![Ozonation mechanism of phenol. (A) The resonance structures of carbon cations (the case of ortho position adduct, E is assigned to ozone); (B) the mineralization pathway of phenol (AO is assigned to abnormal process). [(A) was adapted from Beltrán et al. 2007, (B) was adapted from Eisenhauer 1968].](https://www.researchgate.net/profile/Chao-Hai-Wei/publication/313288782/figure/fig4/AS:555543132426241@1509463212350/Ozonation-mechanism-of-phenol-A-The-resonance-structures-of-carbon-cations-the-case_Q320.jpg)
Content uploaded by Chao-Hai Wei
Author content
All content in this area was uploaded by Chao-Hai Wei on Nov 27, 2019
Content may be subject to copyright.
Rev Chem Eng 2016; aop
*Corresponding author: Chaohai Wei, School of Environment and
Energy, South China University of Technology, Guangzhou, 510006,
P.R. China, e-mail: cechwei@scut.edu.cn
Fengzhen Zhang, Yun Hu and Chunhua Feng: School of Environment
and Energy, South China University of Technology, Guangzhou,
510006, P.R. China
Haizhen Wu: School of Bioscience and Bioengineering, South China
University of Technology, Guangzhou, 510006, P.R. China
Chaohai Wei*, Fengzhen Zhang, Yun Hu, Chunhua Feng and Haizhen Wu
Ozonation in water treatment: the generation,
basic properties of ozone and its practical
application
DOI 10.1515/revce-2016-0008
Received February 10, 2016; accepted May 18, 2016
Abstract: The widespread applications of ozone technolo-
gies are established on the basis of large-scale manufac-
ture of ozone generator and chemical reactivity of ozone.
It is hence necessary to summarize the principles of ozone
generation and to analyze the physicochemical proper-
ties of ozone, which are of fundamental significance to
indicate its technical developments and practical applica-
tions. This review presents a summary concerning ozone
generation mechanisms, the physicochemical properties
of ozone, as well as the applications of ozone in water
treatment. Ozone can be produced by phosphorus contact,
silent discharge, photochemical reactions, and electro-
chemical reactions, principally proceeding by the reac-
tion of oxygen atom with oxygen molecule. There are side
reactions to the generation of ozone, however, which are
responsible for ozone depletion including thermal decom-
position and quenching reactions by reactive species. The
solubility of ozone in water is much higher than that of
oxygen, suggesting that it may be reliably applied in water
and wastewater treatment. Based on the resonance struc-
tures of ozone, one oxygen atom in ozone molecule is elec-
tron-deficient displaying electrophilic property, whereas
one oxygen atom is electron-rich holding nucleophilic
property. The superior chemical reactivity of ozone can
also be indirectly revealed by radical-mediated reactions
initiated from homogenous and heterogeneous catalytic
decomposition of ozone. Owing to the reliable generation
of ozone and its robust reactive properties, it is worthy to
thoroughly elaborate the applications of ozone reaction
in drinking water disinfection and pre- or post-treatment
of industrial wastewater including cyanide wastewater,
coking wastewater, dyeing wastewater, and municipal
wastewater. The structural characteristics of ozone reac-
tors and energy requirement of applied technologies are
evaluated. In addition, future directions concerning the
development of ozone generation, ozone reactivity, and
industrial wastewater ozonation have been proposed.
Keywords: energy consumption; ozone generation; ozone
reactor; physicochemical properties; water treatment.
1 Introduction
The electronic and ionic excitations of molecular oxygen
by physical field including electric discharge, ultraviolet
irradiation, and electrolysis are the preliminary reactions
for ozone generation. The electric discharge (e.g. silent
discharge) is the most reliable approach for ozone genera-
tion in both laboratory and industrial scale owing to the
convenience and operational efficiency in different ozone
concentration requirement (Nomoto et al. 1995, Salam
etal. 2013). A configuration of ozone generator adopting
silent discharge was first proposed by Siemens in 1857,
characterized by the presence of a dielectric layer on the
inner surface of electrodes. The electrochemical reactions
proceeded at anode in a variety of aqueous media could
also be capable of generating ozone, whose advantages
comprise low voltage operation, no gas fed of any descrip-
tion, and the possibility to produce high concentration
of ozone in gaseous and aqueous phase (Christensen
etal. 2009). It was found that (˙OH)ads and Oads generated
by means of electrolysis were intermediates involved in
ozone production (Da Silva etal. 2006, Kim and Korshin
2008).
Due to the instability of ozone, only ozone generator
can be operated practically and stably; it is possible to
elucidate the physical and chemical properties of ozone,
focusing on its solubility and chemical reactivity, which
will widen its application in water and wastewater treat-
ment. Ozone is generally colorless and less soluble in
water, with special pungent odor at ordinary tempera-
ture, from which its name was derived (Guzel-Seydim
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
2C. Wei etal.: Ozonation in water treatment
etal. 2004). On the other hand, ozone is a chemical reac-
tive reagent exhibiting electrophilic and nucleophilic
characteristics, which are closely related to its resonance
structures. Kalemos and Mavridis (2008) reported that the
ground state of ozone is a “closed-shell singlet resulted
from O2(1Δg) and O(1D),” demonstrating that its electronic
structure corresponds to two resonant structures with one
O-O single bond and one O=O double bond, which could
be merged into one closed-shell structure by attributing
one and a half bond to each O-O interaction. Compara-
tively, Miliordos and Xantheas (2014) indicated that an
open-shell structure of ozone could be established with
a single bond and two lone electrons on each terminal
atom, based on ground-state multireference configura-
tion interaction wave functions. Although ozone is a pow-
erful oxidant, it reacts less efficiently with some organic
(e.g. saturated aliphatic acid) and inorganic (e.g. NH4+)
compounds. In order to accelerate the mineralization
efficiency, advanced oxidation processes such as O3/UV,
O3/H2O2, catalytic ozonation and photocatalytic ozonation
stimulating the generation of more robust and stronger
radical species, have been suggested as potential alter-
natives. However, owing to the inhibited effect of radical
scavengers (i.e. carbonate and bicarbonate) on ˙OH-medi-
ated reactions, it is encouraged to establish novel reaction
systems based on liquid-liquid or liquid-solid extraction
of ozone and organic substances from aqueous solution
to organic solvent, followed by the reactions proceeded in
non-aqueous phase (Kasprzyk-Hordern etal. 2003).
In view of its strong oxidation ability with a selection
of pollutants, ozone can be potentially used as a broad-
spectrum disinfectant and a powerful oxidant for waste-
water treatment. A large variety of micro-organisms could
be effectively inactivated by ozone through cell lysis and
nucleic acids destruction (von Gunten 2003a, Kingsbury
and Singer 2013, Tachikawa and Yamanaka 2014). Even
though the production of halogenated compounds can be
avoided by ozone disinfection, the vast majority of oxygen
atom containing byproducts including bromate, aldehyde,
ketone, esters, and keto acids may be generated (Richard-
son etal. 1999). Ozone has also been extensively applied
for further treatment of industrial wastewater such as
cyanide containing wastewater, coking wastewater, oil
refining wastewater, and pharmaceutical wastewater,
through the selective oxidative reactions with unsaturated
and conjugated matrix components (Laera et al. 2012,
Chen et al. 2014a, Lin etal. 2014a). It had been estab-
lished that ozone-based technologies (e.g. non-catalytic
ozonation, ozonation catalyzed by ultraviolet irradiation,
hydrogen peroxide and various heterogeneous catalysts)
can be the alternatives or the pre-treatment methods for
biological treatment of actual agro-industrial wastewater,
which were indicated by the improvement of biodegrada-
bility and toxicity removal (Martins and Quinta-Ferreira
2014).
While previous publications have provided a wealth
information on ozone generation (Wei et al. 2014), the
basic properties of ozone (Sonntag and von Gunten
2012), the mechanisms of ozonation and catalytic ozona-
tion (Kasprzyk-Hordern et al. 2003, Hübner etal. 2015),
the disinfection of drinking water, and mineralization of
industrial wastewater (Langlais etal. 1991, Barndõk etal.
2014, Zhang etal. 2014a), an integrated overview concern-
ing ozone production, physico-chemical properties of
ozone, and its practical application is still missing. A criti-
cal review that combines the technical developments of
ozone generation, the analysis of its basic properties, and
the general mechanisms of ozone reaction will be helpful
to the implementation of its application in large scale. The
objectives of this review are to summarize ozone genera-
tion mechanisms and its generator as a whole; to analyze
the fundamental characteristics of ozone, so as to discuss
the pollution control for which ozone-based technologies
applied; and to evaluate the energy consumption of ozo-
nation processes in terms of ozone generation as well as
contaminants removal.
2 The generation of ozone and its
generator
2.1 The principle of ozone generation
2.1.1 Phosphorus contact ozone generation
The existence of oxygen atom produced from excitation of
oxygen molecule is the prerequisite reaction for various
ozone generation techniques. The white phosphorus
contact with wet air, electrolysis of acidic aqueous solu-
tion, and photosensitive reaction of mercury were respon-
sible for ozone generation during early days of its discovery
(Fallon and Vanderslice 1960). The white phosphorus
contact was the most prevalent approach at that moment
due to its simplicity and low investment requirement. In
general, the reaction of white phosphorus with wet air can
be expressed in Eqs. (1–5) (Andrews and Withnall 1988),
with the generation of oxygen atom being the critical
step. Then the resulting mixtures containing ozone and
phosphorus oxides were purified by water. It was found,
however, that ozone productivity by phosphorus reaction
was unsatisfactory, suffering from variable yield results
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment3
and low efficiency, although maximum ozone concentra-
tion of 2.5 mg/l could be attained by an optimized proce-
dure (Leeds 1879, Rubin 2002). Studies dedicated in other
alternative technologies for improved ozone generation
as well as basic mechanisms behind its generation were
therefore conducted.
+→ +
42 4
PO PO O
(1)
+→
44
POPO
(2)
+
+→ +=−
4n 24n1
PO OPOO (n 19)
(3)
+→+
4241
03
P20O PO 10O
(4)
+→
4102
34
PO 6H O4HPO
(5)
23
22
OO MOM, H144.8 kJ/mol,
MN, or O
∆++→+ =
= (6)
Fundamentally, the first preliminary reaction for ozone
generation is the excitation of molecular oxygen by high
energy field, resulting in the generation of oxygen atom.
Ozone can be subsequently produced by the essential
Three-body Collision Reaction involving an oxygen atom,
an oxygen molecule, and a third body as shown in Eq. (6)
(Rubin 2002). In the electronic point of view, ozone forma-
tion can be achieved through the spin-pairing of antibo-
nding πg electrons of the ground state molecular oxygen
with two unpaired electrons of oxygen atom (Harcourt
etal. 1986), which is widely accepted by scientific com-
munities. These achievements underpin the popularity
of silent discharge, photochemical synthesis, and elec-
trolysis techniques, which are in essence proceeded with
energy transferred from physical fields.
2.1.2 Gaseous discharge for ozone generation
The basic principle of ozone generation by means of
gaseous discharge comprises the creation of electrons
in discharge gap as well as the excitation of oxygen mol-
ecule, eventually leading to ozone appearance. Silent
discharge, also known as dielectric barrier discharge
(DBD), is the non-equilibrium discharge process carried
on between discharge gap in which the dielectric barrier
is intercalated (Yehia 2015). Typically, as illustrated in
Figure1, the configurations of dielectric layers are either
covered on the surface of electrodes inside discharge gap
or suspended between them. In general, ozone generation
by silent discharge involves three following steps: (1) a
breakdown of the gap occurs in a few nanoseconds upon
the load of applied voltage, (2) the production of current
pulse occurs as a result of increasing density of charged
particles and then the transfer of electric charge within
10 ns, (3) the ozone generation reactions take place in
H.V.
H.V.
ABC
FED
H.V. H.V.
H.V. H.V.
Figure 1:The schematic configurations of silent discharge electrodes assembled by plated electrode [(A)–(C)] and coaxial tube electrode
[(D)–(F)]. (Common dielectric materials consisted of glass, ceramics, enamel, and mica; the average thickness of these dielectrics is
0.5–3mm. The gray color parts are referred to electrodes, while the blue color parts are assigned to insulating dielectric materials).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
4C. Wei etal.: Ozonation in water treatment
micro-discharge current channel (Eliasson et al. 1987).
The chemical reactions consisting of electron-impact
reactions, neutral-neutral reactions, and charged parti-
cle reactions mainly contribute to ozone generation, with
some exemplary reactions discussed below (Kitayama and
Kuzumoto 1999, Lee etal. 2004). When air or pure oxygen
gas is fed through the discharge gap, O2 can be excited
from its ground state ∑
3
2
-
(( ))OX g to metastable state
+
∑∑
3-3
22
OB , (( )( )
O)
A
uu
by inelastic collision with high-
energy electrons in <3 ns, producing O (3P) and O (1D), as
shown in Eqs. (7–9) (Kitayama and Kuzumoto 1997). Ozone
can be then produced through the well-established Three-
body Collision Reaction [Eq. (6)]. Besides, ozone can also
be produced via metastable reaction of oxygen molecule
with +
∑
3
2
()
)OA u [Eq. (10)] in <3 μs (Benson 1959). In con-
trast to the significant contribution of high-energy elec-
tron, low-energy electron is capable of exciting oxygen
molecule into its negative ion state [Eq. (11)], which imme-
diately reacts with oxygen molecule to produce ozone as
illustrated in Eq. (12) (Benson 1959). On the other hand,
the formed ozone may be inevitably destroyed by oxygen
negative ion, oxygen atom, and electron [Eqs. (13–16)],
where M is assigned to any particles present in the gas.
Also, heat accumulated from discharge gap could promote
thermal decomposition of ozone with a reaction rate con-
stant of 4.61±0.25×1012 exp(-24,000/RT) l/(mol·s) (Jones
and Davidson 1962).
+→+→++
∑∑
3331
22
--
eOXeOB eO(P)O(D) Reaction Threshold: 8( .)(
)4
eV
gu (7)
∆+→ +
131
22
g
O(
D(
)O O( P)
O)
(8)
+
+→+→++
∑∑
33
-33
22
eOXeOA eO(P)O(P)Reaction Threshold: 6()
(e
V
).
1
gu (9)
++→+
∑
3
22
3
(O)OA
OO
u (10)
-
2
eO OO
R
eaction Threshold: 3.6 eV+→+ (11)
+→+
-
23
OO
Oe
(12)
∆+→
+=
--
322 m
OO OO H-82 kcal/mol (13)
∗
+→ +
322
OO
OO
(14)
∗+→ +
22
OMOM
(15)
∆
+→++ =
32 m
eO OO eH-10 kcal/mol
(16)
Based on the concept that discharge area is essential
for ozone generation, modified discharge assembly of
DBD including surface discharge and hybrid discharge
is widely employed for ozone generation in a variety of
applications. The invention of surface dielectric barrier
discharge (SDBD) enables propagation of micro-discharge
in a non-uniform field along dielectric surface and a
larger discharge area than channel diameter (Nassour
etal. 2016). Typically, there is a dielectric surface in SDBD
with thin parallel electrode strips on one side of dielec-
tric barrier, while a metallic electrode is covered on the
reverse side of barrier, leaving the gas gap unfixed as
depicted in Figure 2A–B (Pavon etal. 2007). An extended
discharge area on dielectric barrier surface can be devel-
oped as a result of the unfixed gas gap in SDBD, which is
confirmed by stronger emission discovered from the edges
in the form of long filaments (streamers) with increasing
airflow velocity (Figure 2C). Similarly, Xu (2001) reported
the extended discharge area of SDBD and indicated that it
depended on the accumulated surface charge during dis-
charge development, starting on the dielectric surface and
flowing towards the surface electrode in case of positive
polarity.
The ozone generation can be improved by the hybridi-
zations of different discharge types. Nomoto etal. (1995),
for instance, specially designed a discharge unit inte-
grating silent discharge with surface discharge for ozone
generation, which was assembled of inner coil electrode
and external copper cylinder electrode (Figure 2D). The
length and diameter of inner coil electrode were 80mm
and 0.25 mm, respectively, keeping in contact with inner
wall of coaxial glass tube (inner diameter was 12.2 mm,
thickness was 1.4 mm). The inner diameter of grounded
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment5
Airflow ⊥ stripes
AB
C
D
Electrode
H.V.
H.V.
Flo
w
Dielectric barrier
External copper cylinder electrode
Silent discharge gap
O2, O3
O2, O3
O2
O2
Coil electrode
Surface discharge area
Coaxial glass tube
Airflow // stripes
Figure 2:The configurations of surface dielectric barrier discharge electrode (A–B) and silent-surface hybrid discharge (D) for ozone
generation, and CCD images of the whole discharge area for surface dielectric barrier discharge with the isentropic flow (corresponding to
velocity of airflow) increasing from left to right (C). [(A) to (C) were adapted from Pavon etal. 2007, (D) was adapted from Nomoto etal. 1995].
outer brass cylinder electrode was 17.0 mm, thereby
leaving 1-mm gap between outer side of coaxial glass
tube and inner side of copper cylinder. The combination
of different electrode types made it possible that silent
discharge occurred in the gap, while surface discharge
proceeded along the coil electrode. The authors revealed
that in the course of increasing applied voltage, surface
discharge was developed first along inner coil electrode
when voltage was <6.0 kV. And then silent discharge
became active in space gap as applied voltage increased
above 8.0 kV. Under optimized operation conditions, the
yield efficiency of ozone using silent-surface hybrid dis-
charge reached 274 g/kWh, which was almost two times
higher than that obtained using silent discharge (roughly
130 g/kWh). It was probably owed to the synergistic effect
of enhanced surface discharge driven by charge created
from silent discharge (Nomoto etal. 1995).
The evaluation of other discharge techniques such as
pulse streamer discharge, plasma jet discharge, pulse DBD,
and pulse corona discharge (PCD) is of significant impor-
tance for rising discharge efficiency of ozone generation
(Masuda etal. 1988, Robinson etal. 1998, Samaranayake
etal. 2011). The pulse dielectric barrier discharge (PDBD), for
example, is equipped with pulsed power with voltage pulse
duration ranging from 50 to 300 ns, improving the genera-
tion rate of ozone, and avoiding massive loss of energy in
heat (Kornev etal. 2006). Nevertheless, the preliminary dis-
charge pathways responsible for ozone generation by PDBD
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
6C. Wei etal.: Ozonation in water treatment
remain unchanged in comparison to conventional DBD,
i.e. ozone generation is continued through three follow-
ing steps described earlier. The PCD (the configurations of
corona electrodes and a PCD ozone generator are displayed
in Figure 3A–D) is an attractive approach in atmospheric
pressure and non-uniform electric filed (Lukes etal. 2005).
Principally, electrons can be created by both negative and
positive corona in a typical PCD process. The created elec-
trons leave ionizing region and move to plate electrode,
completing the circuit while producing pulse current fila-
ments and micro-current column (Šimek and Člupek 2002).
It has to be emphasized that three advantages of PCD rela-
tive to conventional DBD should be taken into account:
(1) the breakdown of gas gap is not a requisite as corona
onset voltage is usually below breakdown voltage, (2) the
dielectric barrier between electrodes is not needed due to
the limited development of spark, and (3) the humidity of
feed gas is not strictly restricted as a result of limited spark
development and perhaps the absence of surface discharge
(Hegeler and Akiyama 1997).
The presence of inert gas in feed air also exhibits a
significant influence on the mechanism of ozone genera-
tion. It was reported that, for instance, low concentration
of N2 (1–10%, volume ratio) in feed air may promote the
generation of ozone (Kogelschatz 2003, von Sonntag and
von Gunten 2012). This was explained by the fact that part
of oxygen atom and electron is capable of reacting with
metastable N2 through the excitation and dissociation of
ground state N2, as shown in Eqs. (17–19). The storage and
liberation of reactive species (i.e. oxygen atom and high-
energy electron) can be therefore accomplished via series
of electron transfer and radical reactions [Eqs. (20–27)],
reducing the probability of ozone depletion with these
species (Tokuaga and Suzuki 1984). However, the con-
centration of NOx produced from above reactions reaches
a level at which the recombination reactions of oxygen
atoms [Eqs. (28–30)] might be dominated or ozone could
be depleted by NOx [Eqs. (31–34)], adversely affecting
the generation of ozone (Toby 1984, Robert et al. 1988,
Eliasson and Kogelschatz 1991). Moreover, the catalytic
Pulsed power
supply
Outer metal
tube
Cooling water
Gas flow
Gas flow High-voltage
wire electrode
HV
HV
A
B
C
D
HV
Figure 3:The schematic configurations of corona electrodes (A), (B), and (C) are assigned for wire-cylinder, needle-plate, and wire-plate
modus, respectively, and the coaxial pulsed corona ozone generator (D).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment7
cycles [Eqs. (29) and (33)] also remarkably contribute
to ozone destruction (Yagi and Tanaka 1979). In order
to obtain the influence mechanisms of other inert gas
(e.g. He, Ar, Kr, Xe) on ozone generation, the readers are
referred to Wei etal. (2014).
Π
+
+→+
∑
33
24
2
O( P) NA NO()N
)(
)
(S
u (17)
Π
+
+→+
∑
13
22
2
O( D) NA NO()N
)(
)
(D
u (18)
ΠΠΠ
+
+→ +→ +
∑
3131
22ggu
eNANa,()
()
B, be2N e
u (19)
+→ +
2
NO NO O
(20)
+→+
2
NNONO
(21)
+
+→
+
∑
3
22 2
()ON
ANOO
u (22)
Π
+
+→
+
∑
33
22
g2
ONA B)
NO
(, 2
u (23)
+
+→ +
22
eN N2e
(24)
++
+→+
22
22
NONO
(25)
++
+→ +
22
NO ONOO
(26)
++→++
22
-
NO ONOO
(27)
++→+
2
ONOM NO M
(28)
+→+
22
ONONOO
(29)
+→2
OO O
(30)
+→ +
32
ONNO O
(31)
+→ +
2
32
1,
22
(ONOB)NO O (32)
+→ +
2
3212
ONONOA)O(
(33)
+→+
32
32
ONONOO
(34)
2.1.3 Photochemical ozone generation
The photochemical reactions are potentially capable of
exciting molecular oxygen, producing oxygen atom, and
thus accelerating ozone generation (Hashem etal. 1997).
Mechanistic studies indicated that ultraviolet (UV) irra-
diation favors the excitation of singlet or triplet oxygen
atom from ground state oxygen molecule [Eqs. (35–36)]
(Salvermoser etal. 2008). Also, it has been reported that
the triplet oxygen atom participating in ozone generation
can be produced from photo-excitation of NO2 in feed gas
[Eq. (37)] (Calvert 1976, Schnell etal. 2009). Other nitrogen
containing species are also found to be beneficial to ozone
generation. The excitation of oxygen atom, for example,
was promoted when TiO2 surfaces were exposed to NOx
(e.g. NO3
-) under illumination via charge transfer reactions
(Monge etal. 2010). Similar with the quenching reactions
of ozone by oxygen atoms [Eqs. (13–16)] excited from elec-
trons, however, the photons with different wave length as
well as oxygen atoms existed in the photoreaction system
could adversely exhaust ozone via Eqs. (38–41) (Levy 1971,
Matsumi and Kawasaki 2003).
+→
+λ
<
31
2
OhvO(P)O(D)175 nm
(35)
+→ <λ<
3
2
Ohv2O( P) 20 0 nm 242 nm
(36)
3
2
NO hv O( P) NO 420 nm
+→
+λ
< (37)
11
32g
OhvO O( D) 200 nm 310 n
)m
(∆+→
+<
λ< (38)
+→
+λ
<
∑1
32
-
3
OhvOXO(D
)4
() 11 nm
g (39)
13
32g
()OhvO O( P) 612 nm∆+→
+λ
< (40)
+→ +λ<
∑
33
32
-
OhvOXO(P)118 m() 0 n
g (41)
2.1.4 Electrochemical ozone generation
The electrochemical reactions in aqueous solution are
generally believed to be able to produce ozone with several
advantages involving no need of gas feed; low voltage oper-
ation; simple system design; and, in particular, reduced
loss of ozone by thermal decomposition during handling
(Foller and Kelsall 1993). Principally, ozone can be gener-
ated from electrolysis of water by employing anode mate-
rials with high oxygen evolution potential (e.g. graphite,
glassy carbon, and lead alloys) through the Six Electron
Transfer mechanism, as illustrated in Eq. (42), with stand-
ard redox potential of 1.51 V (Da Silva etal. 2006). In fact,
as standard redox potential for the oxidation of water into
oxygen (1.23 V) is lower than that of Eq. (42), molecular
oxygen can be simultaneously produced with ozone gen-
eration. Detailed mechanism courses for ozone generation
have been proposed consisting of water spilt and oxygen
atom transfer reactions [Eqs. (43–46)] on the basis of the
assumption that the generation of ˙OH is an essential
step (Feng etal. 1994). As the significant role of oxygen
atom responsible for ozone generation in gaseous phase
has already been discussed previously, the intermediate
oxygen atoms produced by electrolysis also participate in
ozone production in aqueous phase. Ozone generation can
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
8C. Wei etal.: Ozonation in water treatment
be thus additionally achieved by the reaction of oxygen
atoms affiliated on anode surface, which is derived from
the decomposition of ˙OH [Eq. (47)] with dissolved oxygen
(Kötz and Stucki 1987). The delivery of ozone from ozone
generator to treated solution can be avoided by employ-
ing the in situ generation of ozone using electrolysis in
aqueous solution, in which ozone generation and decon-
taminant reaction are supposed to proceed.
+
→+ +
-
23
3H OO6H 6e
(42)
-
2ads
HO (OH) He
̇
+
→+
+ (43)
2ads ad
s3
ads
()O(OH)(H
̇̇
O)+→
(44)
-
3ads 3
HO HO e()
̇+
→+
(45)
++
→+
33
HO
OH
(46)
-
adsads
OH OH
̇
)e
(+
→++ (47)
2.1.5 Summary
The generation of ozone can be reliably achieved through
the reaction of oxygen molecule with oxygen atom, which
can be technically produced by means of gas discharge,
photochemical excitation, and electrochemical reaction.
The silent discharge is widely adopted in ozone generator,
owing to its effectiveness and operational stability. The
ozone produced from silent discharge is, however, inevi-
tably consumed by thermal decomposition and side reac-
tions, thus limiting its wide practical application. In order
to reach a higher ozone yield efficiency, hybrid discharge
combinations such as integrating silent discharge with
surface discharge are superior to the individual technique,
as a result of the synergistic effect of different discharge
patterns. Moreover, PCD, which does not require electrode
insulation, could be an alternative option due to its ultra-
short pulsed power; simple electrode configuration; and,
most importantly, the possibility to operate with humid
gas. Particularly, it is the ability to work with humid gas
that makes PCD promising for in situ application of ozone
without transferring ozonated gas. Nevertheless, if PCD is
employed solely for ozone generation without watering
the electrodes, its ozone productivity per unit of energy
does not differ too much from silent discharge.
2.2 The ozone generator
Almost all ozone generators are practically operated with
silent discharge principle. The ozone generator funda-
mentally consisted of discharge unit, cooling system,
feed gas supplement, applied power, and corresponding
controlling system (Kitayama and Kuzumoto 1999, Alonso
et al. 2005), among which the design and operation of
discharge unit are of significant importance for ozone
generation. The ozone generator assembled using silent
discharge technique is commonly composed of coaxial
glass tube, whose outside wall of outer tube and inner
side wall of inner tube are uniformly coated by tin foil,
connecting to high-voltage power (Nassour et al. 2016).
Generally, the typical industrial ozone generators in early
times were categorized by plate-based, tube-based, and
other complex structural-based equipment, as compared
in Table 1. The plate-based Otto discharge cell (Figure4),
for example, was structured by water-cooled hollow
boxes working as high-voltage electrodes and parallel
glass plates acting as insulator. Technically, in case of
parallel connection of 48 discharge units, the maximum
ozone productivity was expected to be 18kg/h with power
efficiency of 20–22 kWh/ kg O3 (Information Institute of
Shanghai Science and Technology, 1976).
Currently, the most commonly used silent discharge
unit for ozone generation is usually assembled by several
water-cooled discharge tubes installed in parallel, as shown
in Figure 5 (Kogelschatz 2003). The cylindrical discharge
tubes with diameter of 20–50mm and length of 1–3m are
made of borosilicate glass, closed at one side, and mounted
inside slightly wider stainless steel tubes to remain annular
gap of 1–3mm (Figure 5). Metal coatings on the inner wall of
inside glass tubes serve as high-voltage electrodes, whereas
outer steel tubes function as ground electrodes. Some large-
scale ozone generators comprise several hundred discharge
tubes inside big steel tanks in order to provide required dis-
charge area, with maximum ozone productivity >800kg/h
applied in Japan for drinking water treatment and 230kg/h
applied in United States for municipal water treatment
(Loeb etal. 2012). The main obstacles hindering the devel-
opment of large-scale ozone generator are probably the
side ozone depletions and its thermal decomposition in
discharge gap, thus requiring further research efforts.
3 The physicochemical properties
of ozone
3.1 The physical properties of ozone
The physical properties of ozone, including odor, color,
and solubility, are the bases for its wide applications in
water and wastewater treatment. Ozone is an unstable
and colorless gas with pungent fishy smell under ambient
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment9
Table 1:The compositional structure and operation conditions of ozone generators in early period.a
Category
Applied powerSize of discharge unit Discharge
gap (mm)
Energy consumption
per area electrode
(kW/m)
Ozone yield
rateb
Cooling
system
Voltage
(kV)
Frequency
(Hz)
Otto plate Glass plate area, mm; central
pore size, . mm; thickness of
plate, –. mm
. kg/hcWater cooled
Block plate Glass plate diameter, mm;
central pore size, . mm;
thickness of plate, – mm
.. kg/hdOil cooled
Van der Made
tube
Thickness of outer tube, .mm;
diameter, . mm; length,
mm; diameter of inner tube,
. mm; length, mm
<. g/heWater cooled
Siemens & Halske
tube
,Thickness of dielectric glass,
.mm; diameter, mm; length,
mm
. .. kg/hfWater cooled
Welsbach tube –Thickness of outer tube, . mm;
diameter, mm; length, mm
.–.. kg/hgWater cooled
Lowther grid plate– –. . kg O/dAir cooled
aData from Translations of Ozone and Its Applications, Series 2. Information Institute of Shanghai Science and Technology, 1976.
bData were obtained by air as feed gas.
cParallel connection of 48 discharge units.
dParallel connection of 64 discharge units.
eParallel connection of 30 discharge tubes.
fParallel connection of 6 discharge tubes.
gParallel connection of 204 discharge tubes.
Air
E
BB
Air
CCCC
DAO3, O
2
AAD
Figure 4:The schematic configuration of Otto plate based ozone
generator. (A: grounding electrode of water cooled hollow box;
B:dielectric glass; C: discharge gap; D: high-voltage electrode of
water cooled hollow box; E: transformer. The size of discharge cell
could be referred to Table 1).
pressure and temperature (Khadre etal. 2001). The special
odor may be possibly used to indicate the presence of
ozone and to provide a warning of toxic exposure in
advance. The other physical properties of ozone such as
melting point, boiling point, and dipole moment are listed
in Table2. It can be seen that, for example, ozone is a weak
polar molecule taken into account of its dipole moment,
demonstrating that ozone may exhibit various properties
(i.e. solubility and chemical reactivity) in water solution
(Beltrán et al. 2007). The most distinguishable physical
property of ozone concerning its potential application in
water treatment is its solubility. By conducting iodometric
titration, solubility of ozone in water was first accurately
determined to be 0.834 l/l (1°C, 741.5mm Hg), which was
13 times as much as that of oxygen in temperature range of
0–30°C (Rubin 2002), although some other different solu-
bility data had been reported (Rice etal. 1981, Roth and
Sullivan 1981).
The dissolution equilibrium of ozone in aqueous solu-
tion is basically influenced by the partial pressure of ozone
in gaseous phase, the temperature of water, and its bubble
size distributed in solution. The dissolved concentration
of ozone at fixed temperature is linearly proportional to
its partial pressure, following the famous Henry’s law
(Biń 2004). Therefore, the solubility of ozone in aqueous
solution can be increased as partial pressure of ozone in
gaseous phase is elevated, based on which the increase
of gas pressure in ozone contactor will be advantageous
to ozone dissolution (see the discussion in Section 4.6).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
10C. Wei etal.: Ozonation in water treatment
Discharge gap
Fuses
Wiring
Discharge gap
HV fuse
Cooling water Outer steel tube
Glass tube
Gas flow
Metal plating
layer
AB
Figure 5:The schematic configuration (A) and the real figure (B) of the modern industrialized tube ozone generator. Adapted with permis-
sion from Kogelschatz 2003, Copyright 2003, Plenum Publishing Corporation.
Table 2:The physical properties of ozone.
Physical properties Data Reference Physical properties Data Reference
Melting point
(mm Hg)/°C
-.±.Jenkins and Dipaolo Thermal conductivity
(-°C)/cal/(s) (cm) (°C/cm)
.cWaterman etal.
Boiling point
(mm Hg)/°C
-.±.Birdsall etal. Dielectric constant .dThorp
Critical temperature/°C-.aBirdsall etal. Solubility in water/(l/l)e Roth and Sullivan
Evaporation heat
(at b.p.)/(Kcal/mol)
. Hersh etal. °C.
Dipole moment/Debye . Gill and Laidler °C.
Vapor pressure/mm Hg .bBirdsall etal. °C.
Gaseous density at NTP/(g/l). Jenkins and Dipaolo °C.
Solid density
(. K)/(g/cm)
. Jenkins and Dipaolo °C.
aData were derived from 54.6 atm.
bData are valid at 80.2K (-193°C), the triple point of ozone.
cThe pressure at which thermal conductivity was measured is the vapor pressure of liquid at that particular temperature.
dData were obtained at 1 kilocycle per second at temperature of -183°C.
eData were obtained at 1 atm.
It is well recognized that dissolution of gas into water is
an exothermic process. Bablon etal. (1991) reported that
ozone solubility increased as the temperature of water
decreased on the basis of a negative logarithmic relation-
ship between solubility ratio [Sr, referred to Eq. (48)] and
water temperature in the range of 0.5–43°C. Moreover, the
dissolution rate of ozone can be accelerated by decreasing
ozone bubble size due to improved mass transfer, higher
inner pressure in the micro-bubble, as well as longer
hydraulic retention time (HRT) relative to macro-bubble
ozone (Chu etal. 2008). Zheng etal. (2015) investigated the
influence of bubble size (micro-bubble and macro-bub-
ble) on ozone dissolution behavior. The ozone dissolution
can be defined as Eq. (49), where kL (m/s), a (m-1), kd (s-1), ρL
(mg/l), and ρL* (mg/l) were assigned to the mass transfer
coefficient from gaseous into aqueous phase, the specific
surface area for gas-liquid contact per volume, the decom-
position rate constant of ozone, the dissolved ozone con-
centration in water, and the equilibrium concentration of
ozone in aqueous solution, respectively. It was revealed
that kLa of micro-bubble ozone contactor was 2.2 times
higher than that of macro-bubble ozone contactor, which
is consistent with results reported by Chu etal. (2007)
and Liu etal. (2010). Gong etal. (2007) confirmed that the
solubility ratio was higher in the case of smaller diameter
bubble by developing the solubility ratio [Eq. (50)] from
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment11
Eq. (48), where jb (kg/s), tb (s), c0 (kg/m3), and Rb (m) were
the instantaneous mass transfer rate of a single bubble,
the contact time, the initial concentration of dissolved gas
inside bubble, and the bubble diameter, respectively. In
spite of the different dissolution behavior of ozone, the
dissolved ozone concentration would be equal to its solu-
bility at fixed temperature according to Henry’s law, until
equilibrium dissolution is established. In addition, chemi-
cal reactions responsible for ozone decomposition initi-
ated by dissolved organic matter (DOM), OH- in solution
(alkaline condition), and solid catalysts may considerably
influence the dissolution of ozone.
=
r3 3
(mg/l Oin water)/(mg /l Oin gas ph ase)S
(48)
∗
=ρ
ρρ
LLdL
(-) -
L
vkak
(49)
=
=τπ
∫
r3 3
3
b
00
(mg/l Oin water)/(mg /l Oin gas
( )
phase)
d/(4 /3)
b
t
b
S
Rcj (50)
3.2 The chemical reactivity of ozone
3.2.1 The chemical properties of ozone
The extensive applications of ozone in wastewater treat-
ment, potable water disinfection, air cleaning, and food
preservation are fundamentally determined by its active
chemical properties including strong oxidative potential
and reaction with a selection of compounds. In general,
ozone is a relatively strong oxidation reagent (Table 3),
due to +4 valence in its special molecular formula
+−
42
2
O(
O)
from the perspective of valence state theory (Zhang 2008).
The selective chemical reactivity of ozone is closely
associated with its molecular and electronic structure.
Ozone molecule (O3) is composed of three oxygen atoms,
in which one atom is the center atom, while other two
atoms are connected to the central one by covalent bond,
forming an isosceles triangle-like (bond angle of center
atom is 116°49′±30′, the length of two O-O bonds are both
1.278±0.003 Å, see Figure 6A) molecular structure via sp2-
hybridized rearrangement (Trambarulo et al. 1953). The
ground state of ozone, for example, can be identified
as a biradical pattern (Figure 6B) with two σ-bonds and
a long or formal π-bond associated with terminal atoms
(Hay etal. 1975, Harcourt etal. 1986). The four closed-shell
resonance structures (Figure 6C) of ozone molecule were
proposed according to its electronic configuration and
spatial model (Langlais etal. 1991, Kalemos and Mavridis
Table 3:The standard redox potential of common oxidizing
species.a
OxidantEθ(V) Redox potential
relative to ozone
Oxidant Eθ (V) Redox potential
relative to ozone
F. . MnO
-. .
SO˙-b .–. .–. ˙OHads
d>. >.
˙OHfree
c.–. .–. ClO. .
O. . ClO-. .
O. . Cl. .
HO. . Br. .
HO˙. . O. .
aMost data were derived from Lin and Yeh (1993).
bData were derived from Cong etal. (2015).
cThe redox potential of ˙OHfree depends on solution pH. In acid
solution, Eθ(˙OH, H+/H2O)=2.4–2.7 V derived from Wang and Liang
(2014), while Eθ(˙OH/OH-)=1.89–2.0 V in alkaline condition referred
from Neta etal. (1988).
dData were derived from Lawless etal. (1991).
2008). Taking into account these resonance structures,
one oxygen atom is electron-deficient exhibiting electro-
philic property, suggesting that ozone can efficiently react
with unsaturated functional groups, amines, sulfides, and
other reductive compounds, whereas one oxygen atom
is electron-rich possessing nucleophilic property, thus
preferring to react with carbonyl, carbon-nitrogen bond
containing substances and strong Brønsted acids (Riebel
etal. 1960, Cocace and Speranza 1994). Therefore, ozone
is a robust reactive reagent that is capable of oxidizing a
large spectrum of pollutants by direct ozonation reactions
or by indirect reactions with oxygen-containing radicals
produced from ozone decomposition.
3.2.2 The reaction mechanism of ozone with inorganic
compounds
Ozonation of inorganic compounds is basically the redox
reactions featured with electron-transfer from reductive
substrates to ozone. Apart from some direct electron-
transfer reactions including ozone reaction with hydrogen
peroxide ions [Eq. (51)], superoxide anion radicals [Eq.
(52)], and metal-organic anion complexes [Eq. (53)] (Zuo
and Hoigné 1992), the ozonation mechanisms of most
inorganic compounds are, however, carried out by the
oxygen-atom transfer reactions (Løgager etal. 1992). The
resulting unstable intermediates can subsequently hydro-
lyze into the oxidized state. Løgager etal. (1992) inspected
the reaction mechanism of Fe2+ with ozone in acid solu-
tion by stopped-flow spectrophotometer. The ferryl ion
(FeO2+), an unstable intermediate compound, produced
from oxygen-atom transfer from ozone to Fe2+ [Eq. (54)]
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
12C. Wei etal.: Ozonation in water treatment
was measured. It was then subjected to decomposition
dominant in Eq. (55) with the excess of Fe2+, whereas
the decay reaction was mainly governed by Eqs. (56–57)
with the excess amount of ozone. By contrast, ferrous
ion was found to be oxidized by ozone directly via elec-
tron transfer, as shown in Eq. (58) (Holgné etal. 1985), as
Fe2+ could initiate chain reactions responsible for ozone
decomposition, which will be explained later. Concerning
cyanide oxidation, it was indicated that ozonation of CN-
was achieved by forming cyanate (CNO-) via oxygen-atom
transfer mechanism (Parga et al. 2003). CNO- was then
easily further converted into CO3
2-, NH4+-N, NO3
- by ozona-
tion or hydrolysis reactions depending on the introduced
ozone concentration and solution pH value.
--
32
32
OHOO
̇Ȯ
H
+→+ (51)
-
32
-
23
OOO
̇̇
O
+→+ (52)
22-32
24 24 3
--
3
Cu CO OC CO
̇
uO
++
…+→… + (53)
++
+→ +
22
32
OFeFeO O (54)
++
++
++
→+
22 3
2
FeOFe2H2Fe
HO
(55)
23-
2
FeOHOFeOHOH
̇
++
+→++ (56)
3
2
-2
FeOOHFeHO
̇
++
+→ + (57)
23-
33
OFeFe
̇
O
++
+→+ (58)
3.2.3 The reaction mechanism of ozone with organic
compounds
The ozonation of organic contaminants is basically limited
by selective oxidation characteristics of ozone with spe-
cific functional groups. In general, ozonation mecha-
nisms of organic compounds only comprise 1,3-dipolar
cycloaddition, electrophilic addition, and nucleophilic
A
C
B
Figure 6:The spatial structure (A), biradical pattern (B), and closed-shell resonance structures (C) of ozone molecule. Original drawing of
(A) was done by us using ChemBioOffice software and (B) was adapted with permission from Hay etal. (1975). Copyright 2008, AIP Publish-
ing LLC., and Harcourt etal. (1986), Copyright 1969, Royal Society of Chemistry. (C) was adapted from Langlais etal. (1991).
Figure 7:The mechanistic model for the ozonation of olefins
(adapted from Beltrán etal. 2007, von Gunten 2003b).
addition (non-aqueous solution), responsible for degrad-
ing olefins, aromatic compounds, and carbon-nitrogen
bond containing compounds, respectively (Riebel et al.
1960, von Sonntag and von Gunten 2012). The 1,3-dipolar
cycloaddition of olefins subjected to ozone attack, for
example, is shown in Figure 7 (von Gunten 2003b). It
involves the generation of highly unstable trioxolanes
[i.e. ozonide (II) or (III)] through Criegee mechanism, after
which carbonyl compound (VI) and hydroxyhydroperox-
ide (V) can be produced from (III) decomposition. The
intermediate (V) will be then decompose into a carbonyl
compound (VI) and hydrogen peroxide (VII) (Dowideit
and von Sonntag 1998). On the other hand, the cycload-
dition for some substituted olefins does not necessarily
result in the production of ozonide, possibly owing to
sterical hindrance effect as revealed by partial oxidation
of carbon-carbon double bond (Bailey and Lane 1967).
The electrophilic addition is the primary principle of
initial reaction of ozone with electron-rich organic com-
pounds, including phenols/phenolates, aromatic rings
substituted with electron-donating groups, and polyaro-
matic compounds (Larcher et al. 2012). The ozonation
of phenol, for example, is carried out preliminarily by
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment13
formation of carbon cation with substitution on ortho- and
para- positions of electron donating -OH group (Beltrán
etal. 2007). The ozone adduct could be stabilized by the
delocalization of electrons in aromatic ring, allowing four
resonance structures as shown in Figure 8A. Then carbon
cation can be transformed into catechol, hydroquinone,
and benzoquinone via SN1 reaction and deprotonation
reaction. The resulting electrophilic substitution interme-
diates are further decomposed through cycloaddition and
hydrolysis, as illustrated in Figure 8B (Eisenhauer 1968).
In addition, the nitrogen-containing compounds (e.g. ali-
phatic amines) can also be ozonated through electrophilic
reaction at nitrogen atom. It has been shown that N-oxides
and hydroxylamines are formed by ozone adduct of amines
at lone electron pair on nitrogen atom followed by oxygen
loss reaction. Amine radical cations may be alternatively
produced from electrophilic ozonation by abstraction
Figure 8:Ozonation mechanism of phenol. (A) The resonance
structures of carbon cations (the case of ortho position adduct, E is
assigned to ozone); (B) the mineralization pathway of phenol (AO is
assigned to abnormal process). [(A) was adapted from Beltrán etal.
2007, (B) was adapted from Eisenhauer 1968].
Figure 9:The schematic mechanisms of nucleophilic reaction of
benzaldehyde (A); alkyl isocyanides (B); and Schiff bases including
N-benzylideneaniline, N-benzylidene-m-nitroaniline, and N-ben-
zylidene-t-butylamine (C) with ozone. [(A) was adapted with permis-
sion from Bailey 1958, Copyright 1958, American Chemical Society,
(B) was adapted with permission from Feuer etal. 1958 in which R is
assigned to alkyl chain, Copyright 1958, American Chemical Society,
(C) was adapted with permission from Riebel etal. 1960, Copyright
1960, American Chemical Society].
of an ozonide radical anion, leading to the generation of
dealkylated amine, ketone, or aldehyde through rearrange-
ment of these cations (von Sonntag and von Gunten 2012).
On the basis of resonance structures, ozone may also
behave as a nucleophilic reagent, being capable of react-
ing with electron-deficient positions of carbonyl groups,
carbon-nitrogen triple or double bonds. As illustrated
in Figure 9A, benzaldehyde can be nucleophilically
ozonated to form benzoic acid by the addition of ozone
on carbon atom of carbonyl groups, followed by loss of
oxygen (Bailey 1958). The carbon atom of carbon-nitrogen
triple bond (e.g. isonitriles) and the carbon atom of car-
bon-nitrogen double bond (e.g. Schiff bases) are primary
reactive sites upon nucleophilic ozonation, as described
in Figure 9B and C, respectively. The nucleophilic reac-
tion of Schiff bases (I) with ozone, for example, may
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
14C. Wei etal.: Ozonation in water treatment
yield unstable intermediate (II), resulting from reaction
at carbon atom of double bond (Riebel etal. 1960). The
produced (II) will be then decompose into oxazirane (III)
and amide (IV) by ring closure and proton shift reaction,
respectively, with the carbon-nitrogen bond undestroyed.
The cleavage of carbon-nitrogen bond accompanied by
loss of oxygen, in contrast, could lead to the formation
of benzaldehyde (V). Regarding the aromatic ring sub-
stituted with electron withdrawing groups, nucleophilic
ozonation was more favorable than electrophilic ozona-
tion due to the decreasing electron density of aromatic
ring (Hong and Zeng 2002).
3.2.4 The reaction mechanisms of catalytic ozonation
Apart from direct reactions of ozone with a selection of com-
pounds, oxidation can also be achieved by indirect reaction
with oxygen-containing radicals (mainly ˙OH) generated
upon homogenous and heterogeneous catalytic decompo-
sition of ozone. The homogenous catalytic ozone decompo-
sition mechanisms in aqueous solution involving SHB [Eqs.
(52, 59–68)] and TFG [Eqs. (51, 69–75)] models were widely
accepted half a century after Weiss (1935) first described the
decomposition mechanism of ozone catalyzed by OH- ion
(Bühler etal. 1984, Staehelin et al. 1984, Tomiyasu etal.
1985). The general features of SHB and TFG models are
chain reactions, which were initiated by OH- and propa-
gated with the involvement of O3˙-, HO2˙, HO3˙. Thus, ozone
decomposition may be significantly promoted in basic solu-
tion (7<pH<10) whereas be less effective in acidic solution
(pH<3). It should be emphasized that some acidic anions
in solution could adversely affect ozone decomposition.
For example, O3 can be depleted by Cl- in acidic solution,
producing Cl2 and ClO3
- without the involvement of chain
reactions responsible for radical generation (Levanov etal.
2012, Levanov etal. 2015). Indeed, it has been reported as
a promoting effect of Cl2 and HOCl working as additional
oxidants on oxalic acid and p-hydroxylbenzoic acid degra-
dation during ozonation (Nowell and Hoigné 1992, Wang
etal. 2016). Although there is no direct evidence supporting
ozone reaction with CO3
2-, the presence of CO3
2- can inhibit
ozone decomposition by the removal of dominant chain
carrier radical, i.e. O3˙- (Nemes etal. 2000).
-
322
-
Chain initiationOOH HO
O7
0 l/(m )
̇̇ ol sk+→
+=
⋅ (59)
5
22
-
̇
Chain propagationHOH
O7
.9 10 l/(mol s)
̇k
+
→+ =× ⋅ (60)
-5
22
HO HO 5 10 l/(mol )
̇̇ sk
++→ =× ⋅ (61)
-1
0
33
HO HO 5.2 10 l/(mol )
̇s
̇k
++→ =× ⋅ (62)
2-
1
33
-
H OHO3.3 10 s
̇̇
k
+
→+ =× (63)
5-1
32
HO OOH1.s 1
̇̇
10k
→+ =× (64)
9-1
34
OOHHȮ2s
̇ 10k
+→ =× (65)
4-1
422
HO HO O2.s
̇̇ 8 10k
→+ =× (66)
9
4422 3
Chain terminationHOHOHO2O510 l/(mol s
̇̇ ̇)k
+→
+=×⋅
(67)
9
4322 32
HO HO HO OO 510 l/(mol
̇s
̇̇ )k+→ ++ =× ⋅
(68)
-
32
-
2
Chain initiation OOHHOO 40 l/(mols)k+→ +=⋅
(69)
--
32 2
Chain propagation O HO OH OOH2030 l/(mol·s)
̇̇ k+→++ =−
(70)
9
32
--
2
OOHHOO 610 /(mol s)
̇̇̇
l
̇
k
+→
+=×⋅
(71)
2-
-8
33
-
Chain termination CO OH HO CO 4.21 0l/
̇
(mol s)
̇
k
+→
+=×⋅
(72)
2--7-
33 33
CO OOCO 610l/(mo )
̇̇
lsk
+→
+=×⋅
(73)
-6
33
-
HCOOHHOHCO 8.510l/(mols)
̇̇
k
+→+=
×⋅
(74)
-1
33
-
H
̇̇
CO HCO500 sk
+
→+ = (75)
22
2a
-
HO HO Hp11.6K
+
→+ = (76)
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment15
Besides the applications of physical fields (e.g. UV
irradiation and ultrasonic vibration) and other soluble
catalysts (e.g. H2O2, Fe2+, Co2+, Mn2+, Co2+, Ni2+, Cu2+) are
the alternative approaches to catalytically decomposed
ozone into radical species in homogenous solution.
Principally, the energy transfer from applied physi-
cal fields to ozone could accelerate its decomposition.
The formation of ˙OH, for example, can be remarkably
strengthened by coupling ultrasonic vibration with
ozone, primarily resulting from additional thermal
decomposition of ozone occurred in cavitation bubbles
(Hou et al. 2013). The decomposition of ozone can be
facilitated by deprotonated H2O2 (HO2
-), producing O3˙-
and HO2˙ [Eqs. (51, 76)] via electron transfer reactions,
which eventually leads to ˙OH formation (Torres-Socías
etal. 2013). The ozone reactions catalyzed by dissolved
transitional metal ions essentially comprise two mecha-
nisms: (1) the reaction catalyzed by free-state ions and
(2) the reaction strengthened by complex state of metal
ions. Basically, direct electron transfer from free-state
transitional metal ions with variable valence to ozone
will favor its decomposition. Ferrous ion, for example,
can be oxidized to its triple valence state by ozone with
the formation of O3˙- [Eq. (58)] (Holgné etal. 1985), which
is readily transformed into ˙OH [Eqs. (62, 64)]. The ˙OH
may also be produced from the hydrolysis of FeO2+ [Eq.
(56)], resulting from oxygen-atom transfer reaction [Eq.
(54)]. The oxidized Fe3+ can be then reduced to its diva-
lent state, as shown in Eq. (77), in which HO2˙ is produced
from Eqs. (59, 65, 66, 71) (Wilde etal. 2014). The coordina-
tion of metal ions with α-carbonyl or α-hydroxy contain-
ing carboxylate anions (e.g. pyruvic acid, oxalic acid,
citric acid) could, on the other hand, facilitate the cata-
lytic decomposition of ozone. This is owing to the high
electron density (donated by ligand) on the coordinated
metal site, being more favorable for electron abstraction
by ozone and leading to O3˙- formation (Zhang and Croué
2014c). Beltrán etal. (2003) studied the catalytic influ-
ence of homogenous Co2+ on ozonation of oxalic acid.
The results showed that CoC2O4 was formed via bidentate
complexation, increasing the reactivity of CoC2O4 with
ozone attributed to partial donation of electron density
from C2O4
2- to Co2+. The unstable intermediate (CoC2O4)+
could be produced [Eq. (78)] upon ozone reaction. After
that, Co2+ was regenerated by electron extraction from
carboxylic acid ligand to Co3+ [Eq. (79)], giving rise to the
appearance of superoxide ion radical and carbon dioxide
through decarboxylation reaction, as shown in Eq. (80)
(Zuo and Hoigné 1992, Pines and Reckhow 2002). Simul-
taneously, the generation of ˙OH was enhanced from O3˙-
and O2˙- via Eqs. (62, 64) and Eq. (52), respectively.
32
22
Fe HO FH
̇
eO
++
+
+→++ (77)
24
-
32
43
CoCO O(Co
̇
CO)O
+
+→ + (78)
2
2
-
42
4
CoCO C(
̇
O)oC
++
→+ (79)
24
22
2
--
CO O2CO
̇̇
O
+→ + (80)
22-32- -
24
3243
̇
Cu CO OCuCOO
++
≡+→≡ + (81)
Transitional metal oxides, reactive metal supported on
metal oxides, minerals, clays, carbon-based materials,
and ceramic honeycomb have been applied to assist
in the degradation of various organic compounds by
ozonation (Zhao et al. 2009a, Nawrocki 2013) and to
investigate the catalytic ozonation mechanisms (Ikhlaq
etal. 2013, Bing et al. 2015). The latest investigations
of various ozonation catalysts are listed in Table 4.
The mechanisms of heterogeneous catalytic ozonation
include (1) ˙OH generation from reaction of ozone with
surface hydroxyl groups, (2) ˙OH generation from reac-
tion of ozone with metal ion site with variable valence,
and (3) elimination of ozone recalcitrant compounds
via intermediate metal-organic complexes. The reac-
tion mechanism of ozone decomposition at surface
hydroxyl group sites depends on state of surface charge
(Zhang et al. 2015). The surface hydroxyl groups are
positively charged at solution pH below the point of
zero charge (pHPZC) of catalysts, promoting decomposi-
tion of ozone driven by electrostatic force and hydro-
gen bond between ozone and positively charged surface
(Zhao etal. 2009b). With the increase of solution pH,
surface hydroxyl groups are neutrally or negatively
charged at solution pH equal or above pHPZC, favor-
ing interaction of ozone with catalyst surface due to
the electrophilic nature of ozone (Jung etal. 2007). A
positive linear correlation between density of surface
hydroxyl groups and catalytic performance of catalyst,
for example, was established using surface properties
measurements (Zhao et al. 2015). In addition, metal
ion sites with variable valence present on surface of
solid catalysts are also reactive sites for ˙OH generation.
CoOx/ZrO, for instance, was confirmed to be an efficient
catalyst for ozone decomposition due to the oxidation
of surface≡Co2+ by O3, resulting in O3˙- and therefore ˙OH,
as shown in Eqs. (62, 64) (Hu etal. 2008). The electron
transfer from surface metal complexes to ozone can
accelerate its decomposition. It was observed that in
the presence of CuO and oxalate, the coordination of
Cu2+ with organic ligand could reduce the redox poten-
tial of Cu3+/Cu2+ couple (Eθ=2.3 V), making Eq. (81) pos-
sible, which would be favorable for electron extraction
by ozone (Zhang and Croué 2014c).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
16C. Wei etal.: Ozonation in water treatment
Table 4:The latest investigations for the catalytic ozonation of various contaminants.
Pollutant Catalyst Preparation methods of
the catalysts
Catalyst
dosage
Ozone dosage pHbResearch remarks Reference
Pharmaceuticals γ-AlOCommercially available . g/l . ml/min , ., ˙OH mediated reaction Ikhlaq etal.
Ibuprofen FeO/AlO@
SBA-
Incipient wetness
impregnation
. g/l mg/l
(gaseous)
Ozone decomposed into oxygen atom at Al+
sites, oxygen atom transformed into ˙OH and
O˙- at Fe+ sites
Bing etal.
Phenacetin CuFeOCo-precipitation and
calcination
g/l .–. mg/l
(aqueous)
.Ozone efficiently broke down the initial
model compound structure, ˙OH improved the
mineralization of intermediates
Qi etal.
Phenol α-, β-, γ-MnOHydrothermal g/l . mg/min –Particular Mn-O bonds reacted with ozone to
generate oxygen species
Dong etal.
Phenol ZnAlOHydrothermala g/l . mg/min .±.Surface hydroxyl groups and chemisorbed
water on catalyst were catalytic active sites
Zhao etal.
para-chlorobenzoic acidPeroxymonosulfate
(PMS)c
Commercially available . m . m The concomitant production of ˙OH and SO˙-
arose from synergistic effect of O/PMS
Cong etal.
Several emerging
contaminantsd
TiOCommercially available . g/l mg/l
(gaseous)
The combination of photocatalytic
oxidation and ozonation enhanced ozone
decomposition and ˙OH generation
Quiñones etal.
para-chlorobenzoic acidMultiwalled carbon
nanotubes
Commercially available mg/l μeStrong correlation between RCT
f values and
surface oxygen concentrations was found
Oulton etal.
Oxalic acid ElectrongCommercially available – mg/l
(gaseous)
Electro-reduction of O to ˙OH at the cathode,
and O decomposition to ˙OH at high local pH
near cathode
Wang etal.
Indigo Carboxylated
carbon nanotubes
Chemical vapor deposition
and acidification
mg/l . mg/l
(gaseous)
.Functional -COOH groups directly reacted with
amino groups of indigo.
Qu etal.
aZnAl2O4 was synthesized by a one-step hydrothermal method, followed by calcination at different temperature.
bThe pH is referred to as initial pH value without being specified.
cThe chemical formula of Peroxymonosulfate is 2KHSO5·KHSO4·K2SO4.
dSix commonly detected emerging contaminants including acetaminophen, antipyrine, bisphenol A, caffeine, metoprolol and testosterone were degraded by photocatalytic ozonation.
eThe pH value was buffered by 5 m phosphate.
fThe RCT value was defined as total exposure to ˙OH relative to total O3 exposure during ozonation.
gThe electron for catalytic ozone decomposition was provided by electrolysis of cathode (Pt or boron-doped diamond electrode).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment17
3.3 Summary
Ozone exhibits the characteristics of higher solubility
relative to oxygen and active chemical reactivity asso-
ciated with its resonance structures. It mainly involves
two mechanisms concerning the removal of inorganic
and organic compounds. The first one is direct reaction
with molecular ozone proceeding via electron transfer or
oxygen-atom transfer pathways for ozonation of inorgan-
ics. The fundamental pathways for direct ozonation with
organics are the cycloaddition, electrophilic addition, and
nucleophilic addition reactions. The second one is indi-
rect oxidation carried out with oxygen-containing radicals
produced from catalytic decomposition of ozone. Owing
to its special physicochemical properties, ozone has been
potentially applied in water and wastewater treatment.
Indeed, it suffered from some limitations, such as insuf-
ficient oxidation capability, scavenging effect of inorganic
carbon, and DOM on radical-mediated reactions. All of
these definitely need to be carefully investigated in future
studies.
4 The application of ozone in water
and wastewater treatment
On account of its convenient generation and strong oxi-
dation ability, ozone is extensively applied in chemical
products manufacturing, food processing, aquaculture,
health-medical care, and atmospheric and aqueous pollu-
tion control industries. As a broad-spectrum disinfectant,
ozone is able to inactivate micro-organisms and decompose
precursors of chlorine disinfection by-products (DBPs)
with concomitant removal of odor and color in drinking
water treatment. The bio-refractory organic compounds
and reductive inorganics residual in biologically treated
industrial wastewater can be further oxidized by ozone. In
this review, the applications of ozone technology in potable
water disinfection and advanced treatment of industrial
wastewater are analyzed. The performance of ozonation
reactor in which ozone reaction occurs is assessed. The
energy consumptions in terms of ozone generation and
contaminants degradation are finally evaluated.
4.1 Ozone disinfection
Micro-organisms such as bacteria, fungi, viruses, proto-
zoa, bacterial, and fungal spores in water can be effec-
tively inactivated by ozone for disinfection purposes. The
overall disinfection mechanism is realized as cell lysis
results from reactions with ozone molecule or oxygen-
containing radicals (e.g. ˙OH, O2˙-, HO2˙) (Hunt and Marinas
1997). Generally, microbial inactivation is induced by
ozone reaction with several cellular constituents includ-
ing proteins, unsaturated lipids and respiratory enzymes
in cell membranes, peptidoglycans in cell envelopes,
and nucleic acids in cytoplasm (Khadre etal. 2001). The
destruction of lipoprotein on outer shell and lipopolysac-
charide on inner cell wall, for example, were realized by
the oxidation of double bonds in unsaturated lipids and
sulfhydryl groups in enzymes with ozone (Chang 1971).
This will consequently lead to the reduction of cell perme-
ability, eventually causing rapid cell death. The complete
inactivation of microbial cell by ozone should be even
further achieved through the damage of genetic genes,
parasitic bacteria, phages, and mycoplasma residual in
dead cell. It was indicated that the reaction of nucleic
acids inside cell with ozone was carried out by opening
the circular plasmid DNA, producing single- or double-
strand breaks in plasmid DNA and ultimately resulting
in the decrease of transcription activity (Roy etal. 1981).
The clarity of the above basic principles will underpin
the development and application of ozone disinfection in
water treatment. The recent research activities concerning
ozone disinfection are summarized in Table 5.
4.1.1 Non-catalytic ozonation for disinfection
It is well established that direct ozone disinfection mainly
focused on inactivation of micro-organisms residual in
water and elimination of DBPs. The inactivation of two
antibiotic resistance genes (ARGs) in municipal waste-
water by ozone or UV disinfection was compared (Zhuang
etal. 2015). The results showed that although ozone dis-
infection (ozonation dose of 177.6 mg/l for 1.68–2.55 log
reductions of ARGs) achieved less inactivation of ARGs
than did UV irradiation (UV dose of 12,477 mJ/cm2 for
2.48–2.74 log reductions of ARGs), the 16S rDNA was more
efficiently destroyed by ozonation. Hiragaki etal. (2015)
applied ozone foam to inactivate Pseudomonas fluores-
cens with its initial number of more than 108, suggesting
that survival rate log (N/N0) decreased obviously along the
treatment time. Zimmermann etal. (2011) assessed ozone
disinfection for full-scale municipal wastewater treat-
ment, indicating that disinfection capacity was 1–4.5log
units in terms of total cell counts (TCC) and 0.5–2.5 log
units for Escherichia coli.
Agbaba et al. (2015) elucidated the influence of
applied ozonation on natural organic matter (NOM)
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
18C. Wei etal.: Ozonation in water treatment
Table 5:The recent publications in ozone disinfection.
Ozone oxidation Wastewater quality Reaction conditions Main results Reference
Ozonation integrated
with ceramic
ultrafiltration
DOC: .–. mg/l, UV:
.–. m-, Br-: . mg/l, pH:
.–.
Ozone dose: mg/l,
Single membrane sheet:
××mm with total
filtration m
The removal of organic matter was significantly
improved with ozonation in advance, and a close
linear relationship of DOC with the formation
potential of DBPs was established
Fan etal.
Ozonation DOC: .–. mg/l, pH: .–
., UV: .–. cm-,
alkalinity: –mg CaCO/l
Ozone doses: .–.mg O/mg
DOC, ozone delivery rate: l/h
Increasing ozone dose (.–.mg O/mg DOC)
generally led to reductions in DOC (–%) and
trihalomethane formation potential (–%)
Agbaba etal.
Ozonation catalyzed
by TiO
DOC: .±. mg/l, pH: .±.,
total alkalinity: ±mg CaCO/l
Ozone doses: .–.mg O/mg
DOC, TiO concentration: . mg/l
The application of TiO enabled an improved
ozonation in terms of trihalomethane (THM)
precursor content removal (up to %)
Molnar etal.
Flocculation-
flotation followed by
ozonation
COD: mg/l, pH: ., Escherichia
coli: CFU ml-, turbidity:
NTU
Ozone doses: g/h, average
diameter of flocs: –μm,
rise rate of flocs: – m/h
The integrated processes resulted in disinfected
(Escherichia coli <. CFU ml-) and clarified
water ( NTU)
Etchepare etal.
Ozonation/
ozonation-chlorine
Equivalent concentration for amino
acids: – μg N l-, pH:
Ozone doses: mg/l, chlorine
doses: mol/mol precursor
The increases in the formation of chloropicrin
from ozonation-chlorination relative to
chlorination alone varied from % for
-aminophenol to % for ala-ala for the four
amine surrogates
Bond etal.
Ozonation with
magnetic ion
exchange resin
TOC: .–. mg/l, UV: .–
. cm-, bromide: – μg/l
Resin doses: .–. ml/l, alum
flocs doses: – mg/l, ozone
doses: mg O/mg TOC
The amount of bromate produced by ozonation of
resin-treated waters was similar to or less than
that of raw water and alum-treated water
Kingsbury and Singer
Ozonation DOC: mg/l, bromide concentration:
μg/l, pH: .±.
Dissolved ozone: mg/l, water
bath: ±°C
The use of ozone as a primary disinfectant may
cause a shift to more brominated DBPs during
subsequent chlorination
Mao etal.
Ozonation DOC: mg/l, bromide concentration:
– μg/l, pH: .–.
Ozone doses: –mg O/mg
DOC, water bath: ±.°C
The concentration of BrO
- steadily increased
with increasing O dosage at high Br-
concentration (> μg/l)
Lin etal. c
Ozonation Initial concentrations of
β-estradiol and estrone: ng/l
and μg/l, turbidity: .±. NTU
Ozone doses: .– mg/l, water
bath: ±°C, pH: ±.
Both β-estradiol and estrone have been
found to form two main by-products after ozone
disinfection of surface water, following the same
reaction pathways
Pereira Rde etal.
Ozonation TOC: .–. mg/l, UV:
.–. cm-, SUVA: .–
. l/mg m, pH: –
Ozone doses: .–.mg/l,
NaOCl:TOC= (wt),
NHCl:TOC=(wt)
Ozonation reduced the formation of HANs from
EOM, increased the yields of HANs from IOM
Zhu etal.
Ozonation, or UV
irradiation
COD: – mg/l, alkalinity:
– mg/l, original gene copies:
.–. copies/ml
UV irradiation: –,
mJ/cm, UV wave length:
nm, ozone dose: . mg/l
Inactivation of antibiotic resistance genes
underwent by increased doses of disinfectors,
and S rDNA was more efficiently removed by
ozonation
Zhuang etal.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment19
Ozone oxidation Wastewater quality Reaction conditions Main results Reference
Ozonation DOC: .–. mg/l, pH: .±. Ozone doses: .–. g O/g
DOC
Ozonation decreased TCC by –. log units, not
consistently correlating with ozone doses. E. coli
concentrations reduction only partially correlated
with ozone exposure
Zimmermann etal.
Ozonation/ BAC
filtration
DOC: . mg/l, dissolved organic
nitrogen (DON): . mg/l
Dissolved ozone doses:
.–.mg/l, density of BAC:
g/l
Abrupt termination of ozonation resulted in some
N-DBP precursors and then substantial formation
of N-DBP during chlorination
Chu etal.
Ozonation catalyzed
by Fe-Mn oxide or
TiO/α-AlO
DOC: .–. mg/l, UV:
.–. cm-, pH: .–.
Ozone dose: . mg/l, ozone flow
rate: ml/min, catalyst doses:
.–. g/l
The use of both catalysts in catalytic ozonation
effectively removed the precursors of DBPs,
resulting in the formation of fewer THMs and nine
haloacetic acids (HAA).
Chen etal. b
Table 5(continued)
fractionation and DBPs formation. The results indicated
that the reactivity of all individual NOM fractions towards
trihalomethane formation decreased by 47–69% relative
to raw waters when subjected to ozone oxidation (0.8mg
O3/mg dissolved organic carbon [DOC]), which is con-
sistent with findings from Chu etal. (2012). In contrast,
the ozonation treatment of nitrogen containing organic
compounds could increase the formation potential of
DBPs. It was reported that the disinfection of alanylala-
nine with ozone prior to chlorination could accelerate the
formation of chloropicrin (Bond etal. 2014). The authors
suggested that ozone is more effective than chlorine in
mediating an oxidation step in chloropicrin formation,
most plausibly involving conversion of an amine group
to a nitro group. Similarly, Zhu et al. (2015) indicated
that haloacetonitriles (HANs) formation from extracel-
lular organic matter (EOM) on the course of ozonation
decreased from 0.73 to 0.35μg/mg C, whereas HAN yields
from intracellular organic matter (IOM) raised by 21.2%.
This was owing to the lower nitrogen-organic concentra-
tion in EOM than that in IOM, as ozone disinfection might
transform amine compounds to nitrous compounds, being
the precursors of HAN. Mao etal. (2014) also reported a
similar result concerning the increase of formation poten-
tial of chloral hydrate and trichloro nitromethane with
rising ozone doses up to 6mg/l. Moreover, the ozone dis-
infection of emerging estrogens bearing surface water will
lead to the formation of DBPs including 17 β-estradiol and
estrone (Pereira Rde etal. 2011). The authors conducted
experiments at two different concentrations of estrogens
in water (100 ng/l and 100 μg/l) and at varying ozone
dosages (0–30 mg/l). Results showed that these DBPs have
been found to be formed at both high and low concentra-
tions of estrogens and to be persistent even after exposure
to high ozone dosages.
The ozone disinfection of Br- containing water aroused
wide concern due to a potential carcinogen DBP, BrO3
-,
recognized by the World Health Organization (WHO) and
United States Environmental Protection Agency (USEPA)
(USEPA 1998, WHO 2011). It was established that BrO3
- can
be produced from the reaction of ozone with OBr-, result-
ing from ozonation of Br- (Pinkernell and von Gunten
2001). Mao etal. (2014) found that bromate incorporation
factor values of trihalometanes (THMs), trihaloacetic acid
(THAA), dihaloacetic acid (DHAA), and dihaloacetonitrile
(DHAN) increased from 0.62, 0.37, 0.45, and 0.39 without
ozone exposure to 0.89, 0.65, 0.62, and 0.89 at O3 dose
of 6 mg/l, respectively. The production of bromate could
be significantly influenced by its precursor and trans-
ferred ozone doses. Lin etal. (2014c) demonstrated that,
for example, decreasing initial Br- concentration was an
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
20C. Wei etal.: Ozonation in water treatment
effective approach in controlling the formation of BrO3
-.
When Br- concentration was lower than 100 μg/l, while
keeping the ratio of O3 dosage equal to DOC, the BrO3
- pro-
duction was effectively suppressed.
4.1.2 Catalytic ozonation for disinfection
The application of catalysts on the course of ozonation
will generate more reactive and less selective radical
species, which are expected to accelerate the elimination
of DBP precursors as well as residual DOC. The effect of
Fe-Mn oxide and TiO2/α-Al2O3 employed as ozonation cat-
alysts on the formation of DBPs was studied (Chen etal.
2014b). Results pointed out that ozone reactions catalyzed
by Fe-Mn oxide and TiO2/α-Al2O3 effectively removed the
precursors of DBPs, improving 77.5% and 30% of THMs
removal capability compared with non-catalytic ozona-
tion, respectively. Molnar etal. (2012) evaluated the perfor-
mance of catalytic ozonation (O3/TiO2) and non-catalytic
ozonation in the content and structural change of THM
and HAN precursors in groundwater. The results indicated
that TiO2-catalyzed ozonation (18% DOC removal) favored
more effective reduction of NOM in comparison with non-
catalytic ozonation (6% DOC removal). On the other hand,
the structural changes of NOM by both treatments led to
a 70% increased proportion of hydrophilic fraction (HI),
which were the most reactive THM and HAN precursors.
4.1.3 Physical separation techniques assisted ozone
disinfection
In addition to combining catalysts with ozonation for the
purpose of removing DBPs and their precursors, coupling
various separation technologies with ozone oxidation has
been suggested as promising alternatives. Fan etal. (2015)
examined the degradation of DBP precursors by integrat-
ing ozonation with ceramic ultrafiltration from micro-
polluted surface water. The integrated process enabled
73% of DOC removal, in which the reduction of 77% of tri-
halomethane precursor, 76% of haloacetic acid precursor,
83% of trichloracetic aldehyde precursor, 77% of dichloro-
acetonitrile precursor, 51% of trichloroacetonitrile precur-
sor, 96% of 1,1,1-trichloroacetone precursor, and 63% of
trichloronitromethane precursor can be achieved. The per-
formance of magnetic ion exchange (MIEX) resin followed
by ozonation in controlling bromate and chlorinated DBPs
formation was investigated (Kingsbury and Singer 2013).
Results demonstrated that MIEX resin removed 39–85%
of trihalomethane formation potential (THMFP), while
35–45% reduction of THMFP was achieved by ozonation.
This suggested that MIEX resin can be a more promis-
ing pre-treatment for ozone disinfection, as it achieves
superior THM and bromate precursors removal. Chu etal.
(2015) evaluated the N-DBP formation during ozonation
(continuously bubbling and terminated bubbling) cou-
pling with biological activated carbon (BAC) filtration. It
was indicated that more N-DBP precursors passed into
post-BAC water when ozonation was terminated, resulting
in greater formation of N-DBP when the water was sub-
sequently chlorinated, compared to a parallel BAC filter
under continuously bubbling ozonation. This resulted
from the generation of new N-DBP precursors such as
nitrogen containing soluble microbial products (SMPs),
which were likely produced from endogenous respiration
by micro-organisms when ozone bubbling was terminated
(Schiener etal. 1998, Chu etal. 2010).
In summary, inactivation of micro-organisms and
inhibition of conventional chlorinated DBPs can be effec-
tively achieved by ozone disinfection. Nevertheless, this
technology suffers from several limitations as an alterna-
tive approach to chlorine disinfection. Firstly, ozone reacts
with NOMs residual in water to produce low-molecular
weight oxygenated by-products, which are generally more
biodegradable and ozone recalcitrant. The biological
regrowth in the distribution system may be, however, stim-
ulated by these intermediates. Secondly, ozone is unstable
in water with its half-life time <1h under common condi-
tions of drinking water supplement, resulting in insuffi-
cient continuous disinfection functionality (Glaze 1987).
Thirdly, the ozonated by-products including bromate as
well as N-DBPs (e.g. N-nitrosodimethylamine, chloro-
picrin and HANs) have been recently identified during
ozone disinfection (Schwarzenbach etal. 2006, Parrino
etal. 2014, Marti etal. 2015). Moreover, ozonation of some
nitrogen-containing organic compounds will, however,
increase the formation potential of DBPs during following
chlorination. In order to overcome these deficiencies, the
pre-treatments responsible for removing DBPs precursors
such as Br- and amine group containing organics will be of
necessity for ozone disinfection.
4.2 Ozonation of cyanide containing
wastewater
Cyanide in wastewater is an important issue because of its
toxic effect, which normally existed in the form of hydro-
gen cyanide, anion, and various cyanide complexes. The
free cyanide ions, including cyanide anion and hydro-
gen cyanide either in gaseous or aqueous phase, are the
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment21
most poisonous forms (Dash etal. 2009). The ozonation
of cyanide in various sources is promising due to the
intense reactivity of cyanide with ozone and complete
elimination of cyanide without undesirable by-products.
The preliminary product of cyanide ozonation is cyanate,
which can be further degraded via hydrolysis or ozona-
tion proceeding, however, at relatively slower reaction
rate than the oxidation of cyanide (Mert etal. 2014). The
oxidation of cyanide by ˙OH produced upon ozone decom-
position, comparatively, is carried out by producing CNO-
as the less hazardous intermediate through two pathways
[Eq. (82) and Eqs. (83–85)] (Gurol and Bremen 1985a).
Although hydrogen cyanide is less reactive with ozone, it
can be readily degraded by ˙OH-mediated reactions [Eqs.
(86–87)]. The research activities in cyanide abatement by
means of catalytic and non-catalytic ozonation are con-
cluded in Table 6.
--
2
CN OH CNOHO
̇̇
+→ + (82)
--
CN OH CN OH
̇̇
+→+
(83)
2
2 CN (CN)
̇→
(84)
+→++
---
22
CN 2OHCNO CN(H)O
(85)
2
HCNOHHCNO
̇̇
HO+→ +
(86)
+
↔+
-
HCNO HCNO
(87)
2-
-
2
-
Cu(CN) OH Cu 2CNOH
+
+→
++
̇ (88)
4.2.1 Non-catalytic ozonation for cyanide removal
The non-catalytic ozonation of cyanide bearing waste-
water is usually used in alkaline solutions, in which the
Table 6:The ozonation of cyanide containing wastewater.
Ozonation
technology
Solution system Ozone dosage Solution pHResearch remarks Reference
O/ CAC Synthetic solution –. mg/l .CN- first adsorbed on CAC surface
reaching adsorption equilibrium
condition, then oxidation of CN- to
CNO- occurred
Sánchez-Castillo
etal.
Ozonation and
BAF
Electroplating
wastewater
– mg/l .–.Ozonation pre-treatment improved
the wastewater biodegradability
Cui etal.
O/activated
carbon
Mining effluent mg/min .Activated carbon and O
exhibited synergetic effect on the
decomposition of cyanide
Sánchez-Castillo
etal.
O/HO/UV Jewellery producing
wastewater
––The combination of catalytic
ozonation and photolysis
promoted radical generation
Mert etal.
O/HOAutomobile industry
wastewater
– mg/l –Deprotonated HO could
effectively decompose ozone
into ˙OH at basic condition,
accelerating cyanide removal
Mudliar etal.
O/HOSynthetic solution .–. mg/l –Indirect oxidation of CN- was more
effective than direct ozonation
Kepa etal.
OCassava starch
solutions
.– g/ha–Ozonation of cyanide was limited
by the liquid phase volumetric
mass transfer coefficient of ozone
Somboonchai
etal.
OSynthetic solution .–. mol/molbThe cyanide oxidation depended
mainly on the specific ozone dose
Barriga-Ordonez
etal.
OMining wastewater .–. g/min .Intermediate CNO- was less
reactive than CN- against ozone
Parga etal.
O/TiO/UV Synthetic solution cm/minc.Decomposition and adsorption
both accounted for CN- removal
Hernández-Alonso
etal.
OSynthetic solution . g/min .The reaction stoichiometric ratio
of CN-:CNO-:O was ::.
Carrillo-Pedroza
etal.
aThe ozone dosage was referred to ozone producing ability of an ozone generator.
bThe ozone dosage was the ratio of mol O3 feed per mol CN-.
cThe ozone dosage was a final ozone molar fraction in the gas phase of about 1550 ppmv.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
22C. Wei etal.: Ozonation in water treatment
oxidation ability of ozone can be enhanced by OH- ion. A
synthetic alkaline solution containing CN- was ozonated
in a counter-current bubble column, with special empha-
sis on specific ozone dose requirement (Barriga-Ordonez
etal. 2006). The oxidation efficiency mainly depends on
specific ozone dose, with 90% CN- removed under specific
ozone dose of 1.2 mol O3/mol CN-, which was suggested to
be the least specific ozone requirement for ozonation of
cyanide. This significant ratio of ozone with cyanide was
also reported by Gurol and Bremen (1985a). By contrast,
Zeevalkink etal. (1980) and Carrillo-Pedroza etal. (2000)
revealed that the stoichiometric ratio of cyanide ozone
reaction was equal to 1. The discrepancy may resulted
from the presence of other ozone reactive compounds and
different solution pH under which the experiments were
conducted.
In case of cyanide containing industrial wastewater,
the ozonation mechanism of cyanide normally presented
in the form of metal ion-complex is more complicated than
that of free cyanide. A mechanistic study for describing
the degradation of free and copper-complexed cyanide
in a completely mixed ozone contactor was developed
(Kumar and Bose 2005). The authors proposed that copper
cyanide complexes could be ruptured due to interaction
with hydroxyl radicals [Eqs. (88)], without proper evi-
dence supporting the initial reaction of copper cyanide
complexes with ozone molecule. It was also confirmed
that the overall degradation rate of copper-complexed
cyanide was slower than that of free cyanide under identi-
cal conditions, as the breakdown of complexes consumed
extra ˙OH, which was generated from ozone decomposi-
tion. The produced copper presented in cuprous form was
oxidized to cupric form and subsequently precipitated as
Cu(OH)2 under pH value as high as 12.8. This is, however,
contradictory to the results from Gurol etal. (1985b), in
which the enhanced rate of copper cyanide degradation
as compared to that of free cyanide was due to the cata-
lytic activity of free Cu(I)/Cu(II) towards ozone decompo-
sition under pH value as high as 11.5.
4.2.2 Ozonation associated with other technologies for
cyanide removal
The combination of ozone oxidation with biological treat-
ment process has gained significant concerns in degrading
toxic and biological inert wastewater, as the biodegrada-
bility of wastewater could be improved by ozonation. The
combination of ozone reaction with biological aerated
filter (BAF) in treating cyanide containing electroplating
wastewater was employed (Cui et al. 2014). Although the
authors found the increase of m(O3):m(CN-) being benefi-
cial in reducing effluent CN- concentrations (nearly com-
plete removal), the non-catalytic ozonation remained
problematic due to high dosage of NaOH required for
achieving optimal pH condition. Aiming at this obstacle,
the ozone oxidation associated with BAF (BAF1-O3-BAF2)
was proposed for cyanide abatement, removing 99.7%
CN-, 81.7% chemical oxygen demand (COD) under rela-
tively moderate reaction conditions.
The applications of catalyst-assisted ozonation can
also be used to achieve desirable cyanide removal under
neutral conditions. The oxidation processes compris-
ing O3, O3/UV, and O3/UV/H2O2 were employed to treat
cyanide in jewellery manufacturing wastewater (Mert
etal. 2014). It was indicated that total cyanide removal
by O3 reached 86% at pH 12, while total cyanide removal
by O3/UV/H2O2 increased significantly to 99% even at pH
as lower as 10. Ozonation catalyzed by hydrogen perox-
ide was used to destruct cyanide containing automobile
industry wastewater and synthetic wastewater (Mudliar
et al. 2009). Optimized loading of 116.8×103 mg/l H2O2
and 5.0 mg/l O3 was developed, reducing CN- concen-
tration from 250 mg/l below 0.02 mg/l. The results also
indicated that CN- destruction was more efficient in
automobile industry wastewater than that in synthetic
wastewater, ascribed from abundant Fe2+ (212.84±13.8
mg/l) residual in industrial wastewater, which could
potentially accelerate ozone oxidation in homogenous
solution. The activated carbon synthesized by coconut
shell (CAC) was employed to enhance the removal of
cyanide by ozone (Sánchez-Castillo et al. 2015). Under
the optimum reaction conditions, 1200 mg/ml of cyanide
was totally eliminated after 3h by using 1 g of CAC and
2mg O3/min. Importantly, it was clearly found based on
the results that before the oxidation of CN- to CNO-, the
CN- concentration predominantly decreased to adsorp-
tion equilibrium condition on CAC surface. The reason
was that the basic typical sites on CAC surface, includ-
ing quinone and pyrone, could be oxidized by ozone,
generating positively charged sites. In this scenario, the
ion-exchange type of CN- adsorption may be extended by
electrostatic adsorption.
In summary, free cyanide ions can be effectively
abated upon ozone reaction, occurring primarily by oxy-
gen-transfer reactions. The decomplexed reaction driven
by ˙OH will be the prerequisite step for abatement of
complex state cyanide. The promoting effect of produced
metal ions on cyanide ozonation in strong alkaline solu-
tion, however, remains unclear.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment23
4.3 Ozonation of coking wastewater
The coking wastewater has gained immense attention due
to its complex composition and highly toxic feature. After
biological treatment, there are still phenolic, benzene
series, polycyclic aromatic hydrocarbons (PAHs), and
nitrogen-containing heterocyclic compounds residual
in coking wastewater effluent. These non-biodegrada-
ble organic contaminants in coking wastewater can be
effectively eliminated by ozone-based technologies, as
shown in Table 7. It can be found that the most concerned
research interests lie in the reduction of potential risk of
coking wastewater effluent and the improvement of oxida-
tion capability of ozone by coupling with active catalysts.
The toxicological effect of hazardous compounds in
coking wastewater subjected to anaerobic/aerobic/ozona-
tion process on the development of maize embryos and
the activity of amylase and protease in maize seeds was
investigated (Wei etal. 2012). Obviously, after ozone oxi-
dation, the binding ability of poisonous organics in coking
wastewater with α-amylase was inhibited. This result may
be related to the degradation or structural change of toxic
compounds including quinolines, indoles, and PAHs.
Moreover, Chang etal. (2008) evaluated the contribution
of ozone pre-treatment of coking wastewater to the toxicity
reduction, demonstrating that toxic substances compris-
ing cyanide, thiocyanate, and phenol can be destroyed
by ozone and converted to less toxic or non-toxic sub-
stances. The toxicity inhibition of coking wastewater on
aerobic microorganisms after ozonation was lower than
20%. However, the authors (Chang etal. 2008) reported
that biodegradability of wastewater was not enhanced as
evidenced by biochemical oxygen demand (BOD)5/COD
ratio, decreasing from 0.52 to about 0.1, which is not con-
sistent with other studies (Bijan and Mohseni 2005, Cui
etal. 2014).
It is generally believed that the application of non-
catalytic ozonation for wastewater decontamination is
adversely affected by the insufficient oxidation ability of
ozone, making the association of ozone oxidation with
other technologies remain as fundamental interest. The
ozonation of biologically treated coking wastewater cata-
lyzed by ZnFe2O4 was conducted to elucidate the organic
compounds transformation (Zhang et al. 2015). On the
basis of ultraviolet absorption spectroscopy analysis, the
absorbance in the range of 250–300 nm was evidently
Table 7:Catalytic and non-catalytic ozonation of coking wastewater.
Wastewater Ozonation Ozone reactor Research remarks Reference
Coking wastewateraO/ZnFeOThree-necked flask The ZnFeO can accelerate the generation of
radicals upon ozone decomposition, and single
ring aromatic compounds as well as PAHs can be
effectively degraded
Zhang etal.
Simulated coking
wastewater
O/O-
Fenton
Rotating packed bed The BOD/COD value of simulated coking
wastewater treated by O/Fenton reached . and
was % higher than that obtained in O process
Wei etal.
Coking wastewateraO/UV Pilot-scale FBR The ozonation of industrial wastewater highly
depended on the reductive activity sequence of
pollutants and mass transfer of ozone in FBR
Chen etal.
Coking wastewateraO/UV Pilot-scale FBR FBR accelerated the mass transfer of ozone from
gaseous to aqueous phase, and therefore the
removal of PAHs was increased
Lin etal. a
Coking wastewaterbOCylindrical column Under the optimized conditions of ozone dosage
.mg O/mg COD, pH ., ozone combined with
BAF can effectively abate COD, NH+-N, UV
Zhang etal. b
Coking wastewatercOAirtight Pyrex columnOrganic matter and cyanide cannot be completely
degraded, due to the inadequate oxidation ability
of ozone to remove ozonated by products
Chang etal.
Coking wastewaterdOCylindrical column Ozone can initially decompose refractory organics
such as quinolines, indoles, and PAHs, although
derivatives of pyridines and PAHs still remained.
Wei etal.
aThe wastewater was obtained from anaerobic-aerobic-aerobic FBR, Song Shan Coking Plant, Guangdong, China.
bThe wastewater was obtained from anaerobic-anoxic-oxic process, Magang Steel Factory in Ma’anshan, China.
cThe wastewater effluent studied was obtained from a local coke plant.
dThe effluent wastewater sample was obtained from the biofilter underwent anaerobic/aerobic treatment.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
24C. Wei etal.: Ozonation in water treatment
lower for coking wastewater subjected to catalytic ozona-
tion than that treated by non-catalytic ozonation. It was
indicated that the degradation of aromatic organic com-
pounds should be more efficient by means of catalytic
ozonation than that by non-catalytic ozonation. Wei etal.
(2015) combined Fenton reagent with ozone in treating
simulated coking wastewater in a rotating packed bed,
with special emphasis on pollutants degradation and
corresponding reaction pathways. The results suggested
that removal efficiency of phenol, aniline, quinoline, and
NH4+-N by O3/Fenton reached 100%, 100%, 95.68%, and
100%, respectively, which were much superior than those
obtained by non-catalytic ozonation. The improved per-
formance of Fenton ozonation was due to the promoting
effect of Fe2+ and H2O2 on ˙OH generation on the course
of ozone decomposition. In addition, the BAF combined
with ozone oxidation in degrading bio-treated coking
wastewater was examined (Zhang etal. 2014b). The bio-
degradability was found to be substantially improved
from BOD5/COD ratio of 0.09 to 0.43 under optimized oper-
ation parameters. In comparison with BAF process, the
removal of COD and UV254 can be increased remarkably
by BAF/O3, while there appeared nearly no difference for
NH4+-N removal by these two methods. This indicated the
poor oxidizing potential of ozone with NH4+-N, which is
not structured with typical unsaturated functional groups
and conjugated structures.
To sum up, the highly toxic organic compounds in
biologically treated coking wastewater effluent, especially
the aromatic or the conjugated structural organics, will be
preferentially degraded by catalytic and non-catalytic ozo-
nation post-treatment. However, the bio-refractory com-
pounds residual in coking wastewater is normally present
in low dose, inhibiting their kinetic reactions with ozone.
On the other hand, when ozonation was employed as the
pre-treatment for biological process, the biodegradability
could be substantially increased as a result of selective
oxygen atom addition on aromatic structures, which are
more biodegradable than their precursors.
4.4 Ozonation of dyeing wastewater
The textile industry is a water-consuming and seriously
contaminated industry, in which dyeing wastewater
accounts for 80% of total pollution discharge (Lin and
Chen 1997). Dyestuffs and textile auxiliaries, being the
main components of dyeing wastewater, are potentially
toxic and less biodegradable, which result in a threat to
aquatic organisms (Sharma etal. 2007). The effluent COD
of dyeing wastewater after primary sedimentation and
biological treatment is composed of refractory compounds
and SMPs. The SMPs mainly consisting of proteins, poly-
saccharides, and organic colloids are derived from bio-
logical treatment and constituted the majority of soluble
effluent organic matters (EfOM) (Wu etal. 2016a). Table8
summarizes the latest investigations of dyeing wastewater
treatment by means of ozone oxidation.
4.4.1 Non-catalytic ozonation of dyeing wastewater
The color removal from textile dyeing wastewater efflu-
ent treated by ozonation and the evaluation of toxic inter-
mediate compounds were investigated (Mezzanotte et al.
2013). Results indicated that average color unit removal
is 0.0018±0.0004, 0.0016±0.0005, and 0.0006±0.0002 per
mg O3/l for 426, 558, and 660nm absorbance, respectively.
The aldehydes including glyoxal and methylglyoxal were
recognized as the main carbonylic by-products from ozone
reaction. Nevertheless, exposed at 60 mg O3/l, the alde-
hyde concentration ranged from 0.7 to 1.0 mg/l, complying
with the discharge standards. Interestingly, glyoxal and
methylglyoxal concentrations were directly related to color
removal, which can be developed as a simple indicator to
the toxic potential of ozone by-products in textile effluents.
The ozonation mechanisms of anionic sulphonated azo dye
were elucidated (Turhan and Ozturkcan 2013). The molecu-
lar structure of RO16 dye contains both electron-donating
groups (-OH, -NHR) and electron-withdrawing groups (-SO3
and -SO2R). In general, aromatic rings substituted with elec-
tron-donor groups are highly reactive with ozone at carbon
atoms in ortho- and para- positions due to high electron den-
sities. Thus ozone reactions may occur predominantly on
these electron-rich sites. It was found that although nearly
complete decolorization can be achieved within 8-min ozo-
nation by the breakdown of chromophore groups, there
was still 30% COD residual in wastewater. This was owed
to the presence of electron-deficient sites on RO16 molecu-
lar as well as ozonated by-products. Benincá etal. (2013)
reported an interesting phenomenon concerning the dif-
ference in color removal of azo dye solution (Ponceau 4R)
from synthetic water and industrial wastewater. The results
indicated that it took no more than 600s for complete color
removal in synthetic dye solution (pH=5.8), as ozone is able
to cleave the azo bond and electron-rich organic functional
groups in dye molecule. The color removal in real industrial
wastewater (pH=4.7), however, did not exceed 50% under
nearly identical reaction conditions. The reason for such
behavior was probably the formation of suspended solids
from matters initially dissolved, although not fully under-
stood (Lin and Lin 1993).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment25
Table 8:The latest investigations of dyeing wastewater ozonation.
Ozone oxidation Wastewater quality Reaction conditions Main results Reference
Ozonation catalyzed
by sheet loaded with
Cu/Zn/Al/Zr catalyst
Concentration of basic yellow :
mg/l, pH: .
Ozone dose: mg/l, gas
flow: . l/min, temperature:
±.°C
The removal efficiency of BY (%) and COD
(%) can be sustained with O/BY mole
ratios of .–.
Zhu etal.
Ozonation catalyzed
by iron shavings
COD: ± mg/l, Colour: ± times,
pH: .±., BOD: ±. mg/l
Ozone dose: . mg/l, gas
flow: ml/min, catalyst
dose: g/l
Catalytic ozonation effectively removed organic
pollutants with COD decreasing from to
mg/l, below discharge limit
Wu etal. a
Ozonation catalyzed
by copper oxide
Concentration of Reactive Black :
mg/l, pH: ., COD: mg/l
Ozone dose: . mg/min,
catalyst dose: g/l
COD removal reached % in catalytic ozonation
after -min reaction, while it was only % in
non-catalytic ozonation
Hu etal.
Ozonation COD: ± mg/l, pH: .–. Ozone doses: – mg/l mg/l color removal was complete and at
mg O/l, the final aldehyde concentration
ranged between . and . mg/l
Mezzanotte etal.
Ozonation, activated
carbon and BAF
COD: – mg/l, BOD: .–
. mg/l, color: – times
Ozone dose: . mg/mg
COD, apparent density of AC:
kg/m
Outflows with COD of mg/l, BOD of . mg/l,
and color of . times were obtained after the
combined treatment
Zou
Ozonation-anaerobic
process
COD: mg/l, NH+-N: . mg/l,
pH:
Ozone doses: .–. g/l Anaerobic treatment removed COD and color.
Ozonation further reduced the organic content,
especially the aromatic compounds
Punzi etal.
Ozonation Concentration of reactive orange
: mg/l, COD: mg/l,
pH:.
Ozone dose: mg/l min COD of basic dyestuff wastewater was reduced
.% after ozone bubbling treatment
Turhan and
Ozturkcan
Ozonation catalyzed
by Fe(II)
Concentration of Reactive Red :
.mmol/l, pH:
Ozone doses: – mg/l,
flow rate: – ml/min,
Fe(II) doses: – mg/l
The maximum mineralization rate of RR dye was
about %, under optimized operation condition
of Fe(II) mg/l, pH , ozone dose mg/l, flow
rate ml/min
Zhang etal. a
Ozonation COD: ± mg/l, apparent color:
mg PtCo/l, azo dye: mg/l
Ozone flow rate: .mg/s,
pH(synthetic): .,
pH(wastewater): .–.
Azo dye aqueous solution was completely
degraded after only s, and a substantial
reduction of TOC (around %) was noticed
Benincá etal.
Ozonation with
electrocoagulation
(EC)
COD: mg/l, color: mg
PtCo/l, alkalinity: mg/l, pH: .
Ozone dose: . g/h, current
density (EC): . mA/cm
% color removal, % turbidity removal, and
% COD reduction could be attained by using
the integrated process
García-Morales
etal.
Ozonation catalyzed
by bio-composite
Indigo carmine concentration:
mg/l, pH:
Ozone dose: mg/l, catalyst
dose: mg/l, water
bath: ±°C
Nearly complete removal of indigo carmine was
obtained after min by catalytic ozonation
Torres-Blancas etal.
Ozonation with BAF COD: – mg/l, UV: .–.,
Color: – times, BOD:
–mg/l
Ozone doses: – mg/l,
hydraulic retention time
(HRT) of BAF: . h
With the ozone dosage of mg/l and HRT of
BAF of . h, COD of effluent from O-BAF process
was below mg/l
Wu etal. b
Ozonation catalyzed
by interior micro
electrolysis (IM)
Reactive Black solution: . g/l,
pH:., COD: . mg/l
Ozone dose: mg/h,
cm iron scraps filling
with cm AC
Acute toxicity tests showed that pre-treatment
by IM generated effluents that were more toxic
compared with initial wastewater.
Guo etal.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
26C. Wei etal.: Ozonation in water treatment
4.4.2 Catalytic ozonation of dyeing wastewater
The employment of catalytic ozonation could improve the
mineralization of simulated dyeing wastewater as a result
of radical-mediated reactions, besides nearly complete
color removal. The ozonation of Basic Yellow 87 (BY 87)
in synthetic wastewater catalyzed by Cu/Zn/Al/Zr cata-
lyst (i.e. CuO, ZnO, Al2O3, and ZrO2), which was loaded on
porous copper fiber sintered sheet, was evaluated (Zhu
etal. 2014). The removal efficiency of COD and TOC was
improved by two times and five times, respectively, by the
assistance of catalyst chip as compared to non-catalytic
ozonation. For a typical heterogeneous catalytic process,
physical adsorption for gaseous ozone took place due
to the presence of hydrophobicity surface and relatively
small pore size on catalyst chip surface. The BY 87 and its
by-products can be subsequently degraded by oxidizing
species on catalyst surface. Torres-Blancas et al. (2015)
developed a novel method synthesizing iron particles sup-
ported on deoiled Pimenta dioica L. Merrill husk for the
catalytic ozonation of indigo carmine. The acidic pH was
found to be the optimized condition for decolorization as
well as mineralization due to the presence of Fenton reac-
tions introduced by bio-composite catalyst. The reaction
mechanisms of Reactive Red 2 dye with ozone catalyzed by
Fe(II) in homogenous solution were investigated (Zhang
etal. 2013a). It was found that the second-order reaction
constant k2 was improved significantly by Fe(II)-catalytic
ozonation (2248 -1 s) in comparison with non-catalytic
ozonation (1056 -1 s). From the chemical reaction point
of view, the carbon atoms with chromophore azo-linkage
or with strong electron density were primarily attacked by
ozone. In addition, ozone can also undergo cycloaddition
reactions with unsaturated bonds, leading to the forma-
tion of carbonyl group (-C=O) or nitroso group (-N=O).
The toxicity evolution of diazo dye C.I. Reactive Black 5 in
aqueous solution subjected to integrated process of inte-
rior micro-electrolysis (IM) with ozonation was evaluated
(Guo etal. 2013). Although nearly complete decolorization
and 77.8% removal of COD can be achieved, the acute tox-
icity derived from Daphnia magna activity tests increased
in short period of IM-ozonation before eventually being
reduced under long ozonation exposure. This might be
stemmed from the broken azo bonds in RB5 by redox
reaction in IM process, thus producing naphthalene and
benzene derivatives with high toxicity (Maleki etal. 2010).
The evolution of intermediate compounds, change of
biodegradability, and decolorization in catalytic ozona-
tion of industrial dyeing wastewater have been evaluated.
Wu etal. (2016a) employed the iron shavings in catalytic
ozonation of organic pollutants from actual bio-treated
dyeing and finishing wastewater. The results indicated
that among 218 organic species detected by liquid chro-
matography-mass spectrometry, 58, 77, 79, and 4 species
were completely removed, partially removed, increased,
and newly generated, respectively. The BOD5/COD value
increased from 0.01 to 0.17, suggesting an improvement
in biodegradability. The acute toxicity of inhibitory effect
decreased from 51% to 33%, owing to the removal of
hazardous compounds by direct ozonation, indirect ˙OH
oxidation, and co-precipitation. Based on the molecular
structural analysis including molecular weight distri-
bution, three-dimensional excitation-emission matrix
fluorescence, and variation study in organic pollutant
species, the authors summarized that catalytic ozonation
exhibited efficient performance in removing both polar
and non-polar organic pollutants. In order to elucidate
the reaction mechanism of dye molecule with ozone, the
catalytic performance of carbon aerogel supported copper
oxide in ozonation of dyeing wastewater was investigated
(Hu etal. 2016). The UV-Vis spectrum analysis showed that
the reduction of maximum absorbance in visible region
was more rapid than that in UV region. This suggested
that the azo structures whose absorbance lies in visible
region were more efficiently destructed than those (aryl
and naphthalene-like moieties) in UV absorption region.
An integrated process containing ozonation and electro-
coagulation was employed for the treatment of industrial
indigo carmine dye wastewater (García-Morales et al.
2013). Results showed that the integrated process enabled
more efficient COD, color, and turbidity elimination than
non-catalytic ozonation. The authors speculated that the
synergistic effect resulted from the removal of hardness,
alkalinity, and conductivity in wastewater, which served
as radical scavengers in ozone oxidation, by means of
electrocoagulation.
4.4.3 Ozonation combined with biological process for
treating dyeing wastewater
The research activity of dyeing wastewater treatment by
biological process combined with ozonation was focused
on the genotoxicity evolution. The genotoxicity reduction
of bio-treated dyeing wastewater (BTDW) collected from
a cotton textile factory after ozonation coupled with acti-
vated carbon adsorption and BAF was evaluated (Zou 2 015).
The actual genotoxicity of BTDW was greatly reduced from
38.40 μg 4-nitroquinoline-N-oxide/l (initial) to 1.33 μg
4-nitroquinoline-N-oxide/l under optimized operation
conditions. The elimination of genotoxicity was ascribed
to the changes of toxic organic structures comprising
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment27
benzene rings and naphthalene rings according to UV-
visible absorbance analysis. In addition, the anaerobic
biological treatment combined with ozonation has been
applied for treating textile wastewater. Punzi etal. (2015)
employed a novel anaerobic-ozonation process, in which
ozonation functioned as post-treatment for biological
process, for the purpose of degrading the real textile efflu-
ent received from Ten Cate, the Netherlands. The acute
toxicity of untreated and treated wastewater was evalu-
ated through Microtox® and A. salina toxicity tests. The
results suggested that after 6min of ozone exposure, the
effluent was 20 times less toxic than the raw one accord-
ing to Microtox and non-toxic according to Artemia. Cor-
respondingly, mutagenicity was detected in the raw and
biologically treated effluent (p-value=5.407 e-10 and 0.027,
respectively) and the effluent after 1 min of ozonation
(p-value< 2.2 e-16 ). Nearly no mutagenicity was detected
after longer ozonation. This supports the findings that the
produced azo dyes and aromatic amines during treatment
can be mutagenic and carcinogenic. The ozonation-BAF
was used in order to elucidate the removal behavior of
fluorescent DOM in biologically treated textile wastewater
(Wu etal. 2016b). On the basis of high-performance liquid
chromatography with multi-excitation/emission fluores-
cence scan analysis, the removal of triple-excitation peaks
at emission of 460nm was the dominant pathway for color
and UV254 reduction by ozonation. The decomposition of
fluorescent DOM species was established in the order of
humic substances, hydrophobic aniline-like species, and
hydrophilic aniline-like species.
In summary, nearly complete decolorization of dyeing
wastewater by ozonation could be feasibly achieved
because of the selective reactivity of ozone with chromo-
phore groups (i.e. azo structures). The further mineraliza-
tion of decolorization intermediates could be realized by
catalytic ozonation, owing to radical-mediated reactions.
The toxicity of dyeing wastewater subjected to ozonation,
however, will be increased due to the generation of naph-
thalene, benzene derivatives, and aromatic amines during
treatment, which are more mutagenic and carcinogenic
than raw dyeing compounds.
4.5 Ozonation of municipal wastewater
Municipal wastewater treatment plants have been devel-
oped preliminarily to protect natural aquatic systems
and water resources by eliminating EfOM, nutrients, and
pathogens. It is well established, however, that the emerg-
ing contaminants including pharmaceutically active com-
pounds, personal care products, and endocrine disrupting
compounds are often detected in biologically treated
municipal wastewater (BTMW) (Schwarzenbach et al.
2006). Although these compounds are usually presented in
ng/l–μg/l concentration range in effluent, they may cause
ecological risks such as feminization of higher organisms;
microbiological resistance; and finally, accumulation in
soil, plants, and animals (Pal et al. 2010). Thus, further
ozonation treatments of BTMW effluent are of fundamen-
tal concern with special emphasis on the elimination of
emerging contaminants as well as the elucidation of chem-
ical reaction mechanisms of EfOM (Table9).
4.5.1 Non-catalytic ozonation of BTMW
Special emphasis has been paid on the organic trans-
formation and elimination of micro-pollutants in BTMW
subjected to non-catalytic ozonation. The reactivity of
EfOM from municipal wastewater treatment plant with
ozone was examined by Jin etal. (2016). The EfOM could
be categorized into four fractions according to their
hydrophobicities, of which hydrophobic acid (HOA) and
hydrophobic neutral (HON) were especially studied. It
was noticeable that HOA was first changed into HON, and
then the majority of HON fraction was subsequently con-
verted to HI by further ozonation. This can be explained
that although raw HOA and HON consisted of consider-
ably high ratios of aromatic carbon, HON had higher pro-
portion of aliphatic carbon and carboxylic carbon than
HOA (Lin etal. 2014b), demonstrating the higher reactiv-
ity of HOA with ozone than that of HON. The non-catalytic
ozonation was employed for the remediation of micro-
pollutants in BTMW (Prieto-Rodríguez etal. 2013, Uslu
et al. 2015). Prieto-Rodríguez et al. (2013), for example,
have identified 66 target micro-pollutants, with 16 of
those at initial concentration over 1000 ng/l, composing
88% of initial effluent pollutant load. Without carbonate
stripping or pH adjustment, 98% of micro-pollutants had
been degraded after treatment of 60min and ozone con-
sumption of 9.5 mg/l. Importantly, the DOC of real BTMW
effluent before ozonation was 12.6 mg/l and was still 11.8
mg/l after treatment. It was possibly related to the produc-
tion of intermediates formed during ozonation, as neither
complete degradation nor mineralization was attained.
As the application of ozonation in improving the quality
of municipal wastewater effluents was limited by a large
number of structurally diverse micropollutants as well
as the varying quality of wastewater matrices, a strategy
predicting the elimination of ozone-refractory micropoll-
utants in BTMW was proposed (Lee etal. 2013). It was con-
firmed that a DOC-normalized ozone dose, coupled with
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
28C. Wei etal.: Ozonation in water treatment
rate constants for selected micropollutants with ozone
and ˙OH, and the measurement of ˙OH exposure would be
the key parameters for the prediction. For example, the
elimination of ozone refractory micropollutants was well
predicted by measuring ˙OH exposure with the decrease of
probe compound p-chlorobenzoic acid.
In light of genotoxicity evaluation, it was observed that
the inhibition in respirometric assays was reduced from 12%
(before ozonation) to 0% after ozonation treatment (Prieto-
Rodríguez etal. 2013), which is similar with the reports in
Reaume etal. (2015). Nevertheless, toxicity assays after ozo-
nation showed no inhibition on V. fisheri bioluminescence
emissions (Prieto-Rodríguez etal. 2013), while Stalter etal.
(2010) reported an increase of toxicity in sewage effluents
subjected to ozonation. This can be attributed to the for-
mation of toxic ozonated by-products. The increased geno-
toxicity, derived from developmental retardation of fish
embryos, has been found in ozonated secondary effluents
from municipal wastewater treatment plants (Yan et al.
2014). The results indicated that the consumption of 0.5mg
O3/mg DOC by wastewater will produce 67.7 mg/l of total
aldehyde (mixture of formaldehyde, acetaldehyde, propi-
onaldehyde, and glyoxal), increasing the larval deformity
by 53.8%. It is thus proposed that the employment of bio-
filtration as a post-treatment process may be effective in
removing the toxic by-products including aldehydes, thus
reducing embryo toxicity induced by ozone.
4.5.2 Catalytic ozonation of BTMW
The improved performances of municipal wastewater
ozonation catalyzed by heterogeneous or homogenous
promoters have been investigated. TiO2 nano composites
supported on magnetic multiwalled carbon nanotubes
were attempted to improve the photocatalytic ozonation
of micro-pollutants in municipal wastewater treatment
plant effluents (Yu etal. 2015). The results indicated that
although only 44.9% of mineralization degree can be
achieved by non-catalytic ozonation, the initial molecu-
lar structures of target compounds can be completely
destroyed by ozone. By contrast, the employment of
Table 9:The latest investigations of municipal wastewater ozonation.
Ozone oxidation Wastewater quality Reaction conditions Main results Reference
Ozonation DOC: .±. mg/l,
UV: .±. cm-,
pH: .±.
Ozone doses: .–
.mg O/mg DOC
The aromaticity of HON decreased at
ozone dosage up to . mgO/mg DOC),
while aliphatics and ketones increased
at ozone dose of . mgO/mg DOC
Jin etal.
Ozonation DOC: – mg/l, pH: ,
total inorganic carbon:
– mg/l
Ozone dose: .g/h % of micropollutants degradation was
achieved after min of treatment and
the ozone consumption of . mg/l
Prieto-Rodríguez
etal.
Ozonation DOC: .–. mg/l,
UV: .–. cm-,
pH:.–.
Ozone doses: .–
.mgO/mg DOC
A significant reduction (average %) in
wastewater genotoxicity was observed
after ozonation
Reaume etal.
Ozonation DOC: .–. mg/l,
UV: .–. cm-,
pH:.–.
Ozone doses:
–.mgO/mg DOC
The increase of ozone dosage from
. to .mg O/mg DOC produced
aldehyde from . to . mg/l,
elevating the deformed larvae from .%
to .%
Yan etal.
Ozonation DOC: .– mg/l,
pH: .–., HCO
-:
.–.m
Ozone doses: .–
. g O/g DOC
A single indicator has been used
to predict the elimination of micro-
pollutants in BTMW, using kinetic models
Lee etal.
Ozonation catalyzed by
TiO or GAC
DOC: .–. mg/l,
pH: .
Ozone dose: mg/l,
solid catalyst dose:
g/l, HO dose:
mg/mgO
Ozonation of effluent over TiO or GAC
was no more effective on trace organic
removal than non-catalytic ozonation
Barry etal.
Ozonation TOC: – mg/l, pH:
–., pharmaceutical
substance: μ
Ozone doses:
–μ, water bath:
°C
Overall degradation of pharmaceuticals
in BTMW was >% at ozone doses of
.mg O/mg DOC or higher
Uslu etal.
Photocatalytic
ozonation
TOC: . mg/l, pH: .,
UV: . cm-, BOD:
mg/l
Ozone dose: mg/l,
catalyst dose: .g/l,
light intensity:
W/m
Photocatalytic ozonation gave rise to
complete elimination of micropollutants
in min, with TOC removal up to %
in h.
Rey etal.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment29
photocatalytic ozonation enabled 65.7% reduction of TOC,
demonstrating a lower concentration of intermediates
including phenolic and carboxylate compounds. This was
ascribed to the enhancement of ˙OH generation by pho-
tocatalytic ozonation. It was interesting to note that an
obvious improvement of ˙OH generation was observed in
the presence of H2O2 when delivered ozone dose exceeded
an “ozone dose threshold” (Barry etal. 2014). This thresh-
old occurs due to the reactions between ozone and
initiators/promoters within wastewater matrix, also accel-
erating ˙OH generation (Mvula etal. 2009). As a result, the
authors (Barry etal. 2014) defined the ozone dose thresh-
old responsible for exhausting ozonation with these com-
pounds, below which the addition of H2O2 revealed little
effect on radical generation.
In conclusion, it is well established that EfOM can
be further reduced by catalytic and non-catalytic ozona-
tion, as evidenced by TOC reduction and organic structure
transformation. An increase of EfOM genotoxicity after
ozonation will be, however, recognized, which may be
attributable to formation of higher toxic ozonated by-prod-
ucts such as total aldehyde than raw organic compounds.
4.6 Ozonation reactor
Due to the resistance of mass transfer and the limited
dissolution from gaseous to aqueous phase, substantial
efforts have been made in the design of ozonation reactor
for the purpose of extending its HRT in water and
improving mass transfer coefficient. Table 10 lists the
recent research efforts addressing the design and opera-
tional performance of ozonation reactor in wastewater
treatment. The effectiveness of microbubble-ozonation
(average diameter of 45 μm) and macrobubble-ozonation
(average diameter of 1 mm) for treating refractory acrylic
fiber wastewater was, for example, evaluated (Zheng etal.
2015). As depicted in Figure 10A, a TCRI microbubble
generator was used to produce microbubbles, whereas a
40-μm micropore titanium plate was employed to generate
macrobubbles for comparison. The results suggested that
removal of COD, NH4+-N, UV254 in microbubble-ozonation
was 25%, 9%, 35% higher than those achieved in macro-
bubble-ozonation. This was due to the prolonged HRT of
microbubble in reactor, the enhanced mass-transfer of
microbubble ozone from gaseous to aqueous phase, and
consequently the higher dissolved ozone concentration,
being beneficial to greater ˙OH generation. Importantly, it
was found that the gas holdup, ozone mass-transfer coef-
ficient, and ozone utilization efficiency in microbubble-
ozonation were 6.6, 2.2, and 1.5 times higher than those of
macrobubble-ozonation.
The observed promoting effect could also be ascribed
to the defined gaseous and liquid movement regulated
by ozone reactor. Gogate et al. (2014) described a novel
patented combinative reactor, OzonixTM, utilizing the
Table 10:The recent investigations focusing on ozonation reactor.
Ozone oxidation Pollutant Reactor Reactor
performance
Bubbling pattern Reference
O/UV Coking wastewater Pilot-scale FBR HRAa: . g/day Bottom bubbling Lin etal. a
O/acoustic cavitationBacteria OzonixTM BIb: .% Along the water
flow tube
Gogate etal.
OAcrylic fiber wastewaterTubular reactor MTCc: . min- Bottom bubbling Zheng etal.
OOxalate PCD OORd: . mg/(l s)No bubbling used Ajo etal.
Catalytic ozonation Methylene blue Quadrate vessel DCe: . min- Bottom bubbling Zhang etal. b
Catalytic ozonation Catechol FBR kf: . min- Bottom bubbling Moussavi etal.
OAcid Red MTMCRgKGah: . s- Inner tube bubblingSun etal.
Catalytic ozonation Phenolic wastewater Rotating Packed BedKGai: . s- Gas inlet bubbling Zeng etal.
aHealth risk assessment: the reduction of total carcinogenic substance exposure to surface water per day.
bBacteria inactivation: 97.5% for sulfate-reducing bacteria reduction.
cMass-transfer coefficient: the MTC of microbubble-ozonation was 2.2 times higher than that of macrobubble-ozonation.
dOxalate oxidation rate: the degradation rate of oxalate was 0.01 mg/(l s) in PCD reactor, while the reaction rate of oxalate with ozone was
0.00058 mg/(l s).
eDecolorization: the best performance of decolorization rate of methylene blue was 0.255 min-1 using catalytic ozonation under pH 9.
fPseudo-first order reaction rate: the reaction rate of catechol by catalytic ozonation was 0.0839 min-1 which was 6.8 times as big as non-
catalytic ozonation.
gMicroporous tube-in-tube microchannel reactor.
hThe overall volumetric mass-transfer coefficient increased from 2.7 to 3.5 s-1 with pH rising from 3 to 9.
iThe overall volumetric mass-transfer coefficient increased from 0.054 to 0.111 s-1 with the increase of rotation speed from 150 to 1400 rpm.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
30C. Wei etal.: Ozonation in water treatment
synergistic effects of ozone, hydrodynamic cavitation,
acoustic cavitation, and electrochemical oxidation/precipi-
tation in water and wastewater treatment (Figure 10B). The
hybrid OzonixTM reactor is a self-contained 53-ft-long mobile
trailer with an onboard diesel generator and fully automatic
PLC controls. The most important part is the ozone injec-
tion zone, in which ozone gas can be injected along water
flow inside the pipe. Subsequently, the turbulence created
by acoustic cavitation could strengthen ozone dissolution.
In this circumstance, ozone mass transfer limitation can
be eliminated as a result. The authors also tested the effi-
ciency of OzonixTM on 776 bacteria samples taken from 282
wells in Fayetteville Shale over a 3-year period (Gogate etal.
2014). The results indicated that bacteria inhibition of acid-
producing bacteria was 96.5% and sulfate-reducing bacte-
ria was 97.5%, suggesting a superior microbial inactivation
ability of this hybridized reactor.
Several other industrial ozonation reactors includ-
ing porous diffuser contact tank, Raschig Ring contact
tower, improved vortex diffuser, Gagnaux repeat diffuser,
Van der Made-Welsbach diffuser, Torricelli contact tank,
Otto jet aerator, and Yonkerssonic ultrasonic mixer have
also been implemented for industrial wastewater post-
ozonation (Chu etal. 2002). The Torricelli contact tank,
for example, is implanted with baffles of 2-m height and
inlet-outlet water tubes of 10–12-m height in order to regu-
late the flow pattern of ozone gas and to extend its HRT,
as illustrated in Figure 10C. The wastewater mixed with
ozone gas is delivered into reactor through the relatively
long inlet water tube, flowing at fixed direction along
baffles with maximum flow velocity of 160 mm/s. Particu-
larly, the solubility of ozone in this case can be increased
because the residual ozone released from aqueous phase
is under pressure in the reactor according to Henry’s Law.
Under this circumstance, the actual oxidation potential of
ozone could be strengthened as a result of increased solu-
bility on the basis of Nernst equation. The Otto-de Frise
and the Siemens-Otto ozone contactors are equipped with
down flow and long distance Otto jet aerator (Figure 10D),
thus the utilization efficiency of ozone can be improved
arising from prolonged contact time with water (Chu etal.
2002).
Pump
Reservoir
Valve2 Inlet
Outlet
Valve1
Valve3
Wastewater
outlet
Wastewater intlet
Wastewater outlet
Wastewater
intlet
Ozone gas under
pressure
Ozone gas under
pressure
Baffles
Ozone gas
Ozone gas inlet
Off-gas
2% KCI
Tail-gas treatment
Reactor
AB
CD
Ozone
generator Flowmeter
Microbubble
generator
Figure 10:The schematic configurations of ozone reactors, microbubble reactor (A), hybridized reactor (B), Torricelli contact tank (C), and
Otto jet aerator (D). [(A) was adapted from Zheng etal. 2015, (B) was adapted from Gogate etal. 2014, original drawings of (C) and (D) were
done by us. In schematic (B), 1: hydrodynamic cavitation; 2: ozone injection zone, 3: main reactor vessel with ultrasound, 4: final stage
based on electrochemistry].
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment31
The pilot-scale fluidized bed reactor (FBR) imple-
mented with ozone reaction and UV irradiation, for
example, was designed (Figure 11) aiming at reducing
the toxicity of bio-treated coking wastewater (Lin et al.
2014a). The internal components (i.e. draft tube, baffles,
and funnel internal) installed in FBR were used to control
flow pattern and thus to produce inner loop of liquid and
gas, thus decreasing the ineffective volume of FBR while
extending HRT of ozone gas and increasing the ozone
mass transfer and the utilization of ozone from chemi-
cal engineering points of view (Zhang et al. 2012). The
FBR was manufactured from stainless steel, with total
effective volume of 1.3 m3 and geometric dimensions of
ϕ 1.2 m×3.0 m. Under the reaction conditions of ozone
delivery rate of 240 g/h, initial pH 6.5–7.5, HRT of 2 h, and
wastewater flow rate at 1 m3/h, the total benzo[a]pyrene
(BaP) toxic equivalent concentration (TEQBaP) was reduced
from 0.65±0.08μg/l (influent) to 0.41±0.06 μg/l (effluent),
corresponding to a 0.432 g/day reduction of carcinogenic
substances.
The state-of-the-art ozonation reactor, PCD device,
has attracted considerable attention in potable and
wastewater treatment. The highly superior novelties of
PCD are the in situ generation of oxidizing agents (e.g.
ozone and ˙OH) and the avoidance of ozone delivery from
conventional ozone generator into ozonation reactor
(Kornev etal. 2014, Ajo etal. 2015). As gas-liquid contact
surface is the primary interface in mass transfer of ozone
and ˙OH formation site, Ajo et al. (2015) reported that
the ozonation of oxalate in laboratory-scaled PCD was
conducted from the perspective of optimizing contact
surface area at different discharge powers. As shown
in Figure 12, the corona discharge chamber was assem-
bled by wire-plate electrode, which is connected to
pulse power generator with pulse repetition frequency
of 200–840 pulses per second. During the operation,
aqueous solution was showered through the discharge
zone wherein ozone (some other reactive species should
be produced at the same time, i.e. ˙OH) was generated,
and the purification of water droplet occurred simulta-
neously. The results suggested that the optimal contact
area was increased linearly with growing discharge
power, indicating the enhanced ˙OH utilization in oxalate
oxidation. The predominant role of ˙OH by minimum of
an order of magnitude surpassing ozone in oxalate oxi-
dation was observed.
In summary, extending HRT of ozone in solution,
increasing partial pressure over solution, enhancing the
gas-liquid mixing extent, and integrating in situ genera-
tion of ozone with decontaminant reactions are frequently
applied to accelerate ozone dissolution and utilization
efficiency, which are of significance for its practical
applications.
4.7 Energy analysis for ozonation
application
The energy consumption of wastewater ozonation
mainly depends on the generation of ozone and the
maintenance of gas-liquid contact reactions. Theoreti-
cally, the electricity consumption to produce 1200-g
Figure 11:The schematic configuration (A) and real figure (B) of the pilot-scale ozone/UV fluidized bed reactor designed for advanced
treatment of industrial wastewater (1: storage tank, 2–3: ozone/UV fluidized bed reactor, 4: filtering tank, 5: tail gas destruction reactor,
6:jet pump, 7: UV lamp, 8: air compressor, 9: ozone generator, 10: sample inlet, 11: sample outlet, 12: ozonated air, 13: gas inlet, 14: tail gas
outlet; adapted from Lin etal. 2014a).
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
32C. Wei etal.: Ozonation in water treatment
ozone is 1-kWh electric power, corresponding to the
energy consumption of 0.82 kWh/kg O3 (Alonso et al.
2005). In reality, only a small part of electric power is,
however, utilized to produce ozone, while the majority is
depleted in the form of heat, and the power loss is even
more significant when air with lower oxygen content
is fed. Eliasson etal. (1987), for instance, calculated a
maximum ozone yield efficiency of 33% (400 g O3/kWh)
in oxygen feed and 17% (200 g O3/kWh) in dried air feed
on the basis of Boltzmann equation. The ozone genera-
tion efficiency of actual ozone generator is, however,
around 130 g O3/kWh when pure oxygen is fed, which
is much lower than that derived from thermodynamic
calculation (Chang et al. 1991), although some rela-
tively higher ozone generation efficiency can be reached
in specific operation conditions. Therefore, roughly
10% electric power is utilized for production of ozone,
mainly restricted by the side reactions along silent dis-
charge process. Concerning the economic aspect, the
cost of ozone production is estimated to be 2.32 $/kg O3
with the charging standard of electricity being 0.093 $/
kWh for industrial usage, thus the electric consumption
of ozone generation is around 25 kWh/kg O3 supplied by
air (He etal. 2003).
Pressure relief
Plate electrode
Wire electrode Insulator
Sample por
t
PIC
PC
PC
PC
Perforated plate
HV conductor
PCD reactor
Container tank
Drain port
Figure 12:The schematic configurations of laboratory-scaled PCD
device for wastewater treatment in continuous flow (adapted with
permission from Ajo etal. 2015. Copyright 2015, American Chemical
Society).
Besides the maintenance of contact reactions, involv-
ing the transport of gaseous ozone from ozone generator
to reactor and the gas agitation driven by ozone bubble
also consumes a large amount of energy for wastewater
ozonation. It was analyzed that, for an ozone treatment
system at the Belmont Water Treatment Plant, Philadel-
phia, the energy consumption ratios of ozone genera-
tion, ozone-water contacting, equipment maintenance,
and preheating system are 67.1%, 21.2%, 8.9%, and 2.8%,
respectively, relative to the total energy input (Bean 1959).
Recently, increasing research attempts have been
made to reduce the energy efficiency of ozonation with
organic pollutants, defined as energy consumed per unit
mass contaminant or DOC removed, by coupling with
other physical-chemical technologies, as compared in
Table 11. The observed synergistic effect is supported by
the fact that combined technologies can enhance the gen-
eration of radical species in comparison to non-catalytic
ozonation and the elimination of pollutant as well as
the energy efficiency under identical energy input can
be therefore increased. Mehrjouei etal. (2014) indicated
that the energy efficiency of removing unit concentra-
tion oxalic acid by photocatalytic ozonation (TiO2/UVA/
O3) was two and nine times lower than catalytic ozonation
(TiO2/O3) and photocatalysis (TiO2/UVA/O2), respectively.
Basically, TiO2/UVA/O3 gave rise to the highest yield rate
of ˙OH, as a result of the remarkable capture of conductive
electron by ozone, being capable of inhibiting the recom-
bination of photo-generated charge. The energy efficiency
of ozone-based technologies can also be evaluated by the
energy consumed per unit mass of DOC eliminated. Kopf
etal. (2000) reported that the energy efficiency of TiO2/
UV/O3, TiO2/UV, and O3 for degrading monochloroacetic
acid was 5.4, 19, and 110 kWh/g DOC, respectively, which
was ascribed to the synergistic effect of combined tech-
nologies responsible for improved ˙OH generation.
5 Conclusions and future prospects
This paper presents general knowledge concerning the
generation of ozone, the basic physicochemical proper-
ties of ozone, and its application in water and waste-
water treatment. The production of oxygen atom from
molecular oxygen excitation and the Three-body Colli-
sion Reaction are the preliminary reactions for ozone
generation. The application of silent discharge is most
effective and practical for ozone generation, although
several ozone generation approaches have been practi-
cally developed. The thermal decomposition of ozone
and the chemical depletion of ozone consumed by oxygen
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment33
atom and nitrogen-containing active species, however,
adversely affect ozone yield efficiency. Therefore, cooling
of discharge gap, mix of inert gas, and pulsed power have
been used in ozone generator for improving its opera-
tion condition, with the basic characteristics (e.g. ioni-
zation followed by avalanche that results in breakdown
and conductive channel) of silent discharge remaining
unchanged. Further investigations focusing on discharge
steps should be conducted, aiming at controlling the
rise of temperature in discharge gap and thus inhibiting
thermal decomposition of ozone.
Ozone is strongly reactive with a selection of pollut-
ants and extensively used in pollution control due to its
solubility and chemical reactivity. The dissolution behav-
ior of ozone, determined by partial pressure of gaseous
ozone, water temperature, mass transfer condition, dis-
solved organic or inorganic matters, and solution pH, is
the basis of its wide applications in water and waste water
treatment. Other physical properties of ozone such as
odor and color may also be closely related to its applica-
tions. From the viewpoints of chemistry reactions, inor-
ganic pollutants can be directly oxidized by ozone by
means of electron transfer or oxygen-atom transfer reac-
tions. The organic compounds containing electron-rich
or unsaturated functional groups can be selectively ozo-
nated through electrophilic substitution or 1,3-dipolar
cycloaddition, respectively. Also, the organic compounds
structured by carbonyl groups, carbon-nitrogen double
or triple bonds can be oxidized at electron-deficient posi-
tions, e.g. carbon atom. The radical-mediated reactions,
on the other hand, are initiated upon ozone decomposi-
tion, which is catalyzed by homogenous and heteroge-
neous catalysts. The main surface and compositional
characteristics of heterogeneous catalysts correlated with
catalytic activities, however, have not been thoroughly
elucidated, and the standardized relationship between
these essential characteristics and catalysts’ synthesis
routes has not been established.
Ozone-based technologies are able to effectively inac-
tivate micro-organisms and decompose organic pollutants
for the purpose of drinking water disinfection and indus-
trial wastewater treatment, respectively. The employment
of ozone reaction integrated with various oxidative or
physical separation technologies should be taken into
account of the specific wastewater metrics. Nevertheless,
the applications of ozonation have several limitations in
treating water and wastewater. The biological regrowth,
for instance, cannot be completely inhibited in the dis-
tribution system, and some DBPs will be simultaneously
produced by ozone disinfection. Further oxidation of
industrial wastewater by means of ozonation is remark-
ably hindered by inadequate oxidation capability of
Table 11:The specific energy consumption analysis of ozone-based technologies.
Ozone-based
Technology
Pollutants Ozone yield efficiencyEnergy efficiency Reference
Photocatalytic
ozonation
Oxalic acid W/± mg/l O. kW·h/m (photocatalytic ozonation);
. kW·h/m (catalytic ozonation)
Mehrjouei etal.
Photocatalytic
ozonation
Monochloroacetic acid . kW·h/g O. kW·h/g DOC reduction (photocatalytic
ozonation)
kW·h/g DOC reduction (photocatalysis)
kW·h/g DOC reduction (ozonation)
Kopf etal.
Photocatalytic
ozonation
Methanol –. €/m (photocatalytic ozonation)
. €/m (ozonation)
. €/m (photocatalysis)
Mena etal.
O/HOParachlorobenzoic acid– kW·h/kg OHO/O increases the energy requirement
by % compared to O alonea
Rosenfeldt etal.
O/HOParachlorobenzoic acid–. kW·h/m (ozonation)b
. kW·h/m (HO/ozonation)b
Katsoyiannis
etal.
Ultrasonic/OTriphenylmethane dye – kW·h/t dye Zhou etal.
Electrochemical
oxidation/O
Congo Red dye – kW·h/m (ozonation)c
kW·h/m (electrochemical ozonation)c
Elahmadi etal.
Photocatalytic
ozonation
Dichloroacetonitrile – kW·h/kg (ozonation)
kW·h/kg (photocatalytic ozonation)
kW·h/kg (photocatalysis)
Shin etal.
aThe energy efficiency was measured as a function of ˙OH exposure at the equimolar concentration of H2O2 with O3.
bThe energy efficiency was measured for 90% pCBA transformation.
cThe energy efficiency was measured for 80% TOC removal.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
34C. Wei etal.: Ozonation in water treatment
ozone, ultimately resulting in the accumulation of small
molecular fatty acids and saturated aliphatic compounds.
Although the oxidation capability of ozone for removing
pollutants can be improved by coupling with various cata-
lysts, less efforts have been addressed on the pollutants
elimination in practical industrial wastewater, to which
the radical scavenging effect of inorganic carbons and
DOM has to be specially paid.
Overall, all these limitations will make ozone-based
technologies as not devoid of drawbacks. In order to develop
the technologies with high efficiency, operability, and low
energy consumption, further researches should focus on
ozone generator with higher productivity, structure-activity
relationship of catalysts with ozone chemistry, and design
of ozonation reactor. The combination of ozone reaction
with bio-filter, for example, is a promising attempt to over-
come the basic shortcomings of ozone reaction, as ozone
recalcitrant compounds are conversely more biodegrad-
able. It is of top priority to synthesize the state-of-the-art
and highly reactive ozone catalysts to accelerate decom-
position of ozone and therefore generation of oxygen-
containing radicals. This can be achieved by optimizing
crystal structures, electronic properties, chemical composi-
tions, morphologies, and surface states of catalysts. Finally,
research activities of high performance of ozone reactor
should be concentrated on the coordination of chemical
reaction kinetics with fluid dynamics, the practical appli-
cation of counter current flow pattern, and the utilization
of exhausted tail gas by means of multi-level series con-
nection of reactors. The implementation of counter current
flow pattern between liquid and gas inside the FBR, for
example, could enhance mass transfer of ozone in water
and thus accelerate its dissolution to a large extent.
Acknowledgments: We gratefully acknowledge the finan-
cial support from the National Natural Science Founda-
tion of China (nos. U1201234, 51278199, 21037001) and the
Research Project of Production, Education and Research
of Guangdong Province, China (nos. 2012B091100450,
2013ZP0017).
References
Agbaba J, Molnar J, Tubić A, Watson M, Maletić S, Dalmacija B.
Effects of water matrix and ozonation on natural organic matter
fractionation and corresponding disinfection by-products
formation. Water Sci Technol Water Supply 2015; 15: 75–83.
Ajo P, Kornev I, Preis S. Pulsed corona discharge in water treatment:
the effect of hydrodynamic conditions on oxidation energy
efficiency. Ind Eng Chem Res 2015; 54: 7452–7458.
Alonso JM, García J, Calleja AJ, Ribas J, Cardesín J. Analysis, design
and experimentation of a high-voltage power supply for ozone
generation based on current-fed parallel-resonant push-pull
inverter. IEEE Trans Ind Appl 2005; 41: 1364–1372.
Andrews L, Withnall R. Matrix reactions of oxygen atoms with P4
infrared spectra of P4O, P2O, PO and PO2. J Am Chem Soc 1988;
110: 5605–5611.
Bablon G, Bellamy WD, Bourbigot MM, Daniel FB, Dore M, Erb
F, Gordon G, Langlais B, Laplanche A, Legube B, Martin G,
Masschelein WJ, Pacey G, Reckhow DA, Ventresque C. Ozone
in water treatment: application and engineering. Chelsea, MI,
USA: Lewis Publishers, Inc., 1991: 11–132.
Bailey PS. The reactions of ozone with organic compounds. Chem
Rev 1958; 58: 925–1010.
Bailey PS, Lane A. Competition between complete and partial
cleavage during ozonation of olefins. J Am Chem Soc 1967; 89:
4473–4479.
Barndõk H, Cortijo L, Hermosilla D, Negro C, Blanco Á. Removal
of 1,4-dioxane from industrial wastewaters: routes of
decomposition under different operational conditions to
determine the ozone oxidation capacity. J Hazard Mater 2014;
280: 340–347.
Barriga-Ordonez F, Nava-Alonso F, Uribe-Salas A. Cyanide oxidation
by ozone in a steady-state flow bubble column. Miner Eng
2006; 19: 117–122.
Barry MC, Hristovski K, Westerhoff P. Promoting hydroxyl radical
production during ozonation of municipal wastewater. Ozone
Sci Eng 2014; 36: 229–237.
Bean EL. Ozone production and costs. Adv Chem Ser 1959; 21:
430–442.
Beltrán FJ, Rivas FJ, Montero-de-Espinosa R. Ozone-enhanced
oxidation of oxalic acid in water with cobalt catalysts. 1.
Homogeneous catalytic ozonation. Ind Eng Chem Res 2003; 42:
3210–3217.
Beltrán FJ, Zhou YR, Zhu WP. Ozone reaction kinetics for water and
wastewater systems. Beijing: China Building Industry Press,
2007 (in Chinese).
Benincá C, Peralta-Zamora P, Tavares CRG, Igarashi-Mafra L.
Degradation of an azo dye (Ponceau 4R) and treatment of
wastewater from a food industry by ozonation. Ozone Sci Eng
2013; 35: 295–301.
Benson SW. Kinetic considerations of efficiency of ozone production
in gas discharges. Ozone Chemistry and Technology. Adv Chem
Ser 1959; 21: 405.
Bijan L, Mohseni M. Integrated ozone and biotreatment of pulp
mill effluent and changes in biodegradability and molecular
weight distribution of organic compounds. Water Res 2005; 39:
3763–3772.
Biń AK. Ozone dissolution in aqueous systems treatment of the
experimental data. Exp Therm Fluid Sci 2004; 28: 395–405.
Bing JS, Hu C, Nie YL, Yang M, Qu JH. Mechanism of catalytic
ozonation in Fe2O3/Al2O3@SBA-15 aqueous suspension
for destruction of ibuprofen. Environ Sci Technol 2015; 49:
1690–1697.
Birdsall CM, Jenkins AC, Spadinger E. Iodometric determination of
ozone. Anal Chem 1952; 24: 662–664.
Bond T, Templeton MR, Rifai O, Ali H, Graham NJD. Chlorinated and
nitrogenous disinfection by-product formation from ozonation
and post-chlorination of natural organic matter surrogates.
Chemosphere 2014; 111: 218–224.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment35
Bühler RE, Staehelin J, Hoigné J. Ozone decomposition in water
studied by pulse radiolysis. 1. HO2/O2
- and HO3/O3
- as
intermediates. J Phys Chem 1984; 88: 2560–2564.
Calvert JG. Test of the theory of ozone generation in Los Angeles
atmosphere. Environ Sci Technol 1976; 10: 248–256.
Carrillo-Pedroza FR, Nava-Alonso F, Uribe-Salas A. Cyanide oxidation
by ozone in cyanidation tailings: reaction kinetics. Miner Eng
2000; 13: 541–548.
Chang SL. Modern concept of disinfection. J Sanitation Eng Div 1971;
97: 689–707.
Chang JS, Lawless PA, Yamamoto T. Corona discharge processes.
IEEE Trans Plasma Sci 1991; 19: 1152–1166.
Chang EE, Hsing HJ, Chiang PC, Chen MY, Shyng JY. The chemical
and biological characteristics of coke-oven wastewater by
ozonation. J Hazard Mater 2008; 156: 560–567.
Chen XJ, Zhao GB, Wei CH, Jiang ZM, Diao CP, Lin C, Hu Y, Ren Y, Wu
CF. Analysis of composition of coking wastewater oxidized by
O3/UV and the kinetics of the key component. Environ Chem
2012; 31: 1502–1509 (in Chinese).
Chen CM, Chen HS, Guo X, Guo SH, Yan GX. Advanced ozone
treatment of heavy oil refining wastewater by activated carbon
supported iron oxide. J Ind Eng Chem 2014a; 20: 2782–2791.
Chen KC, Wang YH. The effects of Fe-Mn oxide and TiO2/α-Al2O3
on the formation of disinfection by-products in catalytic
ozonation. Chem Eng J 2014b; 253: 84–92.
Christensen PA, Lin WF, Christensen H, Imkum A, Jin JM, Li G,
Dyson CM. Room temperature electrochemical generation of
ozone with 50% current efficiency in 0.5M sulfuric acid at cell
voltages <3 V. Ozone Sci Eng 2009; 31: 287–293.
Chu JY, Wu CD, Chen WJ, Chen ZG. Ozone technology and
application. Beijing, China: Chemical Industry Press, 2002 (in
Chinese).
Chu LB, Xing XH, Yu AF, Zhou YN, Sun XL, Jurcik B. Enhanced
ozonation of simulated dyestuff wastewater by microbubbles.
Chemosphere 2007; 68: 1854–1860.
Chu LB, Xing XH, Yu AF, Sun XL, Jurcik B. Enhanced treatment of
practical textile wastewater by microbubble ozonation. Process
Saf Environ Protect 2008; 86: 389–393.
Chu WH, Gao NY, Deng Y, Krasner SW. Precursors of
dichloroacetamide, an emerging nitrogenous DBP formed
during chlorination or chloramination. Environ Sci Technol
2010; 44: 3908–3912.
Chu WH, Gao NY, Yin DQ, Deng Y, Templeton MR. Ozone-biological
activated carbon integrated treatment for removal of precursors
of halogenated nitrogenous disinfection by-products.
Chemosphere 2012; 86: 1087–1091.
Chu WH, Li CJ, Gao NY, Templeton MR, Zhang YS. Terminating
pre-ozonation prior to biological activated carbon filtration results
in increased formation of nitrogenous disinfection by-products
upon subsequent chlorination. Chemosphere 2015; 121: 33–38.
Cocace F, Speranza M. Protonated ozone: experimental detection
of O3H+ and evaluation of the proton affinity of ozone. Science
1994; 265: 208–209.
Cong J, Wen G, Huang TL, Deng LY, Ma J. Study on enhanced ozonation
degradation of para-chlorobenzoic acid by peroxymonosulfate in
aqueous solution. Chem Eng J 2015; 264: 399–403.
Cui JQ, Wang XJ, Yuan YL, Guo XW, Gu XY, Jian L. Combined ozone
oxidation and biological aerated filter processes for treatment
of cyanide containing electroplating wastewater. Chem Eng J
2014; 241: 184–189.
Da Silva LM, Franco DV, Forti JC, Jardim WF, Boodts JFC.
Characterisation of a laboratory electrochemical ozonation
system and its application in advanced oxidation processes.
JAppl Electrochem 2006; 36: 523–530.
Dash RR, Gaur A, Balomajumder C. Cyanide in industrial
wastewaters and its removal: a review on biotreatment.
JHazard Mater 2009; 163: 1–11.
Dong YM, Li K, Jiang PP, Wang GL, Miao HY, Zhang JJ, Zhang C.
Simple hydrothermal preparation of α-, β-, and γ-MnO2 and
phase sensitivity in catalytic ozonation. RSC Adv 2014; 4:
39167–39173.
Dowideit P, von Sonntag C. Reactions of ozone with ethene and
its methyl- and chlorine-substituted derivatives in aqueous
solution. Environ Sci Technol 1998; 32: 1112–1119.
Eisenhauer HR. The ozonization of phenolic wastes. J Water Pollut
Control Fed 1968; 40: 1887–1899.
Elahmadi MF, Bensalah N, Gadri A. Treatment of aqueous wastes
contaminated with Congo Red dye by electrochemical
oxidation and ozonation processes. J Hazard Mater 2009; 168:
1163–1169.
Eliasson B, Hirth M, Kogelschatz U. Ozone synthesis from oxygen
in dielectric barrier discharges. J Phys D Appl Phys 1987; 20:
1421–1437.
Eliasson B, Kogelschatz U. Modeling and applications of silent
discharge plasmas. IEEE Trans Plasma Sci 1991; 19: 309–323.
Etchepare R, Zaneti R, Azevedo A, Rubio J. Application of
flocculation-flotation followed by ozonation in vehicle wash
wastewater treatment/disinfection and water reclamation.
Desalin Water Treat 2015; 56: 1728–1736.
Fallon RJ, Vanderslice JT. Mechanism of ozone production by the
mercury sensitized reaction with oxygen. J Phys Chem 1960;
64: 505–507.
Fan XJ, Tao Y, Wei DQ, Zhang XH, Lei Y, Noguchi H. Removal of
organic matter and disinfection by-products precursors in a
hybrid process combining ozonation with ceramic membrane
ultrafiltration. Front Environ Sci Eng 2015; 9: 112–120.
Feng JR, Johnson DC, Lowery SN, Carey JJ. Electrocatalysis of anodic
oxygen-transfer reactions. J Electrochem Soc 1994; 141:
2708–2711.
Feuer H, Rubinstein H, Nielsen AT. Reaction of alkyl isocyanides
with ozone. A new isocyanate synthesis. J Org Chem 1958; 23:
1107–1109.
Foller PC, Kelsall GH. Ozone generation via the electrolysis of
fluoboric acid using glassy carbon anodes and air depolarized
cathodes. J Appl Electrochem 1993; 23: 996–1010.
García-Morales MA, Roa-Morales G, Barrera-Díaz C, Miranda VM,
Hernández PB, Silva TBP. Integrated advanced oxidation process
(ozonation) and electrocoagulation treatments for dye removal
in denim effluents. Int J Electrochem Sci 2013; 8: 8752–8763.
Gill EK, Laidler KJ. Some aspects of the theory of unimolecular gas
reactions. Proc R Soc A-Math Phys Eng Sci 1959; 250: 121–131.
Glaze WH. Drinking-water treatment with ozone. Environ Sci Technol
1987; 21: 224–230.
Gong XB, Takagi S, Huang HX, Matsumoto Y. A numerical study of
mass transfer of ozone dissolution in bubble plumes with an
Euler-Lagrange method. Chem Eng Sci 2007; 62: 1081–1093.
Gogate PR, Mededovic-Thagard S, McGuire D, Chapas G, Blackmon
J, Cathey R. Hybrid reactor based on combined cavitation
and ozonation: from concept to practical reality. Ultrason
Sonochem 2014; 21: 590–598.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
36C. Wei etal.: Ozonation in water treatment
Guo XY, Cai YP, Wei ZB, Hou HF, Yang X, Wang ZY. Treatment of diazo
dye C.I. Reactive Black 5 in aqueous solution by combined
process of interior microelectrolysis and ozonation. Water Sci
Technol 2013; 67: 1880–1885.
Gurol MD, Bremen WM. Kinetics and mechanism of ozonation of free
cyanide species in water. Environ Sci Technol 1985a; 19: 804–809.
Gurol MD, Bremen WM, Holden TE. Oxidation of cyanide in industrial
wastewater by ozone. Environ Prog 1985b; 4: 46–51.
Guzel-Seydim ZB, Greene AK, Seydim AC. Use of ozone in the food
industry. Food Sci Technol 2004; 37: 453–460.
Harcourt RD, Skrezenek FL, Wilson RM, Flegg RH. Ab initio valence
bond calculations for the ground state of ozone. J Chem Soc
Faraday Trans 1986; 82: 495–509.
Hashem TM, Zirlewagen M, Braun AM. Simultaneous photochemical
generation of ozone in the gas phase and photolysis of
aqueous reaction systems using one VUV light source. Water
Sci Technol 1997; 35: 41–48.
Hay PJ, Dunning TH, Goddard WA. Configuration interaction studies
of O3 and O3+. Ground and excited states. J Chem Phys 1975; 62:
3912–3924.
He SB, Wang BZ, Wang L, Jiang YF. Treating both wastewater and
excess sludge with an innovative process. J Environ Sci 2003;
15: 749–756.
Hegeler F, Akiyama H. Ozone generation by positive and negative
wire-to-plate streamer discharges. Jpn J Appl Phys 1997; 36:
5335–5339.
Hernández-Alonso MD, Coronado JM, Maira AJ, Soria J, Loddo V,
Augugliaro V. Ozone enhanced activity of aqueous titanium
dioxide suspensions for photocatalytic oxidation of free
cyanide ions. Appl Catal B 2002; 39: 257–267.
Hersh CK, Brabets RI, Platz GM, Swehla RJ, Kirsh DP. Vapor-liquid
equilibria of ozone-oxygen systems. Am Rocket Soc J 1960; 30:
264–266.
Hiragaki K, Ishimaru T, Nakanishi M, Muraki R, Nieda M, Yamabe C.
Generation of ozone foam and its application for disinfection.
Eur Phys J Appl Phys 2015; 71: 20810–20816.
Holgné J, Bader H, Haag WR, Staehelin J. Rate constants of reactions
of ozone with organic and inorganic compounds in water-III.
Inorganic compounds and radicals. Water Res 1985; 19:
993–1004.
Hong PKA, Zeng Y. Degradation of pentachlorophenol by ozonation
and biodegradability of intermediates. Water Res 2002; 36:
4243–4254.
Hou LW, Zhang H, Wang LG, Chen L. Ultrasound-enhanced magnetite
catalytic ozonation of tetracycline in water. Chem Eng J 2013;
229: 577–584.
Hu C, Xing ST, Qu JH, He H. Catalytic ozonation of herbicide 2,4-D
over cobalt oxide supported on mesoporous zirconia. J Phys
Chem C 2008; 112: 5978–5983.
Hu EL, Wu XB, Shang SM, Tao XM, Jiang SX, Gan L. Catalytic
ozonation of simulated textile dyeing wastewater using
mesoporous carbon aerogel supported copper oxide catalyst.
JClean Prod 2016; 112: 4710–4718.
Hübner U, von Gunten U, Jekel M. Evaluation of the persistence
of transformation products from ozonation of trace organic
compounds–a critical review. Water Res 2015; 68: 150–170.
Hunt NK, Marinas BJ. Kinetics of Escherichia coli inactivation with
ozone water. Water Res 1997; 31: 1355–1362.
Ikhlaq A, Brown DR, Kasprzyk-Hordern B. Mechanisms of catalytic
ozonation: an investigation into superoxide ion radical and
hydrogen peroxide formation during catalytic ozonation
on alumina and zeolites in water. Appl Catal B 2013; 129:
437–449.
Ikhlaq A, Brown DR, Kasprzyk-Hordern B. Catalytic ozonation for
the removal of organic contaminants in water on alumina. Appl
Catal B 2015; 165: 408–418.
Information Institute of Shanghai Science and Technology.
Translations of ozone and its applications, Series 2. Shanghai:
Shanghai Commercial Print Press, 1976: 28–61. (in Chinese).
Jenkins AC, Dipaolo FS. Some physical properties of pure liquid ozone
and ozone-oxygen mixtures. J Chem Phys 1956; 25: 296–301.
Jin PK, Jin X, Bjerkelund VA, Østerhus SW, Wang XCC, Yang L. A study
on the reactivity characteristics of dissolved effluent organic
matter (EfOM) from municipal wastewater treatment plant
during ozonation. Water Res 2016; 88: 643–652.
Jones WM, Davidson N. The thermal decomposition of ozone in a
shock tube. J Am Chem Soc 1962; 84: 2868–2878.
Jung H, Park H, Kim J, Lee JH, Hur HG, Myung NV, Choi H. Preparation
of riotic and abiotic iron oxide nanoparticles (IOnPs) and
their properties and applications in heterogeneous catalytic
oxidation. Environ Sci Technol 2007; 41: 4741–4747.
Kalemos A, Mavridis A. Electronic structure and bonding of ozone.
JChem Phys 2008; 129: 0543121–0543128.
Kasprzyk-Hordern B, Ziółek M, Nawrocki J. Catalytic ozonation and
methods of enhancing molecular ozone reactions in water
treatment. Appl Catal B 2003; 46: 639–669.
Katsoyiannis IA, Canonica S, von Gunten U. Efficiency and energy
requirements for the transformation of organic micropollutants
by ozone, O3/H2O2 and UV/H2O2. Water Res 2011; 45:
3811–3822.
Kepa U, Stanczyk-Mazanek E, Stepniak L. The use of the advanced
oxidation process in the ozone + hydrogen peroxide system
for the removal of cyanide from water. Desalination 2008; 223:
187–193.
Khadre MA, Yousef AE, Kim JG. Microbiological aspects of ozone
applications in food: a review. J Food Sci 2001; 66: 1242–1252.
Kim J, Korshin GV. Examination of in situ generation of hydroxyl
radicals and ozone in a flow-through electrochemical reactor.
Ozone Sci Eng 2008; 30: 113–119.
Kingsbury RS, Singer PC. Effect of magnetic ion exchange and
ozonation on disinfection by-product formation. Water Res
2013; 47: 1060–1072.
Kitayama J, Kuzumoto M. Theoretical and experimental study on
ozone generation characteristics of an oxygen-fed ozone
generator in silent discharge. J Phys D Appl Phys 1997; 30:
2453–2461.
Kitayama J, Kuzumoto M. Analysis of ozone generation from air in
silent discharge. J Phys D Appl Phys 1999; 32: 3032–3040.
Kogelschatz U. Dielectric-barrier discharges: their history, discharge
physics, and industrial applications. Plasma Chem Plasma
Process 2003; 23: 1–46.
Kopf P, Gilbert E, Eberle SH. TiO2 photocatalytic oxidation of
monochloroacetic acid and pyridine: influence of ozone.
JPhotochem Photobiol A Chem 2000; 136: 163–168.
Kornev J, Yavorovsky N, Preis S, Khaskelberg M, Isaev U, Chen
BN. Generation of active oxidant species by pulsed dielectric
barrier discharge in water-air mixtures. Ozone Sci Eng 2006;
28: 207–215.
Kornev I, Preis S, Gryaznova E, Saprykin F, Khryapov P, Khaskelberg
M, Yavorovskiy N. Aqueous dissolved oil fraction removed
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment37
with pulsed corona discharge. Ind Eng Chem Res 2014; 53:
7263–7267.
Kötz ER, Stucki S. Ozone and oxygen evolution on PbO2 electrodes in
acid solution. J Electroanal Chem 1987; 228: 407–415.
Kumar R, Bose P. Modeling free and copper-complexed cyanide
degradation in a continuous flow completely mixed ozone
contactor. Ind Eng Chem Res 2005; 44: 776–788.
Laera G, Cassano D, Lopez A, Pinto A, Pollice A, Ricco G, Mascolo G.
Removal of organics and degradation products from industrial
wastewater by a membrane bioreactor integrated with ozone or
UV/H2O2 treatment. Environ Sci Technol 2012; 46: 1010–1018.
Langlais B, Reckhow DA, Brink DR. Ozone in water treatment:
application and engineering. Chelsea, MI, USA: Lewis
Publishers, 1991.
Larcher S, Delbès G, Robaire B, Yargeau V. Degradation of
17 α-ethinylestradiol by ozonation-identification of the
by-products and assessment of their estrogenicity and toxicity.
Environ Int 2012; 39: 66–72.
Lawless D, Serpone N, Meisel D. Role of radicals and trapped holes
in photocatalysis. A pulse radiolysis study. J Phys Chem 1991;
95: 5166–5170.
Lee HM, Chang MB, Wei TC. Kinetic modeling of ozone generation
via dielectric barrier discharges. Ozone Sci Eng 2004; 26:
551–562.
Lee YH, Gerrity D, Lee M, Bogeat AE, Salhi E, Gamage S, Trenholm
RA, Wert EC, Snyder SA, von Gunten U. Prediction of
micropollutant elimination during ozonation of municipal
wastewater effluents: use of kinetic and water specific
information. Environ Sci Technol 2013; 47: 5872–5881.
Leeds AR. Relation between the temperature and volume in the
generation of ozone, with description of a new form of
ozonator. J Am Chem Soc 1879; 1: 8–18.
Levanov AV, Antipenko EE, Lunin VV. Primary stage of the reaction
between ozone and chloride ions in aqueous solution:
oxidation of chloride ions with ozone through the mechanism
of oxygen atom transfer. Russ J Phys Chem A 2012; 86:
519–522.
Levanov AV, Isaykina OY, Amirova NK, Antipenko EE, Lunin VV.
Photochemical oxidation of chloride ion by ozone in acid
aqueous solution. Environ Sci Pollut Res 2015; 22: 16554–
16569.
Levy H II. Normal atmosphere: large radical and formaldehyde
concentrations predicted. Science 1971; 173: 141–143.
Lin SH, Lin CM. Treatment of textile waste effluents by ozonation and
chemical coagulation. Water Res 1993; 27: 1743–1748.
Lin SH, Yeh KL. Looking to treat wastewater? Try ozone. Chem Eng
1993; 5: 112–116.
Lin SH, Chen ML. Treatment of textile wastewater by chemical
methods for reuse. Water Res 1997; 31: 868–876.
Lin C, Zhang WH, Yuan MY, Feng CH, Ren Y, Wei CH. Degradation
of polycyclic aromatic hydrocarbons in a coking wastewater
treatment plant residual by an O3/ultraviolet fluidized bed
reactor. Environ Sci Pollut Res 2014a; 21: 10329–10338.
Lin JL, Huang C, Dempsey B, Hu JY. Fate of hydrolyzed Al species in
humic acid coagulation. Water Res 2014b; 56: 314–324.
Lin T, Wu SK, Chen W. Formation potentials of bromate and brominated
disinfection by-products in bromide-containing water by
ozonation. Environ Sci Pollut Res 2014c;21: 13987–14003.
Liu S, Wang Q, Zhai X, Huang Q, Huang P. Improved pretreatment
(coagulation-floatation and ozonation) of younger landfill
leachate by microbubbles. Water Environ Res 2010; 82:
657–665.
Loeb BL, Thompson CM, Drago J, Takahara H, Baig S. Worldwide
ozone capacity for treatment of drinking water and wastewater:
a review. Ozone Sci Eng 2012; 34: 64–77.
Løgager T, Holcman J, Sehested K, Pedersen T. Oxidation of ferrous
ions by ozone in acidic solutions. Inorg Chem 1992; 31:
3523–3529.
Lukes P, Clupek M, Babicky V, Janda V, Sunka P. Generation of
ozone by pulsed corona discharge over water surface in hybrid
gas-liquid electrical discharge reactor. J Phys D: Appl Phys
2005; 38: 409–416.
Maleki A, Mahvi AH, Ebrahimi R, Zandsalimi Y. Study of
photochemical and sonochemical processes efficiency for
degradation of dyes in aqueous solution. Korean J Chem Eng
2010; 27: 1805–1810.
Mao YQ, Wang XM, Yang HW, Wang HY, Xie YFF. Effects of ozonation
on disinfection byproduct formation and speciation during
subsequent chlorination. Chemosphere 2014; 117: 515–520.
Marti EJ, Pisarenko AN, Peller JR, Dickenson ERV.
N-nitrosodimethylamine (NDMA) formation from the ozonation
of model compounds. Water Res 2015; 72: 262–270.
Martins RC, Quinta-Ferreira RM. A review on the applications of
ozonation for the treatment of real agro-industrial wastewaters.
Ozone Sci Eng 2014; 36: 3–35.
Masuda S, Koizumi S, Inoue J, Araki H. Production of ozone by
surface and glow discharge at cryogenic temperatures. IEEE
Trans Ind Appl 1988; 24: 928–933.
Matsumi Y, Kawasaki M. Photolysis of atmospheric ozone in the
ultraviolet region. Chem Rev 2003; 103: 4767–4781.
Mehrjouei M, Müller S, Möller D. Energy consumption of three
different advanced oxidation methods for water treatment: a
cost-effectiveness study. J Clean Prod 2014; 65: 178–183.
Mena E, Rey A, Acedo B, Beltrán FJ, Malato S. On
ozone-photocatalysis synergism in black-light induced
reactions: Oxidizing species production in photocatalytic
ozonation versus heterogeneous photocatalysis. Chem Eng J
2012; 204–206: 131–140.
Mert BK, Sivrioglu O, Yonar T, Ozciftci S. Treatment of jewelry
manufacturing effluent containing cyanide using ozone-based
photochemical advanced oxidation processes. Ozone Sci Eng
2014; 36: 196–205.
Mezzanotte V, Fornaroli R, Canobbio S, Zoia L, Orlandi M. Colour
removal and carbonyl by-production in high dose ozonation for
effluent polishing. Chemosphere 2013; 91: 629–634.
Miliordos E, Xantheas SS. On the bonding nature of ozone (O3) and
its sulfur-substituted analogues SO2, OS2, and S3: correlation
between their biradical character and molecular properties.
JAm Chem Soc 2014; 136: 2808–2817.
Molnar JJ, Agbaba JR, Dalmacija BD, Klašnja MT, Dalmacija MB,
Kragulj MM. A comparative study of the effects of ozonation
and TiO2-catalyzed ozonation on the selected chlorine
disinfection by-product precursor content and structure. Sci
Total Environ 2012; 425: 169–175.
Monge ME, George C, D’Anna B, Doussin JF, Jammoul, A, Wang JN,
Eyglunent G, Solignac G, Daële V, Mellouki A. Ozone formation
from illuminated titanium dioxide surfaces. J Am Chem Soc
2010; 132: 8234–8235.
Moussavi G, Aghapour AA, Yaghmaeian K. The degradation and
mineralization of catechol using ozonation catalyzed with
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
38C. Wei etal.: Ozonation in water treatment
MgO/GAC composite in a fluidized bed reactor. Chem Eng J
2014; 249: 302–310.
Mudliar R, Umare SS, Ramteke DS, Wate SR. Energy efficient-
advanced oxidation process for treatment of cyanide containing
automobile industry wastewater. J Hazard Mater 2009; 164:
1474–1479.
Mvula E, Naumov S, von Sonntag C. Ozonolysis of lignin models
in aqueous solution: anisole, 1,2-dimethoxybenzene,
1,4-dimethoxybenzene, and 1,3,5-trimethoxybenzene. Environ
Sci Technol 2009; 43: 6275–6282.
Nassour K, Brahami M, Nemmich S, Hammadi N, Zouzou N,
Tilmatine A. Comparative experimental study between surface
and volume DBD ozone generator. Ozone Sci Eng 2016; 38:
70–76.
Nawrocki J. Catalytic ozonation in water: controversies and
questions. Discussion paper. Appl Catal B 2013; 142–143:
465–471.
Nemes A, Fábián I, van Eldik R. Kinetics and mechanism of the
carbonate ion inhibited aqueous ozone decomposition. J Phys
Chem A 2000; 104: 7995–8000.
Neta P, Huie RE, Ross AB. Rate constants for reactions of inorganic
radicals in aqueous solution. J Phys Chem Ref Data 1988; 17:
1027–1284.
Nomoto Y, Ohkubo T, Kanazawa S, Adachi T. Improvement of ozone
yield by a silent-surface hybrid discharge ozonizer. IEEE Trans
Ind Appl 1995; 31: 1458–1462.
Nowell LH, Hoigné J. Photolysis of aqueous chlorine at sunlight and
ultraviolet wavelengths-II. hydroxyl radical production. Water
Res 1992; 26: 599–605.
Oulton R, Haase JP, Kaalberg S, Redmond CT, Nalbandian MJ,
Cwiertny DM. Hydroxyl radical formation during ozonation
of multiwalled carbon nanotubes: performance optimization
and demonstration of a reactive CNT filter. Environ Sci Technol
2015; 49: 3687–3697.
Pal A, Yew-Hoong Gin K, Yu-Chen Lin A, Reinhard M. Impacts of
emerging contaminants on freshwater resources: review of
recent occurrences, sources, fate and effects. Sci Total Environ
2010; 408: 6062–6069.
Parga JR, Shukla SS, Carrillo-Pedroza FR. Destruction of cyanide
waste solutions using chlorine dioxide, ozone and titania sol.
Waste Manage 2003; 23: 183–191.
Parrino F, Camera-Roda G, Loddo V, Palmisano G, Augugliaro V.
Combination of ozonation and photocatalysis for purification
of aqueous effluents containing formic acid as probe pollutant
and bromide ion. Water Res 2014; 50: 189–199.
Pavon S, Dorier JL, Hollenstein C, Ott P, Leyland P. Effects of
high-speed airflows on a surface dielectric barrier discharge.
JPhys D Appl Phys 2007; 40: 1733–1741.
Pereira Rde O, de Alda ML, Joglar J, Daniel LA, Barceló D.
Identification of new ozonation disinfection byproducts of
17 β-estradiol and estrone in water. Chemosphere 2011; 84:
1535–1541.
Pines DS, Reckhow DA. Effect of dissolved cobalt (II) on the
ozonation of oxalic acid. Environ Sci Technol 2002; 36:
4046–4051.
Pinkernell U, von Gunten U. Bromate minimization during ozonation:
mechanistic considerations. Environ Sci Technol 2001; 35:
2525–2531.
Prieto-Rodríguez L, Oller I, Klamerth N, Agüera A, Rodríguez
EM, Malato S. Application of solar AOPs and ozonation for
elimination of micropollutants in municipal wastewater
treatment plant effluents. Water Res 2013; 47: 1521–1528.
Punzi M, Nilsson F, Anbalagan A, Svensson BM, Jönsson K,
Mattiasson B, Jonstrup M. Combined anaerobic-ozonation
process for treatment of textile wastewater: removal of acute
toxicity and mutagenicity. J Hazard Mater 2015; 292: 52–60.
Qi F, Chu W, Xu BB. Ozonation of phenacetin in associated with a
magnetic catalyst CuFe2O4: the reaction and transformation.
Chem Eng J 2015; 262: 552–562.
Qu RJ, Xu BZ, Meng LJ, Wang LS, Wang ZY. Ozonation o f indigo
enhanced by carboxylated carbon nanotubes: performance
optimization, degradation products, reaction mechanism and
toxicity evaluation. Water Res 2015; 68: 316–327.
Quiñones DH, Álvarez PM, Rey A, Contreras S, Beltrán FJ. Application
of solar photocatalytic ozonation for the degradation of
emerging contaminants in water in a pilot plant. Chem Eng J
2015; 260: 399–410.
Reaume MJ, Seth R, McPhedran KN, Silva EFd, Porter LA. Effect
of media on biofilter performance following ozonation of
secondary treated municipal wastewater effluent: sand vs.
GAC. Ozone Sci Eng 2015; 37: 143–153.
Rey A, García-Muñoz P, Hernández-Alonso MD, Mena E, García-
Rodríguez S, Beltrán FJ. WO3-TiO2 based catalysts for the
simulated solar radiation assisted photocatalytic ozonation of
emerging contaminants in a municipal wastewater treatment
plant effluent. Appl Catal B 2014; 154–155: 274–284.
Rice RG, Robson CM, Miller GW, Hill AG. Uses of ozone in drinking
water treatment. J Am Water Work Assoc 1981; 73: 44–57.
Richardson SD, Thruston AD, Caughran TV, Chen PH, Collette TW,
Floyd TL. Identification of new ozone disinfection byproducts in
drinking water. Environ Sci Technol 1999; 33: 3368–3377.
Riebel AH, Erickson RE, Abshire CJ, Bailey PS. Ozonation of carbon-
nitrogen bonds. I. Nucleophilic arrack of ozone. J Am Chem Soc
1960; 82: 1801–1807.
Robert DH, Iraj R, Robert GR. Experimental study of the production
of NO, N2O, and O3 in a simulated atmospheric corona. Ind Eng
Chem Res 1988; 27: 1264–1269.
Robinson JA, Bergougnou MA, Cairns WL, Castle GSP, Inculet II.
A new type of ozone generator using taylor cones on water
surfaces. IEEE Trans Ind Appl 1998; 34: 1218–1224.
Rosenfeldt FJ, Linden KG, Canonica S, von Gunten U. Comparison of
the efficiency of ˙OH radical formation during ozonation and the
advanced oxidation processes O3/H2O2 and UV/H2O2. Water Res
2006; 40: 3695–3704.
Roth JA, Sullivan DE. Solubility of ozone in water. Ind Eng Chem
Fundam 1981; 20: 137–140.
Roy D, Wong PK, Engelbrecht RS, Chian ES. Mechanism of
enteroviral inactivation by ozone. Appl Environ Microbiol 1981;
41: 718–723.
Rubin MB. The history of ozone. II. 1869–1899. Bull Hist Chem 2002;
27: 81–106.
Salam Z, Facta M, Amjad M, Buntat Z. Design and implementation
of a low cost, high yield dielectric barrier discharge ozone
generator based on the single switch resonant converter. IET
Power Electron 2013; 6: 1583–1591.
Salvermoser M, Murnick DE, Kogelschatz U. Influence of water vapor
on photochemical ozone generation with efficient 172nm
Xenon excimer lamps. Ozone Sci Eng 2008; 30: 228–237.
Samaranayake WJM, Miyahara Y, Namihira T, Katsuk S, Hackam
R, Akiyama H. Ozone generation in dry air using pulsed
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment39
discharges with and without a solid dielectric layer. IEEE Trns
Dielectr Electr Insul 2011; 8: 687–697.
Sánchez-Castillo MA, Carrillo-Pedroza FR, Fraga-Tovar F,
Soria-Aguilar MD. Ozonation of cyanide catalyzed by activated
carbon. Ozone Sci Eng 2015; 37: 240–251.
Schiener P, Nachaiyasit S, Stuckey DC. Production of soluble
microbial products (SMPs) in an anaerobic baffled reactor:
composition, biodegradability and the effect of process
parameters. Environ Technol 1998; 19: 391–400.
Schnell RC, Oltmans SJ, Neely RR, Endres MS, Molenar JV, White
AB. Rapid photochemical production of ozone at high
concentrations in a rural site during winter. Nat Geosci 2009;
2: 120–122.
Schwarzenbach RP, Escher BI, Fenner K, Hofstetter TB, Johnson CA,
von Gunten U, Wehrli B. The challenge of micropollutants in
aquatic systems. Science 2006; 313: 1072–1077.
Sharma KP, Sharma S, Sharma S, Singh PK, Kumar S, Grover R,
Sharma PK. A comparative study on characterization of textile
wastewaters (untreated and treated) toxicity by chemical and
biological tests. Chemosphere 2007; 69: 48–54.
Shin D, Jian M, Cui MC, Na S, Khim J. Enhanced removal of
dichloroacetonitrile from drinking water by the combination of
solar-photocatalysis and ozonation. Chemosphere 2013; 93:
2901–2908.
Šimek M, Člupek M. Efficiency of ozone production by pulsed
positive corona discharge in synthetic air. J Phys D Appl Phys
2002; 35: 1171–1175.
Somboonchai W, Nopharatana M, Songkasiri W. Kinetics of cyanide
oxidation by ozone in cassava starch production process.
JFood Eng 2008; 84: 563–568.
Sonntag C, von Gunten U. Chemistry of ozone in water and
wastewater treatment: from basic principles to applications.
UK: IWA publishing; 2012.
Staehelin J, Bühler RE, Hoigné J. Ozone decomposition in
water studied by pulse radiolysis. 2. OH and HO4 as chain
intermediates. J Phys Chem 1984; 88: 5999–6004.
Stalter D, Magdeburg A, Oehlmann J. Comparative toxicity
assessment of ozone and activated carbon treated sewage
effluents using an in vivo test battery. Water Res 2010; 44:
2610–2620.
Sun BC, Gao MP, Arowo M, Wang JX, Chen JF, Meng H, Shao L.
Ozonation of acid red 14 in the presence of inorganic salts in a
microporous tube-in-tube microchannel reactor. Ind Eng Chem
Res 2014; 53: 19071–19076.
Tachikawa M, Yamanaka K. Synergistic disinfection and removal
of biofilms by a sequential two-step treatment with ozone
followed by hydrogen peroxide. Water Res 2014; 64: 94–101.
Thorp CE. Bibliography of ozone technology. Chicago: Armour
Research Foundation, Illinois Institute of Technology, 1954.
Toby S. Chemiluminescence in the reactions of ozone. Chem Rev
1984; 84: 277–285.
Tokuaga O, Suzuki N. Radiation chemical reactions in NOx and SO2
removals from flue gas. Radiat Phys Chem 1984; 24: 145–165.
Tomiyasu H, Fukutomi H, Gordon G. Kinetics and mechanism of
ozone decomposition in basic aqueous solution. Inorg Chem
1985; 24: 2962–2966.
Torres-Blancas T, Roa-Morales G, Barrera-Díaz C, Ureña-Nuñez F,
Cruz-Olivares J, Balderas-Hernandez P, Natividad R. Ozonation
of indigo carmine enhanced by Fe/Pimenta dioica L. Merrill
particles. Int J Photoenergy 2015; 2015: 608412.
Torres-Socías ED, Fernández-Calderero I, Oller I, Trinidad-Lozano MJ,
Yuste FJ, Malato S. Cork boiling wastewater treatment at pilot
plant scale: comparison of solar photo-Fenton and ozone (O3,
O3/H2O2). Toxicity and biodegradability assessment. Chem Eng
J 2013; 234: 232–239.
Trambarulo R, Ghosh SN, Burrus CA, Gordy W. The molecular
structure, dipole moment, and g factor of ozone from its
microwave spectrum. J Chem Phys 1953; 21: 851–855.
Turhan K, Ozturkcan SA. Decolourization and degradation
of reactive dye in aqueous solution by ozonation in a
semi-batchbubble column reactor. Water Air Soil Pollut 2013;
224: 1353.
USEPA. National primary drinking water regulations: disinfection
and disinfection byproducts. Federal Reg 1998; 63: 69390–
69476.
Uslu M, Seth R, Jasim S, Tabe S, Biswas N. Reaction kinetics of
ozone with selected pharmaceuticals and their removal
potential from a secondary treated municipal wastewater
effluent in the Great Lakes Basin. Ozone Sci Eng 2015; 37:
36–44.
von Gunten U. Ozonation of drinking water: part II. Disinfection
and by-product formation in presence of bromide, iodide or
chlorine. Water Res 2003a; 37: 1469–1487.
von Gunten U. Ozonation of drinking water: part I. Oxidation kinetics
and product formation. Water Res 2003b; 37: 1443–1467.
von Sonntag C, von Gunten U. Chemistry of ozone in water and
wastewater treatment: from basic principles to applications.
London: IWA Publishing; 2012.
Wang CW, Liang CJ. Oxidative degradation of TMAH solution with UV
persulfate activation. Chem Eng J 2014; 254: 472–476.
Wang HJ, Yuan S, Zhan JH, Wang YJ, Yu G, Deng SB, Huang J, Wang B.
Mechanisms of enhanced total organic carbon elimination from
oxalic acid solutions by electro-peroxone process. Water Res
2015; 80: 20–29.
Wang YX, Xie YB, Sun HQ, Xiao JD, Cao HB, Wang SB. Efficient
catalytic ozonation over reduced graphene oxide for
p-hydroxylbenzoic acid (PHBA) destruction: active site and
mechanism. ACS Appl Mater Interfaces 2016; 8: 9710–9720.
Waterman TE, Kirsh DP, Brabets RI. Thermal conductivity of liquid
ozone. J Chem Phys 1958; 29: 905–908.
Wei XX, Zhang ZY, Fan QL, Yuan XY, Guo DS. The effect of treatment
stages on the coking wastewater hazardous compounds and
their toxicity. J Hazard Mater 2012; 239–240: 135–141.
Wei LS, Yuan DK, Zhang YF, Hu ZJ, Dong GP. The influence of inert
gas addition on electric breakdown utilizing dielectric barrier
discharge in ozone generation in air. Ozone Sci Eng 2014; 36:
526–531.
Wei Q, Qiao SF, Sun BC, Zou HK, Chen JF, Lei S. Study on the
treatment of simulated coking wastewater by O3 and O3/
Fenton processes in a rotating packed bed. RSC Adv 2015; 5:
93386–93393.
Weiss J. Investigations on the radical HO2˙ in solution. Trans Faraday
Soc 1935; 31: 668–681.
WHO. World Health Organization: guidelines for drinking-water
quality. 2011.
Wilde ML, Montipó S, Martins AF. Degradation of β-blockers
in hospital wastewater by means of ozonation and Fe2+/
ozonation. Water Res 2014; 48: 280–295.
Wu J, Ma LM, Chen YL, Cheng YQ, Liu Y, Zha XS. Catalytic ozonation
of organic pollutants from bio-treated dyeing and finishing
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
40C. Wei etal.: Ozonation in water treatment
wastewater using recycled waste iron shavings as a catalyst:
removal and pathways. Water Res 2016a; 92: 140–148.
Wu Q, Li WT, Yu WH, Li Y, Li AM. Removal of fluorescent dissolved
organic matter in biologically treated textile wastewater by
ozonation-biological aerated filter. J Taiwan Inst Chem Eng
2016b; 59: 359–364.
Xu XJ. Dielectric barrier discharge-properties and applications. Thin
Solid Films 2001; 390: 237–242.
Yagi S, Tanaka M. Mechanism of ozone generation in air-fed
ozonisers. J Phys D Appl Phys 1979; 12: 1509–1520.
Yan ZM, Zhang Y, Yuan HY, Tian Z, Yang M. Fish larval deformity
caused by aldehydes and unknown byproducts in ozonated
effluents from municipal wastewater treatment systems. Water
Res 2014; 66: 423–429.
Yehia A. Consumption of the electric power inside silent discharge
reactors. Phys Plasmas 2015; 22: 013506.
Yu L, Wang DS, Ye DQ. Solar photocatalytic ozonation of emerging
contaminants detected in municipal wastewater treatment
plant effluents by magnetic MWCNTs/TiO2 nanocomposites.
RSC Adv 2015; 5: 96896–96904.
Zeevalkink JA, Visser DC, Arnoldy P, Boelhouwer C. Mechanism and
kinetics of cyanide ozonation in water. Water Res 1980; 14:
1375–1385.
Zeng ZQ, Zou HK, Li X, Sun BC, Chen JF, Shao L. Ozonation of phenol
with O3/Fe(II) in acidic environment in a rotating packed bed.
Ind Eng Chem Res 2012; 51: 10509–10516.
Zhang ZD. Inorganic chemistry, 1st ed. Hefei: University of Science
and Technology of China Press, 2008 (in Chinese).
Zhang T, Wei CH, Feng CH, Zhu JL. A novel airlift reactor enhanced
by funnel internals and hydrodynamics prediction by the CFD
method. Bioresour Technol 2012; 104: 600–607.
Zhang XB, Dong WY, Yang W. Decolourization efficiency and kinetics
of typical reactive azo dye RR2 in the homogeneous Fe(II)
catalyzed ozonation process. Chem Eng J 2013a; 233: 14–23.
Zhang S, Wang D, Quan X, Zhou L, Zhang XW. Multi-walled carbon
nanotubes immobilized on zero-valent iron plates (Fe0-CNTs) for
catalytic ozonation of methylene blue as model compound in a
bubbling reactor. Sep Purif Technol 2013b; 116: 351–359.
Zhang L, Tejada-Martínez AE, Zhang Q, Lei HX. Evaluating hydraulic
and disinfection efficiencies of a full-scale ozone contactor
using a RANS-based modeling framework. Water Res 2014a;
52: 155–167.
Zhang SH, Zheng J, Chen ZQ. Combination of ozonation and
biological aerated filter (BAF) for bio-treated coking
wastewater. Sep Purif Technol 2014b; 132: 610–615.
Zhang T, Croué JP. Catalytic ozonation not relying on hydroxyl radical
oxidation: a selective and competitive reaction process related to
metal-carboxylate complexes. Appl Catal B 2014c; 144: 831–839.
Zhang FZ, Wei CH, Hu Y, Wu HZ. Zinc ferrite catalysts for ozonation of
aqueous organic contaminants: phenol and bio-treated coking
wastewater. Sep Purif Technol 2015; 156: 625–635.
Zhao L, Ma J, Sun ZZ, Liu HL. Mechanism of heterogeneous catalytic
ozonation of nitrobenzene in aqueous solution with modified
ceramic honeycomb. Appl Catal B 2009a; 89: 326–334.
Zhao L, Sun ZZ, Ma J. Novel relationship between hydroxyl radical
initiation and surface group of ceramic honeycomb supported
metals for the catalytic ozonation of nitrobenzene in aqueous
solution. Environ Sci Technol 2009b; 43: 4157–4163.
Zhao H, Dong YM, Jiang PP, Wang GL, Zhang JJ, Zhang C. ZnAl2O4 as
a novel high-surface-area ozonation catalyst: one-step green
synthesis, catalytic performance and mechanism. Chem Eng J
2015; 260: 623–630.
Zheng TL, Wang QH, Zhang T, Shi ZN, Tian YL, Shi SS, Smale
N, Wang J. Microbubble enhanced ozonation process for
advanced treatment of wastewater produced in acrylic fiber
manufacturing industry. J Hazard Mater 2015; 287: 412–420.
Zhou XJ, Guo WQ, Yang SS, Ren NQ. A rapid and low energy
consumption method to decolourize the high concentration
triphenylmethane dye wastewater: operational parameters
optimization for the ultrasonic-assisted ozone oxidation
process. Bioresour Technol 2012; 105: 40–47.
Zhu SN, Hui KN, Hong XT, Hui KS. Catalytic ozonation of basic
yellow 87 with a reusable catalyst chip. Chem Eng J 2014; 242:
180–186.
Zhu MQ, Gao NY, Chu WH, Zhou SQ, Zhang ZD, Xu YQ, Dai Q. Impact
of pre-ozonation on disinfection by-product formation and
speciation from chlor(am)ination of algal organic matter
of Microcystis aeruginosa. Ecotox Environ Safe 2015; 120:
256–262.
Zhuang Y, Ren HQ, Geng JJ, Zhang YY, Zhang Y, Ding LL, Xu K.
Inactivation of antibiotic resistance genes in municipal
wastewater by chlorination, ultraviolet, and ozonation
disinfection. Environ Sci Pollut Res 2015; 22: 7037–7044.
Zimmermann SG, Wittenwiler M, Hollender J, Krauss M, Ort C,
Siegrist H, von Gunten U. Kinetic assessment and modeling
of an ozonation step for full-scale municipal wastewater
treatment: micropollutant oxidation, by-product formation and
disinfection. Water Res 2011; 45: 605–617.
Zou XL. Combination of ozonation, activated carbon, and biological
aerated filter for advanced treatment of dyeing wastewater for
reuse. Environ Sci Pollut Res 2015; 22: 8174–8181.
Zuo YG, Hoigné J. Formation of hydrogen peroxide and depletion
of oxalic acid in atmospheric water by photolysis of iron(III)-
oxalato complexes. Environ Sci Technol 1992; 26: 1014–1022.
Bionotes
Chaohai Wei
School of Environment and Energy, South
China University of Technology, Guangzhou,
510006, P.R. China
cechwei@scut.edu.cn
Chaohai Wei obtained his Bachelor’s degree in Applied Chemistry
from China University of Geosciences and his Master’s degree in
Environmental Engineering from Harbin Institute of Technology. He
completed his PhD in Chemical Engineering at South China Univer-
sity of Technology (SCUT) and was promoted as a professor in SCUT
by 1999. Prof. Wei has presided over 103 research projects and pub-
lished over 390 peer-reviewed papers. Profoundly, he has designed
over 30 practical projects serving for actual wastewater treatment
plants. His research interests are pollution control theories in
industrial wastewater and river basin, particularly focusing on novel
reactors and processes for wastewater treatment, energy saving and
energy recovery from wastewater treatment, and integration and
optimization of wastewater treatment systems.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
C. Wei etal.: Ozonation in water treatment41
Fengzhen Zhang
School of Environment and Energy, South
China University of Technology, Guangzhou,
510006, P.R. China
Fengzhen Zhang graduated from Shenzhen University with a
Master’s degree in Applied Chemistry in 2013 and from Northwest
University for Nationalities with a Bachelor’s degree in Chemical
Engineering and Technology in 2010. He joined South China Univer-
sity of Technology as a doctoral candidate in 2013 under Prof. Wei’s
supervision. His research interests focus on catalytic ozonation of
industrial wastewater and high-performance ozonation reactor. He
has obtained a National Scholarship for Postgraduates and is the
winner of Environmental Science: Processes & Impacts oral prize
during the 8th National Conference on Environmental Chemistry.
Yun Hu
School of Environment and Energy, South
China University of Technology, Guangzhou,
510006, P.R. China
Yun Hu obtained her PhD degree in Applied Chemistry from Osaka
Prefecture University in 2006. She was elected as an Outstand-
ing Young Teacher in the Hundred Talents Program by South China
University of Technology (SCUT) in 2007, after 2years serving as
Research Fellow in Japan Society for the Promotion of Science. She
is now a professor in SCUT, concentrating on the pollution control
and resource recovery from contaminated water or air by means
of photocatalysis and adsorption. Prof. Hu has published over 50
papers, including two recent research articles in Applied Catalysis
B: Environmental.
Chunhua Feng
School of Environment and Energy, South
China University of Technology, Guangzhou,
510006, P.R. China
Chunhua Feng graduated with a PhD degree in Chemical Engineer-
ing from Hong Kong University of Science and Technology in 2007.
Dr. Feng is now a professor at School of Environment and Engineer-
ing, South China University of Technology (SCUT), China. He is
serving as an associate director for Center of Environment Science,
SCUT. He was elected in Program for New Century excellent talents
in University, Ministry of Education, China (2012). His research
interests lie in energy/resource recovery from wastes and bioelec-
trochemical technology for wastewater treatment.
Haizhen Wu
School of Bioscience and Bioengineering,
South China University of Technology,
Guangzhou, 510006, P.R. China
Haizhen Wu obtained her PhD degree in Biological Engineering
from South China University of Technology (SCUT) in 2008. She
is currently an associate professor in School of Bioscience and
Bioengineering, SCUT. Her research interests are concentrated on
the biodegradation of pollutants in contaminated soil as well as
wastewater, the identification of functional micro-organisms and the
development of high-performance bio-reactors. She has published
more than 40 peer-reviewed papers and presided twice over the
National Natural Science Foundations of China.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
Rev Chem Eng 2016 | Volume x | Issue x
Graphical abstract
Chaohai Wei, Fengzhen Zhang, Yun
Hu, Chunhua Feng and Haizhen Wu
Ozonation in water treatment: the
generation, basic properties of
ozone and its practical application
DOI 10.1515/revce-2016-0008
Rev Chem Eng 2016; x(x): xxx–xxx
Review: Ozone can be generated by
pulse corona discharge, principally
avoiding excess thermal decomposi-
tion of ozone, and potentially in-situ
reacting with pollutants dispersed
throughout discharge gap.
Keywords: energy consumption;
ozone generation; ozone reactor;
physicochemical properties; water
treatment.
- 10.1515/revce-2016-0008
Downloaded from De Gruyter Online at 09/14/2016 03:58:01AM
via University of Ottawa OCUL
