Physico-Chemical Processes

Physico-Chemical Processes Parastoo Pourrezaei1, Atefeh Afzal1, Ning Ding1, Md. Shahinoor Islam1, Ahmed Moustafa1, Przemysław Drzewicz1, Pamela Chelme-Ayala1, Mohamed Gamal El-Din*1

ABSTRACT:

This is a review of literature published

wastewater generated from a polyvinyl chloride plant. The

in 2009 that covered issues related physico-chemical

results showed that the combination of alum with

processes used to treat water and wastewaters. The review

polyelectrolyte gave higher turbidity removals than those

is

obtained with ferric and calcium chloride.

divided

into

six

sections,

coagulation/flocculation, sorption

including

processes, filtration,

In a study by Haydar et al. (2009a), the

sedimentation/flotation, oxidation, and air stripping.

combination of alum with cationic and anionic polymers was used to treat tannery wastewater. The results indicated

KEYWORDS:

physical processes, chemical processes,

that the combination of alum with anionic polymer gave

water

wastewater

higher removals in terms of turbidity, total suspended

treatment,

treatment,

removal

of

pollutants.

solids (TSS), total chemical oxygen demand (TCOD), and chromium (Cr) than those obtained with alum combined

doi: 10.2175/106143010X12756668800852

with cationic polymer. Both polymers reduced the sludge volume by 60 to 70%. In another study by Haydar and Aziz

Coagulation/Flocculation

(2009b), the efficiency of different cationic polymers over

The application of the aluminum and ferric salts

metal salts was evaluated. It was found that three cationic

as the coagulants was found to be effective to remove

polymers were able to remove 91 to 95%, 69 to 83%, 25 to

suspended

wastewaters.

29%, and 96 to 97% of turbidity, TSS, TCOD, and Cr,

AlMubaddal et al. (2009) investigated the impact of

respectively. These results demonstrated the viability of the

aluminum sulfate (alum), ferric and calcium chloride on

application of cationic polymers compared to metal salts.

solids

from

a

variety

of

Zonoozi et al. (2009) compared the effect of polyaluminum ————————— 1*

chloride (PACl) and alum as coagulants to remove Acid

Department of Civil & Environmental Engineering, 3-093

Blue 292 dye from aqueous solution. The results indicated

Markin/CNRL Natural Resources Engineering Facility, University

that about 85% of the dye could be removed by both

of Alberta, Edmonton, Alberta, Canada, T6G 2W2; Tel. 780-492-

coagulants at the optimum conditions. Kaolinite as a

5124; Fax. 780-492-8198; e-mail: [email protected]

coagulant aid increased the removal efficiency at lower

997 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

coagulant concentrations. The authors also found that the

Ersoy et al. (2009) compared the effectiveness of

removal efficiency depended on the pH, chemical dose, and

coagulation,

initial dye concentration. The efficiency of PACl and alum

flocculation at various pHs on the turbidity removal from

to treat stabilized leachate from Pulau Burung Landfill Site

natural stone processing wastewater. It was found that

(PBLS), Malaysia was investigated by Ghafari et al.

flocculation and combined process gave higher turbidity

(2009). Based on quadratic models, the optimum conditions

removal. The results showed that at pH 6 and 9, the

were found to be PACl dose of 2 g/L at pH 7.5 and alum

turbidity removal was higher than that at neutral pH by

dose of 9.5 g/L at pH 7. The results indicated that relatively

using aluminum chloride (AlCl3). Charge neutralization

higher COD, turbidity, color, and TSS removal was

mechanism at lower pH and sweep coagulation at neutral

achieved using PACl.

and higher pH was suggested as the removal mechanism.

Moringa oleifera seed extract as a natural

flocculation

and

combined

Harrelkas et al. (2009) used

coagulation-

coagulation-

coagulant was used to remove sodium lauryl sulfate from

flocculation alone and its combination with microfiltration

aqueous solutions (Beltran-Heredia and Sanchez-Martin,

(MF), ultrafiltration (UF), and adsorption on powdered

2009). Freundlich (F), Frumkin-Fowler-Guggenheim (FFG)

activated carbon (PAC) to treat textile wastewater. The

and Gu-Zhu (GZ) models were fitted to the experimental

optimum conditions were found to be pH of 5, 100 mg/L of

data. Gu-Zhu model was found to be the most accurate

alum as coagulant, and 4 mg/L of flocculant. The

model to predict the experimental series.

combination of coagulation with MF, UF and PAC resulted

Chitosan, an amino-biopolymer, has been used

in 37, 42 and more than 80% of COD reduction and 65%,

recently in water treatment to remove dissolved and

74 and 50% of color removal, respectively. In a review by

particulate compounds. Renault et al. (2009) extensively

Leiknes (2009), the significance of the implementation of

studied the use of chitosan as a coagulant for the treatment

the membrane technologies for future applications in water

of various solutions. The effect of different conditions and

and wastewater treatment plants and its combination with

characteristics of chitosan on the overall performance of the

coagulation-flocculation technology was discussed. Some

coagulation-flocculation was also investigated. Szygula et

studies showed that this combination was capable of

al. (2009) used chitosan as a coagulant to treat Acid Blue

overcoming the drawback of the membrane fouling.

92 as a model dye from colored solutions. The results

Walsh et al. (2009) studied the impact of

showed that lower concentration of chiotsan was required

different conditions of coagulation and flocculation

to remove up to 99% of the dye from tap water. Chitosan

pretreatment on the permeate stream of immersed UF. The

could also be recovered from the flocs after removal of the

results indicated that lower alum dose and low flocculation

dye, using 0.001 to 1 M sodium hydroxide (NaOH)

time (around 10 min) and mixing intensities of 100 s

solutions.

enhanced the water quality. Air sparging at an applied

998 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

velocity gradient of 50 s-1 in the UF tank also decreased the

matter removal by coagulation-flocculation process. The

measurements of dissolved organic carbon (DOC) and

results showed a significant linear relationship between

ultraviolet absorbance at 254 nm (UV254). Suarez et al.

DOC removal and fluorophores A, C and T fluorescence

(2009) studied the impact of coagulation followed by

intensities (humic,

flotation as a pretreatment method for hospital wastewater.

fluorescence centers). Guo et al. (2009) investigated the

The results demonstrated that an average of 92% TSS

effect of various factors, including coagulant type and dose,

removal could be achieved by using the combined

initial contaminant load, pH, and interfering ions on the

processes, whereas the application of the single flotation

removal of antimony Sb(V) and Sb(III) from drinking

without coagulation resulted in lower removal efficiency.

water by using coagulation-flocculation process. It was

Maximum removal of 46, 42 and 23% were obtained for

found that the optimum pH for Sb(V) removal with ferric

diclofenac, naproxen, and ibuprofen, respectively.

chloride was in the range of 4.5 to 5.5. Aluminum sulfate

Coagulation

and

fulvic, and

protein-like material

coagulation-flocculation

resulted in a very low removal of both Sb(III) and Sb(V). In

combination processes for reclamation of a secondary

addition, phosphate and humic acid showed significant

effluent were optimized by the use of particle size

inhibitory effect on Sb(V) removal and the most

distribution approach (Liu et al., 2009a). The laser light

influencing factors were found to be coagulant type, Sb

scattering technology and the sequential membrane

species along with pH.

filtration technology were applied as particle size analyzers

Polishing treatment of molasses wastewater was

and the results indicated that turbidity removal in the

performed by coagulation-flocculation process (Liang et

flocculation process increased when the particles size were

al., 2009). The effects of operating variables, including

in the range of 0.2 to 0.3 μm and 5 to 8 μm. Guminska et

coagulant and flocculant type and dose, pH, rapid mixing

al. (2009) investigated the effect of floc rupture on the

intensity as well as time were investigated. The results

flocculation tank and also the coagulation mechanism on

showed that 89% COD and 98% color removal was

natural organic matter (NOM) removal. The investigation

achieved by ferric chloride, whereas 66 and 86% of COD

of the flocs structure showed that stronger flocs were

and color were removed by aluminum sulfate. Lower pH

formed during sweep flocculation mechanism than those

also resulted in higher removal efficiency. In addition,

formed during charge neutralization mechanism. The

cationic polyacrylamide enhanced the settleability of flocs.

findings also indicated that the sedimentation of the flocs

Paopuree et al. (2009) evaluated the effect of the

immediately after rupture resulted in higher quality of the

operational parameters on the efficiency of the coagulation-

treated water.

flocculation process of a water treatment plant. The results

In a study by Gone et al. (2009) fluorescence

demonstrated that increasing the coagulant dose led to the

spectroscopy was used to evaluate the dissolved organic

higher turbidity and NOM removal. The optimum pH value

999 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

for alum and PACl was found to be 6 and 7, respectively.

treatment on the removal of yeastlike fungus Candida

By adding 40 mg/L PACl at initial pH of 7 with the

albicans from aqueous solutions. It was found that

addition of cationic polymer at 2 mg/L, the removal

aluminum dihyrosulfate could remove 99.7% of the yeast.

efficiency was higher than that obtained under current plant Sorption Processes: Removal of Organics

condition. In a study by Zheng et al. (2009a), the feasibility

Activated Carbon. The use of activated carbon

of phthalic acid esters (PAEs) removal from fresh and

(AC) for the removal of organic matters was extensively

stabilized landfill leachates by coagulation-flocculation was

reported in 2009. The AC was obtained from different plant

studied. The results showed that a maximum of 32% of the

materials, including oil palm empty fruit bunches (Alam et

PAEs could be removed from fresh leachate, whereas up to

al., 2009), waste dates stones precursor (Alhamed, 2009),

50% removal was obtained from partially stabilized

vetiver roots (Altenor et al., 2009), coconut coir pith

leachates. The results also showed that the humic-PAEs

(Anirudhan et al., 2009), bamboo (Jiang et al., 2009),

complex could increase the PAE removal. The effect of the

almond and walnut shell (Pajooheshfar and Saeedi, 2009),

cationic and anionic coagulants and flocculants on the

as well as root residue of Hemidesmus Indicus (Srihari and

wood pulp wastewater treatment was investigated by

Das, 2009).

Vucinic et al. (2009). Different coagulants and flocculants

Rodriguez et al. (2009a) found that AC was very

at various concentrations were applied. The best results in

effective for adsorption of anionic dye Orange II and

terms of turbidity, pH, and total suspended solids change

cationic dye methylene blue. An AC prepared from

were found by the application of commercial coagulant

bamboo waste was applied for the removal of organic

named EP-10 and anionic flocculant A-45.

pollutants from the waste of cotton dyeing process (Ahmad

Produced wastewater from contaminated soil washing

containing

petroleum

hydrocarbon,

and Hameed, 2009). A maximum reduction of 91.8% of

sodium

color and 75.2% of chemical oxygen demand (COD) was

dodecyl sulfate (SDS), salts, organic matter and other

achieved. El Nemr et al., (2009) applied AC obtained from

constituents were treated with coagulation-flocculation

orange peels in the removal of a dye, Direct Fast Turquoise

process (Torres et al., 2009). The results obtained using

Blue GL (DB-86), from simulated wastewater. A maximum

different coagulants at different doses and pHs indicated

removal of 92% of 100 mg/L DB-86 was obtained at pH 2

that at pH of 5, iron chloride (FeCl3) at doses of 4 000

for adsorbent dose of 6 g/L at room temperature.

mg/L, and Tecnifloc 998 as flocculant at and 1 mg/L, the

Augulyte et al. (2009) investigated the use of

color, turbidity, COD, and conductivity removals were up

biologically activated carbon sorbent (BAC) in anaerobic

to 99.8, 99.6, 97.1, and 35.0%, respectively. Saprykina et

conditions for the removal of a group of alkylated and non-

al. (2009) studied the effect of coagulation-flocculation

alkylated polycyclic aromatic hydrocarbons (PAHs) from

1000 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

wastewater polluted with petroleum products. A high

biological process. I was fund that AC enhanced the

removal of PAHs using BAC was obtained in various

removal of COD during water treatment.

process conditions, achieving an overall removal of 96.9 to

The removal of steroid estrogen from wastewater

99.7% for the sum of 36 PAHs. Lim et al. (2009) studied

by adsorption on two types of GAC, virgin (F400) and

the adsorption of organic matter from Han River water on

reactivated (C401) carbon, were studied by Rowsell et al.

different types of biologically activated carbons. The most

(2009). The estrogen removal on C401 and F400 was 81

efficient adsorption was obtained on PAC than that

and 65 %, respectively. Yu et al., 2009 studied the

obtained on granular activated carbon (GAC). It has found

adsorption

that organic material above 10 kDa was effectively

carbamazepine, and nonylphenol on GAC. The results

removed from water, while the concentration of low

showed that the adsorption of those compounds was

molecular material under 1kDa increased in the treated

strongly affected by the presence of NOM in water.

water.

of

two

pharmaceutics,

naproxen

and

Inorganic Sorbents. The application of bentonite GAC prepared from Nigerian bamboo was

for the removal of humic acid and o-dichlorobenzene

applied in the removal of organic pollutant from refinery

(DCB) was studied by Gu et al. (2009). The addition of

waste (Ademiluyi et al., 2009). A reduction of COD from

bentonite to the solution improved the removal of humic

an initial value of 378 mg/L to 142 mg/L was obtained after

acid, while the concentration of DCB was not affected. The

one hour in fixed bed absorption process. Periwinkle shell-

sorption efficiency of chlorobenzene (CB) on activated

based granular activated carbon (PSC) was applied in the

bentonite containing montmorillonite was studied by

removal of COD from an industrial wastewater (Badmus

Sennour et al. (2009). It has found that the thermal

and Audu, 2009). A removal of 77.5% of COD was

activation increased the adsorption capacity more strongly

obtained.

than chemical activation, which was performed by acid and Drikas et al. (2009) assessed the impact of MIEX

hydrogen peroxide treatment. Navarro et al. (2009) studied

pre-treatment, followed by either coagulation or MF on the

the adsorption of phenol on clay (bentonite) modified with

effectiveness of GAC filters in a water treatment plant. The

quaternary amines and seaweeds Lessonia nigrescens and

authors investigated the removal of taste and odor

Macrocystis integrifolia cross-linked with calcium chloride.

compounds, 2-methylisoborneol (MIB) and geosmin, from

The results indicated a higher adsorption of phenol on

a surface drinking water source over a 2-year period. A

organoclay than that on biological sorbent.

complete removal of MIB and geosmin was achieved by all

Almeida et al. (2009) studied the adsorption of

GAC filters, for the first 10 months. Wang et al. (2009b)

methylene blue dye on montmorillonite at different

found that AC was very effective in post-treatment removal

conditions. The results indicated that the experimental data

of non-biodegradable compounds after coagulation and

fitted a pseudo-second-order kinetic model, with an

1001 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

activation energy of +28.5 kJ/mol. The sorption efficiency

solution by adsorption on clay (sodium montmorillonite,

of organochlorine pesticides, lindane and dieldrin, on

closite

montmorillonite and bentonite was investigated by Aydin

montmorillonite with intercalated quaternary amines,

et al. (2009). It has found that the acid activation increased

closite 20A (CLO20A) and closite 30B (CLO30B)). The

the efficiency of the pesticides removal. Calcination of the

accumulation tests showed that organoclays materials were

clays at 500 ºC did not reveal any discernible effect on the

capable of adsorbing high quantities of pesticides.

(CLONa))

and

organoclays

(sodium

removal efficiency in comparison to untreated sorbents.

Alkaram et al. (2009) investigated the adsorption

Cao et al. (2009) studied the adsorption of bisphenol

of phenol on clays, bentonite and kaolinite, modified with

polyethersulfone on modified montmorillonite. The highest

different quaternary amines. The study showed a higher

adsorption of bisphenol was achieved after 300 minutes.

phenol adsorption capacity for modified clays than that for

The sorbent could be reused after complete removal of

unmodified clays. Senturk et al. (2009) studied the

bisphenol by washing with ethanol.

adsorption

of phenol on

bentonite

modified

cetyl

Baker and Ghanem, (2009) studied the absorption

trimethylammonium bromide (CTAB). The maximum

of o-chlorophenol on Jordanian zeolite. Before calcination,

phenol removal was observed at pH 9.0 after 1h. The

zeolite samples were treated separately with saturated

obtained adsorption capacity was 333 mg/g.

solution of urea (ZU) and thiourea (ZT). The highest

Other Adsorbents. Li. et al. (2009) studied the

adsorption of o-chlorophenol was obtained for zeolites

removal of 4-chlorophenol (4-CP) by adsorption on β-

calicinated at 800 ºC. The chlorophenol removal efficiency

calixarene polymer (β-CDP). The results of batch

was 79.7, 91.1, and 95.1% for zeolite, thiourea and

experiments showed that β -CDP exhibited high sorption

saturated solution of urea, respectively. Valdes et al. (2009)

capacities toward 4-CP (up to 24.4 mg/g when initial

studied methylene blue removal from model solution by

concentration of 4-CP solution was 140 mg/L at 10 °C).

adsorption

Simultaneous

Saitoh et al. (2009) studied a water soluble

ozonation with adsorption on zeolite showed a maximum of

polymer obtained by the condensation of chitosan and poly

70% methylene blue removal. Li et al. (2009a) investigated

(n-isopropylacrylamide-co-acrylic acid) with 1-ethyl-3-(3-

the adsorption of p-nitrophenol (p-NP) on zeolite modified

dimethylaminopropyl) carbodiimide for the removal of

with

on

zeolite

cationic

and

ozonation.

β-cyclodextrin

and

2,3-

phenol from water solution. The polymer contained a bind

epoxypropyltrimethylammonium chloide. The modification

enzyme, tyrosine, which was able to oxidize phenol. The

of zeolite increased the absorption capacity of p-

polymer deposited above 34 ºC in 50 mM sodium

nitrophenol and shortened the contact time.

phosphate at pH 6.8. The concentration of phenol (19

Baglieri et al. (2009) studied the removal of two

mg/L) was reduced to 0.08 mg/L in 1L of treated water

pesticides, fenhexamid and pyrimethanil, from aqueous

when 1.0 g of polymer containing 8.7% chitosan was

1002 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

employed. Vergili and Barlas (2009) found that polymer

of 500, 800, and 1200°C. The highest adsorption capacity

resin, Lewatit VP OC 1163, was effective for the removal

of benzoic acid (0.361 mmol/g) and specific surfaced area

of pharmaceuticals carbaniazepine, sulfamethoxazole and

(525 m2/g) were obtained for MWCNTs modified by

propyphenazone from aqueous solution.

ultrasonic treatment in nitric acid. Raising calcination

Tian et al. (2009) studied the application of

temperature decreased the adsorption of benzoic acids on

modified mesoporous silica materials (HMS, MCM-41,

MWCNTs. Yang and Xing (2009) studied adsorption of

SBA-15 and MCM-48) for the removal of organochlorine

fluvic acid by single-walled (SWCNT) and MWCNT. The

pesticide,

study showed that SWCNT had higher adsorption capacity

1,1,1-trichloro-2,2'

bis(p-chlorophenyl)ethane

(DDT), from water. DDT was removed by 50% within 2h

than those of MWCNT and AC.

of contact time. The pesticide was easily removed from Sorption Processes: Removal of Inorganics

sorbents by thermal decomposition at 450 ºC, except MCM-41

Activated Carbon. Tamarind wood AC was Microporous carbon was studied for the removal

tested for Cr(VI) removal after activation with zinc chloride

of phenol, 1,3-dichlorobenzene, and 1,3-dinitrobenzene

(Acharya et al., 2009). The adsorption capacity was 28.02

from aqueous solution (Ji et al., 2009a). The synthesized

mg/g. Stanly et al.

microporous carbon showed high adsorption affinity for all

Cr(VI) by adsorption on AC prepared from a flame tree

studied compounds. The achieved contact time was less

seed coat. A removal efficiency of 85% was obtained. AC

than 3 h. Chen et al. (2009a) investigated the adsorption

prepared from cashew nut shells using potassium hydroxide

affinity of atrazine to multiwalled carbon nanotubes

activation at 850 ºC in nitrogen (N2) and carbon dioxide

(MWCNTs) containing 0.85, 2.16, and 7.07% oxygen. The

(CO2) atmosphere was applied for the removal of

results indicated that the adsorption affinity decreased with

chromium ions from aqueous solutions (Tangjuank et al.,

increasing oxygen content. The removal of 2,4,6-

2009). The obtained sorption capacity was 13.93 mg/g. The

trichlorophenol (2,4,6-TCP) using the MWCNTs in the

removal of Cr(VI) from tannery effluent by adsorption on

presence of copper (Cu(II)) was investigated by Chen et al.

AC was studied by Barkat et al. (2009). At optimized

(2009b). The oxidation of MWCNTs increased the

condition, a removal of 65.7% was achieved. The AC

adsorption efficiency of 2,4,6-TCP, whereas the presence

exhibited a high selectivity towards Cr(VI) removal from

of copper cations decreased the removal efficiency.

aqueous solution. Choi et al. (2009a) investigated the

(2009) investigated the removal of

adsorption of Cr(VI) on AC in the presence of a quaternary Kotel et al. (2009) investigated the removal of ammonium compound, cetylpyridinium chloride (CPC). At benzoic acids by adsorption on MWCNTs, modified by a concentration below the critical micelle concentration ultrasonic treatment in nitric acid

and

subsequent (CMC) of CPC, the adsorption of CPC and Cr(VI) reached

calcination in an inert atmosphere of argon at temperatures

1003 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

equilibrium within 60 min, while at concentrations above

Tang et al. (2009) studied the removal of Cr(VI)

CMC, the equilibrium was achieved after 180 min. CPC

by adsorption on row and acid modified AC. At optimized

decreased the adsorption rate of Cr(VI) and increased the

condition, a removal of 97.67 and 99.87% for AC and

adsorption amount of Cr(VI) onto AC. Narayanan and

modified AC, respectively, was achieved. The adsorption

Ganesan (2009) found that the addition of GAC enhanced

capacity was found to be 4.75 and 5.95 mg/g for AC and

the removal of Cr(VI) during electrocoagulation process.

modified AC, respectively. Huang et al. (2009) studied the

Hong et al. (2009) studied the removal of chromate,

adsorption of Cr(VI) on GAC and modified AC with nitric

ferricyanide and arsenate by adsorption on AC in the

acids (MAC). It was found that the MAC had a higher

presence

Cr(VI) adsorption capacity (16.1 mg/g) than that of GAC

of

quaternary

ammonium

compound,

cetylpyridinium chloride.

(6.40 mg/g).

The sorption behavior of the anionic chromium

Venkatraman et al. (2009) studied the removal of

complex dye, Lanasyn Navy M-DNL, from aqueous

various metals by adsorption on AC prepared from an

solution onto AC (Norit RB 08.CC), and as an alternative,

indigenous waste. At optimum conditions, the sorption

the neutral polymeric adsorbent (Macronet MN 200), was

capacity was 30 mg/g at pH 7. Monser and Adhoum (2009)

investigated

conditions

studied the removal of lead (Pb(II)), cadmium (Cd(II)) and

(Kazlauskiene et al., 2009). Using both adsorbents at pH 2,

Cr(III) on AC modified with yellow azodye, tartazine. At

the maximum removal of chromium ions (from 6.16 to 1.5

optimized conditions, the adsorption capacity for Pb(II),

mg/L) and organics (COD from 735 to 100 mg oxygen

Cd(II) and Cr(III) ions was improved with respect to non-

(O2)/L) was obtained.

modified carbon by a 140%.

under

various

experimental

Gabr et al. (2009) studied the sorption of Cr(VI)

Araujo et al. (2009) compared the efficiency of

by biofilm Escherichia coli ASU 7 supported on GAC.

the removal of gold (Au), iron (Fe) and copper (Cu)

Supporting of bacteria on AC decreased both the porosity

cyanocomplexes from ore effluent by adsorption on the

and surface area of the GAC. The sorption capacity for

weak-base ion-exchange resin

Cr(VI) using biofilm, GAC, and E. coli ASU 7 were 97.7,

chemically modified AC. Modified AC showed poorer

90.7, 64.36 mg Cr(VI) /g at pH 2.0, respectively. Sulaymon

efficiency in the recovery of Au complexes in relation to

et al. (2009) studied the removal of lead copper chromium

untreated AC, and it did not adsorb either Cu or Fe

and cobalt ions using GAC in batch and fixed-bed

complexes. The best result by using resin-obtained

adsorbers. It has found that increasing the flow rate and the

recovery for Cu, Fe and Au complexes was 100%.

initial metal ion concentration decreased the bed height and

(LEWATIT

MP

62)

Arivolli et al. (2009) studied the adsorption of Cu

the time of the breakthrough point.

on AC prepared from solid waste. At optimized condition, the highest sorption capacity was 38.35 mg/L at pH 7 and

1004 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

contact time of 40 min. The sorbent could be reused after

highest adsorption capacity, 151.3 mg/g, was obtained for

the desorption of Cu with dilute hydrogen chloride (HCl)

GAC loaded with 15% lithium. It was also found that Ni(II)

acid. Demirbas et al. (2009) studied the adsorption of

could be fully desorbed from sorbent with 0.05 M HCl

Cu(II) on AC obtained from hazelnut shells. The adsorption

solution. Ewecharoen et al. (2009) investigated methods for

capacity was 58.27 mg/g at pH 6 with 90 min of contact

the preparation of sodium polyacrylate grafted AC using γ

time. Milenkovic et al. (2009) studied the effect of

irradiation by increasing the number of surface functional

ultrasound on adsorption of Cu(II) on AC obtained from

group. After irradiation, the adsorption capacity for nickel

hazelnut shells. The ultra-sound increased the efficiency of

increased from 44.1 to 55.7 mg/g.

Cu(II) removal and the adsorption time.

Rao et al. (2009) studied the application of AC

Kalpakli and Koyuncu (2009) studied the

prepared from Ceiba pentandra hulls (ACCPH), Phaseolus

application of GAC, Chemviron C-1300, for the removal of

aureus hulls (ACPAH) and Cicer arietinum waste

Cu(II) from drinking water. The optimum conditions for

(ACCAW) for the removal of mercury (Hg) from water. At

the removal of 10 mg/L Cu(II) were pH 5, 25 min of

initial concentration of 40 mg/L Hg(II), the sorption

contact time, and 750 mg of AC. Kongsuwan et al. (2009)

capacity was 25.88 mg/g for ACCPH, 23.66 mg/g for

studied the removal of Cu(II) and Pb(II) by adsorption on

ACPAH and 22.88 mg/g for ACCAW. Wang et al. (2009)

AC prepared from Eucalyptus bark. The sorption capacities

studied the removal of Hg(II) on AC impregnated with

for Cu(II) and Pb(II) were 0.45 and 0.53 mmol/g,

elemental sulfur at different temperatures. The highest

respectively. It was found that ion exchange on surface

sorption capacity of AC impregnated was obtained at 400

carboxylic, amine and amide groups of AC was not a major

°C. The adsorption capacity was 800 mg/g at pH 5.5.

sorption mechanism. Yang et al. (2009a) found that the

Boudrahem et al. (2009) studied the application

loading of AC with Fe(III) increased the efficiency of

of AC, prepared from coffee residue chemically activated

Cu(II) removal from aqueous solution.

with zinc chloride (ZnCl2), for the removal of Pb(II). At

Rao et al. (2009) investigated removal of Pb(II),

optimum conditions, the sorption capacity was 63 mg/g at

zinc (Zn(II)), Cu(II), and Cd(II) from aqueous solution

pH 5.8 and initial concentration of 10 mg/L Pb(II). Li and

using AC prepared from Phaseolus aureus hulls. The

Wang (2009) studied the adsorptive removal of Pb(II) from

adsorption capacity were 21.8 mg/g for Pb(II), 21.2 mg/g

dilute aqueous solution using AC prepared from Spartina

for Zn(II), 19.5 mg/g for Cu(II), and 15.7 mg/g for Cd(II).

alterniflora treated with phosphoric acid. At optimum pHs

AC was regenerated by washing with HCl acid.

of 4.8 to 5.6, the obtained sorption capacity was 99 mg/g.

Byeon

et

al.

(2009)

examined

various

Konsowa, A. H. (2009) found that GAC

modification of coal-based GAC with sodium, potassium

removed 95 % of initial bromate ions (10 mg/L) from

and lithium acetates for the removal of nickel (Ni(II)). The

aqueous solution. Fouladi Tajar et al. (2009) studied the

1005 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

removal of Cd(II) using AC treated with gaseous sulfur

adsorption of Cr(VI) on clay, hectorite, modified with 2-

dioxide (SO2). The removal of 100 mg/L Cd(II) was 92.4%.

mercaptobenzimidazole. The adsorption capacity of Cr(VI)

The SO2 modification of activated carbons enhanced the

depended on the modification methods. The highest

cadmium removal. Ahn et al. (2009) studied the adsorption

adsorption capacity was 14.01 mmol/g.

of cadmium ions on GAC treated with nitric acid (NGAC),

Maicaneanu et al. (2009) investigated the

and untreated regular granulated activated carbon (RGAC)

removal of heavy metals Zn(II), Pb(II) and Cd(II) from

in the absence and presence of mixtures of anionic (sodium

wastewater by adsorption clay, betonite, from Orasul Nou

dodecyl sulfate, SDS) and nonionic (Triton X-100, TX100)

deposit (Romania). A heavy metal removal of 100% was

surfactants. In the absence of surfactants, NGAC adsorbed

observed at optimum conditions. Mansri et al. (2009) found

8.7 times more Cd (0.165 mmol/g) than did RGAC (0.019

that a modification of clay and bentonite with poly(4-

mmol/g). In RGAC suspensions, the amount of Cd sorbed

vinylpyridinium) enhanced the efficiency of Cr(VI)

increased significantly with increasing dose of SDS, to a

removal. Coruh et al. (2009) found that natural zeolite,

maximum of 0.112 mmol/g.

clinoplilolite, could remove 99% of Cu(II) from water at

Inorganic Adsorbents. Al-Jlil and Alsewailem

low metal concentration. Doula (2009) reported that the

(2009) investigated the adsorptive removal of Pb(II) on

modification

of

natural

zeolite,

clinoptilolite,

with

various untreated clays from Saudi Arabia. The highest

amorphous iron oxide enhanced the removal of Cu,

adsorption capacity was 30 mg/g, obtained for clay from

manganese (Mn), and Zn cations from water.

Tabuk. The acid activation of the clay did not enhanced the

Mamba et al. (2009) studied the adsorptive

adsorption capacity of the investigated clays. Eren el al.

removal of Cu(II) and cobalt (Co(II) cation by acid

(2009a) studied the adsorptive removal of Pb(II) by clay,

activated natural zeolite, clinoptilolite. The obtained

bentonite, from Unye (Turkey). The adsorption capacity on

removal was 79 and 77%, for Co(II) and Cu(II),

untreated clay, acid activated and manganese oxide-coated

respectively. Qian et al. (2009) investigated the removal of

was 16.70, 8.92 and 58.88 mg/g, respectively. In further

phosphate and ammonium cations from wastewater by

study, it has found that the adsorption capacity for the same

adsorption on natural zeolite, clinoptilolite. At optimized

clay coated with iron oxide was 22.2 mg/g (Eren el al.

condition, the efficiency of phosphate and ammonium

2009b).

nitrogen removal was 96%. Vassileva and Voikova (2009) Bedelean et al. (2009) investigated the removal of

studied the adsorptive removal of ammonium (NH4+) by

heavy metals Cd(II), Pb(II) and Cr(III) from wastewater by

natural zeolite, clinoptilolite, from Beli plast deposit

adsorption on clay, betonite, from Petresti deposit

(Bulgaria). At optimum condition, the adsorption capacity

(Romania). At optimum conditions, the removal of heavy

was 18.4 mg/g. Zuo and Li (2009) found that NH4+ could

metals was 100%. Guerra et al. (2009) studied the

be removed by adsorption on natural zeolite, clinoptilolite.

1006 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

After two month biochemical regeneration, 80% of NH4+

removal of Cu(II), Co(II), Ni(II), Pb(II) and Zn(II). It

was removed.

was found that obtained adsorption capacity followed the

Akar et al. (2009a) studied the biosorption of

order: Pb(II) (2.530 mmol/g) > Cu(II) (2.081 mmol/g) >

Cu(II) on natural zeolite, montmorillonite, covered white

Zn(II) (1.532 mmol/g) > Co(II) (1.242 mmol/g) > Zn(II)

rot fungi, Trametes versicolor. The obtained biosroption

(1.154 mmol/g). El-Eswed et al. (2009) investigated the

capacity was 62.8 mg/g. In further investigation, Akar et

adsorption of Pb(II) by alkaline activated natural zeolite

al. (2009b) found that the modification of natural zeolite,

form Jordan. The adsorption capacity was 157 mg/g at

montmorillonite,

pH 6.0.

with

hexadecyltrimethylammonium

bromide enhanced adsorption capacity of Cr(VI).

Other Adsorbents. Chandra and Bhaumik

Chang et al. (2009a) studied the removal of

(2009) developed a method for the preparation of new

NH4+ from textile wastewater by adsorption on zeolite

mesoporous polymer, poly-triallylamine for the removal

covered with biofilm. There was no significant difference

of chromate (CrO42-), permanganate (MnO4-), arsenite

in ammonium adsorption capacity of zeolite pretreated by

(AsO33-), nitrate (NO3-) and phosphate (PO43-) from

heat and hydrochloric acid solution. The removal of NH4+

wastewater. James et al. (2009) developed a method of

on zeolite was higher than that on biofilm covered GAC

preparation of new mesoporous ion imprinted polymer

and sand. Zhao et al. (2009) obtained an average of 99%

with formamidoxime and/or 4-vinyl pyridine. The

ammonium adsorptive removal and 92% of COD

obtained sorption capacity was 80 µmol/g. Aguado et al.

adsorptive removal for coke-plant wastewater using

(2009) developed a method for preparing amine-

natural zeolite covered with biofilm.

functionalized mesoporous silica to remove Cu(II),

Zhang et al. (2009a) studied the removal of

Ni(II), Pb(II), Cd(II), and Zn(II) from water.

ammonia from landfill leachate by commercial zeolite

Su et al. (2009) studied the adsorptive removal

(NanoChem). A removal efficiency of 100% was

of lead from water by porous polystyrene cation

achieved after 20 h of contact time. Shawabkeh (2009)

exchanger resin with impregnated nanosized particles

studied the sorption of Cu(II) on zeolite prepared from

hydrous manganese dioxide. The adsorption capacity

oil shale ash. The adsorption capacity was 504.6 mg/g.

was 395 mg/g. Karthikeyan et al. (2009) studied the

Sreesai and Sthiannopkao (2009) studied the application

application of polyaniline/alumina (PANi-AlO) and

of zeolite for the removal of Cu(II) and Zn(II) from

polypyrrole/alumina (PPy-AlO) composites for the

copper brass pipe industrial wastewater. At optimized

removal of fluoride from water. The adsorption

conditions, the average removal efficiency was 97%.

capacities for PANi-AlO and PPy-AlO were 6.6 mg/g

Qiu and Zheng (2009) studied the application

and 8 mg/g, respectively.

of cancrinite-type zeolite prepared from fly ash for the

1007 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Zhu et al. (2009a) studied the removal of Ni(II)

Botari and Di Bernardo (2009) pointed out that

and Cu by adsorption on magnesia-amended silica

monitoring and the determination of head loss were

granules prepared by calcining magnesium chloride-

important factors affecting porous medium filtration. The

impregnated silicon dioxide at 500 °C. At an initial

study also discussed the development of a model for head

concentration of 50 mg/L, more than 90% removal of

loss and proposed a mathematical semi-empiric model for

metal ions was achieved within 8 h of contact time at a

head loss in clean beds.

weak acid pH value. Azpeitia et al. (2009) studied the

Kim et al. (2009a) stated the household or

removal of lead by adsorption on platinum (Pt) and

residential wastewater originating from all sources other

ruthenium (Ru) supported on multiwall carbon nanotubes

than toilet as gray water. Li et al. (2009b) found that gray

(Pt/MWCNT

removal

water could be reused in gardening and agriculture for

efficiencies were 41 and 29% for Pt/MWCNT and

irrigation and soil fertilization after UF treatment. This

Ru/MWCNT, respectively.

Kabbashi et al. (2009)

treated water could also be used as toilet flushing water

the adsorption of Pb(II) on carbon

after disinfection. Zheng et al. (2009c) found that combined

nanotubes. At optimized condition, the sorption capacity

conventional wastewater treatment and UF membranes

was 102.04 mg/g.

produced particle free and hygienically safe water for reuse

investigated

and

Ru/MWCNT).

The

of domestic wastewater. It was found that UF retained the Filtration Introduction.

biopolymers present in wastewater. It was also noted that The

demand

for

water

is

membrane pore blocking or cake/gel fouling was the main

increasing rapidly due to high population growth and

fouling mechanism.

industrialization. A proper treatment of wastewater is

Sand Filtration. Aronino et al. (2009) showed

necessary in order to protect the environment and to ensure

that sand filtration could remove considerable amount of

availability of freshwater. A study by Vogt et al. (2009)

viruses such as Φ X174 (icosahedral bacteriophage of

revealed that drinking water wells near river were

Escherchia coli), MS2 (icosahedral bacterophage of

influenced by infiltration of river water. The study

Levivirdae family), and T4 (tailed phage of Myoviridae

discussed a multi-step approach consisting of (1) a

family with linear double-stranded DNA ) bacteriophages

qualitative analysis of the time series, (2) a spectral filtering

when the effluent passed through deep filter bed. Lu et al.

of the seasonal temperature and conductivity signals, (3) a

(2009a) revealed that iron-oxide-coated sand (IOCS) filter

cross-correlation analysis, as well as (4) a non-parametric

media adsorbed phosphate from water and wastewater. The

deconvolution of the time series for investigating the

results indicated that the adsorption process was well

infiltration of river water into the drinking water wells

defined by Langmuir, Freundlich and Temkin isotherm at

through underground sand layer.

various temperatures.

1008 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Ferric green rust (FGR) and ferrihydrite (FH)

artificial ground water was 1 log-unit greater than that in

coated sands exhibited high surface area and high redox

demineralized water.

flexibility (Wencka et al., 2009). These materials behaved

The removal of microorganisms such as fecal

as promising materials to treat contaminated water. The use

coliforms (FC), Escherichia Coli, somatic coIiphages and

of two different types of dual media filters, namely,

F-specific bacteriophages were examined by Torrens et al. (

filtralite

and

2009) using two vertical flow constructed wetlands

sand/anthracite filter was investigated by Mitrouli et al.

(VFCWs) and four intermittent sand filters (ISFs). The

(2009). Similar performance was observed for both types of

removal capacity of bacterial indicators was very sensitive

filter system at lower liquid velocity (5 m/h). However, at

compared to viruses and it was dependent on the depth and

higher velocity (10 m/h and 15 m/h), the filtralite

operation of the filters bed.

monomulti

filter

(expanded

clay)

monomulti filter exhibited the best overall performance.

Serikov

et

al.

(2009)

investigated

the

Combined fine sands and anthracite filter media

oxidizability of iron(II) to iron(III), to characterize the iron

by oxidation with air was able to remove manganese up to

colloids, as well as to determine the complexation of iron

97% (Graterol et al., 2009). A 49% removal of manganese

ions with humic acids and coagulation of iron colloids. The

from oxidation-filtration process was obtained by using

coagulation behavior of the iron colloids was abnormal at

calcium hypochlorite as oxidant instead of air. A 95%

pH 11 and higher. Sorbed humic substances on iron

manganese removal was reached by using combined

colloids were highly stable in solution at pH range 4.5 to 11

coagulation-flocculation and oxidation-filtration process,

and they did not allow the coagulation and formation of

where ammonium polychloride was used as coagulant.

suitable flocs for sedimentation and filtration. Membrane

A study was carried out to treat natural

filtration or flocculation followed by filtration through

wastewater using buried sand filtration (BSF) and buried

different solids materials was able to remove the iron

subsurface flow constructed wetland (BSSF-CW) system

colloids coated with humic substances.

(Gunes and Tuncsiper, 2009). The results showed that the

A study showed that the transport of copper

removal of biochemical oxygen demand (BOD), total

oxychloricle-based fungicides (COFs) colloid particles in

nitrogen (TN), and total phosphorous (TP) were 97, 85 and

water-saturated quartz sands columns under varying

69%, respectively. To investigate the role in the transport

electrochemical

of bacteria in groundwater, demineralized water and

affected by the hydrodynamic shear influences (Paradelo et

artificial ground water were kept separately in two

al., 2009).

and

hydrodynamic

conditions

were

saturated quartz sands bed of 5 m height (Lutterodt et al.,

Membrane Filtration. Ravanchi et al. (2009)

2009). The sticking efficiency on the sand surface in

discussed the viability of different membrane processes in petrochemical processes such as olefin/paraffin separation,

1009 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

light solvent separation, solvent dewaxing, phenol and

solids (TDS) by using hybrid RO and nanofiltration (NF)

aromatic recovery, dehydrogenation, oxidative coupling of

process.

methane and steam reforming of methane. Ghidossi et al.

A study was carried out to observe the effect of

(2009) found that high oily wastewater generated from

dissolved oxygen (DO) on the treatment of municipal

naval and commercial vessels could be treated effectively

wastewater (Dong et al., 2009a). The results indicated that

by using membrane process. Barrouk et al. (2009) showed

the DO concentrations could affect the treatment of

that

membrane,

municipal wastewater. At DO concentration 0.5 mg/L, the

prepared from natural moroccan phosphates by extrusion

COD, ammonia and TN removal efficiency were 94.5, 96.0

process, was effective to filter yeast suspension.

and 78.4%, whereas at 4.0 mg/L DO concentration, the

monotubular

macroporous

supports

Microfiltration-GAC system was effective for

removal of the above parameters were 96, 50.4 and 26.4%,

removal of color, NOM and other synthetic chemicals from

respectively

wastewater (Kim et al., 2009b). A 30% removal of UV260

Sutherland (2009) reviewed the developments in

from wastewater was obtained by using MF only, whereas

membrane media and membrane filtration systems. Seo and

MF-GAC system could remove 60% of UV260. The

Vogelpohl, (2009) investigated activated sludge separation

removal efficiencies of DOC, COD, TN, TP and turbidity

using membrane filtration. The authors examined biomass

were in the range of 42, 53, 15, 13, and 100% with the

separation using tubular membranes The results showed

GAC-MF hybrid membrane system whereas the removal of

that UF membrane could remove 75% of total organic

the above parameters were 25 to 30%, 20 to 25%, 5 to

carbon (TOC) and could be used for a long time due to its

10%, 5 to 8% and 100% with the MF membrane alone,

very high flux, germ free permeate with a molecular weight

respectively. 97.4% and 92.0% removals of turbidity and

cut-off of 100,000 Dalton (Da).

UV254 were also obtained by using a hybrid module

Simon et al. (2009) investigated the impact of

ceramic tubular MF membrane-GAC system (Lee et al.,

chlorine attack on the rejection of pharmaceutically active

2009a).

compounds (PhACs) by nanofiltration (NF) and RO Dixit et al. (2009) showed that reverse osmosis

membranes. For RO membrane, the rejection of PhACs

(RO) process was the cheapest and the easiest way to

was not changed after hypochlorite exposure, whereas the

obtain potable water from the brackish water normally

rejection was slightly increased in the case of NF, when

available at the taps. The authors developed a fundamental

exposed to dilute hypochlorite solution.

model of RO process for the production of drinking water

Park et al. (2009) developed a counting technique

from brackish water for domestic purposes. Singh (2009)

by using membrane filtration-differential mobility analyzer

foumd that 88% product water recovery was achieved from

(MF-DMA) to quantify suspended nanoparticles and

a brackish water contaning 3 700 mg/L total dissolved

dissolved solids in water in real time. The mass

1010 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

concentrations of dissolved solids estimated by this method

forward osmosis (FO)-RO process, the main operating

were similar to those obtained by the TDS method.

parameters of this process as well as their relationships

Wang et al. (2009c) found that polyvinylidene

with FO-RO process for the tratment of seawater. Hancock

fluoride (PVDF) MF could be used effectively for the

and Cath (2009) showed that the FO process had significant

treatment of laboratory prepared oily wastewater, and the

implications in the application of desalination of seawater

fouling could be removed successfully by applying

and reclamation of wastewater.

conventional cleaning method. Polyakov (2009) discussed

Membrane Fouling. Baek and Chang (2009)

the effect of parameters such as transmembrane pressure

showed that membrane fouling was dependent on the

(TMP), pore depth and initial radius, inlet concentration of

membrane material characteristics, water chemistry, and

suspended particles, as well as particle-collection efficiency

the degrees of pretreatment applied. The study was carried

of pore walls on the permeate rate and selectivity of UF and

out using two types of UF membranes and revealed that

MF membranes with same pore diameter as used in depth

hydrophilic membrane with pretreatment showed better

filtration. The study showed that the pore blocking and

fouling resistance.

resistance solely depended on the studied parameters.

A study was performed to model and predict the

Tansel et al. (2009) investigated the changes in

membrane fouling rate in a pilot scale drinking water

flux and membrane resistance with TMP. The membrane

production system at different operating conditions (flow

showed the minimum resistance in clean RO and NF

rate and filtration time) and feed water quality (turbidity,

membranes using logarithmic and second order polynomial

temperature, algae, pH) using a genetic programming (GP)

correlations. It was found that a second order polynomial

(Tae-Mun et al., 2009). The study revealed that GP model

function

more

could predict the filtration performance satisfactorily.

adequately than the linear correlation. Van Wagner et al.

Lippa et al. (2009) showed that low pressure membranes

(2009) showed that the rejection of sodium chloride in RO

suffered from particulate, organic and biological fouling

process was strongly affected by feed pH and water flux

during operation. During filtration, smaller particles (20 to

through the membranes. Wang et al. (2009e) revealed that

30 nm) dropped the permeability significantly than the

the addition of humic acids and alginate with proteins

larger particles (100 to 250 nm). Mondal and De (2009)

increased the rejection of proteins by using dead end MF.

pointed out that two mechanisms, namely, cake formation

described

the

flux-pressure

profile

Xia et al. (2009) found that membrane bioreactor

and pore blocking were responsible for membrane fouling.

with gravitational filtration (GFS-MBR) was an effective

A study showed that cross flow velocity, TMP,

combination for removal of biological phosphorous. It was

concentration and temperature affected the specific cake

also noted that COD/TP was the key factor to remove

resistance (SCR) (Wang et al., 2009d). Their relative

phosphorous biologically. Bamaga et al. (2009) described

degree of influence on SCR were 38.85, 28.32, 19.34, and

1011 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

1.3.49%, respectively. Ball clay suspension increased 5.9

aluminum oxide (Al2O3) composite MF membrane with an

times the cake resistance for dead end filtration compared

average pore size of 0.2 µm improved membrane

to cross flow filtration mode (Choi et al., 2009b).

hydrophobicity and shifted isoelectric point to the lower pH

van den Brink et al. (2009) varied the free

(Zhang et al., 2009d). These properties of composite

calcium concentration, total ionic strength and alginate

membrane enhanced membrane performance by reducing

concentration to observe the effect of increasing ionic

fouling for the treatment of oil emulsion water.

strength. The study revealed that the increments of ionic

Esquivel et al. (2009) investigated the fouling by

concentration had no impact on membrane fouling rate in

characterizing two natural waters using modified fouling

low fouling experiments, but decreased the fouling by 66 to

index (MFI)-UF and other parameters such as turbidity,

72% at high fouling conditions. Zhang et al. ( 2009c) stated

NOM, and UV254. The result showed that it was impossible

that air sparging could overcome concentration polarization

to

and was able to enhance the permeate flux significantly.

parameters. The characteristics and effect of biofouling

According to Masuelli et al. (2009), the membrane

materials

containing

20%

identify

fouling

using

traditional water quality

potential of soluble microbial products (SMP) and

sulfonated

extracellular polymeric substances (EPS) on membrane

polycarbonate (SPC) and the rest PVDF could eliminate

were studied by Zhang (2009). The result showed that SMP

irreversible fouling. Feng et al. (2009a) showed that MF

and EPS had negative effect on membrane fouling.

with polypropylene (PP) membrane was more sensitive to

Janus et al. (2009) developed a mathematical

fouling compared to PVDF membrane in the treatment of

model on fouling of MF and UF membranes. The model

wastewater containing Klebsiella oxytoca strain. Chae et al.

accounted the effect of different parameters, including

(2009) found that pressurized PVDF MF membrane was

backwash

more susceptible to fouling compared to submerged PVDF

compressibility. Badruzzaman et al. (2009) revealed that

MF membrane at high turbidity conditions, without

RO process was the most exhaustible technology for the

pretreatment; whereas at low turbidity conditions with

treatment of brackish water. The study also showed that

coagulation/sedimentation

two

membrane fouling and disposal of concentrate generated

membranes exhibited similar fouling behaviors at the same

from membrane process were the major problems of RO

TMP.

process, particularly for inland RO operation.

pretreatment,

the

mechanism,

cake

and

SMP

deposit

A study was carried out to investigate the fouling

Reduction of Membrane Fouling. Xu et al.

of MF using oil-water emulsion (Lue et al., 2009). The oil

(2009a) showed membrane fouling remediation and

retention was as high as 99.5% and as the oil content in the

cleaning strategies for hollow membrane filtration by

feed increased, the flow resistance was increased and the

ultrasonic reflectometry and wavelet analysis. Rocha et al.

flux was decreased. Titanium dioxide (TiO2)-doped

(2009) noted that the use of ultrasonic waves during

1012 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

filtration was able to retain 150% more flux compared to

At permeation velocity of 45 L/h·m2, MF process

conventional membrane filtration. The sonication also

decreased up to 33% of UV254 compounds, 9% of TOC,

improved medium regeneration capability, even under the

and 65% of iron, whereas the combined coagulation-MF

conditions of high TSS and oil and grease content.

process reduced up to 70, 47 and 100% for UV254

A

study

dielectrophoresis

showed (DEP)

that during

the

application

filtration

of

compounds, TOC and iron, respectively (Bergamasco et al.,

created

2009). In this study, chitosan was used as coagulant.

concentration polarization in membrane, reducing the

Poly

diallydimethylammonium

chloride

fouling in cross-flow membrane (Du et al., 2009). The

(PolyDADMAC) coagulant was used to investigate the

adition of adsorbents and coagulant was able to reduce

effect of fouling of UF and NF membrane (Hilal et al.,

fouling. By contrast, a study showed that the addition of

2009). The fouling of membrane for both filtration systems

more adsorbents or coagulants increased membrane fouling

increased in presence of salinity. For the treatment of TiO2

(Wu et al., 2009).

dispersed water with cross flow MF, a study showed that

Air sparging improved the filtration flux at lower

alum was the most effective coagulant at an optimum

suspension and at lower air velocities and this enhancement

concentration of 40 mg/L (Horcickova et al., 2009).

depended on the size of the particles (Hwang and Wu,

Johir et al. (2009) investigated the performance

2009). Under bubble flow, the enhanced filtration flux

of RO for seawater. The results showed that with inline-

decrased with increasing air velocity, and it became

flocculation-dual media filtration, the normalized flux

negative under slug flow. Al-Zoubi et al. (2009) showed

declined from 0.35 to 0.22 during the first 20 hours of

that the dissolved air flotation-NF/RO hybrid process

operation. Without any pretreatment, the flux declined from

reduced fouling and improved the performance of

0.18 to 0.11 during the first 20 hours of operation.

membrane process.

A study showed that PAC pretreatment was more

Effect of Pretreatment on Membrane Fouling.

efficient than flocculation-coagulation pretreatment for the

Citulski et al. (2009) used in-line addition of alum and

seawater in terms of MFI-UF and silt density index (Zhang

ferric chloride as coagulant with hollow fiber immersed UF

et al., 2009e). Another research showed that the addition of

membrane to treat secondary effluent from a municipal

PAC could reduce the impact of fouling effect of high algae

wastewater treatment plant. The phosphorous level was

due to seasonal variation of algae numbers in surface water

reduced from 5 mg/L to below 0.3 mg/L. Kweon et al.

(Kweon et al., 2009). Lohwacharin et al. (2009) found that

(2009) mitigated the fouling effect due to seasonal variation

the addition of carbon black (CB) prior to membrane

of turbidity on membrane by using inline coagulation

filtration as adsorbent reduced the membrane fouling

pretreatment.

significantly. Smith and Vigneswaran (2009) showed that the replacement of 15 g/d PAC and periodic removal of

1013 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

1.5% of the PAC slurry mixture had a positive impact on

led to more severe fouling in hydrophilic membrane rather

membrane fouling.

than fouling in hydrophilic membrane.

A

pretreatment

using

super-PAC

particles

A study showed that UV and titanium dioxide

compare to conventional PAC particles enhanced the

(UV/TiO2) photocatalysis was effective to control fouling

removal of dissolved organic matters in water (Matsui et

of MF membranes by removing NOM (Erdim et al., 2009).

al., 2009). The cake formed on the membrane surface was

The study also revealed that only TiO2 or UV irradiation

porous and was able to reduce both reversible and

was not effective to control MF membrane fouling. Iron

irreversible membrane fouling.

oxide coated (IOP) membrane adsorbed additional amount

A study was carried out using secondary effluents

of NOM compares to bare coated membrane (Yao et al.,

from wastewater treatment plants containing several types

2009).

The

results

indicated

that

a

hybrid

of organic foulants such as extracellular polymeric

photocatalysis/IOP coated membrane had higher DOC

substances (EPS), SMP, and humic acids (Horng et al.,

removals compares to those of bare membrane. In presence

2009). The study showed that photocatalytic oxidation

of fine colloidal matters, the fine particles entered into the

(PCO) along with membrane system was effective for

pore spaces of IOP coated membrane and they created

removal of EPS, SMP, and humic acids. PCO-MF hybrid

more fouling compared to bared membrane.

process was used to remove UV254 and UV436 of humic

Tratment of Membrane Concentrate. Ning et

acids (Bai et al., 2009). The result showed that near 100%

al. (2009) showed that a 70 to 90% recovery was attained

removal of UV254 and UV436 were obtained and TOC

from brackish water using conventional RO process. The

removal from this process was 84%. Zhang et al. (2009f)

study was also carried out using tandem RO process; the

revealed that one dimensional TiO2 nanowires degraded

recovery was in the range of 96 to 98%. The divalent and

humic acids by PCO and was able to reduce fouling of MF

monovalent

membrane.

Eventually the process became zero discharge process and

Lehman and Liu (2009) showed that ozonation

ions

were

separated

from

concentrate.

environmentally friendly.

was very effective for the degradation of NOM, which

Badruzzaman

et

al.

(2009)

revealed

two

finally reduced the fouling of membrane in the treatment of

innovative beneficial uses of concentrate produced from

water and wastewater using ceramic membrane. Oh et al.

membrane

(2009) showed that seawater created greater fouling in

elctrodialysis (BMED) and electrochlorination (EC). In

hydrophobic MF membrane compared to hydrophilic MF

BMED process, under electrodialysis, the concentrate

membrane. The study was also carried out using

formed mixed acids and mixed bases, whereas EC

preozonated water. It was found that the preozonated water

produced 0.6 % hypochlorite solution. The study did not

processes

including

bipolar

membrane

analyze the economic viability of the process.

1014 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Backwashing/Cleaning of Membrane. Hwang

industries could be treated by using actvated sludge and

et al. (2009) showed that periodic backwash removed

RO/NF combined processes. The result showed that the

completely fouling from membrane surface and part of

water could be reused after this combined treatment.

internal membrane fouling. The study also revealed that the

MF and UF along with NF were used to treat

irreversible membrane fouling was increased progressively

textile wastewater, where MF and UF were used as

during operation and the backwash of the membrane was

pretreatment steps (Fersi et al., 2009). The study revealed

able to recover the flux of the membrane.

that color, turbidity and TDS removal were higher than

Blanpain-Avet et al. (2009) investigated the

90%, accompanied with a substantial COD reduction.

kinetics and the effect of Bacillus cereus spore on cleaning.

The combination MF and NF was able to remove

A 0.5% by weight sodium hydroxide solution was used as

color by 99% and COD by 97% from indigo dyeing rinsing

cleaning reagent. The study revealed that the membrane

wastewater (Unlu et al., 2009). A study by Ahmad et al.

resistance decreased, following first order kinetics during

(2009) showed that bimodal porous silica/γ-alumina

the first 10 minutes of reaction. Due to the spore cells

membrane with improved permeability was able to reject

redeposition on the surface, the hydraulic membrane

more than 90% of the dye, at common operating

permeability could not be restored until after 15 minutes of

conditions. Cailean et al. (2009) used ultrasonication

membrane cleaning.

followed by UF to treat wastewater from textile finishing

Membrane Filtration of Textile Wastewaters.

and dyeing industries. The results indicated that 80% of

Simonic (2009) explained that textile dyeing processes

initial color was removed by this combined process.

could generate highly contaminated water, which was

The integration of photocatalytic oxidation

environmentally unfriendly and contained different types of

(PCO) with RO system removed the synthetic dyestuff

dyes, textile auxiliaries and chemicals. Harrelkas et al.

effluent by more than 95% and was able to reduce the

(2009) fond that conventional treatment method was not

salinity of wastewater generated from dyeing industry

effective to remove dye from textile water. The study also

(Berberidou et al., 2009). Chang et al. (2009b investigated

showed that coagulation-flocculation along with MF/UF

the treatment of digital textile printing wastewater to meet

increased the COD and color removals. In a MF scheme,

the direct discharge criteria. The results showed that

the removal of COD and color were 37 and 65%

ozonation along with UF and RO combined process were

respectively; whereas in a UF scheme, the corresponding

able to produce water, meting the discharged criteria.

results were 42 and 74%, respectively. Raju et al. (2009)

Membrane

Filtration et

of

Agricultural

discussed the electrocoagulation along with RO process for

Wastewater. Benitez

al. (2009a) revealed

the treatment of textile wastewaters in Tamilnadu. Ben

agricultural runoff was the source of herbicides in surface

Amar et al. (2009) noted that wastewaters from dyeing

waters and wastewaters. Combined ozonation and NF

1015 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

that

process was the most effective treatment process for the

obtained. A subsequent treatment of this water by using NF

removal of herbicides from agricultural runoff. A 80%

resulted in 98% rejection of copper.

removal was obtained by applying O3 and NF. Shaalan

Nguyen et al. (2009) discussed two available

(2009) described the treatment process of pesticide industry

forms of arsenic (As) found in water, namely, As(III) and

effluents and contaminated agricultural drainage water. The

As(V). The study also revealed that poly vinyl acetate

results showed that these waters could be treated effectively

(PVA) MF membrane removed a 37% of As(III) and 40%

by using a hybrid process, consisting of adsorption, UF and

of As(V). The removal increased to 84% of As(III) and

NF.

90% of As(V) by adding nanoscale zero valent iron into the Membrane Filtration of Metals. Gabor and

wastewater. Adsorption-membrane filtration process with

Endre (2009) showed that membrane separations, including

0.4 µm diameter removed boron from 2 mg/L to the

electrodialysis (ED), UF, NF and RO were effective to

recommended level set by World Health Organization

remove toxic chemicals such as Ni(II) and Zn(II) from

(Bryjak et al., 2009). An adsorption-MF hybrid process was

industrial wastewaters. Ultrafiltration with 10 kDa pore

able to remove 99.44% cesium by using potassium zinc

sizes was used to remove Cd from an aqueous solution

hexacyanoferrate (K2Zn3[Fe(CN)6]2) as adsorbent (Zhang

(Ennigrou et al., 2009). In this study, a polymer

et al., 2009b).

(ammonium acrylate) was used to adsorb metal by forming

Takahashi et al. (2009) reported that Hg at µg/L

polymer metal complex. The result suggested that Cd

levels could be detected by using dithizone nanofiber-

rejection reached up to 99% at twofold acrylate ion

coated membranes. The study was carried out using

concentration.

cellulose ester membrane with a 500 nm thickness of

NF membrane coated with a strong chelating

dithizone nanofiber coating. The results showed that Hg(II)

agent, diethylene triamine pentaacetic acid (DTPA), was

ions were deposited in the dithizone layer of the membrane

used to remove zinc and iron from wastewater generated

at pH 2.7. Ballet et al. (2009) discussed the effects of

from electroplating industries (Boricha and Murthy, 2009).

membrane characteristics, feed pressure, ionic strength,

The results showed that 94% of zinc and 93% of iron were

concentration, and pH on the removal of heavy metals

removed by this process. UF and NF of PVDF materials

using NF for the wastewater generated from metal

were used in cable industries for separation of waste

processing industries.

emulsions (Karakulski et al., 2009). Using UF with

Membrane Filtration of Refinery Wastewater.

molecular weight cut-off (MWCO) 10 kDa, a 99% removal

A study using UF of polysulfone (PS) (30 kDa) and a

of oil and lubricants in the treated emulsions and a

polyacrylonitrile (PAN) (20 kDa) membranes was carried

complete removal of solids and colloidal substances were

out to treat oily and greasy water at different operating conditions (Salahi et al., 2009). The study showed that

1016 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

PAN membrane was more effective than PS membrane and

toxic components such as sulfate, acids, and different metal

removed 99.7, 77.2, 63.3, 65.4, 29.8, 100% and 99.5% of

species. The results suggested that the membrane filtration

oil and grease content, TOC, COD, BOD5, TDS, TSS and

was able to remove the toxic components from the mine

turbidity, respectively.

water.

Nandi et al. (2009) reported a removal of 96.97% Sedimentation/Flotation

oil (initial concentration of 50 mg/L) in oil-water emulsion by using low-cost ceramic membranes, prepared locally

Sedimentation and flotation processes are mainly

from kaolin, quartz, calcium carbonate, sodium carbonate,

used to remove suspend particles from water and

boric acid, and sodium metasilicate. Silalahi and Leiknes

wastewater. In a study by Boutilier et al. (2009), the

(2009) observed the fouling characteristics of membranes

inactivation, adsorption, and sedimentation of Escherichia

used to treat wastewater from oil industry. The results

coli were investigated in dairy wastewater lagoon and

showed that full restoration of a fouled membrane was not

domestic septic tank effluent. The results showed that the

possible by a single cleaning, and the cleaning efficiency

inactivation of Escherichia coli was the most significant

was dependent on temperature, concentration and TMP of

removal process in the wastewaters and wetlands, with a

the cleaning solution.

first order rate constants of 0.09 d-1 at 7.6 °C to 0.18 d-1 at

Membrane

Filtration

of

22.8 °C for wastewater in the laboratory, and 0.02 d-1 to

Pharmaceuticals

0.03 d-1 at 17 °C for domestic wetlands.

Wastewaters. Busetti et al. (2009) carried out a study on the treatment of pharmaceutical secondary effluent product

Komissarov

et

al.

(2009)

developed

a

water from recycling plants by using MF-RO process. The

mathematical model for the liquid flow pattern in an

results indicated that MF/RO treatment removed the

aerotank-sedimentation tank. The recycle stream was in the

majority of the pharmaceutical contaminants to below the

form of dispersion and it depended on the Peclet number

detection limit.

and recycling stream fraction as the model parameters.

Membrane Filtration of Other Industrial

Compressed air was applied to aerate backwash water from

Wastewater. Ghasemipanah et al. (2009) showed that RO

the filters used for iron and manganese removal from

process removed more than

groundwater (Lomotowski and Wiercik, 2009). The results

95% of solids from

regeneration water generated from an ion exchange plant.

indicated

that

the

aeration

of

the

stream

before

Tannery wastewater was reclaimed by using a combined

sedimentation reduced the backwash time. It also enhanced

treatment method, consisting of pre-treatment by sand

the iron and manganese precipitation rates as well as the

filtration, subsequent UF, followed by RO (Roig et al.,

efficiency of the water clarification in the settling tank.

2009). Rieger et al. (2009) investigated the applicability of

The effect of the pretreatment of drinking water

membrane filtration (NF and RO) to mine water containing

with coagulation/sedimentation before immersed MF

1017 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

membrane process was investigated by Moon et al. (2009).

overall color, COD, and suspended solid removal were

The pretreatment step enhanced the performance of the

97.3, 96.9 and 86.7%, respectively.

membrane system by buffering the sudden shock of solid

Increasing hydraulic loading rates of dissolved air

loading and maintaining the stable flux and transmembrane

flotation (DAF) by increasing the height of the reactor

pressure. The drawback of the system was the membrane

resulted in a higher efficiency due to the deeper bubble bed

fouling due the formation of the inorganic aluminum based

depth (Han et al., 2009). Particle counter was used to locate

coagulant scale. Sedimentation/coagulation was used to

the bubble bed interface and the results indicated that the

remove pollutants from oily wastewaters of car washes

operational conditions changed the bubble bed profile. The

discharge streams (Rubi et al., 2009). Four coagulants,

deeper bed resulted in higher effluent water quality. DAF

including Servical P (aluminum hydroxychloride), Servican

process with surface modified bubbles was performed for

50 (poly(diallyldimethylammonium chloride)), aluminum

algae removal instead of the coagulation-flocculation

sulfate and ferric chloride, were used for coagulation

treatment (Henderson et al., 2009). Bubble modification by

process and the results demonstrated that 82% of oils, 88%

aluminum sulfate resulted in 60% algae removal and a

of TSS, 73% of COD, and 51% of turbidity were removed

decrease in zeta potential and microfiltration generation.

after sedimentation.

63% and 95% algae removals and no change in zeta

Mathematical models using turbulence to study

potential

were

achieved

by

cationic

surfactant

the sediments deposition process in a settling basin was

cetyltrimethyl-ammonium bromide and cationic polymer,

developed by Simanjuntak et al. (2009). The results were

polydiallyldimethylammonium chloride, respectively.

compared with empirical methods, 1 and 2D mathematical models.

Based

on

these

useful

air flotation (SAF) could harvest algae contained within a

recommendations regarding the settling basin design were

wastewater oxidation pond. At a lower air: solids (A/S)

suggested.

ratio, lower energy requirements, and higher loading rates,

Non-degradable

results,

antibiotic

some

Wiley et al. (2009) demonstrated that suspended

fermentation

wastewater was treated by the combination of coagulation,

SAF showed higher algae harvesting than DAF system.

Fenton and sedimentation processes (Xing and Sun, 2009).

Miranda et al. (2009a) conducted a study to

The results showed that at pH 4 and 200 mg/L of polyferric

investigate the effect of the newly developed chemicals to

sulfate as the coagulant, 66.6% of color, and 72.4% of

optimize DAF system to treat paper production wastewater.

COD removal was achieved. The optimum condition for

The results of the experiments, performed at different

Fenton process was found to be 150 mg/L of hydrogen

conditions including various dose or with a flocculant,

peroxide (H2O2), 120 mg/L of iron sulfate (FeSO4) at 1 h of

indicated that polyaluminum nitrate sulfate salt and a

reaction time. At the controlled pH 7 of the effluent, the

polyamine were the most efficient chemicals for the treatment.

In another study by Miranda et al. (2009b)

1018 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

polyaluminum nitrate sulfate salt combined with a

including ozone (O3), ultraviolet light (UV) combined with

quaternary polyamine was tested in a industrial trial to

hydrogen peroxide (H2O2), titanium dioxide (TiO2)

evaluate their efficiency on the DAF. The findings

combined with UV irradiation, Fenton, and photo-Fenton

demonstrated the ability of the new chemical to improve

on the degradation of different classes of organic

the contaminants removal by DAF, even at high

contaminants, especially pharmaceuticals, was reported.

concentration.

Klavarioti et al. (2009) reviewed and assessed the

Motor oil removal efficiency from water in

effectiveness

continuous froth flotation column was evaluated by changing

the

surfactant

concentration

and

of

various

AOPs

for

removal

of

pharmaceutical from aqueous systems.

bubble

Highly concentrated sulfamethoxazole solutions

parameters (Watcharasing et al., 2009). The results showed

were treated using advanced oxidation by photolysis,

that by increasing the concentration of the surfactant,

UV/H2O2 and photo-Fenton processes (Gonzalez et al.,

branched alcohol propoxylate sulfate, sodium salt, size and

2009). The highest removal (79.1%) was obtained by

rising velocity of air bubbles decreased, while the specific

UV/H2O2 reaction using a 254 nm UV lamp with an initial

surface area, bubble surface area flux, bubble number flux,

H2O2 concentration of 200 mg/L.

and residence time of the air bubbles increased after

UV/H2O2

treatment.

process

was

examined

for

the

photodegradation characteristics of pharmaceuticals and personal care products (PPCPs) by Kim et al. (2009d).

Oxidation

Knowing that most of PPCPs could not be removed in UV

Oxidation processes are chemical treatment

disinfection process in wastewater treatment, it was found

methods used to remove organic and inorganic materials

that UV/H2O2 treatment was capable of more than 90%

from water and wastewater. This section includes oxidation

removal of all the PPCPs, except seven PPCPs including

processes such as advanced oxidation, ozonation, Fenton

cyclophosphamide and 2-QCA. The effectiveness of UV

processes, electrochemical processes, wet air oxidation, and

and UV/H2O2 process for the removal of pharmaceuticals

supercritical oxidation as well as miscellaneous oxidation

in real wastewater was investigated by Kim et al. (2009c).

processes.

The presence of 41 pharmaceuticals, including 12

Advanced Oxidation Processes. A report of the

antibiotics and 10 analgesics were detected in tested water.

recent studies using advanced oxidation processes (AOPs)

Some pharmaceuticals such as ketoprofen, diclofenac and

photochemical processes was presented by Huang et al.

antipyrine were removed using UV. However, the removal

(2009b). The impact of important conditions such as light

efficiencies of macrolide antibiotics such as clarithromycin,

sources, catalysts and reactors were summarized. In another

erythromycin and azithromycin for UV alone process were

review paper by Melo et al. (2009), the efficiency of AOPs,

very low. In UV/H2O2 process, 90% removal efficiency

1019 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

was achieved in 39 pharmaceuticals. Kim et al. (2009e)

that doping of Fe3+ ion improved the photodegradation

investigated the O3, UV/H2O2 and O3/UV treatment

performance of TiO2 coated surfaces and its kinetics

processes for water reuse of pharmaceuticals and PPCPs.

followed a pseudo-first-order reaction, with a rate constant

The results showed that for the effective removal of PPCPs

of 0.0202 min-1. In another study, the kinetics of

in secondary effluent, the O3 treatment was the most cost-

decolorization of MG from textile industry was carried out

effective treatment option. However, using an ozone dose

by using ultrasound (US)/UV/H2O2 process (Behnajady et

of more than 4 mg/L, the formation of bromate was

al., 2009). The results indicated that the decolorization

expected. UV/H2O2 treatment was a beneficial method

kinetics fitted pseudo-first order kinetics. It was shown for

because of no formation of bromate.

cost analysis that the figure-of-merit electrical energy per

In an O3/H2O2 system, a bubble reactor was used

order was sensitive to the operational parameters such as

for ozonation of the antibiotic ciprofloxacin (De Witte et

initial concentrations of H2O2 and MG, temperature, and

al., 2009). One of the observed by-products was

power of the lamp.

desethylene ciprofloxacin, which was identified using high

UV/H2O2 was used for removal of Rhodamime B

performance liquid chromatography mass spectrometry

(AlHamedi et al., 2009). The results showed that dye

(HPLC-MS) analysis. The formation of desethylene

concentration, pH, H2O2 dose and irradiation time

ciprofloxacin

influenced the degradation of the dye. A maximum of 73%

depended

on

pH,

with

the

highest

concentration at pH 10.

decoloration of the 10 mM dye was achieved under the

Three treatment methods, including two AOPs,

optimum conditions of 1.67 mM of H2O2 at pH 7,

and GAC adsorption/biosorption were compared using

following a first order kinetics. It was also shown that the

synthetic landfill leachate as a contaminant (Abdul et al.,

low molecular weight aliphatic alcohols and acids were

2009). In AOPs, UV/TiO2 and H2O2/Fe+2 were used. The

some of the degradation products of Rhodamine B.

results showed that the percentage of TOC removal by

Various AOPs, including H2O2, UV, UV/H2O2,

photocatalysis, Fenton oxidation and bio-sorption was 30,

Fe2+/H2O2, and UV/Fe2+/H2O2 were used for decolorization

60, and 85%, respectively. However, the Fenton's process

of textile dye Reactive Red 195 (de Amorim et al., 2009).

showed faster degradation kinetics compared to the other

The results showed that photo-Fenton system with the use

two methods.

of blast furnace dust (BFD) was more efficient for

The degradation of Malachite Green (MG) dye in

decolorization; however, the use of BFD in the Fenton

aqueous solution under UV and vis-light irradiation in

system without irradiation reached the same efficiency as

presence of two catalysts was investigated (Asilturk et al.,

when no BFD was used. The use of BFD increased the

2009). Fe3+ ion-doped TiO2 and undoped TiO2 were used

rates of reactions and seemed to be very promising as a

for coating the glass surface for irradiation. It was shown

source of iron.

1020 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Photocatalytic degradation of C.I. Basic Red 46

concentrations of dye and H2O2, pH, and temperature were

(BR46) and C.I. Basic Yellow 28 (BY28) dyes was investigated by Gozmen et al. (2009).

effective for decolorization.

The rate of

The quality of an industrial textile effluent before

degradation of BR46 was higher than BY28 for all

biological treatment was evaluated using H2O2/UV process

experiments in single dye solutions. At pH 3, the highest

(Mounteer et al., 2009). The results showed that the

TOC removal efficiency was observed by adding 5 mM

removal efficiency increased with increasing H2O2 dose

periodate ion to the solution along with 1 g/L TiO2 for both

from 0 to 5 mM; however, increasing pH from 4 to 10

dye solutions. Mineralization of 68, 76 and 75% were

showed a negative effect on color and toxicity removals.

found after 3 h of illumination for 100 mg/L BY28, 100

Based on the results, it was expected that combined AOP-

mg/L BR46 and 50:50 mg/L mixed solutions, respectively.

biological treatment of the mill effluent would be a good

Photocatalysis of Reactive Black 5 dye was

treatment option.

carried out using TiO2 P-25 Degussa and zinc oxide (ZnO)

Ahmed et al. (2009) studied the treatment of pulp

in a mixed batch reactor (Kapoor and Kanwar, 2009). The

and paper mill wastewater (PPMW) using UV/H2O2. The

effect of some parameters such as pH, initial dye

system led successfully to the almost-complete elimination

concentration, and catalyst dose on the decolorization

of absorbance at 330 and 281 nm and COD using 2.1 g/L of

efficiency was studied. It was found that photocatalyst ZnO

H2O2 at 28 °C. During the UV/H2O2 treatment of PPMW, a

was more efficient compared with TiO2.

continuous decrease of pH and a fast total phenols

The photocatalytic degradation of three textile

disappearance were observed, suggesting the mechanism of

dyes, including C.I. Acid Orange 10 (AO10), C.I. Acid

photochemical oxidation of organics by degradation of

Orange 12 (AO12) and C.I. Acid Orange 8 (AO8) was

lignin derivatives aromatic intermediates.

investigated to study the effect of chemical structure on

Photocatalysis of lignin, the major constituent of

photocatalysis efficiency (Khataee et al., 2009a). The

paper mill, by UV/TiO2 was investigated using model

UV/TiO2 experiments were carried out using a 15-W UV

compounds (Krishna et al., 2009). The optimum catalyst

lamp (365 nm). The results showed that the photocatalytic

dose and pH for the best possible degradation was

decolorization of the dyes followed the order of AO10 >

evaluated.

AO12 > AO8. After 6 h of reaction time, the dye solutions

compounds were established. The effect of the nature of

could be completely decolorized and mineralized, with a

phenolic units on photo degradation was studied by

TOC removal higher than 94%. Decolorization and

comparing the initial degradation rates.

The

absorption

characteristics

of

model

mineralization of C.I. Reactive Blue 268 by the UV/H2O2

Three AOPs, including Fenton, electro-Fenton,

process was investigated by Novak et al. (2009). The

and electrochemical oxidation with iron promoting (EOIP) were investigated for treatment of an actual industrial

1021 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

wastewater (Chu et al., 2009d). It was found that all three

60 min, indicating the formation of some intermediate

processes were able to treat the wastewater with different

compounds. Chu et al. (2009a) also investigated the

efficiencies. With the same H2O2 concentration, the

degradation of simazine by UV/TiO2. The optimum TiO2

oxidation power of the AOPs increased in the order of

dosage was found to be 0.1 g/L and the optimum pH value

Fenton < electro-Fenton < EOIP. The results showed that

was 9.0. The electrospray ionization (ESI)/LC/MS results

EOIP was a promising alternative for removal of COD and

suggested that dealkylation was the major pathway of

color from organic wastewater.

simazine photodecay in UV/TiO2 system, with the final

A combined wastewater treatment including

product of cyanuric acid.

coagulation, flocculation, neutralization, and oxidation was

UV/H2O2/micro-aeration process was employed

studied by Duran et al. (2009). Different AOPs, including

for the decomposition of dichloroacetic acid (DCAA) in

UV/H2O2, Fenton, UV/Fenton, and UV/H2O2/O2 were

water (Chu et al., 2009b). UV radiation, H2O2 or micro-

investigated as oxidation treatments. The results showed

aeration alone could not remove DCAA, while their

that the total cyanide destruction was achieved in the

combination

photocatalytic process after 60 min, while 180 min was

completely. More than 95.1% of DCAA could be removed

needed to remove 80% of formates.

in 180 min under UV intensity of 1 048.7 µW/cm2, H2O2

Treated wastewater using AOPs as a source of

was

able

to

degrade

the

compound

dosage of 30 mg/L and at micro-aeration flow rate of 2

reuse water with the characteristics of drinking water was

L/min.

studied by Luiz et al. (2009). UV irradiation at 254 nm with

UV/H2O2/microaeration (MCA) was employed

and without H2O2 was employed for tertiary treatment of a

by Gao et al. (2009a) for the photochemical degradation of

slaughterhouse wastewater. The results showed that the

trichloroacetic acid (TCAA). UV and H2O2 alone were

H2O2/UV treatment was 5.2 times faster than UV alone in

relatively slow treatments for TCAA degradation and MCA

removal of aromatic compounds.

alone could not remove TCAA. However, the combination

Peroxon treatment (O3/H2O2) was employed for

process of three of them was more effective than UV/H2O2.

degradation of simazine in aqueous solution (Catalkaya and

More than 93.4% of TCAA was degraded within 180 min

Kargi, 2009). With a constant ozone concentration of 45

using UV radiation, 30 mg/L of H2O2 dosage and MCA

mg/L, both simazine and H2O2 doses affected simazine

flow rate of 25 L/min in neutral conditions.

removal, while pH and pesticide dose had more prominent

The

degradation

of

halogenated

2,4-

effect on TOC removal. At pH7, almost 95% of the initial

dichlorophenoxyacetic acid (2,4-D) was carried out using

simazine concentration (2 mg/L) was removed within 5 min

UV/H2O2/micro-aeration (Chu et al., 2009c). More than

using 75 mg/L H2O2. However, at simazine concentration

95.6% of 2,4-D with initial concentration of 100 µg/L was

above 2 mg/L, mineralization was not completed even after

removed in 90 min of UV radiation in presence of 20 mg/L

1022 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

H2O2 at pH 7 and at room temperature. The results showed

was highest, with a first-order rate constant in the order of

a

6.0 × 10-3 s-1.

higher

removal

efficiency

of

2,4-D

by

using

UV/H2O2/micro-aeration process compared to UV/H2O2

The improvement in the biodegradability of

process.

persistent organic compounds by pre-oxidation was The effect of nitrate on the UV oxidation of 2,4-

investigated by Christensen et al. (2009). A non-

DCP was studied by Ko et al. (2009). It was found that

biodegradable compound, dichlorodiethyl ether (DCDE),

nitrate enhanced the oxidation of 2,4-DCP by producing the

was used as a test chemical. Fenton reagent, ozonation, and

hydroxyl radicals (•OH) from nitrate photolysis with the

UV/H2O2 were used for oxidation of DCDE. Pre-oxidized

low initial H2O2 concentrations of 0 to 5 mg/L; however, it

DCDE solutions were then subjected to biological

hindered the oxidation with an initial H2O2 concentration of

treatment using activated sludge. The results showed that

less than 10 mg/L. This adverse effect was not observed

the biodegradability of pre-oxidized DCDE increased,

with a high initial H2O2 concentration of 20 mg/L at the

reaching about 90% for all three oxidation methods versus

reaction times of 1 to 2 min.

zero for non-oxidized DCDE.

The

(3-CP),

Arslan-Alaton et al. (2009a) investigated the

dichlorophenol (2,4-DCP) and pentachlorophenol (PCP) in

treatment of four aryl sulfonates (naphthalene sulfonic

both water solutions and synthetic domestic wastewater

acids, 1 amino-8-naphthol-3,6-disulfonic acid (H-acid), 2

containing

oxidation

chlorophenols

of

chlorophenol

using

O3/OH-,

O3/H2O2,

naphthylamine 3,6,8trisulphonic acid (K-acid), 7 amino-4-

O3/H2O2/OH- and H2O2/UV was studied by Kucharska and

hydroxynaphthalene-2-sulfonic acid (J-acid) and benzene

Naumczyk (2009). The efficiency of treatment was as

sulfonic acid (Para base)) using H2O2 combined with UV-C

follows: PCP > 3-CP > 2,4-DCP. The results also showed

light in aqueous solutions. The highest treatment efficiency

that the O3/OH- process had better degradation, followed by

and reaction kinetics were obtained for the relatively

O3/H2O2/OH- > O3/H2O2 > H2O2/UV.

simpler structured Para base. It was identified using mass

Alnaizy and Ibrahim (2009) investigated the

spectrometric analysis that the photodegradation products

degradation of methyl tert-butyl ether (MTBE) using

of the H2O2/UV-C treatment were mainly hydroxylated

UV/H2O2 process. A low-pressure and a high-pressure

compounds.

mercury lamp were employed. Neither H2O2 nor UV alone

Chen et al. (2009c) studied the kinetics of

was very effective for MTBE oxidation; however, a

photocatalytic degradation of aliphatic carboxylic acids

complete MTBE degradation was achieved in less than 15

using artificial UV light and nano-TiO2 powder as the

min in presence of UV/H2O2. The results indicated that the

catalyst. The results indicated that the experimental data

MTBE degradation rate with the high-pressure UV source

fitted the Langmuir-Freundlich-Hinshelwood model, with

1023 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

the coefficient of determination (R2) varying from 0.880 to

was investigated in order to treat organic polluted

0.999.

wastewaters (Ji et al., 2009b). The results of photocatalytic Dnieper River and model fulvic acids solutions

experiments showed that the thermodynamics of the

were treated using O3, UV radiation, and O3/UV, then the

degradation reaction for the organic pollutants in AOPs

impact of H2O2 on the change of the generalized indicators

corresponded with the experimental measurements rate of

of water quality was investigated (Goncharuk et al., 2009).

degradation reaction.

It was confirmed that during O3/UV treatment, the

Levadnaya et al. (2009) treated microorganism

additions of 1 to 5 mg/L of H2O2 hampered the destruction

Escherichia coli K-12 with ozone in water in the presence

of fulvic acid at pH 6.3. However, it had a contribution in

of humic acids and H2O2. It was found that for water

the oxidation process of organic contaminations by all

decontamination using ozone, the radicals played an

methods at the pH higher than 7.

important role. Stable activated oxygen-containing radicals

The treatment efficiency of UV/TiO2 and

as well as radicals of organic compounds were formed

UV/TiO2/chemical oxidant processes for the removal of

during ozonation. Photocatalytic degradation of Michler's

hazardous heavy metals and humic acid in aqueous TiO2

Ketone (MK) using TiO2/UV was investigated by Lu et al.

suspensions was investigated by Jung et al. (2009). The

(2009b). The results showed complete oxidation of MK

reaction rate of heavy metals and humic acid increased with

after 24 h and more than 97.5% MK mineralization after a

increasing TiO2 dosage in the TiO2 concentration range of

32h exposure to UV irradiation at 365 nm.

0.1 to 0.3 g/L, after which the removal efficiency was

The degradation of p-chlorophenol using AOPs

reduced. It was also shown that with the addition of

UV/H2O2, microwave/H2O2 and both in the absence of

oxidants to the UV/TiO2 system, the degradation efficiency

hydrogen peroxide was studied by Movahedyan et al.

increased.

(2009). It was found that the optimum conditions achieved

The decomposition of aqueous ametryn using

for the best rate of degradation were pH 7 and H2O2

UV/H2O2 was studied by Gao et al. (2009b). The results

concentration of 0.05 M for UV/H2O2 system and pH 10.5,

showed that the rate of removal was affected by H2O2 and

H2O2 concentration of about 0.1 M and microwave

ametryn concentrations and not influenced by pH. It was

irradiation power of about 600W for microwave/H2O2

also indicated that chlorine (Cl-), bicarbonate (HCO3-), and

system, at constant p-chlorophenol concentration. It was

carbonate (CO32-) significantly decreased the degradation

proved that the energy consumption of UV/H2O2 process

rate; however, sulfate (SO42-) did not have any impact on

was 67% compared with the microwave/H2O2 process.

the rate of ametryn removal.

The removal of 3-chloro-1,2-propanediol (3-

The application of AOPs for the degradation of

MCPD) from water was evaluated using hydrolysis and

several chlorinated aliphatics, benzene and its derivatives

photolysis processes (Nienow et al., 2009). It was shown

1024 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

that 3-MCPD underwent hydrolysis at near neutral pH. It

A comparative study was carried out to assess the

was also indicated that 3-MCPD did not undergo direct

2,4,6-Trichlorophenol (2,4,6-T) degradation by advanced

photolysis.

oxidation processes, including UV, UV/H2O2, Fenton,

Racyte et al. (2009) investigated the effect of pH

UV/Fenton and UV/TiO2 (Saritha et al., 2009). UV/Fenton

on the UV/H2O2 process in decolorizing textile wastewater

process was found to be more effective in degrading 2,4,6-

polluted with commercial reactive dyes, Reactive Yellow

T. The optimum conditions were pH 3, Fe2+ at 5 mg/L,

84 and Reactive Red 141. At pH 3, UV/H2O2 was found to

peroxide concentration of 100 mg/L for an initial 100 mg/L

be more efficient than at the original wastewater pH, with

of 2,4,6-T concentration at room temperature. Because of

decolorization in 2 h versus 5 h at original pH. Rivas et al.

color and organic problem of industrial wastewater

(2009a) compared different advanced oxidation in the

outflow, Shu et al. (2009) conducted a study using coupling

presence of perovskites in degradation of pyruvic acid. It

the zero-valant iron (ZVI) nanoparticles with UV/H2O2

was found that UV and H2O2 (with or without perovskite)

oxidation process to treat a simulated industrial wastewater

gave the best pyruvic acid removal, while the best results of

containing a di-azo dye, C.I. Acid Black 24. TOC and color

mineralization was obtained with O3/UV in the presence of

removals as well as organic mineralization were successful

perovskites. In one study by Salgado et al. (2009), AOPs,

achieved and shorter time was needed compared to those

Fe2+/H2O2, UV/H2O2, and direct photolysis were applied to

obtained by UV/H2O2 process.

decolorize two synthetic wastewater containing indigo and

Ugurlu and Karaoglu (2009) investigated the

azo dyes and laundry effluent. It was demonstrated that at

removal of adsorbable organic halogen (AOX), total

pH 3 and 27 ºC, the wastewater containing 20 mg/L indigo

nitrogen and chlorinated lignin from bleached Kraft mill

carmine and Congo Red dyes was completely decolorized.

effluents by UV oxidation in the presence of H2O2, utilizing

Santos

UV/H2O2

TiO2 as photocatalyst. It was found that the optimal

photodegradation of polyethyleneglycol. It was proved that

condition for the removal of AOX was found using an

the UV/H2O2 involved consecutive reactions, where the

initial H2O2 concentration of 20 mg/L and reaction time of

larger and ethyleneglycols degraded to smaller and low

50 min. The UV/TiO2/H2O2 system was capable to degrade

molecular weight carboxylic acids, such as glycolic, oxalic

total nitrogen and chlorinate and degrade lignin in bleached

and formic acids. The NOM degradation by UV/H2O2 in

Kraft mill effluents. The combination of UV photolysis and

drinking water was investigated by Sarathy and Mohseni

ozonation was used to inhibit the regeneration of N-

(2009). The treatment involved the degradation of

nitrosodimethylamine (NDMA) in drinking water (Xu et

recalcitrant

NOM

al., 2009d). The regeneration potential of NDMA was less

compounds,

with

et

al.

(2009)

into

investigated

more

increments

readily in

the

biodegradable

formaldehyde

and

treated by UV/O3 than treated by UV irradiation alone.

acetaldehyde concentrations.

Yuan et al. (2009) investigated the degradation of four

1025 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

pharmaceutical compounds (PHACs), including ibuprofen,

damaged after regeneration because of excessive oxidation

dephenhydramine, phenazone, and phenytoin by UV

of its surface.

photolysis and UV/H2O2 process with a low-pressure lamp.

The oxidation of local scrubber wastewater

The predicted oxidation rate constants approximated the

(LSW) using ozonation, catalytic ozonation (O3/Al2O3 and

experimental

O3/TiO2-Al2O3), and photo-catalytic ozonation (UV/TiO2-

ones.

The

intermediates

created

after

photodegradation were also analyzed.

Al2O3, O3/UV and O3/UV/TiO2-Al2O3) was investigated by

UV/H2O2 and Fenton processes were investigated

Chou et al. (2009). Based on the results, catalyst Al2O3 and

for the degradation of 2-hydroxybeiizoic (2-HBA) (Zanta

TiO2-Al2O3 promoted the TOC removal during catalytic

and Martinez-Huitle, 2009). It was shown that Fenton

ozonation of LSW, under neutral or alkaline buffer

process was the most effective under acidic conditions, so

condition. Using the Al2O3, a highest promotion in TOC

that 2-HBA could be degraded in a very short time. The

removal was achieved.

optimum pH was around 4 to 5. Zhao and Zhao (2009)

A complex industrial park wastewater was treated

investigated the decoloration of sulfuric acid (H2SO4)

using ozonation (Fanchiang et al., 2009). A low efficiency

leachate from phosphorus-saturated alum sludge using

of COD removal with increasing of BOD5 appeared after

H2O2 and AOPs (H2O2/Fe2+, UV/H2O2/Fe2+). All the three

ozonation. It was shown that the ratio of BOD5/COD

processes were shown to be efficient in decoloration.

increased from an initial of 0.27 to a maximum of 0.38.

Ozonation. The use of intermediate ozone for

A post-ozonation method followed by sand

primary disinfection of Henrico County VA water

filtration was investigated for the removal of 220

treatment plant was investigated by England et al. (2009).

micropollutants in a wastewater treatment plant (Hollender

The cost of the whole process with achieving the

et al., 2009). Post-ozonation was capable of reacting with

disinfection goals was also included in the study.

activated aromatic moieties such as sulfamethoxazole,

Alvarez et al. (2009) studied the removal of

diclofenac, and carbamazepine at pH 7. However, the more

organic compounds using two methods involving ozone

resistant compounds to oxidation by ozone such as atenolol

and GAC, simultaneous ozonation and adsorption and

and benzotriazole were eliminated with increasing ozone

GAC/O3-regeneration. The results showed that the use of

doses. It was demonstrated that biological sand filtration

ozone in combined process was more efficient than

was an efficient additional barrier for the elimination of

ozonation process alone. In the GAC/O3-regeneration, two

biodegradable compounds formed during ozonation.

steps were involved: dynamic adsorption onto GAC

A

winery

wastewater

containing

organic

followed by regeneration of the spent GAC with gaseous

substances was treated in a bubble column ozonation

ozone. This method showed limited capacity for COD

reactor (Lucas et al., 2009). It was observed that COD

removal. It was also observed that the GAC became

decreased steadily under ozonation at the natural pH of the

1026 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

wastewater (pH 4). The degradation rate was accelerated at

studied

alkaline and neutral pH due to the formation of •OH

(Matheswaran and Moon, 2009). The overall reaction rate

radicals formed during the ozone decomposition.

constant between ozone and phenol was developed at 25

Catalytic ozonation and its applicability to water

in

a

phenol

wastewater

treatment

system

ºC. The TOC removal of the bubble column reactor and

treatment were investigated (Nawrocki and Fijolek, 2009).

bubble diffuser were compared and reported.

The catalytic ozonation had some advantages over

Beltran et al. (2009a) studied the photocatalytic

ozonation alone such as high rate of the process, higher

ozonation of sulfamethoxazole (SMT) in water. Different

efficiency of organic matter mineralization, and the higher

scavengers were applied to the system to investigate the

extent of ozone utilization. It was shown that throughout

reaction mechanism involving direct ozonation, •OH

homogeneous catalytic ozonation, •OH radicals were

radical reactions, direct photolysis, and photocatalytic

formed.

reactions. The results indicated that the main contributions The oxidation efficiency of micropollutants from

to SMT removal were the direct ozone reaction and •OH

wastewater by ozone was investigated by Nothe et al.

radical reactions; whereas for the TOC removal, the main

(2009). The •OH radical scavenging capacity of the

contributions were the •OH radical reactions. Beltran et al.

wastewater DOC was calculated at 3 × 104 (mg DOC)-1 s-1.

(2009b) treated SMT in water using ozone in presence of

It was found that the contribution of bicarbonate to the •OH

catalysts (copper and cobalt type perovskites and cobalt-

scavenging capacity was small, similar to 10% of DOC. It

alumina) and promoters (activated carbons). The removal

was indicated that at 5 mg/L O3, only the most reactive

of the SMT achieved by ozone alone was fast; however, a

micropollutants with the rate constant higher than 3 × 103

catalytic or promoted ozonation was required for reduction

M-1 s-1 were eliminated, but at 10 mg/L O3, the much less

of the resulting organic carbon. Thus, the removal of SMT

reactive compounds (rate constant of 300 M-1 s-1) were

was mostly through direct ozonation, while the removal of

oxidized.

remaining TOC was due to •OH oxidation. The results of a study by Dong et al. (2009b)

The removal of four pharmaceuticals (metoprolol,

showed that the addition of nanocatalyst to an ozone

naproxen, amoxicillin, and phenacetin) using ozone was

system improved the degradation of phenol in water. The

studied at the pH range between 2.5 and 9 (Benitez et al.,

transformation from O3 molecules to •OH radicals was

2009b). The results showed that the rate constants

improved by using of nanocatalyst with higher specific

depended on the pH. The simultaneous ozonation of the

surface area, proper pH, and surface hydroxyl groups

pharmaceuticals in different water matrices was also

during the heterogeneous catalysis process.

carried out and a kinetic model was proposed to evaluate

The effective mass transfer between gas and

contribution of both direct ozonation reaction and the

liquid phase in a bubble column ozonation reactor was

radical pathway. The oxidation of pharmaceuticals,

1027 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

endocrine disrupting compounds and pesticides during

decolorization was achieved and the BOD5/COD ratio

ozonation was investigated by Broseus et al. (2009).

increased from 0.102 to 0.406.

Progestogen endocrine disruptors reacted slower with

Pillai et al. (2009) investigated the effect of

ozone than phenolic estrogens. The results showed that

ozonation catalyzed with Fe2+, H2O2, and UV light to treat

ozone was effective to remove trace organic contaminants

three major toxic organic components, terephthalic acid

from water. Pesticides were found to be the most

(TPA), isophthalic acid (IPA) and benzoic acid (BA)

recalcitrant compounds to oxidize.

present in wastewater. This system showed high oxidizing

Ozonation of C.I. Reactive Red 120 was carried

power for COD with 90% degradation in 240 min, and

out in a hollow fiber membrane contactor to study the

100% reduction for TPA, IPA and BA in 150 min.

effect of dyeing auxiliary reagents on decolorization

Degradation studies were also carried out with direct

performance (Atchariyawut et al., 2009). Sodium carbonate

molecular oxidation and indirect free radical oxidation. Qi

(Na2CO3) and sodium chloride (NaCl) were used as

et al. (2009a) demonstrated that catalytic ozonation with

additives. It was found that the ozone flux increased in the

aluminum

presence of Na2CO3 in the dye solution; however, it

substantially enhance the removal of 2,4,6-trichloroanisole

decreased

that

in drinking water. The uncharged surface hydroxyl groups

decolorization performance by ozone was slowed down

on γ -AlOOH in water could induce aqueous ozone

when Na2CO3 existed in the dye solution.

decomposition to generate hydroxyl radicals. Qi et al.

with

NaCl.

It was

also

indicated

oxihydroxide

boehmite

(γ-AlOOH)

could

The degradation of an azo-dye, Congo Red, using

(2009b) investigated the ozonation of 2-methylisoborneol

ozone was investigated by Khadhraoui et al. (2009). It was

(MIB) in drinking water. The results showed that ozone

found that ozone by itself was strong enough to decolorize

was efficient in removing MIB from aqueous solution,

the solution in the early stage of the oxidation process.

regardless of the initial MIB concentration. The qualitative

However, the efficient mineralization was not achieved. It

and quantitative analyses of ozonation products were also

was also indicated that the ozone process reduced the

carried out.

phytotoxicity

of

the

solution

and

improved

the

Ramos et al. (2009) explored the remediation of

biodegradability of the treated azo-dyes-wastewater.

lignin and its derivatives from pulp and paper industry

The treatment of azo dye Reactive Brilliant Red

wastewater by combination of chemical precipitation and

X-3B in a wastewater using sequential ozonation and

ozonation. There were a couple of by-products generated

upflow biological aerated filter process was investigated by

followed by ozonation, and the biodegradability of

Lu et al. (2009c). It was found that after 120 min ozonation

wastewater increased after ozonation. The effect of the

with an ozone concentration of 34.08 mg/L, the

precipitation and ozonation on decolorization was also evaluated.

Rivas

et

al.

(2009b)

investigated

1028 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

the

mineralization of bisphenol (BPA) by several oxidation

systems flow, using ozonation followed by UV irradiation.

treatments. It was demonstrated that ozonation or

It was determined that an oxidative reduction potential

photolysis

from

probe located at the outlet of the O3 contact chamber and

wastewater; and the addition TiO2 to O3 or UV-C light

immediately before water entered the UV irradiation unit

could

The

was effective to continuously monitor and control O3 dose.

completely

Turhan and Turgut (2009) explored the factors affecting the

were

capable

significantly

combination

of

enhance

of O3/UV-C

was

removing

TOC

BPA

removal.

able to

mineralize BPA.

rate of COD of a synthetic water solution containing water

The combination of ozone and H2O2 was

soluble direct dyes (Sirius Red F3B and Sirius Blue SBRR)

investigated to remove the dissolved organic matter in the

by ozone gas. Around 60% COD was reduced for water

effluent of a sewage treatment plant (Rosal et al., 2009). A

containing those dyes after ozone treatment for 2 h. The

complete mineralization was obtained in less than 1 h. The

ozonation by-products were also analyzed by HPLC, ion

results showed that the mineralization process took place in

chromatography

two stages and the rates were dependent on COD/BOD

spectrometry (GC-MS).

(IC)

and

gas

chromatography-mass

ratio and chloride content in the wastewater. Sallanko and

Van Leeuwen et al. (2009) demonstrated that the

Okkonen (2009) investigated the effects of ozonation on

methylene blue was removed by 95% in the ozonated

municipal treated wastewater. The effects of ozonation on

process versus 40% removal in the non-ozonated control.

COD, BOD7, color, and turbidity removal were evaluated.

The by-products generated were also analyzed. Wang et al.

An ozone dosage of 2.7 mg/L substantially decreased the

(2009f) compared the decomposition of two haloacetic acid

COD of biochemically treated municipal wastewater. With

(HAAs), dichloroacetic acid (DCAA) and trichloroacetic

the higher dosage, the COD decreased rapidly. Sanchez-

acid (TCAA) by combination of O3/UV radiation,

Polo et al. (2009) investigated the role of the tannic acid

H2O2/UV radiation, O3/H2O2, and O3/H2O2/UV radiation.

(TAN) component of organic matter dissolved in water, in

The decomposition rates of each contaminant by each AOP

the removal of sodium dodecylbenesulphonate (SDBS) by

method were evaluated. Wert et al. (2009) used UV

ozone, O3/H2O2, O3/GAC, and O3/PAC advanced oxidation

absorbance and color to assess pharmaceutical oxidation

processes. Low doses of TAN (1 mg/L) during SDBS

during ozonation of wastewater. The results showed that

ozonation increased the ozone decomposition rate and

UV at 254 nm and true color removal could be used as

SDBS removal rate. It was also found that O3/GAC,

surrogates to evaluate pharmaceutical oxidation in the

O3/PAC, and O3/H2O2 could

presence or absence of dissolved ozone residual during

remove SDBS more

efficiently in the presence of TAN.

advanced wastewater treatment with O3 or O3/H2O2. The

Summerfelt et al. (2009) determined the process

ozonation of nitrobenzene in the presence of TiO2

requirements to disinfect the full recirculating aquaculture

supported on silica-gel catalyst was discussed by Yang et

1029 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

al. (2009b). An approximate increase of 21% in removal

oxidation on degradation of olive oil mill wastewater

efficiency was achieved by catalytic ozonation than

(OOMW) was investigated. The treatment with fungi of

ozonation alone. A kinetic study was also carried out. Zeng

OOMW samples promoted a reduction of their acute

et al. (2009) investigated the decolorization of molasses

toxicity to Daphnia longispina. The fungi species did not

fermentation wastewater by tin oxide (SnO2)-catalyzed

remove color; however, it was responsible for 91, 72 and

ozonation. The results showed that SnO2 accelerated the

77% reductions in total phenolic compounds, COD, and

ozone oxidation reaction and the decolorization of molasses

organic

fermentation wastewater. Zhang et al. (2009g) evaluated

oxidation was a successful process for color reduction after

the degradation of C.I. Acid Orange 7 by ozone with

biological treatment; however, the OOMWs remained

ultrasound (US/O3) and H2O2/O3. An increase of ultrasound

highly toxic after photo-Fenton oxidation. The treatment of

power and gas flowrate would lead to the increase of TOC

photo-Fenton followed by biological treatment was able to

removal rate using US/O3 system.

reduce 53 to 76% COD, 81 to 92% total phenolic content

Fenton

Processes

(Fenton,

Photo-Fenton,

compound,

respectively.

The

photo-Fenton

and 100% organic compounds content.

Electro-Fenton). Fenton and photo-Fenton processes were

NOM oxidation and bacterial inactivation in river

applied as a pretreatment to combined wastewater (Arslan

water, which was treated by photo-Fenton reaction at pH

and Ozturk, 2009). Based on the results, 100% color and

6.5 with 0.6 mg/L of Fe3+ and 10 mg/L of H2O2, was

44% TOC removal was achieved using 12 mM of Fe2+ and

investigated by Moncayo-Lasso et al. (2009). The results

130 mM H2O2 at pH 3. It was also found that using the

indicated that 55% of the initial DOC (5.3 mg/L) was

photo-Fenton process at pH 3 in presence of 26 mM Fe2+

mineralized, while total disinfection was detected without

and 130 mM H2O2, 84% TOC and 87% color were

re-growth after 24 h in the dark.

removed.

The effect of sulfate and chloride ions on the The detoxification of non-biodegradable chemical

yield of Fe2+ during the photolysis of Fe3+ in Fenton

pollution using Fenton and photo-Fenton process was

process was studied at pH 3, in the absence of H2O2

studied under direct sunlight and simulated UV irradiation

(Machulek et al., 2009). The data from the model as well as

(Kenfack et al., 2009). The effluent containing 2.2 mM of

the experimental data indicated that the availability of Fe2+

chlorohydroxy-pryridine was treated and the optimal

produced by photolysis of Fe3+ was inhibited in the

condition for detoxification was found to be pH value of

presence of sulfate ion.

2.8, Fe2+ concentration of 5.2 mM, and H2O2 concentration

Synthetic Acid Blue 193 and Reactive Black 39

of 768 mM.

wastewaters and real Reactive Black 39 effluent were

In a study by Justino et al. (2009), the efficiency

treated using photo-Fenton-like process (Arslan-Alaton et

of two treatments involving fungi and photo-Fenton

al., 2009b). Based on the optimum conditions, the best

1030 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

color, COD, and TOC removals were achieved using

visible light photo-Fenton > Fenton. A TOC removal of

Fe3+:H2O2 molar ratio of 0.073 for 45 min of reaction time.

36%, 27% and 16%, for the mentioned processes was

Under these conditions, 99% color, 83% COD and 58%

observed, respectively.

TOC were removed. For real Reactive Black 39 effluent,

Devi et al. carried out four studies regarding

the efficiency of photo-Fenton-like treatment was found to

advanced photo-Fenton processes (APFP). In their first

be lower than that of the synthetic acid and reactive dye

study, the heterogeneous advanced photo-Fenton processes

wastewaters.

of the type Fe0/H2O2/UV and Fe0/ammonium persulfate

The treatment of an azo-dye, Direct Red 28 (DR

(APS)/UV for Congo Red (CR) degradation was studied. It

28) by photo-Fenton was carried out by Ay et al. (2009). It

was found that inorganic anions such as chloride (Cl-) and

was found that with increasing the H2O2 and Fe2+, the color

sulfate (SO42-) hindered the degradation by quenching the

removal increased up to a level after which, H2O2 and Fe2+

generated •OH radicals. The anions such as nitrate,

adversely affected the color and TOC removals. A

carbonate, and bicarbonate decreased the degradation rate

complete removal of color was reached within 5 min, while

by scavenging the generated •OH radicals. The APS found

complete mineralization took almost 15 min. The optimal

to be a better oxidant than H2O2 for treating the effluent

H2O2/Fe2+/DR 28 ratio resulting in the maximum color

containing CR.

removal (100%) was predicted to be 715/71/250 (mg/L);

Devi et al. (2009b) investigated the advanced

however, this ratio was 1550/96.5/250 for the highest

Fenton process using zero valent metallic iron for

mineralization (97.5%).

degradation of azo dyes. It was proven that the degradation

Iron-pillard montmorillonitic (Fe-Mt/H2O2) as a

rate decreased at higher iron dose and also at higher oxidant

heterogeneous photo-Fenton reagent was used for the

concentration. The degradation of Methyl Orange (MO)

decolorization and mineralization of Reactive Brilliant

using Fe0 was shown to be an acid driven process with

Orange X-GN by Chen et al. (2009d). It was shown that

higher efficiency at pH 3. Devi et al. (2009c) also

98.6% discoloration and 52.9% TOC removal of X-GN

investigated the treatment of an azo dye, methyl red (MR)

were achieved using 140 min of visible irradiation, pH 3.0,

by the homogeneous photo-Fenton's process (HPFP), and

temperature of 30 °C, 4.9 mM H2O2, and 0.6 g/L of catalyst

also by the APFP using peroxides such as H2O2 and APS as

dosage.

oxidants. The efficiency of APFP showed to be higher than The effect of reaction time, H2O2 concentration

their homogeneous counterparts because of having the

and Fe2+ dosage on the decolorization of Remazol Black B

faster reduction of Fe3+ to Fe2+ ions on the surface of iron.

dye in Fenton and photo-Fenton processes was investigated

According to the experiments, the kinetics of decolorization

(da Silvao et al., 2009). The results showed that the more

by various oxidation processes was in the order of:

efficient dye removals were: UVA light photo-Fenton >

Fe0/H2O2/UV

>

Fe0/H2O2/dark

>

Fe0APS/UV

1031 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

>

Fe2+/H2O2/UV > Fe0/UV > Fe0/APS/dark > Fe0/dark

A comparison between UV/Nano-TiO2, Fenton,

approximate to H2O2/UV > Fe2+/APS/UV > APS/UV >

Fenton-like, electro-Fenton (EF) and electrocoagulation

Fe2+/H2O2/dark > Fe2+/APS/dark approximate to Fe2+/UV.

(EC) treatments was carried out for removal of C.I. Acid

Diazo dyes Brilliant Yellow (BY) and Bismark

Blue 9 (AB9) by Khataee et al. (2009b). The results

Brown (BB) were treated by the photo-Fenton-like process

indicated that the decolorization efficiency was in order of

Fe2+/APS/UV in acidic pH (Devi et al., 2009d). According

Fenton > EC > UV/Nano-TiO2 > Fenton-like > EF. In the

to the results, the BB degraded at a faster rate than BY. It

Fenton-based processes, the optimal concentrations of Fe2+

was proven that photo-Fenton-like process could be an

and H2O2 were found to be 10-4 M and 2 × 10-3 M,

efficient and useful method for the mineralization of diazo

respectively. In the UV/Nano-TiO2 process, the complete

dyes at lower iron concentrations in acidic condition.

removal of color using optimal parameters was achieved in

The decolorization of 2 mM Orange II was

about 25 min. It was found that in the electrocoagulation

carried out using photo Fenton process in presence of UV-

process, for a solution of 20 mg/L AB9, about 98% color

C light, catalysts containing Fe, and 100 mM H2O2 at pH 3

was removed at pH 6, with 8 min electrolysis and the

(Feng et al., 2009b). The catalysts were Fe nanocomposite

current density of approximately 25 A/m2.

(Fe-Lap-RD), betonite clay based Fe nanocomposite (Fe-

Fenton process combined with coagulation was

B), and iron oxide hydrated (FeOOH). All of the catalysts

applied

showed good activity for color removal in the process;

wastewater (Ma and Xia, 2009). In presence of 50 mg/L

however, only Fe-Lap-RD and Fe-B showed good photo

H2O2, 25 mg/L FeSO4 and 30 min settling time at pH 4,

catalytic activity in the mineralization of Orange II. In

86.4% of color and 92.4% of COD was removed.

terms of the overall TOC removal, the following order of

Polyaluminum chloride (PAC) and FeSO4 were used as

the three catalysts was observed: Fe-Lap-RD > Fe-B >

coagulants to improve the Fenton and enhance the color

FeOOH.

and COD removal. The degradation of two monoazo pigments, Red

for

treatment

of

water-based

printing

ink

The degradation of methylene Blue azo dye (MB)

53:1 and Red 48:2, were conducted using Fenton, photo-

under

Fenton's

and

photo-Fenton's

conditions

Fenton and UV/H2O2 systems (Ilha et al., 2009). It was

investigated by Melgoza et al. (2009). The results showed

shown that the efficiency of the Fenton reactions increased

that the efficiency of the photo-Fenton's system was higher

with temperature. Based on the results, the best rate

than the Fenton’s process. It was found that photo-Fenton's

constants for cleavage of the azo bond and the naphthalene

reactions were practical processes for treatment of MB, due

rings were observed in photo-Fenton reactions irradiated by

to the high levels of color and TOC removal. The

sunlight. In terms of H2O2 consumption, the UV/H2O2

degradation of azo dye Acid Orange 7 (AO7) from water

system showed the highest efficiency.

was carried out by the electro-Fenton process using

1032 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

was

electrogenerated •OH radicals (Ozcan et al., 2009). It was

Kuo and Lin (2009) investigated the use of solar

found that the rate constant of AO7 hydroxylation reaction

irradiation combined with Fenton reagent to enhance the

was 1.20 ± 0.17 × 1010 M-1 s-1. The rates of degradation

biodegradability (BOD5/COD) of chlorophenol wastewater

decreased by increasing the Fe3+ concentration to a value

(2-CP, 4-CP, and 2,4-DCP). According to the results, the

higher than 0.1 mM.

solar photo-Fenton process significantly improved the

The

compounds

hexadecylammonium-chloride

benzyl-dimethyl-

(16-BAC)

dimethyl-stearylammonium-chloride

and

(18-BAC)

biodegradability of chlorophenol wastewater. With a 15-

benzyl-

min treatment, the value of BOD5/COD was increased from

were

0 for untreated solution up to 0.231, 0.248, and 0.193 for 2-

treated by the O3 and photo-Fenton processes at different

CP, 4-CP, and 2,4-DCP, respectively.

O3 doses and H2O2 concentrations (Dantas et al., 2009).

A 200 mg/L mixture of four pesticides (Laition,

Based on the results, the photo-Fenton process achieved up

Metasystox, Sevnol and Ultracid) was treated using a

to 80% of mineralization after 90 minutes of treatment

combination of a photo-Fenton pretreatment and an

using the UV lamp. Using O3, 50% mineralization was

activated sludge (Martin et al., 2009a). The optimal

reached.

biotreatment time was found to be shorter than of The

treatment

of

di-2-ethylhexyl

phthalate

commonly used in municipal wastewater treatments.

(DEHP) in wastewater was carried out in photo-Fenton

However, the higher pesticide concentrations should be

coupled with a biological system (Chen et al., 2009e). It

taken into account for both the photocatalytic and the

was found that the toxicity of wastewater containing DEHP

biological oxidation. Solar photo-Fenton and biological

was reduced after pretreatment by the photo-Fenton

oxidation was applied for the treatment of wastewater

reaction, with optimal time of 60 min after which the

containing a mixture of five commercial pesticides, Vydate,

effluent was introduced to the biological system.

Metomur, Couraze, Ditumur and Scala (Martin et al.,

The degradation products and pathway of

2009b). The mineralization required for combining with

chlorfenvinphos (CFVP) treated by photo-Fenton driven by

biodegradation of intermediates by activated sludge was

solar irradiation was investigated by Klamerth et al. (2009).

55% and 33% at 500 mg/L and 200 mg/L, respectively.

Strong mineralization and the degradation of CFVP were

The kinetic modeling of the Fenton and photo-

observed in all the experiments. It was also found that the

Fenton degradation of formic acid for 1 to 9 mg/L of iron

degradation products, such as 2,4-dichlorophenol, 2,4-

and temperature of 20 and 55 ºC was studied by Farias et

dichlorobenzoic

were

al. (2009). The proposed kinetic model was able to

decomposed into organic substances such as acetate,

reproduce the effects of changing the reaction temperatures,

formate, maleate, and inorganic ions, like chloride and

ferric iron concentrations, and formic acid to H2O2 molar

phosphate.

ratios on the degradation rate. The maximum root-mean

acid

and

triethylphosphate

1033 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

square error of 7.64% was calculated using the model and

H2O2:COD molar ratio 1.5, H2O2:Fe2+ molar ratio 20 and

Fenton and photo-Fenton experimental runs.

pH 3. It was observed that under optimal condition, all the

Citrate and hypophosphite were degraded using Fe2+/H2O2,

UV/Fe2+/H2O2,

antibiotics were completely degraded in 2 min; however, as

electrolysis/Fe2+/H2O2

a result of organic carbon and nitrogen mineralization, an

(Huang et al., 2009c). It was observed that the Fenton

increase in ammonia and nitrate concentration was

process was not able to completely degrade citrate in the

observed.

and

presence of hypophosphite; however, the application of UV

Arsenic and chromium removal by Fenton's and

light (photo-Fenton) or electron current (electro-Fenton)

FeSO4/ K2Cr2O7 reagent was conducted on different water

improved the degradation efficiency of the Fenton process.

samples (Karacan and Ugurlu, 2009). The highest removal

The photochemical degradation of phenol-red

efficiency was obtained using a 150 g zero-valent iron

using photo-Fenton reaction was studied by Jain et al.

column with 40 mg, FeSO4/20 µ g/L H2O2 and 40 mg

(2009). The effect of various organic additives such as

FeSO4/20 mg K2Cr2O7 for 100-mL samples. The As and Cr

hydroquinone, resorcinol and catechol on the rate of

removal in the stream water for both methods were 90.2,

photodegradation was evaluated. The effect of pH,

89.95 and 95, 93.4%, respectively. In the tap water, the As

concentration of dye, Fe3+ and additives, amount of H2O2,

and Cr removal were above 98% for both methods.

and light intensity on the rate of photodegradation was also

The oxidation of atrazine and fenitrothion was

investigated.

investigated using H2O2 as the oxidant and Fe(II) as the

An Fe3+/H2O2/UV-C flow system was used for

catalyst (Kassinos et al., 2009). The degradation was

the photodegradation of methyl parathion to optimize the

observed during the first 2 h of dark Fenton reactions. An

[H2O2]:[Fe3+] ratio (Diagne et al., 2009). The experiment

increase of the reaction time did not improve the pesticide

was performed at pH 3 and room temperature. The total

removals. Using the photo-Fenton reaction, fenitrothion

methyl parathion concentration was removed after a few

was mineralized completely, but the TOC of the atrazine

minutes, following a pseudo-first-order decay kinetics. At

solution was removed by 57%.

the optimum ratio, a total mineralization was achieved after

Photo-Fenton degradation of polyacrylamide

120 min due to the effect of the •OH radicals produced

(PAM) was evaluated using Fe(III)-silicon dioxide (SiO2)

during the treatment.

catalysts with two iron salts as precursors, ferric nitrate

Photo-Fenton process was used to degrade

(Fe(NO3)3) and FeSO4 (Liu et al., 2009b). The results

antibiotics in aqueous solution (Elmolla and Chaudhuri,

showed that Fe(III)-SiO2 catalysts had an excellent

2009). Based on the results, for the removal of 104, 105

photocatalytic activity in the degradation of PAM. Also, the

and 103 mg/L amoxicillin, ampicillin, and cloxacillin,

precursor species and the OH-/Fe mole ratio affected the

respectively, the optimal condition was as follows:

1034 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

photocatalytic activity of Fe(III)-SiO2 catalysts to a certain

concentration) values were maintained. R. oryzae was not

extent.

as effective as photo-Fenton processes to remove color and Fenton,

photo-Fenton

and

photocatalysis

COD, but it was more promising in reducing toxicity.

processes were compared for treatment of catechol

Phenol degradation was tested by photocatalysts

(Lofrano et al., 2009). A high efficiency of Fenton and

with tungsten oxide (WOx)-TiO2 (Piszcz et al., 2009). The

photo-Fenton were achieved at 30 min reaction time in

•OH generated from WOx-TiO2 was much higher than

presence of H2O2/FeSO4 at 600/500 by weight. The

generated from TiO2. It was found that the presence of

analyses showed that the total removal of catechol could

WOx in TiO2 suppressed the transformation of anatase to

occur after Fenton (2000/500 w/w, 30 min), photo-Fenton

rutile. Pourata et al. (2009) studied the removal of the

(600/500 w/w, 30 min), and photocatalysis (3 g TiO2/L,

herbicide bentazon from contaminated water in the

240 min) treatments.

presence of synthesized nanocrystaline TiO2 powders under

Photo-Fenton processes were found to be the

UV light (30W). A kinetic model was established to predict

most efficient methods to treat effluents from water-washed

the removal of bentazon by the UV/TiO2 system and the

spray-booths, in terms of COD removal and mineralization,

optimum condition achieved 99% removal of bentazon in

in comparison to TiO2, TiO2/H2O2 and the photo-Fenton

90 min. Sarnet et al. (2009) evaluated the dark Fenton and

processes (Palacios et al., 2009). A 67% and 51% reduction

the solar photo-Fenton advanced oxidation processes for

in COD and mineralization were achieved and an important

the treatment of solutions containing 4-chloroguaiacol (4-

removal of solvents was detected. Acetic acid degradation

CG). At reaction time of 24 min, hydrogen peroxide to

was also carried out by TiO2-UV-H2O2, Fe2+-H2O2-UV,

ferrous iron molar ratio (H2O2/Fe2+) of 2, initial COD 640

UV-H2O2 and TiO2-UV system (Park and Lee, 2009). The

mg/L, pH 3, and 25 ºC, the 4-CG degradation and COD

COD removal rate was found to be fastest in the UV-H2O2

removal by the solar photo-Fenton process were greater

process. Paspaltsis et al. (2009) demonstrated that TiO2-

than 80 and 89%, respectively. Segura et al. (2009)

based heterogeneous photocatalytic oxidation was able to

investigated the integrated heterogeneous sono-photo

significantly reduce the infectivity of prion, which is a

Fenton processes for the degradation of phenolic aqueous

misfolded protein that causes transmissible spongiform

solutions. A total phenol degradation and 90% TOC

encephalopathies (TSE). Peteira et al. (2009) compared the

reduction were achieved by sequentially ultrasound

effectiveness of a biological treatment with Rhizopus

followed by UV-visible light irradiation.

oryzae and a photo-Fenton oxidation in the mitigation of

A real pharmaceutical wastewater containing 775

toxicity of a bleached Kraft pulp mill effluent. It was

mg/L of dissolved organic carbon was treated by a solar

reported that COD and color were significantly reduced by

photo-Fenton/biotreatment (Sirtori et al., 2009a). Photo-

photo-Fenton processed, but low EC50 (median effective

Fenton treatment of 190 min and 66 mM H2O2 was

1035 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

necessary for adequate biodegradability of the wastewater.

solubilization of excess sludge in activated sludge process

Sirtori et al. (2009b) investigated the solar photo-Fenton

using the solar photo-Fenton reaction was investigated by

treatment

Tokumura et al. (2009a). It was found that increasing initial

of

pharmaceutical

wastewater

containing

nalidixic acid (NXA) after biotreatment. Total degradation

Fe

and

H2 O 2

concentrations

enhanced

the

sludge

of NXA and the intermediate formed during degradation

solubilization. Solar light on dissolving COD in this study

were analyzed and the reduction of toxicity was observed.

was more effective than UV light. Tokumura et al. (2009b)

So et al. (2009) described that for a 10 ton/day

examined the treatment of colored effluent coupled with

pilot-scale treatment system, photo-Fenton oxidation was

energy production using a modified photo-Fenton process.

able to remove approximately 90% of 1,4-dioxane by using

Decolorization of colored effluent and production of

2 800 mg/L of H2O2 and 1400 mg/L of FeSO4 along with

electricity

10 UV-C lamps (240 mu W/cm2), installed and operated

simultaneously and effectively.

and

hydrogen

could

be

carried

out

continuously during aeration. Textile dyeing effluent

Tony et al. (2009) studied the photo-catalytic

treatment by Fe2+/H2O2, Fe3+/H2O2, O3 and chemical

degradation of an oil-water emulsion using a photo-Fenton

coagulation was compared by Solmaz et al. (2009).

treatment process. It was found that the COD removal rate

Optimum conditions (chemical species and pH) were

was affected by Fe2+, H2O2 concentration and the initial pH

determined, and 150 mg/L FeSO4 at pH 12 provided the

of the aqueous solution. Torabian et al. (2009) conducted a

maximum color and COD removal efficiency for one

case study of photochemical oxidation of phenol in olefins

industrial wastewater, and 200 mg/L FeSO4 and 200 mg/L

plant effluent by UV/H2O2 and photo-Fenton process. The

H2O2 provided the maximum color and COD removal for

study showed that the photo-Fenton process was the most

another industrial wastewater. Sun et al. (2009b) evaluated

effective treatment process under acidic conditions and had

the feasibility of photo-Fenton oxidation process for the

a high phenol degradation rate in a short reaction time. The

degradation of ciprofloxacin hydrochloride. The optimum

reaction was influenced by pH, the input concentration of

dosages of H2O2 and ferrous ion were 5.0 and 0.05

H2O2, and the amount of the iron catalyst, and the type of

mmol/L, respectively. The degradation of ciprofloxacin

iron salt.

hydrochloride followed a first order reaction.

The photocatalytic degradation of the antibiotic

Tiburtius et al. (2009) demonstrated that aromatic

sulfamethoxazole by solar photo-Fenton at pilot scale was

hydrocarbons (BTXs) in gasoline contaminated water could

evaluated in both distilled water and in seawater (Trovo et

be degraded by photo-Fenton process assisted by solar or

al., 2009). The influence of H2O2 and iron concentration on

artificial UV-A radiation. BTXs removal was observed in

the efficiency of the photocatalytic process was evaluated.

reaction of 5 min, and about 90% mineralization was also

The degradation level was more significant in distilled

observed by applying a multiple H2O2 addition system. The

water than in seawater. Tryba et al. (2009) investigated the

1036 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

photodecomposition of dyes on iron-modified carbon-

commercial pesticides (Zapata et al., 2009b). Photo-Fenton

coated TiO2 (Fe-C-TiO2) photocatalysts under UV radiation

was found to be more active than ferric in terms of active

supported by photo-Fenton process. Three dyes were tested

ingredient degradation. Zhang et al. (2009i) investigated

and the high rate of dyes decomposition was noted on Fe-

the application of a new photo Fenton like catalyst with a

C-TiO2 photocatalysts under UV radiation with addition of

nano-lamellar structure, iron tetrapolyvanadate (Fe2V4O13),

H2 O2 .

in

Vermiyea

and

Voelker

(2009)

conducted

the

degradation

of

organic

pollutants.

It

was

experiments using photo-Fenton reaction at near neutral

demonstrated that Fe2V4O13 could effectively catalyze the

pH. The Suwannee River fulvic acid was degraded at pH 7,

degradation of Acid Orange II by H2O2 in visible light.

and the rate of •OH generation was evaluated. Fenton

Zheng et al. (2009d) explored the degradation of organic

process was also applied on the effects of reaction

contaminant in landfill leachate by photo-Fenton process.

conditions on nuclear laundry water treatment (Vilvea et

The results indicated that photo-Fenton process could

al., 2009). It was found that the most cost-effective

effectively remove color. The optimum condition was

degradation was at H2O2/Fe2+ stoichiometric ratio of 2 with

found to be Fe2+ concentration of 5 mmol/L and H2O2

H2O2 dose of 1 000 mg/L for 5 min.

concentration of 5.7 × 102 mmol/L.

Xing et al. (2009) investigated the degradation of

Electrochemical

Processes.

Electrochemical

methylene blue upon exposure to ultrasound at 24 kHz

processes are developed to remove toxic and recalcitrant

using a direct immersion ultrasound probe. The degradation

organic in water and wastewater. These methods are based

was increased by a factor of 3.4 when adding a small

on generation of hydroxyl radicals. The fundamentals and

amount of Fe(II). Xu et al. (2009c) investigated the

new developments of electrochemical advanced oxidation

degradation of dimethyl phthalate (DMP) by UV/H2O2

processes (EAOPs) such as anodic oxidation, electro-

process. DMP degradation was found to be affected by

Fenton and photoelectron-Fenton processes were reported

H2O2 concentration, intensity of UV radiation, initial DMP

by Alexandru et al. (2009). The application of these

concentration, and solution pH. The rate constant and the

methods for removal of triphenylmethane dye Crystal

kinetic model were also described.

Violet was also investigated. The capability of oxidation

Zapata et al. (2009a) evaluated the operational

and mineralization of all these EAOPs to decontaminate

parameters involved in solar photo-Fenton degradation of a commercial pesticide mixture. Photo-Fenton

acidic aqueous solutions of common dyes were explained.

process

Conductive-Diamond Electrochemical Oxidation

removal efficiency increased with increasing temperature.

(CDEO), ozonation and Fenton oxidation were compared

Other influenced parameters were also analyzed. A

for treatment of wastes produced in fermentation processes

combined solar photo-Fenton and biological treatment were

(Canizares et al., 2009a). It was found that the results of

also discussed for the decontamination of a mixture of five

COED strongly depended on the addition of an electrolyte

1037 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

salt such as sodium chloride, for both decreasing the energy

greater than those in other common anode systems such as

cost and improving the efficiency. CDEO was assessed

SnO2 and lead dioxide (PbO2) anode cells.

along with two other advanced oxidation processes for

Electro-Fenton’s reagent was used to degrade

technical and economic feasibilities (Canizares et al.,

dinitrotoluenes (DNTs) and 2,4,6-trinitrotoluene (TNT) in

2009b). Only CDEO was found to be able to achieve

wastewater (Qi et al., 2009c). Nitrotoluenes could be

complete mineralization of pollutants for all wastewater

completely decomposed by Electro-Fenton’s reagents,

tested. However, the efficiency depended on the nature of

wherein H2O2 was generated from catholic reduction of

the pollutants.

oxygen, supplied by anodic oxidation of water. The

Anglada et al. (2009) provided an overview of

influence of electrolytic temperature on the degradation of

fundamental aspects of electrochemical oxidation and their

nitrotoluenes was the most significant, among other factors.

applications, such as effluents from landfill and a wide

Anoxic oxidation was used to treat paper mill effluent (El-

diversity of industrial effluents including the agro-industry,

Ashtoukhy et al., 2009). COD and color were significantly

chemical,

removed by the method. Prabhakaran et al. (2009) assessed

textile,

tannery

and

food

industry.

The

electrochemical oxidation of aqueous wastes polluted with

the

use

of

electrochemical

oxidation

using

batch

4-nitrocathecol was studied on boron-doped diamond in an

recirculation reactors to treat resin effluents. The best effect

acid medium (Bensalah et al., 2009). The oxidation of these

of total organic content reduction occurred at 3.75 A/dm2

wastes resulted in the complete mineralization of the

with flow rate of 20 L/h. A review paper by Martinez-

organics. Electrochemical oxidation on boron doped

Huitle and Brillas (2009) also analyzed electrochemical

diamond anodes (BDD-EO) was also applied in treatment

oxidation of decolorization and degradation of synthetic

with synthetic aqueous wastes polluted Congo Red

organic dyes in industrial wastewater.

(Elahmadi et al., 2009). It was evidenced that BDD-EO was

Landfill leachate as a very complex wastewater

more efficient and economic than ozonation in terms of

was treated by combined membrane biological reactor and

COD and TOC removal. The consecutive destruction of

electro-oxidation

azoic groups was proposed during BDD-EO.

Electrochemical oxidation using platinizzed titanium grid

processes

(Aloui

et

al.,

2009).

Zhu et al. (2009b) treated biologically pretreated

(Ti/Pt) was applied as post-treatment after the biological

coking wastewater by electrochemical oxidation using

process. At pH 9, current density 4 A dm-2 and electrolysis

BDD-EO. Under the experimental conditions (current

time of 60 min, COD and ammonia nitrogen were reduced,

density 20 to 60 mA cm-2, pH 3 to 11, and temperature 20

accompanied by significant detoxification. Mohan et al.

to 60 °C) a complete mineralization of organic pollutants

(2009) evaluated the function of microbial fuel cell (MFC)

was almost achieved. In addition, the TOC and ammonia-

as bio-electrochemical treatment of chemical wastewater at

nitrogen removal rates in BDD anode cell were much

high loading conditions (18.6g COD/L, 56.8g TDS/L) with

1038 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

power

generation.

MFC

as

an

integrated

bio-

(Scialdone, 2009). A good agreement was observed

electrochemical treatment system showed some advantages

between theoretical predictions and experimental data of

over other degradation approaches.

electrochemical oxidation of oxalic and formic acid at IrO2-

Electrochemical oxidation processes are also

Ta2O5.

effective in treatment of herbicides. Atrazine degradation

Scialdone et al. (2009) investigated the role of

by indirect electrochemical advanced oxidation in aqueous

several parameters on the performance of the organic

medium was investigated by Balci et al. (2009). A

oxidation in the presence and in the absence of sodium

mineralization rate of 82% was obtained. The absolute rate

chloride, both theoretically and experimentally. It was

of the reaction between atrazine and hydroxyl radicals was

confirmed that in the presence of suitable amount of

estimated to be 2.54 × 109 M-1 s-1. Dhaouadi and Adhoum

chlorides, the oxidation of oxalic acid was due to a

(2009) applied three electrochemical advanced oxidation,

homogeneous process. In the absence of chloride, a high

including anodic oxidation (AO), electro-Fenton (EF) and

current efficiency was obtained at BDD, when low current

photoelectron-Fenton (PEF) methods to the degradation of

and high flow rate were imposed.

paraquat, a highly toxic herbicide, in aqueous solution at

Wet Air Oxidation. Wet air oxidation (WAO) is

pH 3. PEF and EF displayed the most efficient treatment

one of the effective methods to eliminate organic

and were sufficiently powerful for paraquat treatment.

contaminants in wastewater. The non-catalytic WAO was

Esquivel et al. (2009) developed a TiO2 modified fiber

electrode

a

et al., 2009). The effect of operating conditions, including

photoelectrochemical reactor for wastewater treatment. It

initial organic loading, reaction temperature, treatment

was able to remove 15 mg/L Azo Orange dye II and 57%

time, initial pH, and the use of H2O2 as an addition oxidant

TOC with 60 min degradation time. Jeong et al. (2009)

on treatment efficiency was evaluated. It was found that

examined the role of electrode materials on the generation

only organic loading and reaction temperature were

of oxidants, and found that the efficiency of hydroxyl

significant on the treatment. At optimum condition (180 ºC,

radical generation was BDD >> Ti/RuO2 ≈ Pt. The

1h treatment and initial COD of 8 100 mg/L), the removal

production of active chlorine was Ti/IrO2 > Ti/RuO2 >

of COD, total phenol and color were 34, 94, and 74%,

Ti/Pt-IrO2 > BDD > Pt. The electrochemical oxidation of

respectively. A continuous heterogeneous catalytic wet

organic in water at metal oxide was investigated to discuss

peroxide oxidation (CWPO) with nanocomposite catalyst

the

current

Fe2O3/SBA-15 was applied to assess the treatment of

efficiency and operative conditions by considering both the

pharmaceutical wastewater (Melero et al., 2009). It was

hypothesis of a direct oxidation process and of an indirect

found that in an up-flow fix bed reactor, the catalyst shown

process

high activity in terms of TOC mineralization, and a high

correlations

mediated

and

incorporated

between

by

the

it

instantaneous

adsorbed

hydroxyl

into

investigated to treat olive mill wastewater (Chatzisymeon

radicals

1039 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

oxidation degree of organic compounds in the outlet

condition and the leaching was negligible. Tang et al.

effluent.

(2009b) studied the mechanisms of WAO of emulsification Daniel et al. (2009) investigated CWPO of maleic

wastewater. WAO was found to effectively treat high

acid in aqueous phase over copper/micelle templated silica-

concentration,

3-aminopropyltrimethoxysilane catalyst. Macleic acid was

wastewater

completely converted to acetic acid under mild conditions,

temperature was greater than 220 ºC, the catalyst could

and the oxidation reaction of maleic acid was 100% in the

increase the production of fatty acid and promoted its

presence of copper on micelle templated

degradation.

silica-3-

non-biodegradable

containing

emulsification

nonionic matters.

When

the

aminopropyltrimethoxysilane catalyst. The CWPO of

Goi et al. (2009) performed treatment studies of a

phenol with AC as the catalyst was tested in a novel type of

landfill leachate with WAO and the addition of H2O2. It

two-impinging-jets reactor. The results showed the superior

was found that WAO was more advantageous in AOX

performance of this reactor for phenol and TOC removal

reduction and biodegradability enhancement of leachate

than conventional reaction systems. Xu et al. (2009b)

than Fenton processes. Chung et al. (2009) studied the

characterized rectorite by X-ray fluorescence (XRF),

factor affecting the sludge degradation and conversion to

Brunauer, Emmett, Teller (BET), X-ray diffraction (XRD),

subsequent intermediates at low critical wet oxidation conditions. The reaction time and temperature were found

Fourier transform –infrared (FT-IR), scanning electron

to be significant factors. The optimum conditions were

microscopy (SEM) and temperature programmed reduction

approximately 240 ºC, 30 min, 60 atm and 2.0 L/min

(TPR) as catalyst for wet air oxidation of phenol. The iron

oxidant dose.

impurity acted as active centers and showed good

Dotzauer et al. (2009) improved WAO with

performance without significant iron leaching. Rodriguez et tabular

al. (2009b) applied both WAO and CWAO on degradation

ceramic

membranes

modified

with

polyelectrolyte/platinium nanoparticle films. It was found

of several azodyes from wastewaters. CWAO was found to

that the tubular membranes, modified by Layer-by-layer

be more efficient on decolorization and mineralization. The

deposition of polyelectrolyte/Pt nanoparticle films, showed

final solutions with CWAO treatment for 180 min could be

2 to 3 times higher specific activities than similar

disposed to the environment.

membranes modified

Polyoxomolybdate nanotubes were developed for

by

other traditional

methods.

Martinez et al. (2009) studied CWAO with catalysts based

catalytic wet air oxidation of dye pollutants under room

on copper supported on AC. The catalyst’s activity was

temperature (Zhang et al., 2009h). The catalyst was

tested in the oxidation of methylene blue (MB) and

efficient in the treatment of wastewater containing 10

polyvinyl alcohol (PVA) in aqueous phase with pure

mg//L safranin-T, by removing 98% color and 95% COD in 40 min. The catalyst was stable under tested operating

1040 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

oxygen. It was found that higher temperatures were

A new SCWO was applied for the simultaneous

required to degrade PVA than MB. Supercritical

Angeles-

from acrylonitrile manufacturing processes and copper-

Hernandez et al. (2009) investigated the oxidation of a

plating processes (Shin et al., 2009). Copper-plating

nonbiodegradable and highly stable nitrogen containing

wastewater was found to accelerate the TOC conversion of

heterocyclic organic compound (quinotine) at supercritical

acrylonitrile wastewater from 17.6 to 67.3% at 450 ºC, and

conditions over a mixed catalysts. It was found that the

to generate copper and copper oxide particles. The

catalytic reaction was strongly dependant on temperature

synergistic effect of this treatment could completely

and pressure. The kinetics of catalytic oxidation of

convert TOC, remove color, detoxify, eliminate odor, and

quinoline was studied as well. The destruction of acrylic

recover copper. Xiu and Zhang (2009) also investigate

acid in wastewater was studied under SCWO with H2O2 as

copper and lead recovery from waste printed circuit board

the oxidant (Gong et al., 2009). Different experimental

by SCWO. At optimum condition of 60 min treatment, 440

conditions were examined for acrylic acid degradation. A

ºC, 296 atm and electrokinetic processes, SCWO could

destruction higher than 99% was observed at 450 ºC, 276.3

decompose polychlorinated biphenyls (PCBs), and recover

atm, and 34.3 s. Lee et al. (2009b) explored the

copper oxide, cuprous oxide, and β-PbO2.

decomposition

of

Water

treatment of mixed wastewater containing liquid waste Oxidation.

2-chlorophenol

by

SCWO

with

Cui et al. (2009) investigated the parameters

zirconium corrosion. At low feed concentration of

affecting the oil sludge oxidation. The results indicated that

zirconium, the decomposition efficiency increased, while at

the COD was significantly removed in 10 min, and the rate

high feed concentration of zirconium, the efficiency

increased with time. Jing et al. (2009) found that carbon

deteriorated.

dioxide and acetic acid were the intermediate and CO2 was

Li et al. (2009c) studied the oxidation of reactive

the ultimate product of oilfield sludge oxidation. Under

Red M-2B in a transpiring-wall SCWO reactor. It was

optimum condition at 440 ºC, pressure of 236.8 atm,

found

oxidant

residence time of 10 min, the oil removal achieved a 95%.

concentration, and flowrate were the most significant

Moussiere et al. (2009) investigated the destruction of

parameters controlling the dyes’ degradation. Sogut and

nuclear organic waste by SCWO using a scale-up process.

Akgun (2009) investigated the removal of C.I. Basic Blue

A 2D and 3D simulation of the fluid dynamics and heat

41 from aqueous solution by SCWO in a continuous-flow

transfer during the oxidation process was performed. The

reactor. It was demonstrated that TOC was degraded by

results showed that the scaling up of the reactor volume to

99.87% in very short reaction time. The reaction rate and

reach a capacity of 1 kg/h of pure organic could be

energy consumption were also determined.

obtained,

that

temperature,

dye

concentration,

with

the

necessary

residence

time

temperature distribution.

1041 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

and

Bermejo et al. (2009) presented a new-scaled-up

520 kHz ultrasonic reactors (Chand et al., 2009). It was

design of the cooled-wall reactor, which isolated the

found that the 300 kHz sonochemical reactor had the

temperature and pressure stress caused by SCWO

highest effect for •OH radical production. It was indicated

processes. The weak and strong points to the application of

that the degradation of phenol increased in the presence of

this new design were discussed and a mathematical model

the catalyst and H2O2. It was also found that with ZVI, a

was developed to describe the behavior of the new reactor.

complete phenol and 37% TOC removal was achieved

Veriansyah et al. (2009) developed a concentric vertical

within 25 min when 300 kHz was used. By using 20 kHz

double wall reactor of SCWO. This reactor overcame the

US treatment, complete phenol and 39% TOC removal

reactor corrosion problem, and was able to achieve more

were achieved within 45 min. By using of ZVC with 20,

than 99% removal of TOC, without producing chars and

300 and 520 kHz US reactors, phenol was removed

undesired gases.

between 10 to 98%, whereas the TOC was removed only a

A novel adaptive differential evolution (ADE)

26%.

algorithm with application to estimate kinetic parameters of

Huang and Huang (2009) applied a two-stage

oxidation in supercritical water was explored by Hu and

oxidation [UV- sodium persulfate/H2O2-Fe(II,III)] process

Yan (2009). ADE was demonstrated to outperform the

for bisphenol A (BPA) removal at pH 7. The high oxidation

original DE algorithm, and satisfied results were obtained

potentials of sulfate radicals and persulfate were applied as

once ADE was applied to develop the kinetic model of the

the first-stage oxidant, followed by a traditional photo-

2-chlorophenol oxidation. Fourcault et al. (2009) developed

Fenton process. In the second-stage reaction, H2O2 and iron

a mathematical model for a continuous flow tubular reactor

alone were used to observe the effect of enhancement of

devoted to hydrothermal oxidation of supercritical water.

photo-Fenton. The overall TOC removal of BPA were 25 to

The numerical prediction of the model fitted the

34%, 25%, and 87 to 91% for additional Fe(II,III)

experimental

activation,

results.

Koda

(2009) summarized

the

oxidation reactions of solid carbonaceous and resinous

H2 O 2

promotion,

and

Fe(II,III)/H2O2

promotions, respectively.

substances in supercritical water. The author proposed the

TiO2 photocatalysis by UV and visible irradiation

importance of mass transfer, internal and external processes

and salt-free electrolysis over boron-doped diamond

in designing SCWO processes for solid substances. The

electrodes to inactivate total (TC) and fecal (FC) coliforms

latest model calculation and information for future

was evaluated in municipal wastewater (Melemeni et al.,

development were also discussed.

2009). The electrochemical disinfection showed to be about

Miscellaneous Oxidation. The degradation of

two orders of magnitude faster than photocatalysis.

phenol in the presence of zero valent iron (ZVI) and zero

The

valent copper (ZVC) was investigated using 20, 300 and

performed

degradation by

using

of

ibuprofen

(IBP)

sonophoto-Fenton

1042 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

was (FS),

sonophotocatalysis (TS) and TiO2/Fe2+/sonolysis (TFS)

showed suitable activity and stability in the oxidation of

(Mendez-Arriaga et al., 2009). In the sonophoto-Fenton

DMSO with H2O2 in dilute aqueous solution, at room

process, a 95% IBP degradation and 60% mineralization

temperature.

were

achieved

with

photo-Fenton

(FH).

Ultrasonic

Gad-Allah et al. (2009) studied the treatment of

irradiation improved the iron catalytic activity. It was found

synthetic dyes wastewater using a magnetically separable

that the total IBP removal and elimination of 50% of DOC

photocatalyst (TiO2/SiO2/Fe3O4). The optimum condition

were observed by photocatalysis with TiO2, in the presence

was found to be 2 500 mg/L TiO2 at pH 3. By a kinetic

of ultrasound irradiation. Only 26% of mineralization was

study, three parameters were found to control the reaction

observed by photocatalysis with H2O2 (TH) in the absence

rate, including photocatalyst load, dye concentration, and

of ultrasound irradiation. It was also shown that, in the TFS

transmittance inside the photoreactor. Qi et al. (2009c)

system within 240 min, 92% of DOC and all IBP were

explored the ozonation of 2,4,6-trichloroanisole (TCA)

removed.

catalyzed by raw bauxite in drinking water. The catalytic A novel microwave assisted photochemical

ozonation removal effectiveness of TCA was investigated

process was used for removal of Acid Orange 7 in an

under various physiochemical conditions. It was found that

aqueous H2O2 solution (Ferrari et al., 2009). The method

raw bauxite in ozonation enhanced the TCA removal.

could activate a chemical reaction with microwaves and

The degradation kinetics and mineralization of

UV radiation, using an immersed source without the need

diclofenac by TiO2 photocatalysis was explored by Rizzo et

of a microwave oven. The method showed to be adaptable

al. (2009). A set of bioassays were utilized to develop the

and the scale up for industrial applications was feasible.

kinetic models. UV absorbance analysis was found to be a

Silicon or its oxide can be used as catalysts for

useful tool for a fast and easy measurement to obtain

oxidation of organic in water and wastewater. Bahruji et al.

preliminary information on the organic intermediates

(2009) investigated the photoactivated reaction of water by

formed during oxidation. Nanocrystaline TiO2 was used as

silicon nanoparticles. The silicon nanoparticles were

catalysts in the photocatalytic degradation of phenol under

suspended in water, once exposed to UV light at room

UV light (Silva and Faria, 2009). Several operational

temperature, generating hydrogen. The authors explored the

parameters were evaluated in the efficiency of the

stability of the silicon surface towards air and water in the

photodegradation process. The effect of two different co-

presence of UV. Cojocariu et al. (2009) investigated the

oxidants (hydrogen peroxide and sodium thiosulfate) in the

removal of dimethylsulfoxide (DMSO) from wastewater

photodegradation process was also described, and a kinetic

using mild oxidation with H2O2 over titanium-based

model was developed.

catalysts. The author demonstrated that a SiO2-TiO2

Sinha et al. (2009) described the treatment DTT

mesoporous xerogel prepared by titanium silicate TS-1

contaminated water by TiO2/UV and the effect of surfactant

1043 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

(Surfox) on this process. A novel photocataytic system was

were discussed. Xu et al. (2009f) performed a study on the

designed and the best results were at 200 mL/min air flow,

degradation of melatonin by UV, UV/H2O2, Fe2+/H2O2 and

CMC (critical micelle concentration) and above CMC of

UV/Fe2+/H2O2 processes. The degradation of melatonin

the surfactant. The photodegradation of azo dye Congo Red

was enhanced by UV/H2O2 process, and the fastest

from aqueous solution by the tungsten oxide (WO3)-

degradation and highest TOC removal was achieved using

TiO2/activated carbon (AC) photocatalyst under UV

UV/Fe2+/H2O2 process. Yogi et al. (2009) investigated the

irradiation was investigated (Sun et al., 2009a). The

photocatalytic degradation of methylene blue by gold-

optimum conditions for Congo Red degradation were found

deposited TiO2 film under UV irradiation. Particles

to be a dosage of catalyst 10 mg/L, pH 7, and H2O2 at 114

deposited on the TiO2 film improved the photocatalytic

mM. A kinetics study was investigated and the Congo Red

activity under oxygen (O2) bubbling condition. Zheng et al.

photodegrdation was found to follow pseudo-first order

(2009b)

kinetic. The photocatalytic degradation of bisphenol A

production

(BPA) in the presence of TiO2 and UV radiation was

nanoparticles under UV irradiation. The results showed that

performed in a self-designed horizontal circulating bed

hydrogen production could be enhanced by depositing a

photocatalytic reactor (HCBPR) (Wang et al., 2009g). The

suitable amount of Pt on the TiO2 surface.

results showed that the BPA degradation efficiency could

investigated from

Criquet

the

acetic

and

photocatalytic

acid

Leitner

solution

(2009)

by

hydrogen Pt/TiO2

studied

the

be improved by increasing pH from 3.4 to 12.3 or

degradation of acetic acid with sulfate radicals by

decreasing the initial BPA concentration from 50 to 10

persulfate ions photolysis. It was found that the maximum

mg/L. The optimum TiO2 carrier dosage was found to be

degradation of acetic acid occurred at pH 5. Gara et al.

around 1%.

(2009) studied the sulfate radical degradation of fulvic acid

Wu (2009) conducted the photodegradation of

in water. A theoretical model was performed and

C.I. Reactive Red 2 in UV/TiO2-based systems, and

demonstrated the formation of hydrogen bond between the

evaluated the effect of ultrasound (US) irradiation in

sulfate radicals and the humic substances. The experimental

photocatalysis. While adding sodium chloride (NaCl) in

enthalpy change corresponded well with the theoretical

US/TiO2,

values for some tested adducts.

UV/TiO2

and

UV/US/TiO2

systems,

the

efficiency of decolorization was improved. The effect of Air Stripping

TiO2 dosage, pH and temperature on decolorization of C.I. Reactive Red 2 in a UV/US/TiO2 system was also

Air-stripping is one of the most effective

evaluated by Wu and Yu (2009). Xu et al. (2009e) explored

technologies to remove volatile organic compounds

the degradation of n-butyl benzyl phthalate (BBP) using

(VOCs) from contaminated solutions. Multipass membrane

TiO2/UV. The parameters affecting the BBP degradation

air-stripping

was used

to

remove volatile organic

1044 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

compounds (VOC) from a mixed surfactant solution

Based on the results, nanofiltration showed the highest

(Cheng et al., 2009). The results indicated that Henry's law

removal efficiency.

constant of tetrachloroethylene (PCE) decreased due to the presence of the surfactants and this decrease was

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Removal of Fenhexamid and Pyrimethanil from Aqueous

Natural Clays. Clay Miner., 44(4), 487–495.

Solutions by Clays and Organoclays. J. Environ. Sci. Health

Behnajady, M. A.; Vahid, B.; Modirshahla, N.; Shokri, M. (2009)

Part B-Pestic. Contam. Agric. Wastes. 44, 220–225.

Evaluation of Electrical Energy Per Order (EEo) with

Bahruji, H.; Bowker, M.; Davies, P. R. (2009) Photoactivated

Kinetic Modeling on the Removal of Malachite Green by

Reaction of Water with Silicon Nanoparticles. Int. J.

US/UV/H 2O2 Process. Desalination, 249(1), 99–103.

Hydrogen Energy, 34 (20), 8504–8510.

Beltran, F. J.; Aguinaco, A.; Garcia-Araya, J. F. (2009a)

Bai, H.; Zhang, X.; Pan, J.; Sun, D. D.; Shao, J. (2009)

Mechanism

and

Kinetics

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Sulfamethoxazole

Combination of Nano TiO2 Photocatalytic Oxidation with

Photocatalytic Ozonation in Water. Water Res., 43(5),

Microfiltration (MF) for Natural Organic Matter Removal.

1359–1369.

Water Science and Technology: Water Supply, 9(1), 31–37.

Beltran, F. J.; Pocostales, P.; Alvarez, P. M.; Lopez-Pineiro, F.

Baker, H. M.; Ghanem, R. (2009) Evaluation of Treated Natural

(2009b)

Catalysts

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Abatement

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Zeolite for the Removal of O-Chlorophenol from Aqueous

Sulfamethoxazole and the Resulting Organic Carbon in

Solution. Desalination. 249, 1265–1272.

Water During Ozonation. Appl. Catal. B Environ., 92 (3-4),

Balci, B.; Oturan, N.; Cherrier, R.; Oturan, M. A. (2009) Degradation

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Beltran-Heredia, J.; Sanchez-Martin, J. (2009) Removal of Sodium

Electrocatalytically Generated Hydroxyl Radicals. A Kinetic

Lauryl Sulphate by Coagulation/Flocculation with Moringa

and Mechanistic Study. Water Res., 43(7), 1924–1934.

Oleifera Seed Extract. J. Hazard. Mater., 164(2-3), 713–

Ballet, G. T.; Hafiane, A.; Dhahbi, M. (2009) Influence of

719.

Operating Conditions on the Retention of Nickel in Water

Ben Amar, N.; Kechaou, N.; Palmeri, J.; Deratani, A.; Sghaier, A.

by Nanofiltration. Desalin. Water Treat., 9(1-3), 28–35.

(2009) Comparison of Tertiary Treatment by Nanofiltration

Bamaga, O. A.; Yokochi, A.; Beaudry, E. G. (2009) Application of

and Reverse Osmosis for Water Reuse in Denim Textile

Forward Osmosis in Pretreatment of Seawater for Small

Industry. J. Hazard. Mater., 170(1), 111–117.

Reverse Osmosis Desalination Units. Desalin. Water Treat.,

Benitez, F. J.; Acero, J. L.; Real, F. J.; Garcia, C. (2009a)

5(1-3), 183–191.

Combination of Chemical Oxidation-Membrane Filtration

Barkat, M.; Nibou, D.; Chearouche, S.; Mellah, A. (2009) Kinetics

Processes for the Elimination of Phenyl-Ureas in Water

and Thermodynamics Studies of Chromium(VI) Ions

Matrices. J. Chem. Technol. Biotechnol., 84(12), 1883–

Adsorption onto Activated Carbon from Aqueous Solutions.

1893.

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Benitez, F. J.; Acero, J. L.; Real, F. J.; Roldan, G. (2009b)

Barrouk, I.; Younssi, S. A.; Kabbabi, A.; Albizane, A.; Rafiq, M.;

Ozonation of Pharmaceutical Compounds: Rate Constants

Maghnouj, J.; Persin, M.; Larbot, A. (2009) Preparation of

and Elimination in Various Water Matrices. Chemosphere,

Ceramic Supports Based on Natural Moroccan Phosphate

77(1), 53–59.

1048 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Bensalah, N.; Ahmadi, M. F.; Gadri, A. (2009) Electrochemical

Botari, A.; Di Bernardo, L. (2009) Modeling of the Head Loss in

Treatment of Wastewaters Containing 4-Nitrocathecol

up Flow Coarse Sand and Gravel Direct Filtration.

Using Boron-Doped Diamond Anodes. Can. J. Civ. Eng.,

Engenharia Sanitaria E Ambiental, 14(2), 245–256.

36(4), 683–689.

Broseus, R.; Vincent, S.; Aboulfadl, K.; Daneshvar, A.; Sauve, S.;

Berberidou, C.; Avlonitis, S.; Poulios, I. (2009) Dyestuff Effluent Treatment

by

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Photocatalytic

Pharmaceuticals, Endocrine Disruptors and Pesticides

Oxidation and Membrane Filtration. Desalination, 249(3),

During Drinking Water Treatment. Water Res., 43(18),

1099–1106.

4707–4717.

Bergamasco, R.; Bouchard, C.; da Silva, F. V.; Reis, M. H. M.;

Bryjak, M.; Wolska, J.; Soroko, I.; Kabay, N. (2009) Adsorption-

Fagundes-Klen, M. R. (2009) An Application of Chitosan as

Membrane Filtration Process in Boron Removal from First

a Coagulant/Flocculant in a Microfiltration Process of

Stage Seawater RO Permeate. Desalination, 241(1-3), 127–

Natural Water. Desalination, 245(1-3), 205–213.

132.

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Busetti, F.; Linge, K. L.; Heitz, A. (2009) Analysis of

Experimental Performance and Modeling of a New Cooled-

Pharmaceuticals in Indirect Potable Reuse Systems Using

Wall Reactor for the Supercritical Water Oxidation. Ind.

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Tandem Mass Spectrometry. J. Chromatogr. A, 1216(31),

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Kinetics and Related Mechanisms of Bacillus Cereus Spore

Byeon, S. H.; Kavitha, D.; Ponvel, K. M.; Kim, K. M.; Lee, C. H.

Removal During an Alkaline Cleaning of a Tubular Ceramic

(2009) Surface Modified Granular Activated Carbon for

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Enhancement of Nickel Adsorption from Aqueous Solution.

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Korean J. Chem. Eng., 26, 1748–1753.

Boudrahem, F.; Aissani-Benissad, F.; Ait-Amar, H. (2009) Batch

Cailean, D.; Teodosiu, C.; Brinza, F. (2009) Studies Regarding

Sorption Dynamics and Equilibrium for the Removal of

Advanced Processes Used for Reactive Dyes Removal from

Lead Ions from Aqueous Phase Using Activated Carbon

Textile Effluents. Environ. Eng. Manage. J., 8(5), 1045–

Developed from Coffee Residue Activated with Zinc

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Chloride. J. Environ. Manage., 90, 3031–3039.

Canizares, P.; Hernandez-Ortega, M.; Rodrigo, M. A.; Barrera-

Boutilier, L.; Jamieson, R.; Gordon, R.; Lake, C.; Hart, W. (2009)

Diaz, C. E.; Roa-Morales, G.; Saez, C. (2009a) A

Adsorption, Sedimentation, and Inactivation of E. Coli

Comparison between Conductive-Diamond Electrochemical

within Wastewater Treatment Wetlands. Water Res., 43(17),

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Comparison

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1049 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Cao, F. M.; Bai, P. L.; Li, H. C.; Ma, Y. L.; Deng, X. P.; Zhao, C.

Thermodynamics

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Atrazine

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Montmorillonite Hybrid Particles for the Removal of

3), 912–918.

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Chen, G.; Shan, X.; Wang, Y.; Wen, B.; Pei, Z.; Xie, Y.; Liu, T.;

Catalkaya, E. C.; Kargi, F. (2009) Degradation and Mineralization

Pignatello,

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Trichlorophenol by Multi-Walled Carbon Nanotubes as

Peroxide Advanced Oxidation. J. Environ. Eng.-ASCE,

Affected by Cu(II). Water Res. (Oxford), 43(9), 2409–2418.

135(12), 1357–1364.

Chen, Q.; Song, J. M.; Pan, F.; Xia, F. L.; Yuan, J. Y. (2009c) The

Chae, S. R.; Yamamura, H.; Choi, B.; Watanabe, Y. (2009)

Kinetics

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Aliphatic

Fouling Characteristics of Pressurized and Submerged

Carboxylic Acids in an UV/TiO2 Suspension System.

PVDF (Polyvinylidene Fluoride) Microfiltration Membranes

Environ. Technol., 30(11), 1103–1109.

in a Pilot-Scale Drinking Water Treatment System under

Chen, Q. Q.; Wu, P. X.; Li, Y. Y.; Zhu, N. W.; Dang, Z. (2009d)

Low and High Turbidity Conditions. Desalination, 244(1-

Heterogeneous Photo-Fenton Photodegradation of Reactive

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Chand, R.; Ince, N. H.; Gogate, P. R.; Bremner, D. H. (2009)

under Visible Irradiation. J. Hazard. Mater., 168(2-3), 901–

Phenol Degradation Using 20, 300 and 520 Khz Ultrasonic

908.

Reactors with Hydrogen Peroxide, Ozone and Zero Valent

Chen, C. Y.; Wu, P. S.; Chung, Y. C. (2009e) Coupled Biological

Metals. Sep. Purif. Technol., 67(1), 103–109.

and Photo-Fenton Pretreatment System for the Removal of

Chandra, D.; Bhaumik, A. (2009) A New Functionalized

Di-(2-Ethylhexyl)

Mesoporous Polymer with High Efficiency for the Removal

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of Pollutant Anions. J. Mater. Chem., 19(13), 1901–1907.

Cheng, H. F.; Hu, Y. N.; Luo, J.; Sabatini, D. A. (2009) Multipass

Chang, W. S.; Tran, H. T.; Park, D. H.; Zhang, R. H.; Ahn, D. H.

Membrane Air-Stripping (MAS) for Removing Volatile

(2009a) Ammonium Nitrogen Removal Characteristics of

Organic Compounds (VOCs) from Surfactant Micellar

Zeolite Media in a Biological Aerated Filter (BA) for the

Solutions. J. Hazard. Mater., 170(2-3), 1070–1078.

Treatment of Textile Wastewater. J. Ind. Eng. Chem., 15(4),

Choi, H.; Jung, W.; Cho, J.; Ryu, B.; Yang, J.; Baek, K. (2009a)

524–528.

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Chang, I. S.; Lee, S. S.; Choe, E. K. (2009b) Digital Textile

Activated Carbon. J. Hazard. Mater., 166(2/3), 642–646.

Printing (DTP) Wastewater Treatment Using Ozone and

Choi, Y.; Kim, C.; Kwon, O.; Noh, S. (2009b) Fouling

Membrane Filtration. Desalination, 235(1-3), 110–121.

Mechanisms of an End-Free Submerged Membrane (Yonsei

Chatzisymeon, E.; Diamadopoulos, E.; Mantzavinos, D. (2009)

End Free;Yef) Module under Different Filtration Modes.

Effect of Key Operating Parameters on the Non-Catalytic

Desalination, 247(1-3), 108–124.

Wet Oxidation of Olive Mill Wastewaters. Water Sci.

Chou, C. Y.; Huang, C. P.; Shang, N. C.; Yu, Y. H. (2009)

Technol., 59(12), 2509–2518.

Treatment of Local Scrubber Wastewater for Semiconductor

Chen, G. C.; Shan, X. Q.; Zhou, Y. Q.; Shen, X. E.; Huang, H. L.;

by Using Photo-Catalytic Ozonation. Water Sci. Technol.,

Khan, S. U. (2009a) Adsorption Kinetics, Isotherms and

59(11), 2281–2286.

1050 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Christensen, A.; Gurol, M. D.; Garoma, T. (2009) Treatment of

Copper

Ions

from

Aqueous

Solutions

by

Using

Persistent Organic Compounds by Integrated Advanced

Clinoptilolite. Environ. Prog. Sustainable Energy. 28, 202–

Oxidation Processes and Sequential Batch Reactor. Water

211.

Res., 43(16), 3910–3921.

Criquet, J.; Leitner, N. K. V. (2009) Degradation of Acetic Acid

Chu, W.; Rao, Y. F.; Hui, W. Y. (2009a) Removal of Simazine in a

with Sulfate

UV/TiO2 -Heterogeneous System. J. Agric. Food Chem.,

Radical Generated by Persulfate Ions

Photolysis. Chemosphere, 77(2), 194–200.

57(15), 6944–6949.

Cui, B. C.; Cui, F. Y.; Jing, G. L.; Xu, S. L.; Huo, W. J.; Liu, S. Z.

Chu, W. H.; Gao, N. Y.; Deng, Y. (2009b) Performance of a

(2009) Oxidation of Oily Sludge in Supercritical Water. J.

Combination Process of UV/H2O2/Micro-Aeration for

Hazard. Mater., 165(1-3), 511–517.

Oxidation of Dichloroacetic Acid in Drinking Water. Clean

Daniel, L.; Katima, J. H. Y. (2009) Factors Influencing Catalytic

Soil Air Water, 37(3), 233–238.

Wet Peroxide Oxidation of Maleic Acid in Aqueous Phase

Chu, W. H.; Gao, N. Y.; Li, C.; Cui, J. (2009c) Photochemical

over

Copper/Micelle

Templated

Silica-3-

Degradation of Typical Halogenated Herbicide 2,4-D in

Aminopropyltrimethoxysilane Catalyst. Water Sci. Technol.,

Drinking Water with UV/H2O2 /Micro-Aeration. Sci. China

60(10), 2621–2627.

Series B Chem., 52(12), 2351–2357.

da Silvao, L. C.; Neto, B. D.; de Silva, V. L. (2009) Homogeneous

Chu, Y. Y.; Qian, Y.; Bai, M. J. (2009d) Three Advanced

Degradation of the Remazol Black B Dye by Fenton and

Oxidation Processes for the Treatment of the Wastewater

Photo-Fenton Processes in Aqueous Medium. Afinidad,

from Acrylonitrile Production. Water Sci. Technol., 60(11),

66(541), 232–237.

2991–2999.

Dantas, R. F.; Darcissac, M.; Lesueur, C.; Contreras, S.; Sans, C.;

Chung, J.; Lee, M.; Ahn, J.; Bae, W.; Lee, Y. W.; Shim, H. (2009)

Fuerhacker, M.; Esplugas, S. (2009) Assessment of Cationic

Effects of Operational Conditions on Sludge Degradation

Surfactants Mineralization by Ozonation and Photo-Fenton

and Organic Acids Formation in Low-Critical Wet Air

Process. Water Environ. Res., 81(2), 201–205.

Oxidation. J. Hazard. Mater., 162(1), 10–16.

de Amorim, C. C.; Leao, M. M. D.; Moreira, R. (2009)

Citulski, J.; Farahbakhsh, K.; Kent, F. (2009) Optimization of Phosphorus Immersed

Removal

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Secondary

Effluent

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Membranes

with

in-Line

Comparison of Various Advanced Oxidation Processes for Azo Dye Degradation. Engenharia Sanitaria E Ambiental, 14(4), 543–550.

Coagulant Pretreatment - Implications for Advanced Water

Demirbas, E.; Dizge, N.; Sulak, M. T.; Kobya, M. (2009)

Treatment and Reuse Applications. Can. J. Civ. Eng., 36(7),

Adsorption Kinetics and Equilibrium of Copper from

1272–1283.

Aqueous Solutions Using Hazelnut Shell Activated Carbon.

Cojocariu, A. M.; Mutin, P. H.; Dumitriu, E.; Vioux, A.; Fajula, F.;

Chem. Eng. J., 148, 480–487.

Hulea, V. (2009) Removal of Dimethylsulfoxide from

De Witte, B.; Dewulf, J.; Demeestere, K.; Van Langenhove, H.

Wastewater Using Mild Oxidation with H2O 2 over Ti-Based

(2009) Ozonation and Advanced Oxidation by the Peroxone

Catalysts. Chemosphere, 77 (8), 1065–1068.

Process of Ciprofloxacin in Water. J. Hazard. Mater.,

Coruh, S.; Turan, G.; Akdemir, A.; Ergun, O. N. (2009) The

161(2-3), 701–708.

Influence of Chemical Conditioning on the Removal of

1051 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Devi, L. G.; Kumar, S. G.; Reddy, K. M.; Munikrishnappa, C.

Dong, Y. M.; Jiang, P. P.; Zhang, A. M. (2009b) Catalytic

(2009a) Effect of Various Inorganic Anions on the

Ozonation Degradation of Phenol in Water by Mesoporous

Degradation of Congo Red, a Di Azo Dye, by the Photo-

Alpha-Feooh. Chin. J. Inorg. Chem., 25(9), 1595–1600.

Assisted Fenton Process Using Zero-Valent Metallic Iron as

Dotzauer, D. M.; Abusaloua, A.; Miachon, S.; Dalmon, J. A.;

a Catalyst. Desalin. Water Treat., 4(1-3), 294–305.

Bruening, M. L. (2009) Wet Air Oxidation with Tubular

Devi, L. G.; Kumar, S. G.; Reddy, K. M.; Munikrishnappa, C.

Ceramic Membranes Modified with Polyelectrolyte/Pt

(2009b) Photo Degradation of Methyl Orange an Azo Dye

Nanoparticle Films. Appl. Catal. B-Environ., 91(1-2), 180–

by Advanced Fenton Process Using Zero Valent Metallic

188.

Iron: Influence of Various Reaction Parameters and Its

Doula, M. K. (2009) Simultaneous Removal of Cu, Mn and Zn

Degradation Mechanism. J. Hazard. Mater., 164(2-3), 459–

from Drinking Water with the Use of Clinoptilolite and Its

467.

Fe-Modified Form. Water Res., 43, 3659–3672.

Devi, L. G.; Raju, K. S. A.; Kumar, S. G. (2009c)

Drikas, M.; Dixon, M.; Morran, J. (2009) Removal of MIB and

Photodegradation of Methyl Red by Advanced and

Geosmin Using Granular Activated Carbon with and

Homogeneous Photo-Fenton's Processes: A Comparative

without Miex Pre-Treatment. Water Res., 43, 5151–5159.

Study and Kinetic Approach. J. Environ. Monit., 11(7),

Du,

1397–1404.

F.;

Hawari,

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Baune,

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Devi, L. G.; Raju, K. S. A.; Rajashekhar, K. E.; Kumar, S. G.

Filtration. J. Membr. Sci., 336(1-2), 71–78.

(2009d) Degradation Mechanism of Diazo Dyes by Photo-

Duran, A.; Monteagudo, J. M.; Sanmartin, I.; Garcia-Pena, F.;

Fenton-Like Process: Influence of Various Reaction

Coca, P. (2009) Treatment of IGCC Power Station Effluents

Parameters on the Degradation Kinetics. Bulg. Chem.

by Physico-Chemical and Advanced Oxidation Processes. J.

Commun., 41(4), 385–390.

Environ. Manage., 90(3), 1370–1376.

Dhaouadi, A.; Adhoum, N. (2009) Degradation of Paraquat Herbicide

by

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Advanced

Elahmadi, M. F.; Bensalah, N.; Gadri, A. (2009) Treatment of

Oxidation

Aqueous Wastes Contaminated with Congo Red Dye by

Methods. J. Electroanal. Chem., 637(1-2), 33–42.

Electrochemical Oxidation and Ozonation Processes. J.

Diagne, M.; Oturan, N.; Oturan, M. A.; Sires, I. (2009) UV-C Light-Enhanced

Photo-Fenton

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Methyl

El-Ashtoukhy, E. S. Z.; Amin, N. K.; Abdelwahab, O. (2009)

Parathion. Environ. Chem. Lett., 7(3), 261–265.

Treatment of Paper Mill Effluents in a Batch-Stirred

Dixit, S.; Baredar, P.; Dixit, G. (2009) Brackish Water Treatment

Electrochemical Tank Reactor. Chem. Eng. J., 146(2), 205–

Using Desalinating Device for Domestic Purpose. Desalin.

210.

Water Treat., 11(1-3), 283–287.

El-Eswed, B.; Yousef, R. I.; Alshaaer, M.; Khalili, F.; Khoury, H.

Dong, W. Y.; Wang, H. J.; Li, W. G.; Ying, W. C.; Gan, G. H.;

(2009) Alkali Solid-State Conversion of Kaolin and Zeolite

Yang, Y. (2009a) Effect of DO on Simultaneous Removal

to Effective Adsorbents for Removal of Lead from Aqueous

of Carbon and Nitrogen by a Membrane Aeration/Filtration

Solution. Desalin. Water Treat., 8, 124–130.

Combined Bioreactor. J. Membr. Sci., 344(1-2), 219–224.

Elmolla, E. S.; Chaudhuri, M. (2009) Degradation of the Antibiotics Amoxicillin, Ampicillin and Cloxacillin in

1052 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Aqueous Solution by the Photo-Fenton Process. J. Hazard.

Ewecharoen, A.; Thiravetyan, P.; Wendel, E.; Bertagnolli, H.

Mater., 172(2-3), 1476–1481.

(2009) Nickel Adsorption by Sodium Polyacrylate-Grafted

El Nemr, A.; Abdelwahab, O.; El-Sikaily, A.; Khaled, A. (2009)

Activated Carbon. J. Hazard. Mater., 171, 335–339.

Removal of Direct Blue-86 from Aqueous Solution by New

Fanchiang, J. M.; Tseng, D. H.; Guo, G. L.; Chen, H. J. (2009)

Activated Carbon Developed from Orange Peel. J. Hazard.

Ozonation of Complex Industrial Park Wastewater: Effects

Mater., 161(1), 102–110.

on the Change of Wastewater Characteristics. J. Chem.

England, C.; Navratil, R.; Hunter, G. (2009) Optimizing an

Technol. Biotechnol., 84(7), 1007–1014.

Intermediate Ozone System Used for Primary Disinfection

Farias, J.; Albizzati, E. D.; Alfano, O. M. (2009) Kinetic Study of

at a 55 Mgd Surface Water Treatment Plant. Ozone Sci.

the Photo-Fenton Degradation of Formic Acid Combined

Eng., 31(6), 461–471.

Effects of Temperature and Iron Concentration. Catal.

Ennigrou, D. J.; Gzara, L.; Ben Romdhane, M. R.; Dhahbi, M.

Today, 144(1-2), 117–123.

(2009) Cadmium Removal from Aqueous Solutions by Polyelectrolyte

Enhanced

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Feng, L.; Li, X. F.; Du, G. C.; Chen, J. (2009a) Adsorption and

Desalination,

Fouling

246(1-3), 363–369.

Characterization

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Klebsiella

Oxytoca

to

Microfiltration Membranes. Process Biochem., 44(11),

Erdim, E.; Soyer, E.; Tasiyici, S.; Koyuncu, I. (2009) Hybrid Photocatalysis/Submerged

Microfiltration

1289–1292.

Membrane

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System for Drinking Water Treatment. Desalin. Water

Fenton Degradation of High Concentration Orange II (2

Treat., 9(1-3), 165–174.

Mm) Using Catalysts Containing Fe: A Comparative Study.

Eren, E. (2009a) Investigation of a Basic Dye Removal from Aqueous

Solution

onto

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Modified

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Unye

Ferrari, C.; Longo, I.; Tombari, E.; Bramanti, E. (2009) A Novel

Bentonite. J. Hazard. Mater., 166(1), 88–93.

Microwave Photochemical Reactor for the Oxidative

Eren, E. (2009b) Removal of Lead Ions by Unye (Turkey)

Decomposition

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Mw/UV/H 2O2 Process. J. Photochem. Photobiol. A Chem.,

Hazard. Mater., 165(1-3), 63–70.

204(2-3), 115–121.

Esquivel, K.; Arriaga, L. G.; Rodriguez, F. J.; Martinez, L.;

Fersi, C.; Gzara, L.; Dhahbi, M. (2009) Flux Decline Study for

Godinez, L. A. (2009) Development of a TiO2 Modified

Textile Wastewater Treatment by Membrane Processes.

Optical Fiber Electrode and Its Incorporation into a

Desalination, 244(1-3), 321–332.

Photoelectrochemical Reactor for Wastewater Treatment.

Fouladi Tajar, A.; Kaghazchi, T.; Soleimani, M. (2009) Adsorption

Water Res., 43(14), 3593–3603.

of Cadmium from Aqueous Solutions on Sulfurized

Ersoy, B.; Tosun, I.; Gunay, A.; Dlkmen, S. (2009) Turbidity

Activated Carbon Prepared from Nut Shells. J. Hazard.

Removal from Wastewaters of Natural Stone Processing by

Mater., 165, 1159–1164.

Coagulation/Flocculation Methods. Clean Soil Air Water,

Fourcault, A.; Garcia-Jarana, B.; Sanchez-Oneto, J.; Marias, F.;

37(3), 225–232.

Portela, J. R. (2009) Supercritical Water Oxidation of Phenol with Air. Experimental Results and Modelling. Chem. Eng. J., 152(1), 227–233.

1053 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Gabor, B.; Endre, N. (2009) Removal of Zinc and Nickel Ions by

Ghidossi, R.; Veyret, D.; Scotto, J. L.; Jalabert, T.; Moulin, P.

Complexation-Membrane Filtration Process from Industrial

(2009) Ferry Oily Wastewater Treatment. Sep. Purif.

Wastewater. Desalination, 240(1-3), 218–226.

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Goi, D.; Di Giorgio, G.; Cimarosti, I.; Lesa, B.; Rossi, G.; Dolcetti,

H. A.; Shoreit, A. A. M. (2009) Biosorption of Hexavalent

G. (2009) Treatment of Landfill Leachate by H2o2

Chromium Using Biofilm of E. Coli Supported on

Promoted Wet Air Oxidation: COO-AOX Reduction,

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Magnetically Separable Photocatalyst (TiO2/SiO2 /Fe3O 4):

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Parametric and Kinetic Studies. Desalination, 244(1-3), 1–

on the Destruction Degree of Fulvic Acids and Organic

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Application of Response Surface Methodology (RSM) to

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and Binary Mixture by UV/TiO2/Periodate System. J.

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Purification of Wastewater of Ion Exchange Plant of Shiraz

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Method. Asian J. Chem., 21(5), 3817–3824.

Removal of Humic Acid and O-Dichlorobenzene in

1054 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Drinking Water by Combined Ozonation and Bentonite

Replacement of Metal Salts. Water Sci. Technol., 59(2),

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and Equilibrium Study. J. Hazard. Mater., 172, 507–514.

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Substance Coagulation and Membrane Filtration under

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Removal from Water. Ochrona Srodowiska, 31(2), 31–34.

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Gunes, K.; Tuncsiper, B. (2009) A Serially Connected Sand

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Filtration and Constructed Wetland System for Small

Siegrist, H. (2009) Elimination of Organic Micropollutants

Community Wastewater Treatment. Ecol. Eng., 35(8),

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a Full-Scale Post-Ozonation Followed by Sand Filtration.

Guo, X. J.; Wu, Z. J.; He, M. C. (2009) Removal of Antimony(V)

Environ. Sci. Technol., 43(20), 7862–7869.

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Hong, H. J.; Kim, H.; Lee, Y. J.; Yang, J. W. (2009) Removal of

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Ability by Pretreatment of Secondary Effluent Using a New

N. (2009) Treatment of Textile Dye Effluents Using

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of Tannery Wastewater Using Cationic Polymers as a

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1055 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Huang, W. Y.; Wang, B. B.; Guo, L.; Wu, F.; Deng, N. S. (2009a)

Janus, T.; Paul, P.; Ulanicki, B. (2009) Modelling and Simulation

Photochemical Processes and the Related Advanced

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Material on the Generation of Oxidants and Microbial

Powerful Radicals Involved in the Mineralization of

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UV/TiO2 and UV/TiO2 /Chemical Oxidant Processes for the

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Marques, S. M.; Goncalves, F.; Rocha-Santos, T. A. P.; Freitas, A. C. (2009) Toxicity and Organic Content Characterization of Olive Oil Mill Wastewater Undergoing

1056 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

a Sequential Treatment with Fungi and Photo-Fenton

Applications of Advanced Oxidation Processes: A Case

Oxidation. J. Hazard. Mater., 172(2-3), 1560–1572.

Study of Technology Transfer from Switzerland to Burkina

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Faso on the Field of Photochemical Detoxification of

S.; Alam, M. D. Z.; Yahya, N. (2009) Kinetic Adsorption of

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Kalpakli, Y. K.; Koyuncu, I. (2009) Characterization of Activated

B. (2009) Discoloration and Detoxicification of a Congo

Carbon and Application of Copper Removal from Drinking

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Decolorization of CI Acid Blue 9 Solution by UV/Nano-

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(2009b) A Hybrid Microfiltration-Granular Activated

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Kim, I.; Yamashita, N.; Tanaka, H. (2009a) Performance of UV

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1057 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Kim, I.; Yamashita, N.; Tanaka, H. (2009b) Photodegradation of

Kotel, L. Y.; Brichka, A. V.; Brichka, S. Y. (2009) Adsorption

Pharmaceuticals and Personal Care Products During UV and

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Ko, K. B.; Lee, J. Y.; Yoon, Y. H.; Moon, T. H.; Ahn, Y. H.; Park,

and Pac Adsorption Pretreatments on Membrane Filtration

C. G.; Min, K. S.; Park, J. H. (2009) Effects of Nitrate on

for a Surface Water in Korea: A Pilot Study. Desalination,

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Kongsuwan, A.; Patnukao, P.; Pavasant, P. (2009) Binary

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Component Sorption of Cu(II) and Pb(II) with Activated

with Pre-Ozonation for Treatment of Secondary Wastewater

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1058 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Levadnaya, T. I.; Savluk, O. S.; Soboleva, N. M.; Potapchenko, N.

Liu, H. B.; Sun, L. P.; Wang, Y.; Xia, S. Q.; Le, L. S. (2009a)

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Activated Carbon Prepared from Spartina Alterniflora:

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Systems for the Treatment of an Industrial Pharmaceutical

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Flux Decline Mechanism and Economic Feasibility. Sep.

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of Acid Orange 7 from Water by Electrochemically

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1062 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Rhizopus Oryzae and of a Photo-Fenton Oxidation in the

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the Effluent of a Sewage Treatment Plant Using Ozone

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from Tehran Drinking Water. J. Water Supply Res. Technol.

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and Cost Indicators. Desalin. Water Treat., 5(1-3), 153–158.

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Theoretical Model Including Direct and Indirect Oxidation

(2009) Synergetic Effect of Copper-Plating Wastewater as a

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Shu, H. Y.; Chang, M. C.; Chang, C. C. (2009) Integration of Nanosized Zero-Valent Iron Particles Addition with

1065 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

UV/H2O2 Process for Purification of Azo Dye Acid Black

Sirtori, C.; Zapata, A.; Oller, I.; Gernjak, W.; Aguera, A.; Malato,

24 Solution. J. Hazard. Mater., 167(1-3), 1178–1184.

S. (2009b) Solar Photo-Fenton as Finishing Step for

Silalahi, S. H. D.; Leiknes, T. (2009) Cleaning Strategies in

Biological Treatment of a Pharmaceutical Wastewater.

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Environ. Sci. Technol., 43(4), 1185–1191.

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Parameters on the Photocatalytic Oxidation of Phenol by

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Consideration on the Sedimentation Process in a Settling

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1066 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Su, Q.; Pan, B. C.; Pan, B. J.; Zhang, Q. R.; Zhang, W. M.; Lv, L.;

Microfiltration

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Activated Carbon in Batch and Fixed-Bed Adsorbers.

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Innovative Water Treatment System Coupled with Energy

1067 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Production Using Photo-Fenton Reaction. Water Sci.

Laboratory Investigation. Desalin. Water Treat., 11(1-3),

Technol., 60(10), 2589–2597.

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Sherbiny, M. F. (2009) Photo-Catalytic Degradation of an

Nitrogen and Chlorinated Lignin from Bleached Kraft Mill

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Effluents by UV Oxidation in the Presence of Hydrogen

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1068 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Activated Low Cost Carbon-Kinetic, Thermodynamic and

Emulsified Oily Wastewater from the Processing of

Equilibrium Studies. E- J. Chem., 6, S1–S11.

Petroleum Products. Desalination, 249(3), 1223–1227.

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Technol., 43(13), 4858–4863.

1069 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Wiley, P. E.; Brenneman, K. J.; Jacobson, A. E. (2009) Improved

Xu, A. H.; Yang, M.; Yao, H. Q.; Du, H. Z.; Sun, C. L. (2009a)

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UV/TiO2 -Based Systems: Effects of Ultrasound Irradiation.

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Methylene Blue in Water by Combined Sonolysis and

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Visualization of Fouling and Diffusion Behaviors During

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1070 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Yu, Z.; Peldszus, S.; Huck, P. M. (2009) Adsorption of Selected

Zhang, F.; Jing, W. H.; Xing, W. H. (2009c) Modeling of Cross-

Pharmaceuticals and an Endocrine Disrupting Compound by

Flow Filtration Processes in an Airlift Ceramic Membrane

Granular Activated Carbon. 1. Adsorption Capacity and

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Submerged Microfiltration Coupled with Physcio-Chemical

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Parameters Involved in Solar Photo-Fenton Degradation of a

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of

The Combination of Ozone with Ultrasound or Hydrogen

Ecotoxicity and Biodegradability. Appl. Catal. B-Environ.,

Peroxide for the Degradation of CI Acid Orange 7.

88(3-4), 448–454.

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and

Effect of

Water Treatment. Water Res., 43(5), 1179–1186.

Assessment

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Zhang, Y.; Li, D. L.; Chen, Y.; Wang, X. H.; Wang, S. T. (2009h)

Molasses Fermentation Wastewater by SnO2-Catalyzed

Catalytic Wet Air Oxidation of Dye Pollutants by

Ozonation. J. Hazard. Mater., 162(2-3), 682–687.

Polyoxomolybdate Nanotubes under Room Condition. Appl.

Zhang, Y.; Sun, P. D.; Song, Y. Q.; Fang, J.; Ma, W. G. (2009a)

Catal. B-Environ., 86(3-4), 182–189.

Removal of High Concentration NH4+-N by Nanochem

Zhang, Y. Y.; He, C.; Deng, J. H.; Tu, Y. T.; Liu, J. K.; Xiong, Y.

Zeolite Ion Exchange Technology. Prog. Environ. Sci.

(2009i) Photo-Fenton-Like Catalytic Activity of Nano-

Technol., Vol II, Pts A and B, 1551–1557.

Lamellar Fe2V4O13 in the Degradation of Organic Pollutants.

Zhang, C.; Gu, P.; Zhao, J.; Zhang, D.; Deng, Y. (2009b) Research

Res. Chem. Intermed., 35(6-7), 727–737.

on the Treatment of Liquid Waste Containing Cesium by an

Zhao, W.-T.; Huang, X.; He, M.; Mang, P. Y.; Zuo, C. Y. (2009)

Adsorption-Microfiltration Process with Potassium Zinc

NH4+-N Removal Stability of Zeolite Media Packed

Hexacyanoferrate. J. Hazard. Mater., 167(1/3), 1057–1062.

Multistage-Biofilm System for Coke-Plant Wastewater Treatment. Huanjing Kexue, 30(2), 594–599.

1071 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation

Zhao, X. H.; Zhao, Y. Q. (2009) Decolouration of H2SO4 Leachate

Zuo, J. L.; Li, J. S. (2009) Bench Scale Study on the Adsorption

from Phosphorus-Saturated Alum Sludge Using H2O2 and

and Regeneration of Clinoptilolite for Ammonia Removal.

Advanced Oxidation Processes in Phosphorus Recovery

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Strategy. J. Environ. Sci. Health Part A-Toxic/Hazard.

Control, Automation and Systems Engineering, (CASE

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Zheng, Z.; Zhang, H.; He, P. J.; Shao, L. M.; Chen, Y.; Pang, L. (2009a) Co-Removal of Phthalic Acid Esters with Dissolved Organic Matter from Landfill Leachate by Coagulation and Flocculation Process. Chemosphere, 75(2), 180–186. Zheng, X. J.; Wei, L. F.; Zhang, Z. H.; Jiang, Q. J.; Wei, Y. J.; Xie, B.; Wei, M. B. (2009b) Research on Photocatalytic H-2 Production

from

Acetic

Acid

Solution

by

Pt/TiO2

Nanoparticles under UV Irradiation. Int. J. Hydrogen Energy, 34(22), 9033–9041. Zheng, X.; Ernst, M.; Jekel, M. (2009c) Identification and Quantification of Major Organic Foulants in Treated Domestic Wastewater Affecting Filterability in Dead-End Ultrafiltration. Water Res., 43(1), 238–244. Zheng, H. L.; Pan, Y. X.; Li, D. D.; Wu, Y. Q. (2009d) Degradation of Organic Contaminant in Landfill Leachate by Photo-Fenton Process. Spectrosc. Spectr. Anal., 29(6), 1661–1664. Zhu, P. Y.; Wang, H. Z.; Li, X.; Tang, X. F. (2009a) Enhanced Removal of Metal Ions from Water by Novel Composite Magnesia-Amended Silica Granules. Adsorpt. Sci. Technol., 27(4), 383–394. Zhu, X. P.; Ni, J. R.; Lai, P. (2009b) Advanced Treatment of Biologically

Pretreated

Coking

Wastewater

by

Electrochemical Oxidation Using Boron-Doped Diamond Electrodes. Water Res., 43(17), 4347–4355. Zonoozi, M. H.; Moghaddam, M. R. A.; Arami, M. (2009) Coagulation/Flocculation

of

Dye-Containing

Solutions

Using Polyaluminium Chloride and Alum. Water Sci. Technol., 59(7), 1343–1351.

1072 Water Environment Research, Volume 82, Number 10—Copyright © 2010 Water Environment Federation