Scholarly article on topic 'Removal of Organic Matter from Landfill Leachate by Advanced Oxidation Processes: A Review'

Removal of Organic Matter from Landfill Leachate by Advanced Oxidation Processes: A Review Academic research paper on "Chemical engineering"

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Academic research paper on topic "Removal of Organic Matter from Landfill Leachate by Advanced Oxidation Processes: A Review"

Hindawi Publishing Corporation International Journal of Chemical Engineering Volume 2010, Article ID 270532, 10 pages doi:10.1155/2010/270532

Review Article

Removal of Organic Matter from Landfill Leachate by Advanced Oxidation Processes: A Review

Wei Li,1 Qixing Zhou,1 and Tao Hua12

1 Key Laboratory of Pollution Process and Environmental Criteria (Ministry of Education), College of Environmental Science and Engineering, Nankai University, Tianjin 300071, China

2 TEDA Environmental Protection Co. Ltd., Tianjin 300350, China

Correspondence should be addressed to Qixing Zhou, Received 15 January 2010; Accepted 12 April 2010 Academic Editor: Josiane Nikiema

Copyright © 2010 Wei Li et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

In most countries, sanitary landfill is nowadays the most common way to eliminate municipal solid wastes (MSWs). However, sanitary landfill generates large quantity of heavily polluted leachate, which can induce ecological risk and potential hazards towards public health and ecosystems. The application of advanced oxidation processes (AOPs) including ozone-based oxidation, Fenton oxidation, electrochemical oxidation, and other AOPs to treatment of landfill leachate was reviewed. The treatment efficiency in term of chemical oxygen demand (COD) of various AOPs was presented. Advantages and drawbacks of various AOPs were discussed. Among the AOPs reviewed, Fenton process should be the best choice, not only because it can achieve about 49-89% of COD removal with COD ranging from 837 to 8894 mg/L, but also because the process is cost-effective and simple in technological aspect, there is no mass transfer limitation (homogeneous nature) and both iron and hydrogen peroxide are nontoxic.

1. Introduction

Due to rapid economic development in recent years, the excessive generation of municipal solid wastes (MSWs) has been identified as one of the most serious environmental problems in the world which needs to be addressed urgently for environmental protection. Up to 95% total MSW collected worldwide is disposed using the landfilling method [1]. After landfilling, solid waste undergoes a series of physicochemical and biological changes. Consequently, the degradation of the organic fraction of the wastes in combination with percolating rainwater leads to the generation of a highly contaminated liquid called "leachate". Leachate may contain large amount of organic matter (biodegradable, but also refractory to be biodegraded), ammonia-nitrogen, heavy metals, and chlorinated organic compounds and inorganic salts.

The characteristics of landfill leachate are affected by many factors, such as age, precipitation, weather variation, and waste types and compositions. In particular, the composition of landfill leachate varies greatly depending on the age

of the landfill [2]. According to the landfill age, the leachate can be classified into three types: young, intermediate, and old, and the relationship of the characteristics of landfill leachate versus the age of landfill is summarized in Table 1 [3, 4]. The young landfill leachate is commonly characterized by high biochemical oxygen demand (BOD) (4000-13,000 mg/L) and chemical oxygen demand (COD) (30,000-60,000 mg/L), moderately high content of ammonium nitrogen (500-2000 mg/L), high ratio of BOD/COD (ranging from 0.4 to 0.7), and low pH values (as low as 4.0), with biodegradable volatile fatty acids (VFAs) appear to be its major constituents [5]. With an increase in the landfill age and decomposing of VFAs in the landfill leachate by anaerobe bacteria over a period of 10 years, the old leachates are catalogued as stabilized and characterized by a relatively low COD (<4000 mg/L), slightly basic pH (7.5-8.5), low biodegradability (BOD5/COD < 0.1), and high molecular weight compounds (humic substances) [6].

Toxicity analysis carried out using various test organisms such as Vibrio fisheri, Daphnia similes, Artemia salina, and Brachydanio rerio has confirmed that the potential dangers

Table 1: Landfill leachate classification versus age [3,4].

Type of leachate Young Intermediate Old

Age (years) <5 5-10 >10

pH <6.5 6.5-7.5 >7.5

COD (mg/L) >10,000 4000-10,000 <4000

BOD5/COD 0.5-1.0 0.1-0.5 <0.1

Organic compounds 80% volatile fatty acids (VFA) 5%-30% VFA + humic and fulvic acid Humic and fulvic acids

Ammonia nitrogen (mg/L) <400 N.A >400

TOC/COD <0.3 0.3-0.5 >0.5

Kjeldahl nitrogen (g/L) 0.1-0.2 N.A N.A

Heavy metals (mg/L) Low to medium Low Low

Biodegradability Important Medium Low

of landfill leachate [7-10] and the necessity to treat is so as to meet the standards for discharge in receiving waters. Laboratory studies to determine the effectiveness of various biological, physical, and chemical treatment processes on landfill leachate have been investigated since the early 1970s. Biological treatment processes, including anaerobic and aerobic processes, are quite effective for leachate generated in the early stage with a high BOD5/COD. However, they generally fail to treat a leachate with a rather low BOD5 /COD, or high concentration of toxic metals [11]. Hence, physical-chemical processes are mostly used for pretreatment or full treatment for this type of landfill leachate.

Among the various types of physical-chemical treatments, advanced oxidation processes (AOPs) has been reported as one of the most effective method to degrade a variety of refractory compounds in landfill leachate [12]. This can be attributed to the role of a highly reactive radical intermediate such as hydroxyl radical (•OH) as an oxidant. The radicals can be produced in ozone oxidation, Fenton oxidation, and electrochemical oxidation systems.

With an oxidation potential (E0) of 2.80 V (Table 2), the • OH radical can rapidly degrade recalcitrant organics such as aromatic, chlorinated, and phenolic compounds [13]. Once a reaction of the free radical is initiated by ozone or H2O2, a series of oxidation reactions occurs in the solution and the radicals rapidly react with most of the target compounds. The kinetic rate of AOPs depends on the concentration of radicals and pollutants, temperature as well as the presence of scavengers such as bicarbonate ion [14].

2. Treatment of Landfill Leachate via AOPs

2.1. Ozone-Based Oxidation Processes. Ozonation processes are attractive means for the treatment of landfill leachates due to the high oxidative power that ozone possesses [15]. As one of the most powerful oxidants with an oxidation potential (E0) of 2.08 V (Table 2), ozonation alters the molecular structure of refractory organic compounds in landfill leachate, turning them into compounds that are easily assimilated biologically [16].

Depending on the pH values, which play major roles in the ozone decomposition, ozone oxidation follows the two

Table 2: Oxidizing potential of some oxidizing agents [13].

Type of oxidizing agents Oxidation potential (E0) (V)

Fluorine 3.06

Hydroxyl radical 2.80

Oxygen (atomic) 2.42

Ozone 2.08

Hypochlorite 1.49

Hydrogen peroxide 1.78

Chlorine 1.36

Chlorine dioxide 1.27

Oxygen (molecular) 1.23

main pathways: either a direct electrophilic attack of the ozone molecule to the recalcitrant pollutants or a generation of •OH radicals due to the ozone decomposition process and followed by a subsequent attack of the radicals on the pollutants [17].

At an acidic pH range, ozone undergoes selective electrophilic attack on the specific part of the organic compounds that have C=C bonds and/or aromatic ring [18] and decomposes them into carboxylic acid and aldehydes as the end products [19]. When exposed to the pH values ranging from 8.0 to 9.0, in the presence of OH-ions, the hydroxide ion reacts with ozone to yield superoxide anion radicals (^O2-), which in their turn are involved in a series ofreactions as follows:

Initiation O3 + OH- • O2- + HO2^, Radical chain-reaction O3 + ^O2- —► • O3-1 + O2, • O3-1 — • OH + O2, •OH + O3 — HO2 • +O2 — HO4^, (1)

HO4 • — ^O2- +O2, HO2^ — ^O2- +H+, Termination HO4 • +HO4^ — H2O2 +2O3. Overall, 1 mol of O3 yields 1 mol of •OH.

When pH is higher than 9.0, oxidation through the formation of »OH radical is limited by the presence of ozone-resistant compounds or »OH radical scavengers. Under such condition, bicarbonate ions are converted to carbonate ions, which are the scavengers for »OH radicals that slow down the kinetic rate of the oxidation reaction [17]. The corresponding equation is listed as follows:

»OH + P —► end products, (2)

where P represents the scavenger of hydroxyl radicals such as HCO3- and CO32-. Some examples of the reactions are presented as follows:

»OH + CO32- —► OH- + CO3»-,

»OH + HCO3- — OH- +HCO3».

As a single process, oxidation with ozone is not considered as very effective due to the complexity of leachate composition, high ozone doses are often required and the respective reaction may take longer time, rendering this process economically unfavorable [20]. Ozone processes can be made more effective by employing UV irradiation (O3/UV) or the addition of hydrogen peroxide (O3/H2O2). UV and H2O2 initiate a series of radical reactions that enhance ozone decomposition to yield »OH [21]. In the O3/UV process, UV irradiation not only activates the ozone molecules by absorbing the UV light at 254 nm, but also makes other organic molecules susceptible to the oxidation process [22]. The initial step of the radical mechanism in this process is the direct photolysis of the ozone to produce »OH, as shown in the following reactions [23]:

O3 + H2O + hv H2O2 + O2,

H2O2 + hv 2 »OH.

And the net reaction is

O3 + H2O + hv —► 2 »OH + O2. (5)

On the other hand, in the O3/H2O2 system, the addition of H2O2 can accelerate the decomposition of ozone and subsequently enhance the production of »OH radicals, as (6):

2O3+H2O2 2 »OH + 3O2. (6)

The reactions involved are very complex in the systems, since the organic compounds can be degraded either by direct ozonation, photolysis reaction, or »OH oxidation [17].

Performance of O3, O3/H2O2, and O3/UV process can be evaluated thanks to key parameters (COD, BOD, BOD/COD, and oxidant dose) summarized in Table 3. As previously mentioned, ozonation as a single process was not considered as very effective (COD reduction is about 15-50%) [15, 16, 24-29]. Thus, most researchers used ozonation process as pretreatment before biological treatment or tertiary treatment prior to discharge in the environment. COD reduction can be greatly enhanced via combining oxidants (H2O2/O3) (Table 3). Wable etal. [28] and Schulteetal. [30] reported the

efficiency of organic matter removal can be up to 95% and 97%, respectively. However, adding an irradiation system (UV/H2O2) was not as efficient as H2O2/O3 system, with COD reduction at a range between 40% and 63%.

The common drawback of ozone-based oxidation is the high demand of oxidant (O3 or H2O2) and the electrical energy used by UV lamps, which results in rather high treatment costs. However, ozone-based oxidation can improve the biodegradability of landfill leachate (Table 3). Using ozone-based oxidation as pretreatment of biological treatment can lower the cost.

2.2. Fenton Oxidation. Fenton process has been extensively studied in recent years, and analyses indicate Fenton process to be one of the most cost-effective alternatives for this application [37]. In the Fenton process, hydrogen peroxide is added to wastewater in presence of ferrous salts, generating species that are strongly oxidative with respect to organic compounds. »OH is traditionally regarded as the key oxidizing species in the Fenton processes. The classical Fenton free radical mechanism in the absence of organic compounds mainly involves the sequence of reactions below [38]:

Fe2+ + H2O2 — Fe3+ + .OH + OH", (7)

Fe3+ + H2O2 — Fe2+ + HO.2+H+, (8)

• OH + H2O2 — HO.2+H2O, (9)

• OH + Fe2+ — Fe3+ + OH~, (10)

Fe3+ + HO»2 — Fe2+ + O2H+, (11)

Fe2+ + HO»2 + H+ — Fe3+ + H2O2, (12)

2HO.2 — H2O2 + O2. (13)

»OH radicals are rapidly generated through (7). In the above reactions, iron cycles between Fe2+ and Fe3+, and plays the role of catalyst. The net reaction of (7)-(13) is the decomposition of H2O2 into water and O2 catalyzed by iron as follows:

2H2O2 — 2H2O + O2. (14)

Generally speaking, Fenton's oxidation process is composed of four stages including pH adjustment, oxidation reaction, neutralization and coagulation, and precipitation. The organic substances are removed at two stages of oxidation and coagulation [39]. »OH radicals are responsible for oxidation, and coagulation is ascribed to the formation of ferric hydroxo complexes [40]. The relative importance of oxidation and coagulation depends primarily on the H2O2/Fe2+ ratio. Chemical coagulation predominates at a lower H2O2/Fe2+ ratio, whereas chemical oxidation is dominant at higher H2O2/Fe2+ ratios [41]. Wang et al. [42] and Lau et al. [43] reported that oxidation and coagulation were responsible for approximately 20 and 80% of overall COD removal respectively, in Fenton treatment of biologically stabilized leachate.

International Journal of Chemical Engineering Table 3: O3, O3/H2O2, and O3/UV treatments of leachates (updated from Renou et al. [2]).

Initial characteristics of the leachate BOD/COD Removal efficiency (%) O3 (a.g/l) or H2O2/O3 (g/g) UV(W) Reference

COD (mg/L) BOD (mg/L) pH Color (mgP tCo/l) After treatment COD Color (b.gO3/g COD)

6500 500 8.1 12,000 0.5 15 90 1.2a [15]

3096 130 8.2 5759 0.2-0.3 25-50 — 3.0a [16]

3460 150 8.2 5300 — 48 87 3.0a [24]

4850 ± 100 520 ± 30 8.2 — 0.25 30 — 1.3-1.5b [25]

5000 20 — 8300 0.015 33 100 1.7b [26]

5230 500 8.7 — 0.1 27 — — [27]

4850 10 — — 0.1 33 — — [29]

895 43 8.2 — 0.14 28 — 0.76b [31]


5230 500 8.7 — 0.7 48 94 — H2O2:2g/L [27]

2000 — — — — 95 — 3.5b 0.4 [28]

600 — — — — 92 — 3.3b 0.4

2000 160 8.4 — 0.13 92 — 1.5b 0.3 [32]

— — 8 — 97 — 2.5a 2 [30]

— — 8 — 70 — 0.5

1360 <5 8.4 — 0.32 93 — 1.5b 0.3 [31]

480 25 7.7 — 0.13 40 0.05-0.5b 0.25-1 [33]

1280 100 2 — — 54 — 100 [34]

1280 100 2 — — 47 — 500

2300 210 8 — — 40 — 1b 15 [32]

430TOC — — — — 51TOC — 0.1a 300 [35]

26,000 2920 7.8 — 63 0.32 — 3.5b 1500 [36]

26,000 2920 7.8 — 61 0.35 — 4.7b 1500

The introduction of UV irradiation into the Fenton process as well as electro-Fenton process maybe able to improve the removal of COD. Many researchers studied the treatment efficiency of Fenton, photo-Fenton and electro-Fenton processes and the performances are summarized in Table 4. It indicated that leachate quality in terms of COD, odor, and color can be greatly improved following Fenton treatment.

The treatment efficiency of Fenton process depends on pH and the dosage of Fe2+ and H2O. According to Table 4, the optimal pH was in a range 2.0-4.0. The pH value affects the activity of both the oxidant and the substrate, the speciation of iron, and hydrogen peroxide decomposition [44]. Higher »OH radical product yields in the pH range of 2.0-4.0 by a reaction involving in the organometallic complex where either hydrogen peroxide is regenerated or reaction rates are increased [45]. The dosage of Fe2+ and H2O2 are major operational cost items for wastewater treatment. The removal oforganic contaminants is improved as the concentration of Fe2+ and H2O2 increases. However, the extent of increase becomes negligible when the dosage is increased above a certain threshold level. Most researches

indicated that the optimal molar ratio of H2O2 to Fe2+ was from 1.5 to 3.0 [44, 46-48].

Fenton process can significantly remove recalcitrant and toxic organic compounds, and increase the biodegradability of organic compounds [49, 50, 52, 56]. There are four advantages of the Fenton's reagent: (i) both iron and hydrogen peroxide are relative cheap and nontoxic; (ii) there is no mass transfer limitation due to its homogeneous catalytic nature; (iii) there is no form of energy involved as catalyst; (iv) the process is technologically simple. However, Fenton process also shows drawback that large amounts of iron sludge may form, because Fe3+ is converted to ferric-hydroxo complexes.

2.3. Electrochemical Oxidation Processes. Electrochemical oxidation of pollutants in wastewater is fulfilled through two different approaches, as shown in Figure 1: indirect oxidation, where a mediator is electrochemically generated to carry out oxidation, and direct anodic oxidation, where pollutants are destroyed on the anode surface [57]. During indirect oxidation, the agents generated anodically, which are responsible for oxidation of inorganic and organic

Table 4: Fenton, photo-Fenton, and electro-Fenton treatments of leachates.

Initial characteristic of leachate COD (mg/L) BOD (mg/L) pH COD Removal (%) BOD/COD after treatment Optimal condition Reference


1300 30 8.7 — — pH: 3.5, Fe2(SO4)3: 500mg/L, H2O2: 1650 mg/L [39]

8298-8894 — 6.65-6.69 — — pH: 2.5, H2O2/Fe2+ (molar ratio): 1.5, reaction time: 30 min [44]

10540 2300 8.2 60 0.5 pH: 3, Fe2+: 275 mg/L, H2O2: 3300 mg/L, reaction time: 2h [49]

837-6119 42.50-620.00 8.09-8.47 80 (young leachate) 60-70 (old leachate) — pH: 2.5, H2O2/Fe2+ (molar ratio): 1.5, [H2O2]: 0.075M [46]

1100-1300 — 8.18 61 — pH: 3, [H2O2]: 0.24M, H2O2/Fe2+(molar ratio): 3 [47]

8894 — 6.65-6.69 89 — pH: 2.5, [H2O2]: 0.15 M, H2O2/Fe2+ (molar ratio): 3 [48]

5700 ± 300 3600 ± 200 7.8 ± 0.3 66 0.88 pH: 3.5, H2O2: 650 mg/L, H2O2/Fe2+ (molar ratio): 1: 19 [50]


3824 680 7.94 86 — Fe2+: 2000 mg/L, H2O2: 10000 mg/L [51]

5200 ± 27 720 ± 81 8.4 ± 0.1 49 0.4 pH: 2.8, Fe2+: 10 mg/L, H2O2: 2000 mg/L [52]

1150 4.6 70 pH: 3, Fe2+: 56 mg/L, H2O2: 34 mg/L, UV: 80 KW/m3 [53]


5000 — 6.4 83.4 — pH: 3, H2O2: 0.34mol/L, Fe2+: 0.038 mol/L, I: 2 A,d = 2.1cm [54]

2350 — 2.36 72 — pH: 3, H2O2: 2000 mg/L, I: 2 A, reaction time: 20 min [55]

1941 195 8.1 69 0.29 pH: 4, H2O2: 750 mg/L [56]

pollutants may be chlorine and hypochlorite, hydrogen peroxide, ozone and metal mediators such as Ag2+. Direct anodic oxidation is achieved through two different pathways: electrochemical conversion and electrochemical combustion [58]. During electrolysis, two species of active oxygen can be electrochemically generated on oxide anodes (MO*). One is the chemisorbed "active oxygen" (oxygen in the oxide lattice, MOj+i), responsible for the electrochemical conversion through (15). While the other is the physisorbed "active oxygen" (adsorbed hydroxyl radicals, »OH), responsible for electrochemical combustion through (16):

R + MOJ+1 RO + MOj, (15)

R + MOj(»OH)z CO2+ zH+ + ze + MOx, (16)

where R represents organic compounds; z represents the number of absorbed »OH on anode.

During the electrochemical oxidation of landfill leachate, the removal of pollutants may be primarily attributed to

indirect oxidation, utilizing chlorine/hypochlorite formed by anodic oxidation of chlorine originally existing or added in the leachate [59]. However, direct anodic oxidation may to some extent destroy pollutants adsorbed on the anode surface [60]. A series ofreactions involving indirect oxidation during electro-oxidation are shown in (17)-(23)

Anodic reactions : 2Cl- —► Cl2 +2e-, (17)

6HOCl + 3H2O 2ClO3- + 4Cl- + 12H+ + 1.5O2 + 6e-,

2H2O O2 + 4H+ + 4e-, (19)

Bulk reactions : Cl2 + H2O HOCl + H+ + Cl-, (20) HOCl — H+ + OCl-, (21)

Cathodic reactions : 2H2O + 2e- 2OH- + H2, (22) OCl- + H2O + 2e- —► Cl- + 2OH-. (23)

Pollutants Oxidized products

Bulk solution

Oxidation reactions


Electrode |

Bulk solution

Bulk solution

Pollutants Oxidized products


J Anode

Electrons Direct oxidation

Indirect oxidation

Figure 1: Pollutant removal pathways in electrochemical oxidation (indirect and direct oxidation) [57].

Hypochlorite (OCl~) generated in (20) and (21) is a strong oxidant that can oxidize aqueous organic compounds. So, it can oxidize the organic matters in the leachate.

Some researchers have investigated the treatment efficiency of electrochemical oxidation in treating landfill leachate [59-63]. The pollutant removal efficiency was influenced by a number of operating factors, including anode materials, pH, current density, Cl~ concentration, and electrolytes added (Table 5). The common anode materials are ternary Sn-Pd-Ru oxidecoated titanium (SPR), binary oxide-coated titanium Ru-Ti oxide (DSA), PbO2-coated titanium (PbO2/Ti), graphite, SnO2-coated titanium (SnO2/Ti), iron (Fe) and aluminum (Al), and the COD removal efficiency when using the anode material followed the order of SPR > DSA > PbO2/Ti > graphite [59]. Moraes and Bertazzoli [61] found that the removal rates achieved were 73% for COD, 57% for TOC, 86% for color and 49% for ammonium at a current density of 116.0 mA/cm2, using oxide-coated titanium anode. Bashir et al. [63] used graphite carbon and got 70% BOD removal, 68% COD removal, and 84% color removal when the current density was 79.9 mA/cm2 and reaction time was 2 hours.

Electrochemical oxidation of landfill leachate under appropriate conditions can remove most COD and significantly remove color. The important advantage of electrochemical oxidization is to oxidize organic pollutants into CO2 and water to avoid a problem of contaminants shifting from one phase to another. Also, the operation at room temperature and atmospheric pressure prevents volatilization and discharge of unreacted wastes, and the reaction can be simply terminated in seconds by cutting o the power [64]. However, there are two drawbacks of electro-oxidation which may limit its wide application for landfill leachate treatment, one is high energy consumption, and the other is potential for formation of chlorinated organics. Especially because of its expensive operating costs compared with other available technologies (for example, biological processes), electro-oxidation will be favored as a finishing step in a combined process or an auxiliary unit in emergency situations, instead of a full treatment for landfill leachate [65].

2.4. Other AOP Processes. Wet air oxidation (WAO) is a useful treatment method for reduction of aqueous pollution

bound to heavily contaminated wastewater, in particular when it is necessary to treat low volumes. This process consists in the oxidation of dissolved or suspended aqueous solution of organic and inorganic substances by means of oxygen, at elevated temperature (450-590 K) and pressure (2-15 MPa), assuring wet conditions of reaction. Under these conditions organic waste streams too dilute to incinerate and too concentrated for biological treatment can be degraded to simpler, frequently more biodegradable, organic compounds or completely converted to CO2 and H2O [66]. Typically, WAO process has shown promising results (80%-99% of COD removal) for a complete mineralization of organic compounds or for their degradation into a less complex structure, which is more biodegradable [67]. This process is cost-effective for leachate treatment with COD concentrations ranging from 10,000 to 100,000 mg/L. If complete COD removal is not required, the operating conditions such as the air flow rate, temperature, and pressure can be lowered to reduce the operational cost [68]. Although WAO offers some advantages such as a small plant for operations and its ability to deal with varying flow rates and composition of the effluent, this process is not cost-effective for leachate treatment with a COD concentration of less than 5000 mg/L.

Ultrasonic process is considered as a possibility in wastewater treatment for several decades. It is able to remove pollutants through the production of radicals in the bubble of cavitation that can react with refractory compounds [69]. Ultrasonic irradiation is an effective method for the removal of organic matters and ammonia nitrogen from landfill leachate. After 180 minutes ultrasound irradiation (ultrasonic power input: 150 W, pH: 11) up to 96% ammonia nitrogen removal efficiency can be obtained [70]. Due to the high cost of ultrasonic, it is always used as pre-or posttreatment of the biological treatment. Ultrasound pretreatment of raw leachate can significantly improve the removal rates of COD and nitrogen compound (frequency: 20 kHz and amplitude: 12 ^m) [71].

It is obvious that WAO and ultrasonic show a better treatment efficiency of the landfill leachate. However, there are two drawbacks of the two AOPs. One is high energy consumption, and the other is the operation mode restrain its practical application. They are suitable for small quantity and high strength wastewater.

Table 5: Influence of operating factors in electro-oxidation of leachate [57].

Operating factor Influence

Anode materials with high electrocatalytic activity and high anodic oxygen evolution potential cause a high COD and NH3-N removal efficiency; usage of metal anode such as Fe and Al causes simultaneous electro-oxidation and electro-coagulation

The influence ofpH is unclear. Reported results are inconsistent

Increase in current density causes increase in removal efficiencies of COD and color

Increase in Cl- concentration improves removal of pollutants, but increase the hazard of formation of chlorinated organics

Eects of additional electrolytes depend on their species and properties

Table 6: Summary of the highest reported COD removal of some AOPs.

AOPs Optimal condition Initial COD (mg/L) COD removal efficiency (%) Reference

O3 3 g/L 3460 48 [24]

O3/H2O2 O3: 3.5g/gCOD H2O2g/gO3 2000 95 [28]

O3/UV O3: 3.5 g/gCODUV:1500 W 26,000 63 [36]

Fenton pH: 2.5, [H2O2]: 0.15M, H2O2/Fe2+ (molar ratio): 3 8894 89 [48]

Photo-Fenton Fe2+: 2000 mg/L, H2O2: 10000 mg/L 3823.8 86 [51]

Electro-Fenton pH: 3, H2O2: 0.34mol/L, Fe2+: 0.038 mol/L, I: 2 A, d = 5000 83 [54]

2.1 cm

Electrochemical _ , . ,„,-,- _„

. Current density: 116.0 mA/cm2 1855 73 L61J


Anode materials pH

Current density

Chloride ion concentration

Additional electrolytes

3. Comparison of Various AOP's Performance

The outcomes of AOPs applied to treat the landfill leachate can be classified into two types: (i) oxidize organics substances to their highest stable oxidation states being carbon dioxide and water (i.e., to reach complete mineralization); (ii) improve the biodegradability of recalcitrant organic pollutants up to a value compatible with subsequent economical biological treatment. Thus, the comparison of various AOP's performance was evaluated from these two aspects.

Table 6 presents the outstanding treatment performance and optimum operate condition of various AOPs for COD removal from landfill leachate. The ozone-based process can achieve 40-95% of COD removal with COD concentration ranging from 2000 to 26,000 mg/L, while electrochemical oxidation process and Fenton process can achieve 70-90% of COD removal with COD concentration ranging from 1855 to 8894 mg/L. It should be noted that the treatment efficiency of Fenton process is better than ozone-based process and electrochemical oxidation. In term of biodegradability improvement, BOD/COD ratios are 0.29-0.88 [49, 50, 52, 56] and 0.1-0.5 (Table 3) were reported after oxidation by Fenton process and ozone-based oxidation, respectively.

Concerning the cost of various AOPs, electrochemical oxidation, wet air oxidation, and ultrasound oxidation are more expensive due to the high demand of electrical energy

for devices ozonizers, UV lamps, ultrasounds. The only exception is the Fenton's process. In such a process, in fact, under acidic condition, a Fe2+/H2O2 mixture produces • OH radicals in a very effective way [49]. Tizaoui et al. [27] estimated the treatment cost of O3/H2O2 system was about 2.3US$/kg COD. Kurniawan et al. [17] showed that the treatment coat of leachate using ozone-GAC adsorption varies between US$ 2 and 4 per m3 of the treatment effluent. While Rivas et al. [72] estimated the operational cost for Fenton treatment of leachate was per m3 of

leachate and ppm of COD removed. Based on the analysis and Lopez et al. [49], Fenton process seems to be the best compromise because the process is technologically simple, there is no mass transfer limitation (homogeneous mature) and both iron and hydrogen peroxide are relatively cheap and nontoxic. But Fenton's process required low pH and a modification of this parameter is necessary.

4. Conclusions

The application of AOPs including ozone-based oxidation, Fenton oxidation, electrochemical oxidation, wet air oxidation, and ultrasound oxidation to treatment of landfill leachate was reviewed. Among the AOPs reviewed, ozone-based oxidation and Fenton oxidation are the most frequently studied and widely applied methods for the

treatment of landfill leachate. Both techniques can achieve about 15-95% of COD removal with COD concentration ranging from 600 to 26,000 mg/L. In particular, Fenton process can improve BOD/COD ratio to close 0.5. Fenton process seems to be the best compromise because the process is technologically simple, there is no mass transfer limitation (homogeneous mature) and both iron and hydrogen peroxide are cheap and nontoxic. From the economic point of view, using Fenton process as the pretreatment ofbiological treatment can lower the cost and improve the treatment efficiency.

In the past, most of works were focused on the removal efficiency of organic matters from landfill leachate. Only a few researches considering the toxicity reduction were involved. However, the toxicity assessment of landfill leachate is very important, which determines the effect of the subsequent biological treatment or the influence on the environment. So, the toxicity reduction of AOPs should be evaluated in the future research.


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