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Article

Lead Ion Sorption by Perlite and Reuse of the Exhausted Material in the Construction Field

by
Andrea Petrella
1,*,
Danilo Spasiano
1,
Vito Rizzi
2,
Pinalysa Cosma
2,
Marco Race
3 and
Nicoletta De Vietro
4
1
Dipartimento di Ingegneria Civile, Ambientale, Edile, del Territorio e di Chimica, Politecnico di Bari, via E. Orabona, 4, 70125 Bari, Italy
2
Dipartimento di Chimica, Università degli Studi di Bari “Aldo Moro”, via E. Orabona, 4, 70125 Bari, Italy
3
Dipartimento di Ingegneria Civile e Meccanica, Università di Cassino e del Lazio Meridionale, via Di Biasio 43, 03043 Cassino, Italy
4
Istituto di Nanotecnologia (Nanotec), Consiglio Nazionale delle Ricerche (CNR), c/o Dipartimento di Chimica, Università degli Studi di Bari “Aldo Moro”, via E. Orabona, 4, 70125 Bari, Italy
*
Author to whom correspondence should be addressed.
Appl. Sci. 2018, 8(10), 1882; https://doi.org/10.3390/app8101882
Submission received: 26 September 2018 / Revised: 4 October 2018 / Accepted: 5 October 2018 / Published: 11 October 2018
(This article belongs to the Special Issue New Materials and Techniques for Environmental Science)
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Versions Notes

Abstract

:
This paper deals with the possibility of using perlite as a lead ion sorbent from industrial wastewater. Dynamic (laboratory column) operations were carried-out using beads, which were percolated by metals in a 2–10 mg·L−1 concentration range. To this purpose, lead ion solutions were eluted in columns loaded with different amounts of sorbent (2–4 g) within a 1–2 mm bead size range, at 0.15–0.4 L·h−1 flow-rates. Tests were performed to complete sorbent exhaustion (column breakthrough). The highest retention was obtained at 0.3 L·h−1, with 4 g of perlite and 10 mg·L−1 of influent, lead ion concentration. Film diffusion control was the kinetic step of the process in the Nerst stationary film at the solid/liquid interface. At the end of the sorption, perlite beads were used as lightweight aggregates in the construction field (i.e., for the preparation of cement mortars). Specifically, conglomerates showing different weights and consequently different thermal insulating and mechanical properties were obtained, with potential applications in plaster or panels.

Graphical Abstract

1. Introduction

Anthropogenic activity causes the direct and indirect discharge of billions of contaminants of different natures and origins [1,2,3,4,5], which need specific treatment for their removal [6,7,8,9]. Potential toxic metals (PTMs) pollution comes from different sources—such as batteries, metal products, and industrial chemical discharge [10,11]—and generates adverse health effects. The presence of PTMs in the environment is increasing in some parts of the world, especially in emerging countries [12,13,14,15,16].
In recent years, cheap and eco-friendly sorbents [17,18,19] have been used to remove PTMs from wastewater. These sorbents may be considered an alternative to conventional activated carbon—which has a high cost of production and regeneration [20,21]—or ion exchange resins, which are expensive and pH-dependent [22]. Compared to conventional methods, the use of these cheap materials allows for “once-through operations” (i.e., PTM-laden, or exhausted, sorbents can be put into a cement conglomerate as aggregate) [17,23,24,25,26], thus overcoming the expensive regeneration procedures and problems related to the large, hazardous sludge production that is typical of traditional sorbents.
In this paper, a silico-aluminate sorbent, such as expanded perlite, was used to remove lead ions from wastewater. Lead ion was chosen, because it was considered an important pollutant, as it is very toxic to mammals and aquatic life, with its presence in the environment the result of various applications [27,28]. The typical concentration of lead ion in industrial wastewater is between 5–15 mg·L−1 for battery production, while for fertilizers, mining, and metallic industries, it is approximately 2 mg·L−1; accordingly, in this study, synthetic lead ion concentration was chosen in a range comparable to industrial practice (2–10 mg·L−1) [29,30]. Perlite is a vitreous, volcanic rock that, if heated over 870 °C, expands up to 20 times its original volume, leading to the formation of an excellent thermal insulating and ultra-lightweight material, characterized by interesting mechanical and chemical resistances [31]. For these reasons, and due to its relatively low cost (40–80 USD per m−3), perlite has recently been suggested for many applications, regarding wastewater treatment (i.e., for the synthesis of filtration membranes; as a carrier in biological, fluidized beds; as support for TiO2; and as a sorbent for Cr(III) ions and dyes) [31,32,33,34,35]. Additionally, the correct adoption of perlite for wastewater treatment may be considered a sustainable solution, as it is in agreement with most of the twelve principles of green chemistry [36].
In this study, packed bed columns were prepared and lead ion separation tests carried out at room temperature and in distilled water, with different sorbent dosages, influent concentrations, and flow-rates being used. The analysis was carried out by evaluating the thermodynamic and kinetic aspects, together with the microstructural characterization, of perlite.
Exhausted perlite residues were reused as cheap and eco-friendly aggregates to produce construction materials—such as cement conglomerates—thus overcoming problems associated with the cost of regeneration. PTM-laden beads can be encapsulated by a matrix, minimizing the leaching of toxic compounds, and are thermal insulating materials with good mechanical resistances [17,23,24]. In this respect, conglomerates with increasing perlite volume and with different specific weights were prepared and characterized by thermal mechanical tests.
Consequently, besides proposing a sustainable wastewater treatment, the reuse of exhausted, expanded perlite to increase the insulating properties of cement is in accordance with circular economy principles [37] and with the recent trend towards sustainable water treatments [38,39,40].

2. Materials and Methods

2.1. The Sorbent

Perlite was supplied by Maltek Industrie S.r.l. (Terlizzi, Bari, Italy). In the present investigation, grains between 1–2 mm were used, with the following chemical compositions: SiO2 (74.5%), Al2O3 (12.3%), K2O (4.2%), Na2O (4%), Fe2O3 (1%), and CaO (1.4%). Scannig Electron Microscopy (SEM) and Energy Dispersive X-ray Analysis (EDX) characterization of the particles was carried out by an electron microscope (an Field-emission scanning electron microscopy-Energy Dispersive X-ray Analysis (FESEM-EDX) Carl Zeiss Sigma 300 VP). The samples were applied onto aluminum stubs and covered with carbon film, after sputtering with a Sputter Quorum Q150 thermal evaporator. Perlite porosity determinations were carried out by an Autosorb IQ Chemi TCD instrument (Quantachrome Instruments, Boynton Beach, FL, USA), through adsorption–desorption N2 isotherms, at 77 K.

2.2. Lead Ion Sorption Tests

Pb(NO3)2 (99.5%) was purchased from Carlo Erba (Milan, Italy) and the solutions prepared in distilled water (pH = 6). Perlite beads (1–2 mm) were packed into columns with diameters of 1 cm and heights of 50 cm. They were then eluted with lead ion solutions. Breakthrough curves were obtained from thermodynamic study. These curves represented the relative lead ion concentration (C/C0) vs. bed volumes (BV = V/V0). When the liquid-phase solution started to be leached by the column, the breakpoint was reached (i.e., the minimum lead ion retention capacity of the sorbent occurred and the final exhaustion of the bed was obtained, when the concentration of the effluent was approximately the same as that of the influent). The first set of experiments was carried out with 2–4 g of perlite at 0.3 L·h−1 and with 2 mg of Pb2+ L−1. Successively, experiments were carried-out at different influent concentrations (2–10 mg of Pb2+ L−1), at 0.3 L·h−1, with 4 g of perlite. Finally, the process was evaluated at variable flow-rates (0.15–0.4 L·h−1), with 2 mg of Pb2+ L−1 and 4 g of perlite. Table 1 shows all the experiments performed.
Time-dependent breakthrough curves (kinetic study) were also reported. The sorption kinetics are dependent on the mass transfer phenomena [41]. Specifically, film diffusion control is the rate determining step, because functionalities (silico-aluminate groups) are essentially present on the surface of perlite. The half time of the reaction (t0.5) was obtained as follows [41]:
t0.5 = 1.33 r0 δ D−1 C0−1 S−1
where t0.5 is inversely proportional to the bulk specie concentration (C0) and diffusion coefficient (D), and is directly proportional to the particle radius (r0) and film thickness (δ).

2.3. Reuse of Perlite Particles in the Construction Field after Lead Exhaustion

Perlite grains were reused after lead exhaustion and employed as aggregates in cement composites. As binder, 42.5R cement from Buzzi Unicem (Barletta, Italy) [42] was employed, together with silica sand (0.08–2 mm) [43,44] from Societè Nouvelle du Littoral (Leucate, France). Two sand-containing specimens were prepared as controls: A normalized mortar with a 0.08–2 mm average grain size range, and a sand reference, with a 0.5–2 mm average grain size range and an aggregate volume equal to 500 cm3. Perlite beads were used in partial or total substitution of the sand aggregate (0%, 25%, 50%, 75%, and 100%) and replacement was made based on volume, due to the low specific gravity of the silico-aluminate material. In the case of the perlite samples, a 500 cm3 aggregate volume was used. The water/cement ratio of the specimens was 0.5. Compression tests were carried out (using a MATEST device from Milan, Italy) on samples obtained, following flexural tests, using 40 × 40 × 160 mm prisms [43], and 28 days of curing. Thermal conductivity (λ) tests were carried out by an ISOMET 2104 device (Applied Precision Ltd., Bratislava, Slovakia) by application of a heating probe on the surface of cylinders, after 28 days curing. The heating probe had a diameter of 100 mm and height of 50 mm. Before measurements were taken, the samples were dried at 105 °C, until a constant weight (±0.5%) had been reached, and then cooled to room temperature.

3. Results and Discussion

3.1. Perlite Characterization and Perlite as a Lead Ion Sorbent

Figure 1 shows the morphological structure of a perlite bead, together with its inner porosity.
Perlite is considered a mesoporous material (20–500 Å pore diameter), with an average pore radius of 16.535 Å, a BET total surface area of 1.664 m2·g−1, a total volume of the pores of 0.008 cm3g−1, and a surface area of 1.010 m2·g−1.
Figure 2 shows the breakthrough curves for experiments carried out at a 0.3 L·h−1 flow-rate, with 2 mg·L−1 of lead ion concentration and a variable amount (2–4 g) and bed volume (16–30 cm3) of the sorbent. In these tests, as perlite dosage and volume increased, metal removal efficiency was higher, because a more effective diffusion of lead ions throughout the sorbent was obtained, together with breakpoints reached at increasing bed volumes. Overall retention capacities were experimentally determined at 1.1, 1.45, 1.7, and 2.0 mg/gsorbent−1 and breakpoints were determined at 55, 80, 91, and 100 BV, respectively, for 2, 2.6, 3.2, and 4 g of perlite, as shown in Table 1.
From the reported microscopic observations and Brunauer-Emmett-Teller measurements (BET) measurements, metal retention by the sorbent was ascribed to the specific surface area and to the corresponding large sorbent pores exposed to the liquid-phase, allowing for free migration of the hydrated lead ions (4.01 Å hydrated radius) to the functional groups of the silico-aluminate matrix. As previously observed [45], lead ions are mostly absorbed/adsorbed by ion exchange (65–70%)—especially with Na+ ions, but also with Ca2+ and K+ ions—at the negative silicate functional groups present on the perlite surface. This is represented by the following reaction:
nPerlite-(Cm+) + Pb2+ → (Perlite)n-Pb2+ + n(Cm+)
Sorption may also be attributed, on a smaller scale, to Van der Waals forces at non-specific, functional groups.
Figure 2B shows the kinetic study for lead ion retention on perlite, at different sorbent dosages. Time-dependent breakthrough curves showed a direct linear dependence of t0.5 vs. gsorbent, as demonstrated in Figure 2C.
Figure 3A shows the breakthrough curves for experiments carried out at a 0.3 L·h−1 flow-rate, with 4 g of perlite and variable lead ion concentration (2–10 mg of Pb+2 L−1).
In comparing the curves, it was observed that, as the initial metal concentration C0 increased, an retention capacities also increased, together with anticipation of the breakthrough point (perlite exhaustion). Specifically, for 2, 4, 7, and 10 mg·L−1 of lead ion influent concentrations, retention capacities of 2.0, 2.5, 3.1, and 3.5 mg gsorbent−1, respectively, were obtained, as shown in Table 1. A concern, regarding the breakpoint, was detected in the case of the most concentrated solution (27 BV, 10 mg of Pb+2 L−1), with respect the 2 mg of Pb+2 L−1 solution (100 BV). Figure 3B shows the kinetic study of lead ion retention on perlite at different influent concentrations. Quicker saturation of the column was observed at high metal concentrations, thereby decreasing the breakthrough time. Time-dependent breakthrough curves showed a reverse linear dependence of t0.5 vs. C0, as shown in Figure 3C, according to the film diffusion control theoretical model (Equation (2)) [41]. Figure 4A shows, the breakthrough curves for experiments carried out with 2 mg of Pb+2 L−1 influent solution, 4 g of perlite, and at different flow-rates (0.15, 0.2, 0.3, and 0.4 L·h−1).
Retention capacities were 2.5, 2.2, 2.0, and 1.6 mg gsorbent−1 for 0.15 L·h−1, 0.2 L·h−1, 0.3 L·h−1, and 0.4 L·h−1, respectively, while breakpoints were detected at 153, 130, 100, and 73 BV, as shown in Table 1. Thus, at low flow-rates, corresponding to long liquid/solid contact times, a more complete saturation of the column was detected. This result explains the increasing retentions and higher values of the breakthrough points. A typical, “self-sharpening” of the column breakthrough curves was observed at lower flow-rates, associated with an increase of metal sorption, as shown in Figure 4A, due to favorable retention equilibria towards the entering ions, occurring when the rates of motion decreased [41]. Figure 4B shows the kinetic study for lead ion retention on perlite, at different flow-rates. Slower elution determined a delay of the breakthrough (i.e., higher contact times), while faster elution induced an advance of the breakthrough (i.e., lower contact times). Time-dependent breakthrough curves showed an inverse linear dependence of t0.5 vs. flow-rate, as shown in Figure 4C, according to film diffusion control (Equation (2)) [41]. At lower flow-rates, the film at the liquid/solid interface (Nernst film) could be assumed to be thicker, while at higher flow-rates the film could be assumed to be thinner.

3.2. Reuse of the Metal Laden Perlite in the Construction Field

After test no. 7 (4 g of perlite, 0.3 L·h−1 flow-rate, 10 mg of Pb+2 L−1), exhausted beads were characterized by SEM analysis. No changes were observed on the structure of the sorbent, as shown in Figure 5.
The silico-aluminate materials were finally reused in the construction field as lightweight aggregates in cement mortars, so as to minimize technical and economic problems related to regeneration processes [17,23,45,46].
As observed in previous studies [47], metals leaching through the composite were few. Accordingly, the specimens were thermally and mechanically characterized, as shown in Table 2 and Figure 6.
Thermal conductivity, λ, is the property of a material to transfer heat. It indicates the temperature response of specimens to heat flow impulses [48,49]. Perlite-based mortars showed lower thermal conductivities (from 40% to 80%), compared to the normalized mortar, taken as a control. An increase of perlite content induced an exponential decrease of conductivity, as shown in Figure 6A.
The addition of lightweight aggregates creates voids in the composite matrix, thus sensibly limiting heat transport phenomena. These voids barely contributed to the extended internal porosity of perlite, as shown in Figure 1, as there was a strong adherence at the cement/aggregate interface, as shown in Figure 7. This is opposite to what was observed in composites characterized by cement and organic materials, such as tire rubber, where unfavorable adhesion was observed, due to the different nature of the constituents [50]. In the present example, this perfect adhesion may be ascribed to the similar nature of the compounds present in the ligand paste and aggregates (silicates, aluminates). As perlite volume increased, the thermal insulating properties of the samples improved, due to the decrease in the weight of the composites.
In the case of the resistance to compression tests (after 28 days aging), the perlite-based composites showed a decrease in mechanical performance, with increase of the silico-aluminate aggregate volume, as shown in Figure 6B. This result is in accordance with the thermal measurements, as the weight decrease induced a decrease in mechanical strength, due to the large number of voids introduced into the cement conglomerates. It is also worth to noting that the mechanical performances were extremely interesting, specifically in the case of specimens with 50% and 75% perlite, which could be considered a good compromise between thermal insulation and compressive resistance. Applications of these eco-friendly materials may be useful for non-structural composites, such as plaster or panels [24,50,51], thanks to the presence of lightweight, insulating silico-aluminate aggregates.

4. Conclusions

A silico-aluminate material, perlite, was used as an alternative and cheap sorbent of lead ions, present in industrial wastewater. Solutions at different metal concentrations (2–10 mg·L−1) were eluted at different flow-rates (0.15–0.4 L·h−1) in packed bed columns, filled with different weights (2–4 g) and volumes (16–30 cm3) of perlite. The main results are summarized as follows:
-
From microscopic and BET measurements, metal retention was ascribed to surface area and to the large sorbent pores exposed to the liquid-phase, which allowed for free migration of hydrated lead ions to the functional groups of the silico-aluminate matrix.
-
Metal removal efficiencies increased with increasing amounts of perlite, together with breakpoints being reached at increasing bed volumes.
-
Increase in retention capacities was observed with an increase of initial metal concentration, together with anticipation of the breakthrough point.
-
A more complete saturation of the column was detected at low flow-rates, associated with long liquid/solid contact times, and with corresponding higher values of the breakthrough points.
-
The best lead ion retention was obtained at 0.3 L·h−1, with 4 g of perlite and 10 mg·L−1 of Pb2+ (3.5 mg of Pb2+gsorbent−1).
-
Film diffusion control was the kinetic step of the process.
-
After column breakthrough, the sorbent was considered a special waste and incorporated into cement conglomerates as a lightweight, eco-friendly aggregate.
-
With the increase of perlite volume, thermal insulating properties of the samples were improved, together with a decrease in mechanical strength.
-
The cement conglomerates could be used in the construction industry in plaster or panels, without adverse environmental effects, as the metals would be incorporated into the matrix, with negligible leaching.

Author Contributions

A.P.: experimental tests and discussion of the results; D.S.: experimental tests and discussion of the results; V.R. and P.C.: characterization of the materials and discussion of the results; M.R.: elaboration data and discussion of the results; N.D.V.: porosity measurements.

Funding

This research received no external funding.

Acknowledgments

The authors thank Adriano Boghetich for the SEM-EDX analysis. Regione Puglia is gratefully acknowledged for her financial support (X-ray Lab Project–Reti di Laboratori Pubblici di Ricerca, cod. n. 45 and 56).

Conflicts of Interest

The authors declare no conflicts of interest.

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Applsci 08 01882 g001 550
Figure 1. SEM images of the surface of a perlite bead (top) and of the inner perlite structure (bottom).
Figure 1. SEM images of the surface of a perlite bead (top) and of the inner perlite structure (bottom).
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Applsci 08 01882 g002 550
Figure 2. (A) Breakthrough curves for lead ion retention at different perlite dosages (2, 2.6, 3.2, and 4 g; 1–2 mm bead size range; 0.3 L·h−1 flow-rate; 2 mg of Pb+2 L−1; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. perlite dosage.
Figure 2. (A) Breakthrough curves for lead ion retention at different perlite dosages (2, 2.6, 3.2, and 4 g; 1–2 mm bead size range; 0.3 L·h−1 flow-rate; 2 mg of Pb+2 L−1; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. perlite dosage.
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Figure 3. (A) Breakthrough curves for lead ions retention at 2, 4, 7, and 10 mg of Pb+2 L−1 (0.3 L·h−1 flow-rate; 4 g perlite; 1–2 mm bead size range; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. influent concentration.
Figure 3. (A) Breakthrough curves for lead ions retention at 2, 4, 7, and 10 mg of Pb+2 L−1 (0.3 L·h−1 flow-rate; 4 g perlite; 1–2 mm bead size range; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. influent concentration.
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Figure 4. (A) Breakthrough curves for lead ion retention at 0.15, 0.2, 0.3, and 0.4 L·h−1 flow-rates (1–2 mm bead size range; 2 mg of Pb+2 L−1; 4g perlite; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. flow-rate.
Figure 4. (A) Breakthrough curves for lead ion retention at 0.15, 0.2, 0.3, and 0.4 L·h−1 flow-rates (1–2 mm bead size range; 2 mg of Pb+2 L−1; 4g perlite; T = 298 K). (B) Time-dependent breakthrough curves. (C) Correlation of the half exchange time, t0.5, vs. flow-rate.
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Figure 5. SEM image of a perlite bead, after the sorption process (top) and magnification (bottom).
Figure 5. SEM image of a perlite bead, after the sorption process (top) and magnification (bottom).
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Figure 6. (A) Thermal and (B) mechanical tests of the controls and perlite specimens.
Figure 6. (A) Thermal and (B) mechanical tests of the controls and perlite specimens.
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Figure 7. Cement/perlite composites, after mechanical tests (inset), SEM image of the structure of the conglomerate (top) and magnification of the ligand paste/perlite interface (bottom).
Figure 7. Cement/perlite composites, after mechanical tests (inset), SEM image of the structure of the conglomerate (top) and magnification of the ligand paste/perlite interface (bottom).
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Table
Table 1. Summary of the column tests carried out on the perlite sorbent (T = 298 K).
Table 1. Summary of the column tests carried out on the perlite sorbent (T = 298 K).
Test No.Flow Rate
(L·h−1)		Influent Conc.
(mg·L−1)		Bead Size
(mm)		Bed Volume
(cm3)		Bed Amount
(g)		Qexp
(mg·g−1)		BV
10.321–21621.10 ± 0.0555 ± 3
20.321–2202.61.45 ± 0.0780 ± 4
30.321–2243.21.7 ± 0.0891 ± 5
40.321–23042.0 ± 0.1100 ± 5
50.341–23042.5 ± 0.1253 ± 3
60.371–23043.1 ± 0.1540 ± 2
70.3101–23043.5 ± 0.1727 ± 1
80.1521–23042.5 ± 0.12153 ± 8
90.221–23042.2 ± 0.11130 ± 7
100.421–23041.6 ± 0.0873 ± 4
Table
Table 2. Thermal and mechanical properties of the controls and perlite-based composites.
Table 2. Thermal and mechanical properties of the controls and perlite-based composites.
Sampleρ (Kg m−3)λ (W m−1 K−1)Rc (Mpa)
Normalized mortar1960 ± 1002.02 ± 0.1049 ± 3
Sand (100%)1920 ± 1001.59 ± 0.0848 ± 3
Sand (75%)/Perlite (25%)1750 ± 881.2 ± 0.0634.5 ± 2
Sand (50%)/Perlite (50%)1600 ± 800.90 ± 0.0526 ± 1
Sand (25%)/Perlite (75%)1350 ± 680.60 ± 0.0321 ± 1
Perlite (100%)1050 ± 530.39 ± 0.0216.4 ± 1

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MDPI and ACS Style

Petrella, A.; Spasiano, D.; Rizzi, V.; Cosma, P.; Race, M.; De Vietro, N. Lead Ion Sorption by Perlite and Reuse of the Exhausted Material in the Construction Field. Appl. Sci. 2018, 8, 1882. https://doi.org/10.3390/app8101882

AMA Style

Petrella A, Spasiano D, Rizzi V, Cosma P, Race M, De Vietro N. Lead Ion Sorption by Perlite and Reuse of the Exhausted Material in the Construction Field. Applied Sciences. 2018; 8(10):1882. https://doi.org/10.3390/app8101882

Chicago/Turabian Style

Petrella, Andrea, Danilo Spasiano, Vito Rizzi, Pinalysa Cosma, Marco Race, and Nicoletta De Vietro. 2018. "Lead Ion Sorption by Perlite and Reuse of the Exhausted Material in the Construction Field" Applied Sciences 8, no. 10: 1882. https://doi.org/10.3390/app8101882

APA Style

Petrella, A., Spasiano, D., Rizzi, V., Cosma, P., Race, M., & De Vietro, N. (2018). Lead Ion Sorption by Perlite and Reuse of the Exhausted Material in the Construction Field. Applied Sciences, 8(10), 1882. https://doi.org/10.3390/app8101882

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