides (LDHs). In Layered Double Hydroxides: Present and Future; Rives, V., Ed.; Nova Science Publishers: Hauppauge, NY, USA, 2001; pp. 139–192. [Google Scholar]
- Jia, Y.; Wang, H.; Zhao, X.; Liu, X.; Wang, Y.; Fan, Q.; Zhou, J. Kinetics, isotherms and multiple mechanisms of the removal for phosphate by Cl-hydrocalumite. Appl. Clay Sci. 2016, 129, 116–121. [Google Scholar] [CrossRef]
- Zheng, L.; Xia, S.; Lu, X.; Hou, Z. Transesterification of glycerol with dimethyl carbonate over calcined Ca-Al hydrocalumite. Cuihua Xuebao/Chinese J. Catal. 2015, 36, 1759–1765. [Google Scholar] [CrossRef]
- Ren, H.; Gao, Z.; Wu, D.; Jiang, J.; Sun, Y.; Luo, C. Efficient Pb(II) removal using sodium alginate-carboxymethyl cellulose gel beads: Preparation, characterization, and adsorption mechanism. Carbohydr. Polym. 2016, 137, 402–409. [Google Scholar] [CrossRef] [PubMed]
- Veglio, F.; Esposito, A.; Reverberi, A.P. Copper adsorption on calcium alginate beads: Equilibrium pH-related models. Hydrometallurgy 2002, 65, 43–57. [Google Scholar] [CrossRef]
- Felderhof, B.U.; Deutch, J.M. Concentration dependence of the rate of diffusion-controlled reactions. J. Chem. Phys. 1976, 64, 4551–4558. [Google Scholar] [CrossRef]
- United States Environmental Protection Agency Lead and Copper Rule (LCR), 56 FR. 1991; pp. 26460–26564. Available online: https://nepis.epa.gov/Exe/ZyPDF.cgi?Dockey=60001N8P.txt (accessed on 27 February 2019).
Figure 1. PXRD patterns of (a) NaAlg, (b) CaAlg beads, (c) hydrocalumite (HC), and (d) CaAlg/HC beads.
Figure 2. FT–IR spectra of (a) NaAlg, (b) CaAlg beads, (c) HC, (d) CaAlg/HC beads.
Figure 3. TG/DTA curves of HC powder as well as CaAlg and CaAlg/HC beads.
Figure 4. SEM images of (a) HC, (b) AlgCa beads, (c) and (d) CaAlg/HC beads.
Figure 5. pH vs t curves (a,c) and proton uptake (ΓH) kinetics (b,d) for AlgCa (a,b) and AlgCa/HC beads (10 units) placed in 100 mL solutions of increasing [HCl]. One out of 20 points are represented in the curves.
Figure 6. Cu2+ uptake isotherms of (A) AlgCa (left axis, filled squares) and HC (right axis, void circles) (B) AlgCa/HC beads, with and without filtration of the supernatants after bead removal. pH kinetics during the uptake experiment with (C) AlgCa beads and HC (Inset), (D) AlgCa/HC. Every pH kinetic curve presented a correspondence with a point of the isotherm that was marked in the corresponding curve in layers A and B.
Table 1. Fitting constants of proton uptake kinetics according to the diffusion model.
|[HCl] a||ΓH, 150 b||ΓH, 0 b||kD d||R2||ΓH, 150 b||ΓH, 0b||kD d||R2|
a mmol L−1, b µmol bead−1; c min; d µmol min−1/2 bead−1
Table 2. Fitting parameters of ΓCu vs [Cu]eq using the Langmuir model.
|Sample||ΓCu, max (mg/g)||KL (ppm−1)||R2|
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