Original Research ARTICLE
Morphology of Modified Biochar and Its Potential for Phenol Removal from Aqueous Solutions
- School of Mineral Resources Engineering, Technical University of Crete, Chania, Greece
In the present study, the efficiency of phenol removal from synthetic aqueous solutions by chemically modified biochar with the use of 1M KOH or 1M FeCl3 was investigated. Initially, biochar was produced after slow pyrolysis of three different agricultural wastes, namely pistachio (Pistacia vera L.) shells, pecan (Carya illinoinensis) shells, and wood sawdust. The quality of biochar was assessed by evaluating its main properties, such as pH, surface area, porosity and C content. X-ray diffraction (XRD), Scanning Electron Microscopy (SEM), and Fourier Transform Infrared Spectroscopy (FTIR) were used for the identification of biochar's structure. The efficiency of phenol removal from synthetic solutions was assessed with the use of kinetic and equilibrium experiments. The experimental results show that the KOH-modified biochar exhibited the highest phenol removal efficiency. Hydrophobic sorption on its surface is the main phenol removal mechanism. The pseudo-second order model fits best the kinetic data, while the Freundlich model, as deduced from an equilibrium study describes very well sorption of phenols on all biochars examined.
Biochar is a carbon rich and porous material which is produced by thermal conversion of biomass in low oxygen atmosphere at temperature usually not exceeding 600°C. Slow pyrolysis of biomass has the advantage of retaining almost half of its carbon in stable biochar (Manyà, 2012; Kim et al., 2013). Biochar can be produced in every country using various raw materials including energy crops (e.g., corn, cereals, wood pellets, and oilseed rape), agricultural wastes (e.g., wheat straw, rice husk, waste wood, pistachio, peanut, hazelnut shells, and manure) and other wastes including sewage sludge (Liu et al., 2012; Moussavi and Khosravi, 2012; Agrafioti et al., 2013, 2014; Inyang et al., 2014; Frišták et al., 2015).
Biochar is an environmentally friendly material and may exhibit similar properties with activated carbon. Due to its chemical and biological stability it may be utilized as carbon sink in soils for thousands of years. Also, biochar's ability to retain nutrients is considered very important in terms of improving soil fertility and crop productivity (Steiner et al., 2008; Sánchez et al., 2009; Cayuela et al., 2013; Kloss et al., 2014; Sánchez-García et al., 2014).
Due to its strong adsorption capacity, which is related to the large surface area and the presence of negatively charged organic functional groups, biochar can be used as adsorbent for the removal of various contaminants from wastewaters. Contaminants may include metals such as Pb, Cu, Zn, As, Ni, and Cd, as well as organic compounds, such as pesticides and phenols. Adsorption on biochar may be considered as a feasible approach due to its high efficiency, low cost, ease of application and minor by-product generation compared to traditional alternatives (Beesley et al., 2011; Yu et al., 2015).
Phenolic compounds which are present in various concentrations in several waste streams, e.g., 0.5–24 g·L−1 in olive mill wastewater (OMW), cause toxic effects on aquatic organisms, bacteria and yeast and prevent seed germination. They are reported as human carcinogens, exhibit poor biodegradability and may also cause long-term ecological damage (Bayramoglu et al., 2009; Di Bene et al., 2013; Inyang and Dickenson, 2015). The removal of phenolic compounds with the use of biochar was reported so far in a limited number of studies. According to Mubarik et al. (2016), highly porous biochar produced from sugarcane bagasse can be used as efficient and low-cost adsorbent to remove 2,4,6-trichlorophenol from stock solutions. The potential of biochar produced from switchgrass, hardwood and softwood on removing phenols was mainly related to its microporous surface (Han et al., 2013). Rice straw biochar was used to decrease the concentration of pentachlorophenol in leachates produced from contaminated sediments which were then used to increase the germination rate of wheat seeds (Lou et al., 2011). Biochar produced after pyrolysis of municipal wastewater biosolids removed effectively halogenated phenols, while its sorption capacity was improved at lower solution pH (Oh and Seo, 2016). Sewage sludge biochar showed excellent adsorption capacity for sulfonated methyl phenol resins which are used as additive in drilling fluids (Liu et al., 2015). Also, biochar prepared from paper mill sludge was used for the removal of pentachlorophenol by simultaneous adsorption and dechlorination (Devi and Saroha, 2015).
According to the Federal Register of Environmental Protection Agency (Environmental Protection Agency, 1995), the benchmark established for the content of total phenols in stormwater discharge is 1 mg·L−1. In Greece, no limits for phenol disposal in water receivers have been so far established. Also, no health-based thresholds for the concentration of phenols in drinking water have been proposed; an indicative acceptable value of 0.5 μg·L−1 has been proposed in accordance with the Council Directive 98/83/EC on the quality of water intended for human consumption (Greek Government Gazette, 2007)1. According to the Canadian Soil Quality Guidelines the recommended concentration of phenols in soils to avoid adverse effects is 3.8 mg·kg−1 (Canadian Council of Ministers of the Environment, 2007).
Chemical modification of biochar with the use of acids, bases or polymers usually enhances its adsorption efficiency. The so called modified/activated/engineered biochars may be produced by treating the feedstock either prior to or after pyrolysis. The final product is characterized by increased surface area, modified chemical functionality and presence of high-affinity adsorption sites which enhance chemical bonding with contaminants (Mayer et al., 2014; Wang et al., 2015).
According to Qian et al. (2013), Al-modified crop straw biochar resulted in adsorption of larger amounts of As(V) from aqueous solutions at pH < 7, in comparison with the respective non-modified biochar. High As adsorption potential was also shown for modified corn straw biochar which was prepared by pyrolysis of the raw material that was initially soaked in aqueous KMnO4 solution (0.079 mol·L−1) (Yu et al., 2015). Sun et al. (2015) have shown that eucalyptus saw dust biochar modified with citric, tartaric, and acetic acids can efficiently remove methylene blue from aqueous solution. Also, more than 90% NO3 removal was attained using biochar produced from conocarpus green waste which was chemically modified with magnesium and iron oxides prior to pyrolysis (Usman et al., 2016). Finally, hydrogel-biochar composites modified with NaCl were found to improve sorption of phenols (Karakoyun et al., 2011).
Various models have been widely applied to describe adsorption of contaminants from solutions and elucidate the mechanisms involved. These models are based either on solution concentration, e.g., first-order, second-order reversible or irreversible and pseudo-first, pseudo-second order or on adsorption efficiency, e.g., Lagergren's first-order equation, Zeldowitsch's model and Elovich's equation (Ho and McKay, 1999; Ho, 2006a,b; Dari et al., 2015; Zahir et al., 2015).
The present paper aims to characterize the morphology of biochar modified with the use of either 1M KOH or 1M FeCl3 and also assess, through kinetic and equilibrium experiments, the effect of modification on the removal of phenols from synthetic solutions.
The raw materials used for the production of biochar were (i) pistachio (Pistacia vera L.) shells (PIr) from trees cultivated in Aegina island, Greece (ii) pecan (Carya illinoinensis) shells (PEr) from trees cultivated in the region of Chania, island of Crete, Greece and (iii) pine wood sawdust (SDr) obtained from a carpentry workshop located in Akrotiri, Chania, Crete.
Biochar Production and Characterization
The raw materials were oven dried (ON–O2, MEDLINE) for 24 h prior to use in order to remove moisture. Then, slow pyrolysis was carried out in a modified laboratory furnace N–8L SELECTA at 400°C for 60 min using porcelain capsules. The heating rate was 10°C·min−1. Nitrogen was purged in the oven for 60 min at a rate of 100 cm3·min−1 to remove air. The obtained biochars from pistachio shells, pecan shells and sawdust are hereinafter mentioned as PI, PE, and SD, respectively.
All biochars were pulverized using a FRITSCH pulverizer to obtain grain size < 100 μm, as evaluated using a Mastersizer S (Malvern Instruments) particle size analyzer. The following parameters were determined in feedstocks and biochars. Pyrolysis yield (yP) was determined from the % weight loss after heating. pH was measured using a solid:liquid ratio of 1:10 with a Hanna 211 pH/Eh meter. Porosity (%) was measured by mercury intrusion porosimetry using a Micromeritics AutoPore 9400 porosimeter. Brunauer–Emmett–Teller (BET) surface area was measured using a NOVA Surface Area Analyzer (Quantachrome instruments). The elemental C, H, S, and N analysis was carried out in a Flash 2000 Elemental Analyzer Thermo Scientific calibrated using BBOT standards (2,5-Bis(5-tert-butyl-2-benzo-oxazol-2-yl)thiophene) containing carbon; the oxygen content was subsequently calculated as the difference. Biochars were subjected to thermogravimetric (TG) analysis using a differential thermogravimetric analyzer TGA-6/DTG of Perkin Elmer as described in detail in Komnitsas et al. (2015, 2016); volatile matter (VM) and ash content were determined, while char fraction (100%–%VM) and fixed carbon (FC) content (% char–% ash content) were calculated.
The following analyses were also carried out for feedstock and biochar characterization. X–ray diffraction (XRD) analysis was performed using a Bruker AXS (D8 Advance type) diffractometer with Cu tube, scanning range from 4° to 70° 2θ, step 0.02° and measuring time 0.2 s/step. The qualitative analysis was assessed with the use of the DIFFRACplus EVA v. 2006 software and the Powder Diffraction File (PDF-2) database. SEM analysis was performed with a JEOL 6380LV scanning electron microscope equipped with an EDS INCA microanalysis system with low vacuum, pressure 30 Pa, voltage 20 kV and 10–12 mm working distance from the detector. FTIR analysis was carried out using pellets produced after mixing a pulverized sample of feedstock or biochar with KBr at a ratio of 1:100 w/w, using a Perkin-Elmer Spectrum 1000 spectrometer (USA).
Modification of Biochar
Pulverized biochars PI, PE, and SD were subjected to chemical modification. In brief, 10 g of each biochar were added in 250 mL of 1M KOH (pH 13.5) or 1M FeCl3 (pH 0.4) and the solution stirred with magnetic stirrers (Agimatic-ED, Spain) at 350 rpm for 24 h at room temperature. The supernatant solution was discarded and the solid material was collected and washed repeatedly with distilled water to remove excess of KOH or FeCl3 and then was oven-dried at 40°C for 24 h. The biochars modified with KOH or FeCl3 were named as PI-K, PE-K, SD-K or PI-F, PE-F, SD-F, respectively, and characterized as previously described.
Kinetic and Equilibrium Studies
Kinetic and equilibrium experiments were carried out using biochars PI, PE, and SD and modified biochars PI-K, PE-K, SD-K and PI-F, PE-F, SD-F. A synthetic phenol solution 100 mg·L−1 was prepared and used in all experiments by dissolving the required quantity of phenol C6H5OH (Sigma Aldrich, Germany) in distilled water.
For the kinetic experiments the adsorbent-biochar concentration used was 5 g·L−1. The selection of this specific concentration was based on previous studies carried out by the authors (Komnitsas et al., 2015, 2016). Agitation took place in 200 mL glass beakers at room temperature at 350 rpm, using a Vibromatic (Spain) rocking mixer. Reference tests were also carried out using 5 g·L−1 of activated carbon (AC) (Donau Chemie, Austria), which is an established commercial adsorbent. At various time intervals (0.5, 1, 2, 5, 18, 24, 48, and 72 h) 10 mL of liquid samples were withdrawn and filtered through Whatman filters (0.45 μm) for the determination of phenol concentration in solution using the Folin–Ciocalteu method (Box, 1983) and a SMART3 Lamotte, USA, colorimeter. All tests and measurements were carried out in triplicate.
Equilibrium experiments were carried out using four adsorbent-biochar concentrations, namely 0.5, 1, 2, and 5 g·L−1, while the adsorbed phenol concentration was calculated as the difference between the initial and the concentration at equilibrium in liquid phase. The other experimental conditions were similar to those described previously for the kinetic experiments.
Results and Discussion
Characterization of Biochars
The characterization of the three raw materials, namely pistachio shells (PIr), pecan shells (PEr), and sawdust (SDr) as well as of the biochars produced after pyrolysis at 400°C for 60 min (PI, PE, SD) and the modified biochars using 1M KOH (PI-K, PE-K, SD-K) or 1M FeCl3 (PI-F, PE-F, SD-F) is presented in Table 1. It is shown that the pyrolysis yield varies between 17.7 and 34.7% depending on pyrolysis temperature, heating rate and residence time (Komnitsas et al., 2015; Tripathi et al., 2016).
Table 1. Characterization of pistachio shells (PIr), pecan shells (PEr), sawdust (SDr), and produced biochars.
The paste pH (biochar:water ratio 1:10 w/w) of biochars PI, PE and SD is 6.4, 6.1, and 4.8, respectively, which is higher compared to the paste pH of the respective raw materials. Slightly lower values are obtained for the KOH-modified biochars, while a further slight decrease of pH is shown for the FeCl3-modified biochars due to the acidity of the ferric chloride solution. The volatile matter (VM) content of all biochars is substantially decreased compared to the raw materials, while the VM content of biochar PI is higher compared to PE and SD biochars. The char and fixed carbon (FC) contents increased in all biochars due to their higher content of bioavailable carbon. The ash content (difference between char and FC content), which expresses the inorganic matter content, is low and varies in all raw materials and biochars between 1.6 and 1.8%. The C content in all biochars increases substantially compared to the raw materials, while the hydrogen, nitrogen, and oxygen contents decrease accordingly. Decreased H/C and O/C ratios were obtained compared to those present in the raw materials, while chemical modification resulted in a further decrease of the O/C ratios, as also shown in other studies (Dehkhoda et al., 2016). Finally, it is mentioned that no sulfur was identified in any of the raw materials used.
Increased porosity of all biochars was also shown (29.3, 25.3, and 22.5%, for PI, PE, and SD, respectively) compared to the raw materials due to the transformation of aliphatic C structures to aromatic C structures (Brewer et al., 2014; Gray et al., 2014). The porosity was substantially increased for all and especially the KOH-modified biochars. The surface area of the non-modified biochars followed the sequence PI>PE>SD, and was also significantly increased after modification following the same trend, namely PI-K (572.4 m2·g−1) > PE-K (397.3 m2·g−1) > SD-K (124.6 m2·g−1) and PI-F (421.5 m2·g−1) > PE-F (351.6 m2·g−1) > SD-F (110.8 m2·g−1). Porosity and surface area are parameters of major importance in terms of adsorption efficiency, as discussed in the following sections.
The XRD analysis of the starting materials and the non-modified biochars has been presented in detail in previous studies (Komnitsas et al., 2015, 2016). In brief, in all raw materials (PIr, PEr, and SDr) the characteristic amorphous peaks of cellulose, which is one of the structural components of the primary cell wall of green plants, are detected. However, after pyrolysis the intensity of these peaks was reduced. The peaks of residual inorganic phases, such as calcite, quartz, whewellite, halite, and thermonatrite are only visible in non-modified biochars, after partial decomposition of organic matter.
Figure 1 shows the XRD patterns of biochars modified with KOH or FeCl3 (PI-K, PE-K, SD-K or PI-F, PE-F, SD-F, respectively), which exhibit a more or less elevated background between 15 and 30° 2-theta, due to the presence of organic matter (Cao and Harris, 2010). The cellulose peak is broader and of lower intensity in all biochars, compared to the starting materials, indicating a less ordered structure. Residual inorganic phases, such as quartz and calcite are more easily detected in modified biochars due to the partial decomposition of the organic matter during modification. Sodium carbonate is present in PE-F and PE-K biochars, as a result of atmospheric carbonation; this phase is soluble and disappears when samples are washed with water.
Figure 1. XRD patterns of biochars modified with 1M KOH (PI-K, PE-K, SD-K) or 1M FeCl3 (PI-F, PE-F, SD-F).
SEM and FTIR analyses were carried out for biochars produced from pistachio shells, which show the highest phenol adsorption capacity compared to biochars produced from pecan shells and wood sawdust, as deduced from the experimental results discussed in the following sections. Indicative SEM images of raw pistachio shells (PIr), biochar PI, KOH-modified biochar PI-K and FeCl3-modified biochar PI-F, are shown in Figure 2. The matrix of raw pistachio shells PIr is heterogeneous, while after pyrolysis for the production of PI biochar agglomeration takes place and a porous structure is formed due to the release of volatiles. SEM images of modified biochars (PI-K and PI-F) reveal their microporous structure as a result of their high porosity (49.8% and 41.4%, respectively, Table 1). Moreover, very fine particles with an average size of 15 μm are present in modified biochars resulting in a substantial increase of the surface area (572.4 and 421.5 m2·g−1 for PI-K and PI-F, respectively).
Figure 2. SEM images of raw pistachio shells (PIr) and biochars PI, PI-K (x500, x1000), and PI-F (x700, x1500).
The FTIR spectra of raw pistachio shells (PIr), biochar PI, KOH-modified biochar PI-K and FeCl3-modified biochar PI-F, are presented in Figure 3. The respective FTIR spectra band assignments are listed in detail in Table 2. The broad peaks shown in all samples at around 3420 cm−1 indicate the presence of hydroxyl group (−OH) stretching and strong hydrogen bonding, while those at 2920 and 2850 cm−1 are due to aliphatic C−H deforming vibration. The band at 1735 cm−1 for PIr is slightly shifted for all biochars to 1700 cm−1 and is assigned to ν(C = O) vibration in carbonyl group or the presence of carboxylic bonds. The band of PIr at 1630 cm−1, which is due to C = O or C = C stretching in aromatic groups, is slightly shifted to 1612 cm−1 in modified biochars indicating that chemical interactions occurred on the modified biochar surface. The shifting of the peaks around 1600–1700 cm−1 is also related to the conjunction of the carbonyl groups with the aromatic ring. The band at 1385 cm−1, shown in all patterns, is attributed to d(C = H) vibration in alkanes and alkyl groups and is more intense for the modified biochars PI-K and PI-F. In PIr, the band at 1260 cm−1 is attributed to C = C stretching while the sharp peak at 1045 cm−1 is mainly attributed to alcohol C−O or Si−O−Si functional groups. Both bands almost disappear in all biochars, either due to decomposition of cellulose after pyrolysis at 400°C or chemical modification. The bands at 900–600 cm−1 shown mainly in PIr and non-modified biochar PI, are assigned to C–H wagging vibrations due to the presence of aromatic and heteroaromatic compounds.
Table 2. FTIR spectra band assignments presented in Figure 3.
The kinetics of phenol adsorption on biochars PI, PE, SD and modified biochars PI-K, PE-K, SD-K and PI-F, PE-F, SD-F was studied using the pseudo-first and pseudo-second order Lagergren kinetic models which are described by the linear Equations (1) and (2), respectively:
where qt and qe (mg·g−1) is the uptake of phenols per unit weight of adsorbent at time t and at equilibrium, respectively, k1 (h−1) and k2 (h−1) are the rate constants for the pseudo-first and pseudo-second order kinetics, respectively.
The linear plot of log(qe−qt) vs. t, according to Equation (1), provides k1 and qe values for the pseudo-first order model. The plot of t/qt vs. t, according to Equation (2), provides k2 and qe for the pseudo-second order model. Parameters for the pseudo-first and pseudo-second order of Lagergren kinetic models, as derived from the experimental tests, are presented in Table 3. Equilibrium in all tests was achieved in 24 h.
Table 3. Parameters for the pseudo-first and pseudo-second order of Lagergren kinetic models for phenols adsorption on biochars PI, PE, SD and modified biochars PI-K, PE-K, SD-K and PI-F, PE-F, SD-F.
As shown in Table 3, for all biochars, modified or not, the pseudo-second order model fits the data much better (R2 values are higher than 0.998) than the pseudo-first order model. These results indicate that the reaction rate is proportional to the number of the active sites present on the adsorbent surface. It is known that adsorption in batch systems is affected by both surface or pore diffusion (Mohan et al., 2007; Li et al., 2010). Additional modeling is required to define which diffusion type is the rate limiting step (Hui et al., 2003).
Adsorption of Phenols on Biochars
Table 4 shows the % phenol adsorption from synthetic solution (initial concentration 100 mg·L−1) on non-modified biochars PI, PE, SD as well as on biochars modified with 1M KOH (PI-K, PE-K, SD-K) or 1M FeCl3 (PI-F, PE-F, SD-F). It is shown that for all adsorbent concentrations considered (0.5, 1, 2, and 5 g L−1), biochars modified with 1M KOH exhibit the highest phenol adsorption efficiency.
Table 4. Percentage phenol adsorption on biochars PI, PE, SD and modified biochars PI-K, PE-K, SD-K or PI-F, PE-F, SD-F for various adsorbent concentrations (0.5, 1, 2, and 5 g·L−1).
Experimental data shows that phenols are adsorbed more efficiently on KOH-modified biochars following the sequence PI-K>PE-K>SD-K, and the maximum adsorption reaches 76.6, 61.7, and 46.2%, respectively, when the adsorbent concentration is 5 g·L−1. Lower adsorbent concentrations result in reduced adsorption efficiency due to the presence of less surface adsorption sites (Wang et al., 2006).
The same trend is also noticed for the FeCl3-modified biochars and non-modified biochars, namely PI-F>PE-F>SD-F and PI>PE>SD, respectively. Activated carbon, which was used as reference adsorbent, shows quite similar with PI biochar adsorption efficiency, for all adsorbent concentrations used. An important finding of this study is that modification of PI biochar with KOH or FeCl3 results in better phenol adsorption efficiency than activated carbon. It is mentioned that biochar is a cheap, environment friendly and readily available product that can be easily chemically activated. On the other hand, commercial activated carbon, which is usually prepared from coal, lignite, coconut shells or wood and is widely used for the cleanup of contaminated water and wastewater, is usually an expensive material. Its production cost is mainly related to the reactivation process and is increased when high quality activated carbon is needed (Mohan and Chander, 2006; Quintelas et al., 2008; Al-Lagtah et al., 2016).
- For all adsorbents used the adsorption rate of phenols increases with decreasing adsorbent concentration.
- The highest adsorption rate of phenols, 2.74 mg·g−1·h−1 at equilibrium, is shown for 0.5 mg·L−1 PI-K biochar concentration (Figure 5).
- The KOH-modified biochars exhibited the highest phenol removal capacity compared to FeCl3-modified and non-modified biochars. More specifically, biochar PI-K exhibited the highest adsorption rate compared to biochars PE-K and SD-K, for all adsorbent concentrations tested (Figure 5). A similar trend was also noticed for FeCl3-modified biochars (Figure 6) and non-modified biochars (Figure 4).
- Activated carbon shows almost identical adsorption rates with PI biochar, namely 1.28, 1.20, 0.78, and 0.45 mg·g−1·h−1, for 0.5, 1, 2, and 5 g·L−1, respectively (Figure 4).
Figure 4. Adsorption rates, mg·g−1·h−1, of phenols on biochars PI, PE, and SD for adsorbent concentration 0.5, 1, 2, and 5 g·L−1 (AC: activated carbon, used as reference adsorbent).
Figure 5. Adsorption rates, mg·g−1·h−1, of phenols on biochars PI-K, PE-K, and SD-K for adsorbent concentration 0.5, 1, 2, and 5 g·L−1 (AC: activated carbon, used as reference adsorbent).
Figure 6. Adsorption rates, mg·g−1·h−1, of phenols on biochars PI-F, PE-F, and SD-F for adsorbent concentration 0.5, 1, 2, and 5 g·L−1 (AC: activated carbon, used as reference adsorbent).
Biochar PI-K shows the highest phenol adsorption capacity due to its highest surface area and porosity i.e., 572.4 m2·g−1 and 49.8%, respectively. For biochars exhibiting lower surface area and porosity such as PE-K (397.3 m2·g−1 and 34.7%, respectively) the adsorption capacity decreases accordingly. Similar behavior has been reported by Dai et al. (2013) for biochars produced from wetland plant residues. It is known that the potential of biochar as adsorbent in batch systems depends on its structure, its specific surface area and the available active sorption sites, properties which are affected by modification (Qu et al., 2013).
The main mechanism affecting adsorption of phenols on biochars is most probably the hydrophobic sorption on biochar surface which is also related to their increased carbon content and the number of oxygenated functional groups (Yu et al., 2015; Oh and Seo, 2016). Also aromatic hydrocarbons present in phenols can be covalently bonded to surfaces of biochar (Cornelissen et al., 2005).
Phenol Sorption Isotherm Models
In order to describe adsorption of phenols on biochars, the Freundlich and Langmuir models have been used. The Freundlich model, which assumes a multilayer sorption on heterogeneous adsorbent surface, is described by Equation (3):
where qe (mg·g−1) is the uptake of phenol per unit weight of adsorbent in equilibrium, Ce (mg·L−1) is the equilibrium concentration of phenol in solution, Kf (L·g−1) is the constant related to the adsorption capacity of the adsorbent and 1/n is the constant related to the adsorption intensity.
The Langmuir model, which assumes a monolayer adsorption on a homogenous surface when the adsorbent has a constant number of adsorption sites, is described by Equation (4):
where Ce (mg·L−1) is the equilibrium concentration of phenol in solution, qe (mg·g−1) is the uptake of phenol per unit weight of adsorbent in equilibrium, qmax is the maximum adsorption capacity of the adsorbent (mg·g−1) and b (L·mg−1) is the Langmuir constant related to the energy of the adsorption.
The Freundlich and Langmuir isotherms for phenol adsorption on biochars PI, PE, SD and modified biochars PI-K, PE-K, SD-K or PI-F, PE-F, SD-F, are presented in Figures 7, 8, respectively. The respective equations and the correlation coefficients R2 are also shown in these figures which were prepared using the equilibrium concentration of phenols in solution for four different adsorbent concentrations (Table 4). It is shown that for all investigated biochars the Freundlich model gives a better fit compared to Langmuir model, while the highest R2 values correspond to the PI-K biochar, which shows the highest phenol adsorption efficiency.
Figure 7. Freundlich isotherms for phenols adsorption on biochars PI, PE, SD, and modified biochars PI-K, PE-K, SD-K or PI-F, PE-F, SD-F.
Figure 8. Langmuir isotherms for phenols adsorption on biochars PI, PE, SD, and modified biochars PI-K, PE-K, SD-K or PI-F, PE-F, SD-F.
The Freundlich model describes very well sorption probably due to surface heterogeneity of the produced biochars, including pore size distribution and presence of functional groups (Girods et al., 2009). The Langmuir model is not suitable to describe adsorption of phenols on biochars as also discussed in other relevant studies (Huang and Chen, 2010; Han et al., 2013; Agrafioti et al., 2014).
Thus, the Freundlich Equation (3) for PI-K biochar (logKf = −0.78, 1/n = 1.45) becomes
Three different agricultural wastes, namely pistachio shells, pecan shells and pine wood sawdust were pyrolyzed for the production of biochars which were also chemically modified with the use of 1M KOH or 1M FeCl3 and tested for the removal of phenols from synthetic solutions.
The results of this study show that KOH is a more efficient biochar modifier compared to FeCl3, since it results in increased carbon content, porosity and surface area. Phenols are adsorbed on KOH-modified biochars following the sequence PI-K>PE-K>SD-K.
Modification of PI-biochar with KOH or FeCl3 results in better phenol adsorption efficiency compared to commercial activated carbon.
Porosity and surface area are considered the main parameters that affect biochar properties and thus define their potential in environmental applications, including adsorption of contaminants from solutions. The use of analytical techniques, XRD, SEM, and FTIR, offers significant insights regarding the morphology of the produced biochars in terms of content of organic carbon, degree of homogeneity, and existence of porous structure, factors which determine the number of available active sites and assess their adsorption efficiency.
Finally, kinetic and equilibrium studies show that the pseudo-second order model fits best adsorption kinetics data, while the Freundlich model describes very well adsorption of phenols on biochars.
Both authors listed, have made substantial, direct and intellectual contribution to the work, and approved it for publication.
Conflict of Interest Statement
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
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Keywords: biochar, phenols, chemical modification, adsorption, kinetics, isotherms
Citation: Komnitsas KA and Zaharaki D (2016) Morphology of Modified Biochar and Its Potential for Phenol Removal from Aqueous Solutions. Front. Environ. Sci. 4:26. doi: 10.3389/fenvs.2016.00026
Received: 22 February 2016; Accepted: 22 March 2016;
Published: 08 April 2016.
Edited by:Kerstin E. Scherr, University of Natural Resources and Life Sciences, Austria
Reviewed by:Ioannis Konstantinos Kalavrouziotis, Hellenic Open University, Greece
Teresa Hernandez, Consejo Superior de Investigaciones Científicas, Spain
Copyright © 2016 Komnitsas and Zaharaki. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) or licensor are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Kostas A. Komnitsas, email@example.com