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Article

Photocatalytic Degradation of Humic Acids Using LaFeO3

by
Nazli Turkten
1,†,
Isabella Natali Sora
2,*,
Ayse Tomruk
1 and
Miray Bekbolet
1
1
Institute of Environmental Sciences, Bogazici University, Bebek, Istanbul 34342, Turkey
2
Department of Engineering and Applied Sciences, University of Bergamo, viale Marconi 5, 24044 Dalmine, Italy
*
Author to whom correspondence should be addressed.
†
Current address: Department of Chemistry, Faculty of Science and Arts, Ahi Evran University, Kirsehir 40100, Turkey.
Catalysts 2018, 8(12), 630; https://doi.org/10.3390/catal8120630
Submission received: 6 November 2018 / Revised: 28 November 2018 / Accepted: 4 December 2018 / Published: 6 December 2018
(This article belongs to the Special Issue Environmental Applications of Photocatalytic Processes)
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Abstract

:
TiO2 photocatalytic degradation of dissolved organic matter (DOM), namely humic substances composed of humic (HA) and fulvic acids, has been investigated for decades. However, the application of non-TiO2 photocatalysis for this purpose has only received recent attention. Aiming to fill this gap, this study was performed to elucidate the photocatalytic degradation of HAs using the novel photocatalyst LaFeO3 (LF) under simulated solar light irradiation. HA was selectively fractionated by ultrafiltration to two different molecular size fractions representing high molecular fraction as 100 kDa and lower molecular size fraction comprised of humic components expressing size fractions smaller than 30 kDa. Photocatalyst LF was prepared by the citrate auto-combustion method and characterized by using various techniques and Brunauer–Emmett–Teller (BET) surface area. Ultraviolet-visible (UV-vis) and excitation-emission matrix (EEM) fluorescence spectroscopic features were used to characterize the treated HA and photocatalytic mineralization extend was followed by dissolved organic carbon (DOC) contents. Photocatalytic performance of LF was compared to the metal modified version as Cu-doped LF. Highest mineralization was achieved upon the use of a photocatalyst dose of 0.25 mg/mL of LaFe0.90Cu0.10O3−δ (Cu-LF) for 30 kDaHA, whereas lowest mineralization was attained for 100 kDaHA upon the use of LF. Photocatalytic degradation kinetics indicated the possible use of LF and Cu-LF for the degradation of HA.

Graphical Abstract

1. Introduction

Humic substances (HS) comprise the major fraction of natural dissolved organic matter (DOM) and are defined as a category of naturally occurring, biogenic, heterogeneous organic substances that can be generally characterized as being yellow-to-black in color, and of high molecular weight refractory organics [1]. Major fraction of HS is referred to as humic acids (HAs) that are “dark-colored organic molecules that can be extracted from soil by dilute alkali and other reagents and is insoluble in dilute acid” [2]. According to a general understanding, HAs are collections of diverse molecular mass (1–300 kDa) organic molecules forming dynamic supramolecular associations stabilized by hydrophobic interactions and hydrogen bonds. Therefore, their interactions with natural water constituents should be addressed as non-specific molecular size dependent reactivities leading to various manifold reactions.
Due to the adverse environmental significance of DOM in natural waters, removal of DOM by advanced oxidation techniques has been extensively studied under solar light irradiation [3,4,5,6,7]. In this field, TiO2 photocatalysis has been widely used for the removal of DOM, and more specifically, humic and fulvic acids [8,9]. Although TiO2 nanomaterials express superior parameters as being photo-stable, cheap, and non-toxic, they also pose major disadvantages due to the wide band-gap (anatase Ebg = 3.2 eV and rutile Ebg = 3.0 eV) and fast recombination rate of photo-generated electrons and holes. In order to overcome UV light limitations, various methods were developed to modify TiO2 to extend light absorption efficiency to visible region [10]. Recent interest was also diverted to the understanding of non-TiO2 photocatalysts more specifically perovskites in comparison to TiO2 [11].
A review of the photocatalytic performance of visible light active perovskites was presented emphasizing on advantages and limitations [12]. LaFeO3 (LF) has been developed for the degradation of pollutants as well as hydrogen evolution under visible light. LF with a typical ABO3-type perovskite structure (A is usually a rare earth and B is a transition metal) has proven to be effective on catalytic reactions owing to its significant properties as high stability and nontoxicity [13,14]. Furthermore, La ferrites, either sole or modified with various doping elements i.e., Cu, Sr, has been extensively investigated by Natali Sora et al. [15,16,17,18,19,20,21,22,23,24,25]. Focusing on specific application of La ferrites, reduction in eco-toxic effects of micropollutants was achieved via photocatalytic degradation [26].
Characterization of LF and LaFe0.90Cu0.10O3−δ (Cu-LF) samples was reported previously and summarized as follows [21]. X-rays diffraction (XRD) patterns of the LF and Cu-LF samples revealed an orthorhombic single phase. XRD crystallite sizes of the perovskite phases calculated using Scherrer equation were 43 and 35 nm for LF and Cu-LF samples, respectively. Specific surface areas were determined as 13 and 16 m2/g for LF and Cu-LF, respectively. Scanning electron microscope (SEM) images of LF and Cu-LF displayed almost spherical agglomerates of particles. Optical band-gap Ebg of LF and Cu-LF samples were estimated assuming a direct allowed transition by extrapolating a linear fitting in the Tauc plot. LF sample exhibited Ebg = 2.56–2.64 eV, and Cu-LF sample Ebg = 2.51–2.58 eV. These values indicated the possibility of using simulated solar light for the degradation of natural organic matter. In an XPS analysis of the samples, the presence of peak centered at circa 710.5 eV corresponded to Fe 2p3/2 showing Fe(III) ions in the oxidizing environment. The binding energy for O1s was obtained at 529.2 eV and a weak second peak at circa 531 eV that might be assigned to a hydroxylation and/or carbonation at the perovskites surface. In the C1s spectrum, a weak second peak at circa 289.4 eV was detected that might be associated with the formation of surface carbonates.
LF has been shown to express narrow band-gap energy leading to successful utilization as a semiconductor material for photocatalysis [27,28,29]. Shape-dependent photocatalytic activity of LF had been elucidated under visible light irradiation using rhodamine black dye as the model compound [30]. Material preparation and activity testing using common dyes, i.e., rhodamine B [31]; methyl orange [32]; and methylene blue [33] were presented. In general, LF photocatalyst has been applied for the degradation of various organics expressing diverse chemical compositions; however, neither of the organics could be regarded as representatives of building blocks or sub-compounds of humic matter [34].
Upon the use of LF specimens under light irradiation, the prevailing reaction mechanism indicating the primary reactions leading to the formation reactive oxygen species (ROS) has not been investigated in detail. Based on the experimental results, •OH and •O2− were reported as the main active species causing degradation of a model dye compound [35]. Primary e-/h+ pair formation mechanism was expressed upon the use of a LaFeO3/TiO2 composite under visible light irradiation [32].
The use of LF as a non-TiO2 photocatalyst had not been reported so far for the removal of DOM and its analog compounds to the best of our knowledge. Therefore, HA was chosen as a representative compound of DOM that was further processed to lower molecular size fractions to represent diverse sub-groups displaying different chemical compositions. Solar photocatalytic degradation of HA was investigated by using LF and Cu-LF. With the aim of determining the photocatalytic degradation kinetics, degradation rates of HA fractions were elucidated by UV-vis spectral analysis and DOC parameters. Organic matter characterization was further extended to EEM (excitation-emission matrix) fluorescence features.

2. Results and Discussion

2.1. Photocatalytic Degradation of HA

DOC contents of the HA samples were 7.89 mg/L and 2.60 mg/L for 100 kDaHA and 30 kDaHA fractions, respectively. As expected, the UV-vis spectroscopic parameters (absorbance values) for both molecular size fractions followed the general trend UV254 > UV280 > UV365 > Color436 [36]. As an indicator parameter of aromaticity, CbUV254 (carbon based UV254, L/mg m) values were 9.47 and 6.89 for 100 kDaHA and 30 kDaHA, respectively. 100 kDaHA expressed more aromatic character, as expected. Expressing the ratio of aromaticity to color forming moieties, UV280/Color436 values were 5.14 and 5.35 for 100 kDA and 30 kDaHA, respectively [37,38].
Photocatalytic degradation profiles of 100 kDaHA and 30 kDaHA were assessed upon irradiation periods of 0–60 min using 0.25 mg/mL and 0.50 mg/mL catalyst doses. Under all conditions, UV-vis spectra retained a humic-like profile displaying a decreasing logarithmic trend with respect to increasing wavelength (Figure 1). Upon the use of LF, UV-vis spectroscopic profiles expressed distinctly different removal kinetics for both of the HA molecular size fractions irrespective of the applied dose. As could be visualized from the spectra, color forming moieties (λ > 400 nm) were significantly removed in comparison to UV absorbing centers upon an irradiation period of 60 min. An extended irradiation period up to 120 min resulted in extensive removal of all UV-vis parameters although complete mineralization could not be attained (<20%). A different behavior was found with Cu-LF; the effect of photocatalyst dose was more significant in comparison to humic organic matter content and molecular size fraction. Surface interaction should be expected to play a major role prior to the initiation of the photocatalysis. UV absorbing centers (λ < 400 nm) were still evident under all conditions upon the use of Cu-LF, whereas color forming moieties (λ > 450 nm) were still evident upon the use of 100 kDaHA in the presence of both doses as 0.25 mg/mL and 0.50 mg/mL in comparison to the lower molecular size fraction of HA at 30 kDaHA.
Instantaneous adsorption occurring upon the introduction of the photocatalyst specimens to the humic solution (t = 0 condition) indicated prevailing surface interactions prior to the initiation of photocatalytic treatment fulfilling the prerequisite of surface adsorption. Based on the UV254 parameter, a comparative evaluation could be assessed as follows: (i) upon the use of 0.25 mg/mL LF (13.60% 100 kDaHA and 18.42% 30 kDaHA), surface coverage extent due to the increase in humic molecular size could not be regarded as significant, (ii) upon an increase in dose to 0.50 mg/mL (38.52% 100 kDaHA and 29.02% 30 kDaHA), 100 kDaHA was more prone to surface attractions, (iii) Cu-LF dosage did not considerably affect the initial adsorption being more significant for 30 kDaHA (46.83% for 0.25 mg/mL and 51.28% for 0.50 mg/mL) in comparison to 100 kDaHA (10.79% for 0.25 mg/mL and 16.08% for 0.50 mg/mL). Lower molecular size HA fractions could contain more functional groups composed of carboxylic (pKa 3–5) and phenolic groups (pKa > 8) that could be considered as partially deprotonated open to exposure to photocatalyst surface via electrostatic attractions. It has been reported that the point of zero charge (PZC) of LF was 8.9 [39]. At solution pH values lower than the PZC value (as in this case pH 6–7), the adsorbent surface was positively charged attracting negatively charged species. The negatively charged deprotonated humic groups, formed in the aforementioned pH range, could be the dominant groups that interacted with the catalyst surface. It should also be mentioned that under all conditions, adsorption extent was <50% excluding extensive surface coverage that could diminish light absorption leading to retardation of degradation efficiency.
UV280/Color436 variations expressed inconsistent trends with respect to both photocatalyst type and dose revealing diverse role of absorption centers. Although the extent of initial surface coverage by humic sub-fractions could be regarded as sufficient for initiation of photocatalysis, a plausible reaction mechanism could not be attributed to any specific role of aromatic centers or color forming moieties under the specified experimental conditions. Moreover, upon photocatalysis a higher photocatalyst dose was more effective for the removal of both absorption centers. The most significant UV280/Color436 decrease was attained for 30 kDaHA in the presence of 0.50 mg/mL Cu-LF contrary to the removal percentage of DOC (Table 1 and Table 2).
Photocatalytic degradation kinetics of 30 kDaHA using 0.25 mg/mL LF as well as Cu-LF were modeled [40] by a pseudo first-order kinetic model (R2 > 0.80). Kinetic model parameters were discussed in a comparative manner with respect to the role of humic properties (Table 1).
The use of an LF catalyst with 0.25 mg/mL for the removal of 30 kDaHA presented an order of k as follows: 8.54 × 10−3 Color436, 1.08 × 10−2 UV365, 1.10 × 10−2 UV280, and 1.16 × 10−2 UV254 in comparison to DOC removal 1.17 × 10−2 min−1. Half-life (t1/2, min) values displayed the same order as Color436, UV365, UV280, and UV254. However, a similar trend could not be assessed for Cu-LF specimens under solar light simulated conditions. The removal of 30 kDaHA in the presence of Cu-LF resulted in the following values of the kinetic constant: 2.05 × 10−2 Color436, 2.13 × 10−2 UV365, 1.96 × 10−2 UV280, and 1.92 × 10−2 min−1 UV254. Degradation rate constants expressed a decreasing order as UV365 > Color436 > UV280 > UV254, whereas DOC removal was attained as 9.05 × 10−3 min−1. As expected, half-life values followed the same trend. Both color forming moieties and UV absorbing centers were removed concomitantly in the case of Cu-LF, whereas upon the use of LF UV absorbing centers were removed preferentially.
Table 2 summarizes the removal percentages of the UV-vis parameters and DOC as well as CbUV254 and the Fluorescence Index. After 60 min of simulated solar irradiation, the resulting DOC content was sufficient to enable UV-vis and fluorescence measurements. A fast DOC removal of 30 kDaHA was reached with 0.25 mg/mL Cu-LF and considerably slower removal upon use of 0.50 mg/mL of Cu-LF. For 100 kDaHA, the best performance was achieved using 0.25 mg/mL Cu-LF. The highest mineralization was achieved for 30 kDaHA upon use of 0.25 mg/mL Cu-LF whereas lowest mineralization was attained for 100 kDaHA upon use of 0.25 mg/mL LF.
Removal percentages could also be compared to the dose dependent exposed surface area of LF and Cu-LF (Figure 2). The DOC parameter was selected under initial exposure (DOCads, t = 0) and following treatment (DOCrem, tirr = 60 min) conditions. Since the surface areas of LF (13 m2/g) and Cu-LF (16 m2/g) were not significantly different from each other, extensive surface coverage were not expected for either of the photocatalyst specimens and HA samples prior to initiation of light exposure. Incremental increase of exposed surface area could not be directly related to the initial adsorption of DOC for both of the photocatalyst specimens and HA samples. It could be indicated that surface attractions could be most probably occurring via different reaction pathways due to the presence and absence of Cu dopant. On the other hand, the presence of the higher molecular size fraction of HA (100 kDaHA) displayed a more influential effect on mineralization of organic content with increasing surface area of Cu-LF in comparison to LF.
Since UV254 was regarded as a surrogate parameter of DOC, the carbon based parameter (CbUV254) could be used for the assessment of simultaneous removal of UV absorbing aromatic centers in accordance with mineralization efficiency [9]. 30 kDaHA expressed a decreasing tendency of aromaticity (CbUV254 < 4) upon the use of both LF and Cu-LF specimens excluding a lower dose as 0.25 mg/mL LF. However, 100 kDaHA retained an organic matrix composition expressing aromaticity as CbUV254 > 4. Furthermore, the data did not impress a significant correlation between UV254 and DOC removals as attained upon the use of TiO2 [9]. Moreover, no significant correlation could be attained for CbColor436, CbUV365, and CbUV280 parameters with the DOC removal efficiencies. These results indicated that the diverse and complex nature of the humic subgroups present in different molecular size fractions could possibly lead to various surface interactions during the course of the degradation reactions under oxidative conditions. FI did not significantly change under all experimental conditions revealing the simultaneous removal of humic and fulvic like fluorophoric centers within the humic matter as will be further addressed by EEM contour plots. The effect due to the extended irradiation periods at 90 min and 120 min resulted in an enhancement of DOC removal efficiencies being more significant in Cu-LF specimens as ≤10% in comparison to LF upon use of 30 kDaHA.
Photocatalyst stability was assessed through leaching experiments under the specified experimental conditions as t = 0 and under solar light in the absence of humic acid. No significant amount of Fe, Cu, and La was determined with respect to the lowest limit of quantification values as Fe = 0.05 mg/L; Cu = 0.03 mg/L; La = 0.1 mg/L. Only a slight increase in nitrate (<0.03 mg/L) was observed. The reason could be attributed to the usage amount of Fe(NO3)3·9H2O for the preparation of LF.

2.2. EEM Fluorescence Properties

Use of EEM fluorescence contour plots has been shown to be a versatile tool for visualization of the removal of humic-like and fulvic like fluorophores and formation of fragmentation products [37,41]. Depending on the excitation-emission wavelength regions, five regions were ascribed as (i) Region I: Aromatic Proteins I (λexc 220–250 and λemis 280–332), (ii) Region II: Aromatic Proteins II (λexc 220–250 and λemis 332–380), (iii) Region III: Fulvic-like (λexc 220–250 and λemis 380–580), (iv) Region IV: Microbial by-products (λexc 250–470 and λemis 280–380), and (v) Region V: Humic-like (λexc 250–470 and λemis 380–580). EEM fluorescence matrix contour plots of humic acids under initial, initial adsorption and following treatment for an irradiation period of 60 min were presented (Figure 3 and Figure 4). From a general perspective, EEM fluorescence plots of humic acid upon treatment by using LF and Cu-LF mainly indicated the presence of humic-like and fulvic-like fluorophores under all conditions.
In the presence of 30 kDaHA and 0.25 mg/mL photocatalyst, initial adsorptive interactions (t = 0) onto either LF or Cu-LF resulted in slight variations in regional speciation of fluorophores. Following photocatalysis (tirr = 60 min), subsequent to successive removal of all fluorophoric groups, no significant variation in regional distribution could be observed. An increasing photocatalyst dose to 0.50 mg/mL resulted in the removal of both humic-like and fulvic like fluorophores in accordance with UV254 and DOC removals. This effect was more pronounced in the case of Cu-LF in comparison to LF. No further shift to other fluorophoric groups composed of aromatic proteins as well as microbial by-products could be observed.
In the presence of 100 kDaHA and 0.25 mg/mL photocatalyst, initial adsorptive interactions (t = 0) onto Cu-LF was significantly different in comparison to LF. Doubling the photocatalyst dose to 0.50 mg/mL resulted in removal of fulvic-like fluorophores more significantly. This trend was found to be consistent for an irradiation period of 60 min. In a similar fashion, presence of other fluorophoric groups composed of aromatic proteins (Regions I and II) as well as microbial by-products (Region IV) could not be observed upon irradiation period of 60 min. The reason could be attributed to concomitant removal of humic-like and fulvic-like fluorophores via mineralization. It should also be mentioned that 100 kDaHA exhibited higher UV254 and DOC contents in comparison to 30 kDaHA. Role of Cu-doping was more significant irrespecitve of the applied dose during photoatalysis.
From a general perspective [41], upon oxidative treatment of humic acids through degradation and fragmentation along with a shift to lower molecular size fractions, simultaneous removal of all molecular size fractions could also be expected [42]. The resultant organic matrix could retain fractions expressing major fluorophoric regions. Since no leaching of La, Fe or Cu was observed, decrease in fluorescence intensities could not be related to the fluorescence quenching due to metal complexation.

3. Materials and Methods

3.1. Materials and Analytical Methodology

HA was purchased from Aldrich (Sigma-Aldrich, St. Louis, MO, USA) as sodium salt and the 50 mg/L stock solution was prepared in ultra-pure water (18.2 MΩ cm at 25 °C). 100 kDa (100 kDaHA) and 30 kDa (30 kDaHA) molecular size fractions were prepared by filtration through 0.45 μm cellulose acetate membrane filter (Millipore) followed by ultrafiltration process using Amicon 8050 ultrafiltration stirred cell unit (EMD Millipore Corporation, Billerica, MA, USA) using membrane filters with 100 kDa and 30 kDa cut-offs [36]
Organic matrix characterized by dissolved organic carbon contents (DOC, mg/L) was determined as non-purgeable organic carbon using Total Organic Carbon Analyzer Shimadzu TOC VWP (Kyoto, Japan). Calibration was done by using potassium hydrogen phthalate (99.95%, Sigma-Aldrich, St. Louis, MO, USA) in low range as 0–20 mgOrgC/L (R2 > 0.99).
UV-vis spectroscopic measurements were performed using Perkin Elmer Lambda 35 UV-vis double beam spectrophotometer (Waltham, MA, USA) employing quartz cuvettes of 1.0 cm optical path length in the wavelength range of 200–600 nm and expressed as absorbance values (cm−1) at specified wavelengths of 436 nm (Color436), 365 nm (UV365), 280 nm (UV280), and 254 nm (UV254). Specific absorbance ratio as UV280/Color436 and carbon based spectroscopic parameters as CbColor436, CbUV365, CbUV280, and CbUV254 (L/mg m) were presented [38,43].
Fluorescence spectroscopic measurements were carried on Perkin Elmer LS 55 Luminescence Spectrometer (Waltham, MA, USA) equipped with a 150 W Xenon arc lamp using quartz cell. Three-dimensional excitation-emission matrix (EEM) contour plots were created by plotting fluorescence intensity as a function of emission (x-axis) and excitation (y-axis) wavelengths using Matlab R2013a. Fluorescence index (FI) was expressed as the ratio of the emission intensity at λemis 450 nm to that at λemis 500 nm, following excitation at λexc 370 nm [3]
Lanthanum ferrite LaFeO3 (LF) and Cu doped LF as LaFe0.90Cu0.10O3−δ (Cu-LF) were prepared by citrate autocombustion method [15].
Leaching of La, Fe, and Cu was followed by ICP-OES (Perkin Elmer Optima 2100DV ICP-OES, Waltham, MA, USA). Anion contents (chloride, nitrite, nitrate, sulfate and phosphate) were determined by using an ion chromatography (DIONEX ICX-3000).

3.2. Photocatalytic Degradation Experiments

Photocatalytic degradation experiments were carried out using an ATLAS Suntest CPS+ simulator (Atlas, IL, USA) equipped with an air cooled Xenon lamp (250 W/m2 and wavelength range of 300–800 nm) as the light source (Ref. 56052371, Atlas CPS+ Solar Simulator). The 50 mL 30 kDaHA and 100 kDaHA samples were subjected to photocatalytic degradation in the presence of 0.25 and 0.50 mg/mL doses. Photocatalyst dose was selected considering the expected extent of initial adsorption (t = 0) of humic sub-fractions onto the photocatalyst surface. Since 30 kDa and 100 kDa humic molecular size fractions are comprised of various sub-fractions displaying diverse functional groups that could be deprotonated depending on the pH of the reaction medium, different adsorption behaviors could be expected (as explained in Section 2.1). Moreover, pH of the reaction was not changed, neither to acidic (coiled/ condensed) nor to alkaline (extended/linear), since humic molecular size fractions might express different conformational orientations. Therefore, reaction conditions would change in an uncontrollable manner that could also lead to meaningless comparisons. Initial adsorption of humic fractions was determined upon instantaneous introduction onto photocatalyst specimen (t = 0 condition) and no further dark interaction was attained upon prolonged exposure periods. Photocatalytic experiments were performed for irradiation period of 0–120 min with 10 min intervals. Samples were subjected filtration through 0.45 μm membrane filter prior to all analysis.

4. Conclusions

This study was performed to investigate the photocatalytic performance of novel photocatalysts i.e., LaFeO3 perovskite (LF) and copper lanthanum ferrite (Cu-LF). Based on the presented data, photocatalytic degradation kinetics indicated the possible use of LF and Cu-LF for the degradation of humic acids as the model compound of DOM. Furthermore, the dose effect of the respective LF and Cu-LF specimens could be related to the surface interactions in relation to the presence of the organic matter contents expressed by different molecular size fractions. Highest mineralization was achieved upon use of photocatalyst dose as 0.25 mg/mL of Cu-LF for 30 kDaHA, whereas lowest mineralization was attained for 100 kDaHA upon use of LF. Following photocatalytic degradation of humic matter, organic matrix was further characterized by EEM fluorescence contour plots. Upon exposure to solar irradiation for 60 min, organic matrix retained humic-like and fulvic-like fluorophores excluding the formation of new fluorophoric groups that could signify destructive fragmentation products via photocatalysis. It could be emphasized that humic acids are comprised of complex and polydisperse organic compounds with undefined molecular structures; therefore, the attained results holds prime importance in comparison to the simple compounds that are used as models for activity testing. This study brings significant baseline information on the successful utilization of non-TiO2 photocatalysts for degradation of refractory organic compounds present in natural waters as well as wastewaters upon solar light exposure.

Author Contributions

I.N.S. and M.B. conceived and designed the experiments; I.N.S., A.T., and N.T. performed the experiments; I.N.S., N.T., and M.B. analyzed the data; I.N.S., N.T., and M.B. wrote the paper.

Funding

Financial support, provided by Research Fund of the Bogazici University through Project No: 13381, and the University of Bergamo, is gratefully acknowledged.

Conflicts of Interest

The authors declare no conflict of interest.

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Catalysts 08 00630 g001 550
Figure 1. (UV-vis) absorption spectra (left column) and UV280/Color436 (right column) variations humic acid (HA) samples upon the use of an LaFeO3 (LF) specimen in comparison to Cu-LF, recorded for initial t = 0 and t = 60 min irradiation conditions.
Figure 1. (UV-vis) absorption spectra (left column) and UV280/Color436 (right column) variations humic acid (HA) samples upon the use of an LaFeO3 (LF) specimen in comparison to Cu-LF, recorded for initial t = 0 and t = 60 min irradiation conditions.
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Figure 2. Dose dependent DOCads and DOCrem in comparison to exposed surface area (S.A).
Figure 2. Dose dependent DOCads and DOCrem in comparison to exposed surface area (S.A).
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Figure 3. EEM fluorescence contour plots of 30 kDaHA upon use of LF and Cu-LF.
Figure 3. EEM fluorescence contour plots of 30 kDaHA upon use of LF and Cu-LF.
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Figure 4. Excitation-emission matrix (EEM) fluorescence contour plots of 100 kDaHA upon use of LF and Cu-LF.
Figure 4. Excitation-emission matrix (EEM) fluorescence contour plots of 100 kDaHA upon use of LF and Cu-LF.
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Table
Table 1. Kinetic parameters of photocatalytic degradation of 30 kDaHA sample using LF and Cu-LF, dose 0.25 mg/mL.
Table 1. Kinetic parameters of photocatalytic degradation of 30 kDaHA sample using LF and Cu-LF, dose 0.25 mg/mL.
Photocatalyst SpecimenColor436UV365UV280UV254DOC
Rate m−1/mint½ minRate m−1/mint½ minRate m−1/mint½ minRate m−1/mint½ minRate m−1/mint½ min
LF2.2 × 10−4815.4 × 10−4641.4 × 10−3631.7 × 10−3603.0 × 10−260
Cu-LF1.7 × 10−3342.4 × 10−3332.8 × 10−3355.1 × 10−3363.1 × 10−277
Table
Table 2. Removal percentages of UV-vis parameters and DOC in relation to CbUV254 (carbon based UV254) and Fluorescence Index upon an irradiation period of 60 min.
Table 2. Removal percentages of UV-vis parameters and DOC in relation to CbUV254 (carbon based UV254) and Fluorescence Index upon an irradiation period of 60 min.
SampleRemoval %CbUV254 L/mg mFluorescence Index
Color436UV365UV280UV254DOC
30 DaHA-----6.891.04
LF, 0.25 mg/mL40.847.849.751.054.57.441.12
LF, 0.50 mg/mL68.270.970.871.852.74.111.18
Cu-LF, 0.25 mg/mL70.272.570.068.456.33.031.36
Cu-LF, 0.50 mg/mL47.958.963.463.837.51.731.17
100 kDaHA-----9.470.992
LF, 0.25 mg/mL32.731.032.031.626.212.41.06
LF, 0.50 mg/mL64.668.466.867.643.87.701.10
Cu-LF, 0.25 mg/mL10.822.730.030.045.312.11.08
Cu-LF, 0.50 mg/mL14.628.137.438.538.29.411.11

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Turkten, N.; Natali Sora, I.; Tomruk, A.; Bekbolet, M. Photocatalytic Degradation of Humic Acids Using LaFeO3. Catalysts 2018, 8, 630. https://doi.org/10.3390/catal8120630

AMA Style

Turkten N, Natali Sora I, Tomruk A, Bekbolet M. Photocatalytic Degradation of Humic Acids Using LaFeO3. Catalysts. 2018; 8(12):630. https://doi.org/10.3390/catal8120630

Chicago/Turabian Style

Turkten, Nazli, Isabella Natali Sora, Ayse Tomruk, and Miray Bekbolet. 2018. "Photocatalytic Degradation of Humic Acids Using LaFeO3" Catalysts 8, no. 12: 630. https://doi.org/10.3390/catal8120630

APA Style

Turkten, N., Natali Sora, I., Tomruk, A., & Bekbolet, M. (2018). Photocatalytic Degradation of Humic Acids Using LaFeO3. Catalysts, 8(12), 630. https://doi.org/10.3390/catal8120630

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