catalysts
Review
Tungsten-Based Catalysts for Environmental Applications
Fabien Can *, Xavier Courtois *
and Daniel Duprez
CNRS, UMR7285, Institut de Chimie des Milieux et Matériaux de Poitiers (IC2MP), Université de Poitiers,
4 rue Michel Brunet, CEDEX 09, 86073 Poitiers, France; daniel.duprez@univ-poitiers.fr
* Correspondence: fabien.can@univ-poitiers.fr (F.C.); xavier.courtois@univ-poitiers.fr (X.C.)
Abstract: This review aims to give a general overview of the recent use of tungsten-based catalysts
for wide environmental applications, with first some useful background information about tungsten
oxides. Tungsten oxide materials exhibit suitable behaviors for surface reactions and catalysis such
as acidic properties (mainly Brønsted sites), redox and adsorption properties (due to the presence
of oxygen vacancies) and a photostimulation response under visible light (2.6–2.8 eV bandgap).
Depending on the operating condition of the catalytic process, each of these behaviors is tunable by
controlling structure and morphology (e.g., nanoplates, nanosheets, nanorods, nanowires, nanomesh,
microflowers, hollow nanospheres) and/or interactions with other compounds such as conductors
(carbon), semiconductors or other oxides (e.g., TiO2 ) and precious metals. WOx particles can be also
dispersed on high specific surface area supports. Based on these behaviors, WO3 -based catalysts
were developed for numerous environmental applications. This review is divided into five main
parts: structure of tungsten-based catalysts, acidity of supported tungsten oxide catalysts, WO3
catalysts for DeNOx applications, total oxidation of volatile organic compounds in gas phase and gas
sensors and pollutant remediation in liquid phase (photocatalysis).
Keywords: tungsten; WO3 ; deNOx ; VOC; photocatalysis; sensor
Citation: Can, F.; Courtois, X.;
Duprez, D. Tungsten-Based Catalysts
for Environmental Applications.
Catalysts 2021, 11, 703. https://
1. Introduction
doi.org/10.3390/catal11060703
Tungsten is the metal having the highest melting point (3410 ◦ C) and a density
(19.3 g cm−3 ) close to that of gold (19.32 g cm−3 ). α-W (lattice type: body-centered cube) is
the crystallographic stable form of tungsten (lattice parameter: 0.3165 nm) [1]. β-W is a
metastable cubic (type A15) form of tungsten, first found in products of WO3 reduction by
hydrogen [2]. γ-W is an fcc form of tungsten only detected in thin film. Owing to its unique
physical properties, tungsten is widely used in refractory alloys. While group 8–11 elements
are currently used as nanoparticles of metals in catalysis, W-based heterogeneous catalysts contain tungsten in the form of oxides, sulfides, carbides or heteropolytungstates [3].
Although less employed than molybdenum sulfides, tungsten sulfides are essential components of hydrotreating catalysts [4,5]. More recently, catalysts and photocatalysts based
on tungsten sulfides were developed for application in hydrogen production by water
splitting [6–8]. Utilization of tungsten carbides for electrochemical applications was also
developed in the domain of hydrogen evolution reaction [9,10]. Due to their high solubility in water, heteropolytungstates serve as precursors of tungsten in the preparation of
W-based catalysts [11,12]. They are also utilized in many organic syntheses, especially in
oxidation reactions [13]. Associated with metals such cobalt, heteropolytungstates are also
excellent water-splitting catalysts [14].
Tungsten-based catalysts are currently utilized for environmental applications (e.g.,
DeNOx , oxidation in gas and in liquid phases, sensors, photocatalysis). In these catalytic
systems, tungsten is nearly always in an oxidized form, either as tungsten oxide particles
or in strong interaction with specific supports or dopants. The structures of tungsten
oxides, supported or not on other oxides, will be reviewed in Section 2. One of the specificities of tungsten oxides is their acid properties that are examined in Section 3. Catalytic
Academic Editors: Annemie Bogaerts
and Jean-François Lamonier
Received: 11 May 2021
Accepted: 28 May 2021
Published: 2 June 2021
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applications are then reviewed in the following sections: selective catalytic reduction of
NOx by ammonia over WO3 -V2 O5 and other WO3 -supported catalysts (Section 4), other
DeNOx applications (Section 5), total oxidation of pollutants in gas phase and gas sensors
(Section 6) and total oxidation of pollutants in liquid phase with special insight into photocatalytic processes (Section
7). Selective oxidation in gas or liquid phase (for instance, in
ε
the cyclohexanol-to-ε-caprolactone process), as well as the area of heteropolytungstates,
will not be reviewed in these sections. Readers interested in these topics are invited to
read the recent review by Dai et al. [15]. Due to the high number of works published on
the catalytic properties of tungsten-based catalysts, Sections 3–7 will be restricted to the
2014–2020 period, occasionally including some earlier reference papers.
2. Structure of Tungsten-Based Catalysts
Although it is important to stress that the bulk crystal structure may have a limited
impact on catalysis since reactions occur at the surface of the crystalline solids, which may
not exhibit the same chemical composition as the bulk, the structures of tungsten-based
catalysts are summarized in this section to offer an in-depth introduction to the materials
presented in this review.
2.1. Structure of Unsupported Tungsten Oxides
No less than seven tungsten oxides were identified in the tungsten–oxygen system [1,16]. However, three oxides are currently more often encountered in catalysis and in
β
most applications [3]: WO3 (yellow oxide), WO2.9 or β-tungsten
oxide (blue oxide) and
WO2.72 or γ-tungsten
oxide (violet oxide).
γ
2.1.1. Tungsten Trioxide
Tungsten trioxide has several allotropic forms, mainly two monoclinic structures
α
(α-WO3 and
γ γ-WO3 ), a triclinic structure
β (β-WO3 ) and a hexagonal form (h-WO3 ). All
these forms of WO3 consist of corner-sharing octahedra of WO6 units. Monoclinic and
triclinic structures form a quasicubic arrangement of the octahedra. They differ by the
angles of distortion between the adjacent octahedra. Triclinic WO3 is stable only at low
temperature (T < 17 ◦ C) [17]. Ab initio calculations showed that the ideal cubic arrangement
of WO6 blocks is not stable and would tend to tetragonal structure [18]. Sun et al. recently
compared the potentialities of monoclinic WO3 (m-WO3 ) and hexagonal WO3 (h-WO3 ) in
electrochemical and gas adsorption applications [19]. The structures of the two forms of
WO3 are represented in Figure 1.
Figure 1. Structure of hexagonal WO3 (a) and monoclinic WO3 (b) projected along the (001) direction.
Reprinted from Sun et al. [19] with permission from the American Chemical Society.
While monoclinic WO3 possesses arrangements of small rhomboid tunnels whose
great diagonals are alternatively along x and y axes, hexagonal WO3 has a network of large
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hexagonal tunnels alternating with small triangular ones. Accessibility of internal surface
is then better for h-WO3 than for m-WO3 . This was evidenced in the work of Sun et al.
by a higher specific capacitance of h-WO3 with facilitated proton transportation along
the tunnels.
−
Szilágyi et al. investigated the behavior of m- and h-WO3 for the photocatalytic reaction of methyl orange decomposition [20]. The two materials were prepared by annealing
hexagonal ammonium tungsten bronze in air or N2 . Hexagonal WO3 is formed by annealing the tungsten bronze (NH4 )x WO3−y at moderate temperature (470–550 ◦ C), while
−
monoclinic WO3 is formed at higher temperatures (600–650 ◦ C). Decomposition processes
of the hexagonal ammonium tungsten bronze were earlier investigated by the same group,
who showed that residual ammonia and/or ammonium ions are vital for stabilizing the
hexagonal structure [21]. Blue oxides are formed when (NH4 )x WO3−y is decomposed in
N2 , which shows the presence of reduced tungsten oxides. On the contrary, yellow oxides
are obtained by decomposing the tungsten bronze in air. However, XPS of the oxidized
materials shows that small amounts of W5+ and W4+ are still present in the h-WO3 ox,
while tungsten in m-WO3 ox is entirely in the form of W6+ . Monoclinic WO3 ox is more
active than hexagonal WO3 ox in the photocatalysis reaction because the electron–hole recombination is less probable in WO3 having 100% W6+ (no defect sites). In addition to XRD,
Raman spectroscopy is a good technique to distinguish hexagonal and monoclinic WO3
phases (Figure 2). XRD spectra are consistent with m-WO3 (ICDD file 43-1035) and h-WO3
−
(ICDD file 85-2460). Peak width broadening observed on reduced
samples is indicative of
−
distortion and creations of defects in the structure. O-W-O stretching bands allow to clearly
distinguish m-WO3 (two bands at 714 and 806 cm−1 ) and h-WO3 (three bands at 651, 693
and 786 cm−1 ). By contrast, O-W-O deformation vibrations, in the 260–330 cm−1 range,
are virtually recorded at the same wavenumber for the two forms of WO3 . For that reason,
deformation vibration bands cannot be used for the characterization of m- and h-WO3 .
Figure 2. XRD and Raman spectra of monoclinic WO3 (m-WO3 ) and hexagonal WO3 (h-WO3 ) oxidized (air treatment) and reduced (N2 treatment). Reprinted from Szilágyi et al. [20] with permission
from Elsevier.
If the presence of ammonium ions allows h-WO3 to be stabilized, it is also a key factor
in controlling the shape of nanorod crystals [22]. NH4 + ions are preferably adsorbed on the
(001) facets and block the crystal growing along this axis (Figure 3). Hexagonal nanowires
−
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of WO3 were also prepared as anodic materials of Li-ion batteries [23]. Hydrothermal
treatment of lithium tungstate–lithium sulfate mixed solutions in HCl medium leads to
typical nanowires, as shown in Figure 4.
Figure 3. Effect of ammonium ions on the growth orientation of hexagonal single crystal of WO3
nanorods (hydrothermal synthesis from ammonium tungstate). Reprinted from Zhu et al. [22] with
permission from the Royal Society of Chemistry.
Figure 4. TEM image of h-WO3 nanowires (left) and HRTEM image of an individual wire growing in
the (001) direction. Reprinted from Gu et al. [23] with permission from Elsevier.
Crystal structures, phase transition and physical properties of nanostructured WO3 oxides have been reviewed by Zheng et al. [24]. Numerous synthesis methods were reported
for the preparation of films, ribbons, nanowires, nanotubes, nanorods, etc. In many cases,
hexagonal WO3 is observed in these nanostructures. For instance, leaflike nanoplatelets
were prepared by dehydration of orthorhombic tungstite H2 WO4 to monoclinic WO3 [25].
2.1.2. Tungsten Trioxide WO2.9 Blue Oxide (β-Tungsten Oxide W20 O58 ) and Other
Suboxides WO3−δ (δ < 0.13)
Tungsten suboxides phases with formulae Wn O3n−1 and Wn O3n−2 were first described
by Magnéli in 1950 [26,27]. They were fully described by Tilley in 1995 [28]. The lattice
(symmetry P2/m) consists of blocks of WO6 octahedra joined by sharing corners (as in
Catalysts 2021, 11, 703
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δ
β
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−
−
m-WO3 ) with certain octahedra sharing edges along a zig-zag dislocation line, as illustrated
in Figure 5.
β
Figure 5. Structure of β-tungsten
oxide WO2.9 , consisting of WO6 blocks joined by sharing corners (ideal WO3 oxide) or by
sharing edges. WO6 octahedra sharing edges create zig-zag distortion inside the structure. Tungsten atoms located along
the zig-zag stripes are labeled. Reprinted from [29].
WO3−−x suboxides are formed when WO3 is treated in H2 or alcohol at moderate
temperature (>400 ◦ C). First, oxygen vacancies are created without a definite compound
being formedβ [30]. β-Tungsten oxide is usually prepared by heating a mixture of WO3
and tungsten powder at high temperature (~1000 ◦ C), by reduction of WO3 in hydrogen
around 650 ◦ C [1,27] or by reduction of ammonium paratungstate ((NH4 )10 H2 W12 O42 ,
4H2 O) in hydrogen from 430 to 650 ◦ C [31]. It should be noted that the color of ultrafine
“WO3 ” powders may change from yellow for the greatest particle sizes (>50 nm) to blue
for the finest particles (<10 nm) [32]. In the meanwhile, the structure of ultrafine powders
changes from triclinic (>50 nm) to cubic (<10 nm). A cubic phase of blue oxide nanosheets
was synthetized by direct decomposition of H2 WO4 ·H2 O in H2 /N2 [33]. The cubic phase
is stable up to 280 ◦ C and tends to form a monoclinic phase, complete at 410 ◦ C. Structures
similar to those shown in Figure 5 are described as crystallographic shear (CS) by Tilley [28].
By varying the number and orientation of WO3 blocks sharing edges, it seems possible to
reach WO2.889 (W18 O52 ) composition.
2.1.3. WO2.72 Violet Oxide γ(γ-Tungsten Oxide W18 O49 ) and Other Suboxides WO
−δ
−δ 3δ
(δ > 0.2)
More complex structures are obtained when the O/W ratio decreases to less than 2.88.
Solonin et al. described a suboxide WO2.8 directly derived from hexagonal WO3 [34]. They
named it h-WO2.8 ; it is formed at the initial stage of h-WO3 reduction. Mesostructured
WO2.83 (W24 O68 ) was recently prepared by Cheng et al. by using KIT6 silica as a hard template [35]. XRD confirmed the formation of monoclinic WO2.83 (PDF # 36-0103). This result
contrasts with the formation of WO2.9 and WO2.72 by reduction of bulk WO3 (vide infra).
Cheng et al. showed that the reduction of meso-WO3 to meso-WO2.83 occurred at low
temperature due to a fast hydrogen diffusion through the mesoporosity (Figure 6).
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Figure 6. Compared reduction of bulk WO3 and meso-WO3 (a) and corresponding H2 -TPR profiles
(b). From Cheng et al. [35] with permission from the Royal Society of Chemistry.
Violet oxide is generally formed by reduction of WO3 in hydrogen at 900 ◦ C in the
presence of water vapor [1]. Sarin showed that WO2.72 is the most stable oxide formed by
reduction of WO3 [36]. Intermediary blue oxide WO2.90 is difficult to observe. As shown in
Figure 7, violet oxide tends to form whiskers [37] or nanoneedles [38]. This 1D morphology
seems to be characteristic of WO2.72 oxide. While ultrasmall nanoparticles of WO3 are
not easily prepared, Soultanidis et al. succeeded in preparing 1.6 nm particles by thermal
decomposition of ammonium metatungstate in oleyamine [39]. XRD revealed that these
particles are mainly composed of the W18 O49 phase (JCPDS 05-0392).
Interestingly, XPS analysis can be performed to assess the chemical composition
of tungsten oxide nanopowders. The x value in WO3−x can be determined by means
of the ratio between W5+ 4f and W6+ 4f-states. For instance, three series of WO3−x were
synthesized by Shpak et al. at atmospheric pressure by electric explosion of wires (EEW)
with different proportions between argon and oxygen [40]. In Figure 8, WO3−x , WO2.9
and WO2.72 nanopowder compositions were determined using the W6+ response (comps.
d-d, W4f7/2 at 35.7 eV; comps. e-e, W4f7/2 at 36.1 eV for hydroxide) and the W5+ -response
(comps. c-c, W4f7/2 at 34.8 eV).
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−
−
−
Figure 7. Morphology of violet oxide WO2.72 : random-plate-like whiskers
prepared by Pfeifer
et al. [37] (left, reprinted with permission from Elsevier); nanoneedles used by Wu [38] from commercial samples (right, reprinted with permission from Elsevier).
−
−
−
Figure 8. Peak synthesis for W4f-level XPS spectrum of tungsten atoms. The maxima of peak couples
correspond to W4f7/2 and W4f5/2 levels of tungsten atoms for W5+ states of oxide (comps. c-c, W4f7/2
at 34.8 eV) and W6+ states of oxide (comps. d-d W4f7/2 at 35.7 eV) and hydroxide (comps. e-e, W4f7/2
at 36.1 eV). From Shpak et al. [40], with permission from Elsevier.
2.1.4. Tungsten Dioxide (WO2 )
Tungsten dioxide is a rutile-like oxide, but contrary to TiO2 , WO2 has a monoclinic
structure with distorted octahedron of oxygen ions (C5 2h , P21 /c). This was confirmed
by Ben-Dor and Shimony, who succeeded in preparing WO2 monocrystals [41]. The
monoclinic structure was later refined by powder neutron diffraction (PDF# 32–1393) [42].
An orthorhombic form of WO2 was also reported (PDF# 82–728); it was evidenced in
sonochemical preparation [43]. Most preparations of WO2 were carried out by annealing of
WO3 at high temperatures (up to 1000 ◦ C). A facile preparation at low temperature (500 ◦ C)
was reported by Coşkun and Koziol by hydrolysis of WCl6 in the presence of NaBH4 [44].
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Compared to other tungsten oxides, WO2 presents relatively high conductivity properties.
The energy bands and density of states from theoretical calculations confirm a metal-like
behavior of WO2 [45].
2.2. Structure of Supported Tungsten Oxides
The structure of tungsten species dispersed on oxide supports depends on both the
nature of support and the concentration of tungsten. In 2007, Knowles et al. reported
a detailed overview of the surface chemistry of supported oxide, especially tungsten
oxide [46]. WO3 is more easily dispersed on alumina than on silica, on which WO3 tends
to form agglomerated crystallites [47]. The surface structure of tungsten oxide on various
oxide supports (Al2 O3 , TiO2 , Nb2 O5 , ZrO2 , SiO2 and MgO) was investigated by Raman
spectroscopy by Kim et al. [48]. WO3 on Al2 O3 , TiO2 , Nb2 O5 and ZrO2 exhibits strong
bands at 1005–1020 cm−1 characteristic of terminal W=O mono-oxo species. Bands in the
800–960 cm−1 spectral region are also observed. They are attributed to W-O-W species
whose intensity increases with the tungsten surface coverage. Bands at 1005–1020 cm−1 are
not observed in Raman spectra of WO3 /SiO2 and WO3 /MgO. Two intense bands at 802 and
715 cm−1 are visible on the spectra of 5%WO3 /SiO2 . These bands are characteristic of the
formation of crystalline WO3 , due to the poor dispersion of WO3 on this support. Raman
spectra of WO3 /MgO are more complex and suggest the formation of crystalline MgWO4
(as well as CaWO4 due to Ca impurity in MgO). In situ Raman spectroscopy coupled to
18 O/16 O exchange allowed Lee and Wachs to precisely identify the surface structure of
different oxides (including WO3 ) dispersed on silica [49]. In this study, WO3 /SiO2 showed
Raman bands at 968-985-1014 cm−1 shifted to 920-935-963 cm−1 in totally 18 O-exchanged
solids. Monoxo and dioxo tungstate species were formed, while crystallized WO3 was
virtually absent (contrary to the previous study). Decisive information on the structure of
supported tungsten catalysts can be obtained by UV–Vis. Ross-Meedgarden and Wachs
showed that the electronic edge energy (Eg) can be correlated to the nature of W surface
species, especially the number of nearest cations surrounding the central M cation [50].
The number of covalent W-O-W bonds around the central W(VI) cation would be given by
Equation (1):
NW-O-W = 11.89 − 2.37Eg
(1)
with Eg varying from 5.5 eV for isolated WO4 species (as bi-grafted, di-oxo WO4 surface
sites [51]) to 2.7 eV for crystallized WO3 3D structures.
Though WO3 tends to form nanocrystals on silica, there remains an amorphous
fraction more or less dispersed. Chauvin et al. developed a methodology coupling XRD
and Raman studies for the quantification of W species: surface dispersed WOx (monomeric
and oligomeric), amorphous WO3 and crystallized WO3 [52]. On silica, only dispersed
W species (monomeric and polymeric) would be formed below 1 W nm−2 . For higher
concentrations, WO3 nanoparticles (amorphous and crystallized) are evidenced. This
contrasts with other supports (Al2 O3 [53,54], TiO2 [55,56], ZrO2 [57–59]) for which tungsten
impregnation up to 4–5 W nm−2 leads to well-dispersed catalysts. On these supports,
WO3 nanocrystals are generally observed in the 4.5–9 W nm−2 loading range, while
large bulklike WO3 crystals can be observed beyond 9 W nm−2 [60]. In the last decades,
the WO3 -ZrO2 catalytic system has been the subject of a huge number of investigations
owing to its excellent performances in reactions requiring strong acid sites [61,62]. Recent
investigations by HAADF [63] and HRTEM [64] allowed obtaining detailed pictures of the
various tungsten species populating the zirconia surface (Figure 9a,b).
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Figure 9. Models of tungsten surface species evidenced (a) by STEM and HAADF (Zhou et al. [63],
reprinted with permission from Elsevier) and (b) by HRTEM (De Angel et al. [64], reprinted with
permission from Elsevier).
It should be noted that WO3 clusters (crystallized or not) may contain Zr atoms from
the support (Figure 9a). Tungstate species depicted in Figure 9 are in agreement with the
model of growth mode of W species when the surface density exceeds 5 W nm−−2 [65].
Preparation of tunsgtated zirconia catalysts from Lindqvist-type complexes containing
(W5 O18 Zr)2−− moieties confirmed the structure of such surface species containing both W
and Zr atoms, as well as their role in acid catalysis [66]. Structures of oxo-W(VI) species
deposited on TiO2 solids were extensively studied by Tribalis et al. by Raman spectroscopy [56]. Molecular configuration of W surface species depends on the temperature of
1 (Ti OH···OWO , main species at
calcination in O2 . Raman features shifted from 930 cm−
2
3
−
−1 (Ti-O-WO at 100 ◦ C), then 970 cm−1 ((Ti-O) -W(=O) at 120–250 ◦ C)
25 ◦ C) to 950 cm
3
2
2
−
−
and finally 1030−cm−1 for the trisubstituted mono-oxo (Ti-O)3 -W=O at 430 ◦ C.
Though W dispersion is not easily obtained on amorphous silica, recent developments of mesostructured silicas (MCM 41 [67,68], KIT-5 and KIT-6 [69,70], SBA-15 and
SBA-16 [71–73]) has allowed inserting significant amounts of tungsten while limiting the
formation of WO3 nanocrystals. This technique has been extended to spongelike silicate
TUD-1 discovered at Delft University [74]. Isolated WO4 2- species could be anchored
on Ti-modified TUD-1 up to 30% WO3 [75]. Other techniques including aerosol-assisted
sol–gel processes [76] or grafting of tungsten-containing molecules on silica [77,78] were
also developed to obtain highly dispersed “single-site” W species.
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As a final statement, critical insights of tungsten-based materials reveal no less than
seven tungsten–oxygen systems, with three arrangements mainly encountered in the catalysis field: WO3 , WO2.9 (β-tungsten oxide) and WO2.72 (γ-tungsten oxide). WO3 presents
several allotropic forms: monoclinic, triclinic and hexagonal structure. The structure impacts
the photocatalysis activity since the electron–hole recombination is favored by the absence
of defects. Tungsten suboxide phase (WO2.9 ) is formed under H2 treatment and exhibits
oxygen vacancies. More complex structures are obtained when the O/W ratio decreases to
less than 2.88, and WO2.72 is the most stable oxide formed by reduction of WO3 .
3. Acidity of Supported Tungsten Oxide Catalysts
Tungsten oxide WO3 is among the most acidic transition metal oxides [79]. Very few
studies have been devoted to the acid properties of unsupported tungsten oxides. Kanan
et al. studied the change of acid site concentration upon dehydroxylation/dehydration of
the surface of monoclinic WO3 [80]. They concluded that the changes in Brønsted/Lewis
(B/L) acid site concentration were not related to the degree of dehydroxylation but rather
to a mild reduction of the tungsten oxide surface. Choi et al. investigated surface acidity
of mesoporous WO3 synthesized using KIT-6 as a hard template [81]. Acid site characterization (NH3 -TPD, FTIR of adsorbed pyridine) showed that mesoporous WO3 exposes
predominantly Lewis acid sites associated with W6+ and probably cus-W6+ (cus = coordinatively unsaturated sites). A similar study performed by Kasian et al. showed that acid site
concentration of mesoporous tungsten oxide was increased by a mild reductive treatment
in hydrogen at 250 ◦ C [82]. Yue et al. studied the reactivity of m-WO3 , h-WO3 , hexagonal
tungsten bronze (HATB) and (NH4 )0.33−x WO3−z for the hydroconversion of n-heptane
reaction (Pd was added to the W oxides as hydrogenation function) [83]. The tungsten
oxides were reduced in H2 at 440 ◦ C, 35 bar. The n-C7 reactivity revealed the formation
of strong Brønsted acid sites, certainly linked to the reduction of W6+ to lower valence
states, the protons allowing the neutralization of negative charges localized on W-O-W
formed with W(6-x)+ ions. Li et al. investigated the behavior of MoO3 or WO3 clusters in
the conversion of labeled ethanol (CH2 CH3 OD) [84]. Dehydration and dehydrogenation
can occur. The overall alcohol conversion would be correlated to Lewis acidity, while the
selectivity (dehydration vs. dehydrogenation) would reflect the redox properties of the
oxide (i.e., the propensity of Mo or W to reduce from VI to V state in the reaction medium).
The reaction was carried out with (MO3 )3 trimers supported on graphene. Other supports
and other reactions were tested with contrasted differences between Mo and W oxides
depending on the substrate (see the review [85]).
3.1. General Overview
Barton et al. reported that supported tungsten oxide catalysts are able to generate Brønsted acid sites when W6+ species are replaced by tungsten cations with lower valency [86].
A general overview of the acidity of tungstated oxides was performed by Zaki et al., who
compared the relative strength of acid sites of 10% WO3 samples deposited on Al2 O3 (69
m2 g−1 ), TiO2 (34 m2 g−1 ) and SiO2 (136 m2 g−1 ) [87]. All samples were calcined at 500 ◦ C.
Well-dispersed monotungstates and polytungstates were the most abundant surface species
on WO3 /Al2 O3 , while 3D polytungstates were observed on WO3 /TiO2 . On WO3 /SiO2 ,
tungstosilicates and crystallized WO3 would be the dominant surface structures. Acid sites
were monitored by pyridine adsorption, which can lead to four species: LPy (Lewis acid
bound Py), BPy (Brønsted acid bound Py), HPy (hydrogen-bonded Py) and PPy (physically
adsorbed Py). FTIR spectra of adsorbed pyridine were recorded at room temperature
(Figure 10) and after desorption at 100, 200 and 300 ◦ C.
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Figure 10. FTIR spectra of adsorbed pyridine at room temperature on Al2 O3 (Al), TiO2 (Ti), SiO2 (Si)
and 10%WO3 on these supports (code: WAl, WTi and WSi, respectively). From Zaki et al. [87] with
permission from Elsevier.
Hydrogen-bonded pyridine is the main species at RT on WO3 /SiO2 , but it is unstable
and tends to disappear upon heating. Lewis acid sites (LPy) and hydrogen-bonded pyridine
(HPy) are clearly observed on WO3 /Al2 O3 , while both BPy and LPy sites are identified on
WO3 /TiO2 . Brønsted sites would be very strong on WO3 /TiO2 (still intense upon heating
at 300 ◦ C). The work of Zaki et al. [87] clearly underlines the critical role of the support of
tungsten oxides, both in the nature of W species and in their respective acidity.
3.2. Silica-Supported Tungsten Oxides
Due to the quasiabsence of acid sites on silica [88], WO3 /SiO2 materials were often
used to investigate the acidity of tungsten oxides. In their study on WO3 /SiO2 catalysts
(0 to 11.7 wt.% W on a silica of 200 m− 2 g−1 , i.e., 0 to 2.4 W− nm−2 ), Chauvin et al. monitored
the acidity of the samples by FTIR spectroscopy of adsorbed 2,6-dimethylpyridine (lutidine) [52]. The spectra reported in Figure 11a show the presence of Brønsted sites (bands
at 1643 and 1630 cm−1 ). Lewis sites that should give bands at 1620–1600 cm−1 are clearly
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−
−
absent from the samples. Amounts of Brønsted sites linearly increase with the WO3 surface
density up to 1.5 W −nm−2 (Figure 11b).
Figure 11. (a) FTIR spectra following lutidine adsorption and evacuation at 150 ◦ C over WO3 /SiO2 of
various W surface densities; (b) amounts of B sites measured after lutidine evacuation at 150 ◦ C (black
circles), 200 ◦ C (open circles) and 250 ◦ C (black squares). From Chauvin et al. [52] with permission
from the American Chemical Society.
The acidity of WO3 /SBA-15 oxides was characterized by Hu et al. using pyridine
adsorption, solid-state NMR and quantum chemistry calculation [89]. The study was completed by measurements and calculations of 15 N NMR chemical shift tensors of pyridine
interacting with tungsten oxides and silica. It was shown that W-OH-W dimers are the
Catalysts 2021, 11, 703
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principal Brønsted acid sites. W-OH monomers and silanols are very stable with minimal
Brønsted acidity. Contrasting with the work of Hue, Gonzalez et al. found quasiexclusively
Lewis acid sites in a series of WO3 /SBA-15 materials [90]. Acidity was characterized
by pyridine adsorption monitored by FTIR. Bands at 1595 and 1445 cm−1 attributed to
pyridine coordinated to Lewis acid sites are much more intense than the 1545 cm−1 band
characteristic of protonated pyridine bound to Brønsted acid sites. However, even though
it is relatively weak, the Brønsted site density seems very stable when the temperature
of pyridine adsorption is increased from 50 to 100 ◦ C, while the number of Lewis sites is
strongly affected (Table 1).
Table 1. Acid site density on SBA-15 and WO3 /SBA-15 measured by pyridine adsorption at 50
and 100 ◦ C. The number of sites is calculated from the integrated area of the band at 1545 cm−1 for
Brønsted sites and at 1445 cm−1 for Lewis sites. From González et al. [90].
Brønsted Acid Sites
Lewis Acid Sites
Sample
T (◦ C)
SBA-15
50 ◦ C
100 ◦ C
0
0
152
67
5%WO3 /SBA-15
50 ◦ C
100 ◦ C
24
24
920
92
15%WO3 /SBA-15
50 ◦ C
100 ◦ C
34
31
1102
350
25%WO3 /SBA-15
50 ◦ C
100 ◦ C
15
12
1246
458
(µmol
g−1 )
(µmol g−1 )
The reasons for the discrepancy between the work of Hu et al. [89] and that of González
et al. [90] are not clear. They may originate from the nature of the tungsten precursor (WCl6
in toluene for Hu et al. and ammonium metatungstate for González et al.), the final
temperature of calcination (400 ◦ C for Hu et al. and of 600 ◦ C for González et al.) or
the method of acid site detection (NMR for Hu et al. and FTIR for González et al.). This
question should certainly be reconsidered in the future.
WO3 /SiO2 catalysts were prepared by Kulal et al. for liquid phase nitration of aromatics [91]. A sol–gel technique using ammonium metatungstate and ethyl silicate 40
was employed for the preparation. FTIR of adsorbed pyridine revealed the presence of
both Lewis and Brønsted sites. Kulal et al. attributed the formation of Brønsted sites to
the presence of polytungstate species, while Lewis sites would require rather isolated W
ion centers. The B/L ratio increased with the W loading in the catalysts. At low loading
(<5% W), there were virtually no Brønsted sites. Bhaumik et al. developed silica-supported
WO3 and Ga2 O3 catalysts for lignocellulosic biomass to furfural processes [92]. Although
the acidity was not characterized in detail, the authors of this work stated that Lewis sites
are the most abundant acid sites on the catalysts.
Tungsten species are generally added by impregnation on the silica support. They
may also be incorporated during the preparation of the mesoporous silica. Zhu et al.
prepared WZr-KIT6 with various Zr/W ratios by addition of pluronic triblock copolymer
to a mixture of tetraethoxysilane (TEOS), ammonium tungstate and ZrOCl2 [93]. Acidity of
the materials was measured by adsorption of pyridine monitored by NMR. Both Brønsted
and Lewis acid sites coexisted on the catalysts. Lewis acid sites would be mainly linked
to the presence of zirconium while tungsten is necessary to generate strong Brønsted acid
sites. The materials were tested in ethanol dehydration. Interestingly, it was shown that
calcination of the coke catalysts regenerated Brønsted sites, which became even stronger
than those on the fresh materials.
Attempts to modify the activity of WO3 /SiO2 catalysts by means of gold nanoclusters
revealed that the acidity of tungsten oxide is not modified by Au (methanol transformation
tests) [94]. WO3 /SiO2 is highly selective for dimethyl ether, while the presence of gold
Catalysts 2021, 11, 703
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is necessary for the formation of methyl formate and dimethoxymethane. This result
suggests that pure WO3 possesses only acid sites and virtually no redox sites. The addition of WO3 was recently used to give acidity to Pt/SiO2 for glycerol hydrogenolysis to
1,3-propanediol [95]. Tungsten oxide would be present as W25 O73 with a high proportion
of W5+ . It also maintains a high dispersion of platinum.
3.3. Alumina-Supported Tungsten Oxides
Acidity of WO3 /Al2 O3 was studied in the 1980s and 1990s by Soled et al. [96] and
Zhang et al. [97]. While alumina possesses virtually no (or very weak) Brønsted sites,
the addition of tungsten oxide generates both Brønsted and Lewis sites. Most probably,
WO3 titrates the strongest Lewis sites on alumina to form Brønsted sites. The number
and strength of these Brønsted sites increase with the temperature of calcination [96]. The
proportion of Brønsted sites also increases with the tungsten loading (Table 2).
Table 2. Effect of W loading on the number of Lewis and Brønsted sites of WO3 /Al2 O3 (152 m2 g−1 ).
Acid site distribution was determined by a modified Benesi colorimetric technique. From Zhang et al. [97].
WO3 Loading
Lewis Sites
Brønsted Sites
Lewis Sites
Brønsted Sites
(wt.%)
(µmol g−1 )
(µmol g−1 )
(%)
(%)
0
190
14
93
7
2.5
207
69
75
25
10
220
125
64
36
30
242
182
57
43
Combining lutidine adsorption and other spectroscopic investigation, Chen et al.
obtained precise information about the change in acid site concentration with respect to
the W surface density [54]. Their results are summarized in Figure 12, which shows that
monomeric tungsten species contain quasiexclusively Lewis acid sites, while Brønsted sites
are relatively abundant on polymeric species appearing for W density above 1.4 W nm−2 .
The acid properties of WO3 -Al2 O3 catalysts were recently revisited by Kitano et al.,
who showed that the formation of Brønsted sites depended on the temperature of calcination [98]. They proposed that Brønsted sites are predominantly located at the boundaries
between WO3 monolayer domains (Figure 13).
Potassium-doped WO3 /Al2 O3 catalysts are able to transform gas mixtures such as
CO2 /H2 S/H2 , methanol/H2 S or CH4 /H2 S/CO2 into valuable products such as methyl
mercaptan (CH3 SH) [99–101]. All these reactions were reviewed by Taifan and Baltrusaitis [102]. Structural and acid–base properties of K2 O-WO3 -Al2 O3 catalysts were recently
investigated by Wang et al. [103], Zhu et al. [104] and Kiani et al. [105]. Raman spectroscopy
was used to differentiate and detect crystalline WO3 (bands at 273, 719 and 809 cm−1 ),
crystalline K2 WO4 (bands at 324 and 927 cm−1 ) and dispersed surface oligomeric WOx
species on alumina (strong band at 1021 cm−1 ). Conformation and position of most of these
Raman bands were confirmed by DFT calculation [105]. Surface acidity was probed by
NH3 -TPD [103] or NH3 adsorption monitored by FTIR [104], while basicity was probed by
CO2 -TPD. K2 O suppressed both Brønsted and Lewis acidity from the surface WOx species
or exposed Al2 O3 sites [104]. Adsorption of CO2 , nil on unpromoted WO3 /Al2 O3 (no basic
sites), significantly increases on K2 O-promoted catalysts. Residual acidity could play a
major role in catalytic activity, while basicity would be essential for a good selectivity for
methyl mercaptan [103].
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−
−
−
−
Figure 12. Correlation between amounts of (a) polymeric species, (b) Brønsted acid sites and (c) Lewis
acid sites and the tungsten density on WOx /Al2 O3 catalysts. Amounts
of polymeric species were
−
deduced from the integration of the Raman band at 1022 cm−1 . B and L concentrations were deduced
from lutidine adsorption (FTIR). From Chen et al. [54] with permission from Elsevier.
Figure 13. Effect of the temperature of calcination on the formation of Brønsted acid sites at the
junction between WOx monolayer and alumina. From Kitano et al. [98] with permission from John
Wiley and Sons.
3.4. Zirconia-Supported Tungsten Oxides
The system WO3 -ZrO2 was earlier reported to possess strong acid sites with H0
< −14.7 [106]. This “super” acidity makes the catalyst able to replace concentrated sulfuric
acid for alkylation and isomerization reactions of alkanes [62,106] or aromatics [61,107].
Acidic sites certainly play a great role in these reactions, even though redox properties
−
of WO3 -ZrO2 can be put forward for explaining the enhanced activity of reduced materi−
−
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als [108]. The effect of the preparation method on the acidity of WO3 -ZrO2 was studied by
Santiesteban et al. [109]. Acid sites were titrated by adsorption of 2,6-dimethyl pyridine.
−
−
Brønsted sites (0.054 meq g−1 ) were more abundant than Lewis sites (0.013 meq g−1 ), but
−1
−
only 20% of Brønsted sites were strong acid sites (0.011 meq g ) in proportion close to
Lewis sites. The most efficient preparation consists of reflux/impregnation of ZrO(OH)2
and H2 O with ammonium metatungstate. The acid site structure (Scheme 1) is similar to
the model proposed by Afanasiev et al. in 1994 [110].
O
OH
O
W O
Zr O W
Scheme 1. Acid site model of WO3 -ZrO2 with Lewis site born by tungsten oxo species and Brønsted
site on zirconium in the vicinity of tungsten atoms. Adapted from Santiesteban et al. [109] and
Afanasiev et al. [110].
Brønsted/Lewis (B/L) site ratio in WO3 -ZrO2 catalysts was measured by Baertsch et al.
for various tungsten loadings and in various conditions of pretreatment [111]. Acid sites
were evaluated by adsorption/desorption of NH3 or pyridine. Complementary information
about the redox sites was obtained by adsorption of O2 and H2 , while the number of
hydroxyl groups was measured by D2 /OH isotopic exchange. Brønsted sites were virtually
absent on low-loaded catalysts where tungsten was in the form of monomeric species. The
B/L ratio gradually increased with the tungsten loading. The presence of H2 during NH3
adsorption led to the generation of strong Brønsted sites. Platinum nanoparticles used in
bifunctional Pt/WO3 -ZrO2 catalysts would also be a source of Brønsted site by H spillover
between Pt and WO3 [112]. The surface chemistry and acidity of WO3 -ZrO2 catalysts for
skeletal isomerization of alkanes were discussed by Di Gregorio and Keller, who suggested
that a condensation phenomenon between Lewis and Brønsted sites can occur during the
calcination treatment [113] (Figure 14).
A combined theoretical–experimental study on the acidity of tungstated zirconia was
performed by Galano et al. [114]. They confirmed that the Lewis acidity (band at 1444 cm−−1
for pyridine coordinated to L sites) and Brønsted acidity (band at 1539 cm−−1 for protonated
pyridine) is a function of the degree of WO3 polymerization. The number of Brønsted sites
increased while that of Lewis sites decreased as the W centers shifted from tetrahedral to
octahedral coordination, i.e., when the degree of WOx condensation increased. In parallel,
the strength of the Brønsted acid sites tended to decrease. A maximum of Brønsted acidity
was observed for a W loading of 7 W nm−−2 . Recent investigations of tungstated zirconia
designed for acid-driven catalytic reactions showed that active sites are three-dimensional
distorted Zr-WOx clusters of 0.8−1 nm size [59]. Optimum structure for a better activity
−
tt
is obtained when W is in a distorted octahedral environment in close contact with Zr
cations. Calcination temperature (up to 800 ◦ C) and nature of zirconium oxyhydroxide
used as support play a major role in obtaining higher Brønsted acidity [115]. Though
acid properties are generally characterized by adsorption of basic molecules (e.g., NH3 ,
pyridine) monitored by FTIR, other techniques are available. Li et al. showed that 31 PNMR using TMPO (trimethyl phosphine oxide) as a probe molecule reveals the presence
of Brønsted sites on WO3 -ZrO2 prepared by a sol–gel method with Zr(OBu)4 and WCl6 as
reagents [107]. TMPO gives a broad band from 40 to 90 ppm, while chemical shift above
57 ppm is characteristic of Brønsted sites.
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Figure 14. Condensation of Lewis and Brønsted sites to form new surface tungstate species on
WO3 /ZrO2 catalysts. Adapted from [113] with permission from Elsevier.
Yttrium doping of zirconia is often used to stabilize the tetragonal structure of ZrO2 .
The effect of yttrium on the generation of acid sites on WO3 -ZrO2 was investigated by
Yamamoto et al. [116]. Acidity of the catalysts (15% WO3 ) was characterized by means
of model reactions: n-butane skeletal isomerization, alkylation of anisole with benzyl
alcohol, and 2-butanol decomposition. Acidity increased with yttrium content up to 4%
Y. In the meanwhile, the tetragonal-to-monoclinic ratio of zirconia increased to reach
85% of tetragonal phase for 4% Y. This proves that t-ZrO2 is more suitable than m-ZrO2
for stabilizing WOx species with the highest acidity. Above 4% Y, the catalyst acidity
decreased due to the excessive formation of inactive Y-W-O species. The beneficial role
of tetragonal zirconia was demonstrated for different applications of WO3 -ZrO2 catalysts,
such as hydrolysis of cellobiose [117] or viscoreduction of heavy crude oil [118]. The
mode of preparation of the zirconia support can greatly affect the acidity of the materials.
Sol–gel synthesis and extraction of the solvent in supercritical conditions give the most
active catalysts for organic reactions of industrial interest: acylation of veratrole with
acetic anhydride and acylation of anisole with benzoic anhydride [119]. Doping zirconia
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with phosphorus was extensively studied by Miao et al. [120,121]. WO3 was deposited
on mesoporous zirconium oxophosphate [120] or directly incorporated in the one-pot
preparation of meso-ZrPOx to synthesize mesoporous WZrP materials [121]. The catalysts
were tested in benzylation of anisole. Unfortunately, the effect of phosphorus could not
be clearly established due to the absence of reference WO3 /ZrO3 catalyst in these studies.
However, the mode of preparation and the mesoporous texture give the WZrP materials a
high activity and a high stability. The nature of acid sites is similar to the acidity spectrum
characterized in WO3 /ZrO2 : W-free materials possess Lewis sites (83 µmol g−1 ) and very
few Brønsted sites (19 µmol g−1 ). Brønsted site density increases up to 55 µmol g−1 for
W/Zr ratio of 0.2.
3.5. Titania-Supported Tungsten Oxides
WO3 -TiO2 is also an acid catalyst with activity for n-alkane isomerization [55]. These
mixed oxides possess both Lewis sites ascribed to surface Ti4+ species and strong Brønsted
sites generated by WO3 nanoclusters. WO3 -TiO2 was proven to have excellent performances in the reaction of sorbitol transformation into biofuels [122]. The reaction proceeds
via successive steps of dehydration and hydrogenation, which requires metal–acid bifunctional catalysts. WO3 -TiO2 (acid function) associated with Pt/ZrO2 (metallic function)
gave the best performance for the production of C5-C6 hydrocarbons. The main application of WO3 -TiO2 (associated with V2 O5 ) is for the NOx abatement by the NH3 -SCR
process [123–125]. While the chemical state of vanadium and tungsten seems to be crucial
for a good DeNOx activity [126], acid properties could also play a primary role in the
reaction [123,127]. The characterization of V2 O5 -WO3 /TiO2 is examined in Section 4.
3.6. Conclusions
Evaluation of the acidity of supported WOx obviously depends on the used probe
molecule because of its own basic strength. For instance, NH3 , lutidine and pyridine, the
most popular probe molecules for acidity evaluation, display pKa values of 9.23, 6.65 and
5.23, respectively. Consequently, they do not all exhibit the same sensibility toward the
Brønsted (or acidic hydroxyl group) and Lewis acid sites (coordinatively unsaturated sites).
In addition, the acidity of WOx species clearly depends on the W surface coverage.
Indeed, dispersed phase surface sites (WO4 , WO5 ), poorly crystalline WO3 nanoparticles
and bulklike crystalline WO3 all show unique acidity. For instance, crystalline WO3
exhibits Brønsted acidity, not encountered on dispersed WO4 sites. Consequently, the
acidity of catalysts strongly depends on the obtained WOx surface species, which depend
on the preparation protocol and the tungsten loading. Brønsted acid sites are reported
to be mostly dependent on the presence of polytungstate polymeric species. Lewis acid
sites are associated with coordinatively unsaturated W6+ sites or isolated W ions centers.
The B/L ratio depends on the support. Lewis sites are the most abundant acid sites on
WO3 /SiO2 catalysts. Addition of tungsten oxide on alumina generates both Brønsted
and Lewis sites, and the proportion of Brønsted sites increases with the tungsten loading.
The stronger acid sites are encountered on the WO3 -ZrO2 system, where a condensation
phenomenon between Lewis and Brønsted sites can occur during the calcination treatment.
New surface tungstate species appear with various degrees of WO3 polymerization, leading
to octahedral coordination that promotes an increase in the amount of Brønsted acid sites.
4. WO3 Catalysts for DeNOx Applications: WO3 -V2 O5 /TiO2 and Other
Tungsten-Based Materials
Nitric oxide abatement in nitric acid plants was initially carried out by NH3 -SCR
over V2 O5 -TiO2 catalysts. Very soon, it was proven that adding WO3 (or MoO3 ) to the
catalyst formulation led to a dramatic improvement of the performance. These V-W/TiO2
catalysts were also implemented in DeNOx autocatalyst processes, especially for heavyduty engines, working with NO2 /NOx inlet ratio of 0 or 0.5, related to the standard and fast
SCR stoichiometry, respectively. The role of WO3 was summarized by Chen and Yang in
1992 [123]: (i) it increases the activity and widens the temperature window; (ii) it increases
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the resistance to various poisons (alkalis, arsenic); (iii) it reduces ammonia oxidation by O2,
which is a nondesired reaction (especially possible at elevated temperature, T > 400 ◦ C).
Kompio et al. also showed by different techniques (e.g., Raman spectroscopy, EPR, H2 TPR) that tungsten allowed an increase in V-O-V species by confining vanadia in small
clusters [128]. Most of these effects were confirmed and detailed in a recent review by
Lai and Wachs [129], who stressed three important features of the reaction: (i) the role of
V5+ surface species as active sites: WO3 is not active per se but promotes the reaction by
vanadia by formation of oligomeric vanadia (V2 O5 ) sites or crowding; (ii) the specific role
of Brønsted acid sites in NH3 activation: most of the Lewis sites are converted to Brønsted
sites in the presence of moisture at 250 ◦ C; (iii) the detailed mechanisms reported by Topsoe
and Dumesic et al. in the 1990s for V2 O5 -TiO2 [130,131] (see Figure 15) seemed to be still
valid in the 2010s for V2 O5 -WO3 /TiO2, as also recently summarized by Han et al. [132].
Figure 15. Mechanism of NH3 -SCR over V2 O5 -TiO2 . It combines NH3 activation over Brønsted acid
sites and a reoxidation of V4+ to V5+ (Brønsted V4+ -OH to vanadyl V5+ = O species). Insertion of NO
into ammonium ion would be a key step of the mechanism. Reprinted from [130] with permission
from Elsevier.
This mechanism, however, contrasts with the amide–nitrosamide mechanism proposed by Lietti et al. [133] in which NH3 is predominantly activated on Lewis sites as
amide species (Equation (2)). The main steps of this mechanism lead to the formation of
NH2 NO (nitrosamide) (Equation (3)), which further decomposes into N2 + H2 O.
4+
H3 N:→V5+ − O2− ⇒ V
− NH2 + OH−
−
−
−
4+
V4+ − NH
−2 + NO ⇒ V − NH
− 2 NO
−
(2)
(3)
Another important feature to consider is the formation of N2 O. Nitrous oxide is a potent greenhouse gas with a global warming potential of 295–300 times that of CO2 [134,135].
Its concentration in exhaust gases should be controlled. Djerad et al. reported that
N2 O is formed at high temperature (T > 300 ◦ C) in the NH3 -SCR process over V2 O5 WO3 /TiO2 [136]. Nitrous oxide concentration increases with the vanadium loading in the
catalyst and is formed via NH3 oxidation (Equation (4)).
2NH3 + 2O2 → N2 O + 3H2 O
(4)
Liu et al. showed that the use of titania supports with high surface area would be a
key to reduce N2 O formation [137]. Vanadium being more dispersed on these supports,
ammonia oxidation to N2 O could be favored on polymerized vanadyl species.
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4.1. Mechanisms and Surface Intermediates
The nature of active sites and the surface intermediates were investigated by Zhu
et al. by in situ IR spectroscopy [138]. The first step of the mechanism would be the
adsorption of ammonia on acid sites either as NH3ads (on Lewis (L) sites) or NH4 + (on
Brønsted (B) sites). The surface VOx sites (V5+ L and V5+ B ) are the active sites for the
reaction, tungsta sites (W6+ L and W6+ B ) being significantly less active. Both B and L sites
participate in the reaction. However, if Brønsted sites are more abundant, Lewis sites
possess the highest turnover frequency. Overall, ammonia adsorption is part of a complex
NOx removal mechanism and results in hydrogen abstraction to provide –NH2 amide-type
species. Hydrogen migration is involved in both acidity conversion for Lewis to Brønsted
acid site transformation at T > 300 ◦ C and reoxidation for the redox loop of the DeNOx
reaction [139]. In addition, coordination of ammonia on Lewis acid sites does not prevent
the dissociative H2 O chemisorption and the formation of Brønsted acid sites, leading to
adsorbed NH4 + species [140].
Surface acidity and redox properties, as well as their effect on SCR activity, were
investigated by Zhao et al. on a series of Vn W-TiO2 with various vanadium loadings
(1–13 wt.%), while keeping the tungsten loading constant (8 wt.% WO3 ) [141]. The main
characteristics of the series are reported in Table 3. The highest activity observed for the
V9W-TiO2 sample is correlated with both higher V4+ /V5+ ratio and higher Brønsted concentration sites. Redox properties do not seem to play a major role. Additional conclusions
resulting from experimental analyses and DFT calculations show that the structure of
vanadyl species plays a crucial role in DeNOx performances; polymeric species demonstrate higher NH3 -SCR activity than monomeric vanadyl compounds [142]. Besides, based
on XPS results, low-valence vanadium species (V4+ and V3+ ) were recently claimed to
enhance SCR activity compared to the V5+ form [143]. Both low-valence vanadium species
and polymeric surface VOx species drive the NH3 -SCR activity at low temperature (T <
350 ◦ C), as previously mentioned in [142].
Table 3. Vanadium state and acid and redox properties of a series of VnW-TiO2 catalysts (n: vanadium loading (%), 1 ≤ n ≤ 13;
[WO3 ] = 8%). TiO2 (120 m2 g−1 ) mainly as anatase. Acid site concentrations were measured by pyridine adsorption monitored
by FTIR (bands at 1580 and 1633 cm−1 for Brønsted sites; bands at 1597 and 1438 cm−1 for Lewis sites). H2 -TPR peaks are
between 535 and 569 ◦ C, while O2 -TPO gives peaks around 450–460 ◦ C. The mean rate of reduction (νTPR) and oxidation
(νTPO) are given in the table. SCR activity was measured between 150 and 420 ◦ C in a flow of 1000 ppm NO + 1000 ppm NH3
in 5% O2 (WHSV: 20,000 h−1 ). NO conversion at 200 ◦ C is representative of the activity order. From Zhao et al. [141].
Catalyst
V1W/TiO2
V5W/TiO2
V7W/TiO2
V9W/TiO2
V11W/TiO2
V13W/TiO2
V4+ /V5+
B Sites
L Sites
νTPR
νTPO
SCR Activity: NO
Conv. at 200 ◦ C
(XPS)
(µmol m−2 )
(µmol m−2 )
(nmol m−2 s−1 )
(nmol m−2 s−1 )
(%)
0.45
0.99
1.47
1.73
0.88
0.50
28
57
149
164
140
98
131
153
292
318
325
485
2.4
4.6
7.5
8.6
8.8
1.1
0.95
1.4
2.1
2.9
7.6
1.0
19.5
38.0
41.5
60.5
51.5
44.0
The crystallinity of WO3 has a significant effect on vanadia dispersion [127]. Twodimension VOx moieties have a tendency to anchor onto the titania surface in the vicinity
of WOx . Small WO3 crystallites are preferable to WOx amorphous layer occupying a large
surface of titania. Nevertheless, a compromise should be found because bulk tungsten
oxide is less acidic than the dispersed oxide.
Interactions between tungsten oxide and vanadia were reinvestigated by Kompio et al.
to better understand the promoter effect of tungsten on SCR activity during heat treatments
and thermal stress [144]. The study was carried out on a V1.5-W10/TiO2 catalyst (anatase,
140 m2 g−1 after low-temperature calcination at 350 ◦ C). Heat treatments generally provoke
catalyst deactivation. However, several maxima of activity were observed during the
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global decrease in activity when the support BET area reached 42 m2 g−1 and 20 m2 g−1 .
New surface sites were then created because isolated vanadia species, less active, were
replaced by more active bridged V-O-V sites. Similar active species were proposed by
Kwon et al. for non-tungstated V/TiO2 catalysts calcined at 600 ◦ C [145]. Marberger et al.
underlined the fact that the presence of water is required to judge the thermal stability of the
catalysts [146]. Water accelerates sulfate group removal (generally present in commercial
titania), which changes the acidity of the catalysts. Water also accelerates the loss of
BET surface area and V volatility. However, curiously, it tends to increase the vanadium
dispersion (Table 4). Authors recently confirmed the mobility of the VOx and WOx species
of the catalyst exposed to hydrothermal aging together with various structural changes
of surface acidity [146]. Additionally, Liang et al. [147] observed that gas flow containing
SO2 and H2 O decreased the number of NH3 adsorption sites, active component content,
specific surface area and pore volume over F-containing V2 O5 -WO3 /TiO2 catalysts.
Table 4. Comparison of dry (10% O2 in N2 ) and wet (10% O2 + 10% H2 O in N2 ) aging of a commercial
V2 O5 (2%)-WO3 (10%)/TiO2 catalyst. Vanadium emissions and VOx surface coverage (based on
7.9 VOx nm−2 for one monolayer). From Marberger et al. [146].
Gas Feed
550 ◦ C
600 ◦ C
650 ◦ C
V release (µg m−3 )
dry
wet
1.0
2.1
1.4
49.3
34.2
201
VOx coverage (%)
dry
wet
24
27
32
37
42
44
Another possible cause of deactivation is the transformation of anatase to rutile, a
poorer support of vanadia and tungsta for the SCR reaction. Promotion of titania by silica
can prevent rutile formation above 600 ◦ C and give more stable catalysts [148,149]. A
commercial catalyst named VSCR1 has been compared to a catalyst doped with 4–5% SiO2 ,
named VSCR2. Figure 16 shows the global behavior of the two catalysts when they are
calcined at 600, 700 and 800 ◦ C.
A dramatic improvement of the catalyst stability is obtained by Si doping. Maintaining
the anatase phase is correlated with a decrease in the WO3 and V2 O5 phase segregation into
monoclinic tungsten oxide and vanadia crystallites. It seems that SiO2 tends to segregate as
bulky silica crystallite at high temperature (>600 ◦ C) [149]. Only small polymeric entities
formed by a minute amount of silica can prevent catalyst deactivation. Deactivation is
often observed after hydrothermal treatments at high temperature. However, this is not
the case in all circumstances. Chen et al. prepared V-W/TiO2 catalysts in two steps:
(i) WO3 /TiO2 was first prepared by mixing metatitanic acid and ammonium paratungstate;
(ii) the solid, dried and calcined at 550 ◦ C, was then impregnated with 1% V2 O5 using
metavanadate dissolved in monoethanolamine [143]. The resulting catalyst was finally
hydrothermally treated at 750 ◦ C. This treatment induced a decrease in surface area but
resulted in considerably higher SCR activity. In fact, more V4+ and V3+ species were found
on the catalyst treated at 750 ◦ C, which explains its better SCR performances.
WO3 -TiO2 catalysts, without vanadia addition, were investigated by Shin et al. [150].
Tungsten oxide was well dispersed in the interlayer between the grains of titania, avoiding
TiO2 sintering. It created surface acid sites (mainly Brønsted), giving the material a good
SCR activity.
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Figure 16. Changes of the catalyst characteristics upon temperature aging: reference V-W/TiO2
catalyst (a) and Si-doped catalyst (b). From Beale et al. [148].
4.2. Influence of the Preparation Method: Powder and Monolithic Catalysts
Powder V-W/TiO2 catalysts are commonly prepared by impregnation of anatase with
aqueous solutions of ammonium metavanadate (NH4 VO3 ) and ammonium metatungstate
hydrate (NH4 )6 (H2 W12 O40 )·xH2 O or paratungstate hydrate (NH4 )10 (H2 W12 O42 )·4H2 O
precursors. He et al. evaluated the role of the synthesis method and showed that coprecipitation of the three elements—V, W and Ti—gave the best results in terms of SCR
activity [151]. Coprecipitated catalysts possess new O-VO3 and O-WO4 sites that enhance
the ammonia adsorption capacity. The origin of the best results obtained with coprecipitated catalysts is not clear. Titania is present as poorly ordered anatase with many
defects, while acidity is not strengthened with respect to impregnated catalysts. Tungsten–
titanium pillared clays were shown to be excellent supports of vanadia for the NH3 -SCR
reaction [152]. A great advantage of this preparation method is the better control of the
intimacy of contact between W and Ti, which are both inserted in clay pillars. The addition
of S or N compounds during the preparation of TiO2 clearly enhanced the performances.
SCR catalysts should be deposited on monoliths before practical use in DeNOx processes. Differences in color, structure and local activity of the V-W/TiO2 deposit depending
on its location (center, monolith periphery) were studied by Wang et al. on commercial
honeycomb catalysts [153]. As these catalysts were designed for denitrification of flue
gases, NH3 -SCR was tested in presence of SO2 . In the monolith, initially yellow, some grey
areas may appear in used catalysts. This due to changes of the vanadium valence state
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from +5 (V2 O5 is bright yellow) to +4 (VO2 is yellow darker, almost brown) and +3 (V2 O3
is brown). This study confirms that the V-W/TiO2 is tolerant to a certain amount of SOx .
Monoliths pretreated in an acidic medium seem to give good impregnation characteristics [154]. The fabrication process is illustrated in Figure 17. Best results in NH3 -SCR
were obtained with the monolith impregnated three times with 3% V + 10% W.
Figure 17. Preparation of V-W/TiO2 monolithic catalysts. The ceramic is pretreated in nitric acid and
calcined at 500 ◦ C. It is then immersed in a mixture of solutions A and B consisting of butyl titanate
in ethanol (sol. A) and metavanadate + ammonium tungstate in ethanol/nitric acid (sol. B). It is
dried at 80 ◦ C and calcined at 500 ◦ C. From Zhao et al. [154] with permission from Elsevier.
In the NH3 -SCR technology dedicated to automotive applications, ammonia is generally provided by urea decomposition/hydrolysis, even though some applications using
liquid ammonia have been envisaged [155]. Combining WO3 -V2 O5 /TiO2 (upstream) and
Cu-zeolite (downstream) catalysts was proven to give excellent performances in urea-SCR
technology [156]. Deterioration of activity of the W-V/TiO2 catalyst above 270 ◦ C was
compensated by the high performance of the zeolite catalyst. Lower N2 O selectivity was
observed in the dual catalyst. Similar results were obtained by combining WO3 -V2 O5 /TiO2
and Fe-zeolite catalysts [157].
4.3. Poisoning of V2 O5 -WO3 /TiO2 Catalysts
Apart from the physical deactivation of WO3 -based catalysts due to its working time
(e.g., sintering, volatilization of active elements), the system can suffer from chemical
poisoning [158]. In 2008, Kröcher et al. reported a detailed study on the deactivation of
V2 O5 -WO3 /TiO2 catalysts by inorganic impurities of lubricants, biodiesel or urea solutions [159,160]. Among all the poisons tested, potassium had the strongest effect on both
catalytic activity and N2 O selectivity (at 500 ◦ C). The poisons can be ranked as follows:
K >> Ca >> Mg > Zn > P. These results prompted researchers to focus their investigations
on K and Ca poisoning (Section 4.3.1). Another poison present in exhaust gases or flue
gases is sulfur dioxide. The effect of SO2 was also investigated by several authors, as
presented in Section 4.3.2; poisoning by arsenic is presented in Section 4.3.3.
4.3.1. Potassium and Calcium Poisoning
Potassium is a poison of acid sites and inhibits NH3 adsorption. Xie et al. investigated the poisoning of a W-V/TiO2 catalyst exposed to the flue gas of a coal-fired power
plant [161]. They showed that alkali contaminants (mainly K) contained in the flue gas
preferentially poison the vanadium sites (V5+ –OH and/or V5+ =O) rather than the sites
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associated with tungsten oxide or TiO2 . A detailed kinetic analysis reveals that NH3 adsorption/desorption, NH3 oxidation and DeNOx activity are all affected by K poisoning.
Similar tendencies were demonstrated by Siaka et al. [162], who claim that potassium
preferentially neutralizes strong acid sites and alters V=O redox sites, leading to stabilization of well-dispersed VOx species. Contrasting with the results of Xie et al., Chen et al.
concluded that tungsten oxide can serve as a sacrificial agent protecting vanadia from
severe K poisoning [163]. The combined effect of potassium and chloride ions showed
that KCl is a more severe poison than KOH [164]. A higher amount of potassium was
fixed by the catalyst when KCl was used as a potassium precursor. Better performance
and especially higher potassium tolerance were obtained by doping the V2 O5 /TiO2 catalyst with 15% HPA (H3 PW12 O40 , H4 SiW12 O40 or H3 PMo12 O40 ) instead of 10% WO3 [165].
HPA does alter vanadium dispersion and does not increase N2 O formation. A higher
concentration of acid sites could explain the higher K tolerance. By studying multielement
poisoning systems, Mia et al. [166] found that phosphorous–potassium combination results
in lower deactivation than single potassium poisoning. The advanced explanation is that
new active sites generated by phosphorous react with potassium to liberate V-OH acidic
sites. Concomitantly, alkali species may provide additional basic sites for NO2 adsorption,
enabling gaseous ammonia to react with adsorbed NOx compounds for fast SCR stoichiometry [167]. Finally, potassium resistance may be strengthened by Ce and Cu addition
over V2 O5 -WO3 /TiO2 SCR materials due to an enhancement of V5+ amount and active
oxygen species [168].
Calcium poisoning was investigated in detail by Li et al. [169,170]. The degree of
poisoning follows the order CaCO3 > CaO > CaSO4 . It is linked to the ability of the
precursor to form calcium tungstate [170]. CaCO3 decreases oxygen availability, vanadium
reducibility and acid site concentration. If calcium sulfate is a less severe poison than CaO
and CaCO3 , it tends to increase the N2 O selectivity. The catalysts can be regenerated by
using specific treatment based on 1-hydroxy ethylidene-1,1-diphosphonic acid (HEDP)
liquid under weak acid environment [169]. Odenbrand investigated the effect of CaSO4
on kinetic parameters of NH3 -SCR over W-V-TiO2 catalysts [171]. He concluded that Ca
introduced into the pore system by impregnation strongly poisons the catalyst, but in a
different way from that when it is coming from the engine during operation. CaSO4 affects
both activation energy and NH3 heat of adsorption. A moderate effect on N2 O selectivity
was observed.
4.3.2. Sulfur Poisoning
Tungsten-promoted V2 O5 /TiO2 catalysts are not resistant to SO2 for the NH3 -SCR
reaction. Antimony oxide [172], molybdenum oxide [173] or iron oxide [174] are better
promoters of these catalysts for sulfur resistance. Xu et al. confirmed the superiority of
V2 O5 -Sb2 O3 /TiO2 compared with the commercial V2 O5 -WO3 /TiO2 catalyst for SO2 resistance [175]. Sulfur deactivation is due to the formation of a surface layer of NH4 HSO4 [176].
Compared to tungsten, Sb-doped catalysts have a lower activity for SO2 oxidation to SO3 ,
which leads to weaker deposit of ammonium sulfate. Moreover, it seems that NH4 HSO4
is more reactive with NO when it is deposited on V2 O5 -Sb2 O3 /TiO2 [175]. The sulfur
resistance of iron-promoted WO3 /TiO2 is also reported in [177], where non-vanadiumbased catalysts present thorough regeneration. Nobia-doped materials also exhibit significant sulfur resistance [178]. Nb2 O3 -CeO2 /WO3 -TiO2 (NbCeWTi) catalyst presents
mainly ammonium hydrogen sulfate species after H2 O and SO2 exposition that protect
Cex+ active sites.
SO2 resistance of V2 O5 -WO3 /TiO2 catalysts can be improved by the addition of WO3 graphene nanocomposite [179]. WO3 remains well dispersed on graphene, which tends
to decrease the SO2 oxidation activity. Moreover, WO3 acidity is preserved on graphene,
essential for a good SCR activity. In another attempt, sulfur resistance was successfully
increased by the addition of barium sulfate [180]. BaSO4 contributed to reinforcing the
acidity of the catalysts while blocking the SO2 oxidation activity.
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4.3.3. Arsenic Poisoning
Arsenic is present in the gas phase of power plants and may reach concentrations of
up to thousands of micrograms of As2 O3 per cubic meter [181]. Power plant gases can
be treated with limestone to reduce arsenic concentration. The compound thus formed
is (Ca3 (AsO4 )2 ), and it may be condensed or adsorbed on ashes, decreasing the final As
concentration to less than 100 µg m−3 . However, even at this concentration, As remains
a severe poison for NH3 -SCR catalysts. Deactivation of V2 O5 -WO3 /TiO2 catalysts was
investigated by Peng et al. [182,183] and Kong et al. [184]. Arsenic oxides decrease Lewis
acidity and tend to form very unstable As-OH Brønsted sites. At a certain concentration,
As2 O3 is oxidized to As2 O5 , much less active for NH3 -SCR but more active for NH3
oxidation, leading to N2 O in significant amounts. As2 O5 forms a dense layer at the catalyst
surface, which reinforces the deactivation effect of arsenic. It was proven that catalysts
promoted by Mo instead of W are more resistant to As poisoning.
Synergetic poisoning effect of arsenic with potassium was evaluated in [185,186].
Results indicated that the coeffect of As + K was more dramatic than the additive effect
of a single poison. As previously discussed, arsenic loading leads to the formation of
As-OH acid sites, which can be neutralized by potassium deposits. In addition, the effect
of charge-compensating anions was also investigated, with the following enhancement
ranking sequence: SO4 2− < Cl− << NO3 − . Finally, catalysts poisoned by arsenic could
be almost regenerated by sulfuric acid treatment, leading to the recovery of Lewis and
Brønsted acid sites. However, the main drawback remains the formation of chelating
bidentate sulfates and the loss of vanadium species [187]. Alkali solution treatment by
single sodium carbonate [188] or with sodium hydroxide combined with sulfuric acid [189]
also demonstrated interesting regeneration results.
4.3.4. Metal Release and Reuse of V-W-TiO2 Catalysts
A cause of slow but irreversible deactivation of V2 O5 -WO3 /TiO2 catalysts is the metal
release at high temperature (T > 600 ◦ C) [190,191]. Vanadium VO(OH)3 and tungsten
WO2 (OH)2 oxo-hydroxides are responsible for the greatest part of the metal release. This effect is more important on agglomerated vanadium and tungsten particles, especially when
the support undergoes severe sintering. Therefore, metal release is significantly reduced
with catalysts supported on stabilized titania. Tungsten can be recovered from spent catalysts by a chemical treatment consisting of an alkaline leaching–ion exchange method [192].
Spent catalysts were also used to prepare new W-V catalysts. Huo et al. reported a
feasible preparation method for a visible-light-sensitive BiVO4 /Bi2 WO6 heterojunction
photocatalyst from waste SCR catalysts [193].
4.4. Cerium-Promoted WO3 Catalysts for NH3 -SCR
Promotion by ceria was studied in detail in the last decade. Redox properties [194,195]
and oxygen mobility on ceria [196,197] could have a major impact on the NH3 -SCR reaction [198]. Ceria could be added to V2 O5 -WO3 /TiO2 catalysts, WO3 /TiO2 catalysts
(without vanadia) or WO3 catalysts (without vanadia and titania).
4.4.1. Ceria Added to V2 O5 -WO3 /TiO2
The addition of ceria to V2 O5 -WO3 /TiO2 for the NH3 -SCR reaction was investigated
by Chen et al. [199]. The great merit of ceria is the enhancement of the DeNOx activity at low
temperature (below 300 ◦ C). For instance, with a catalyst having typical composition close
to that of commercial materials (1% V2 O5– 9% WO3 ), a NOx conversion of 52% is obtained
at 200 ◦ C in the following conditions: 500 ppm NO, 500 ppm NH3 , 3% O2 and 28,000 h−1 .
Addition of 5% CeO2 increases NO conversion up to 88%, while manganese oxide has
virtually no effect (NO conversion = 50%), and iron oxide decreases NO conversion down
to 15%. Vanadium oxide being responsible for the formation of N2 O at high temperature,
attempts were made by Chen et al. to significantly reduce the vanadium loading down to
0.1% while maintaining a good activity by doping the V0.1 W6 Ti with ceria [199]. Above
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5% CeO2 , activity of V0.1 W6 CexTi becomes equal or superior to that of V1 W9 Ti at 200 ◦ C.
In the meanwhile, N2 O formation is virtually suppressed on the low-loaded vanadium
catalysts. This effect is still more marked on Ce-doped catalysts. Addition of ceria leads to
complex features since the basicity of titania seems to be reinforced while there are stronger
and more active Brønsted acid sites on VWTi.
Series of CeO2 -V2 O5 -ZrO2 /WO3 -TiO2 catalysts with different loadings of ceria were
prepared by Wang et al. [200]. They confirmed the specific role of ceria in improving both
the low-temperature activity and the N2 selectivity at high temperature (less N2 O). However, the zirconia-free catalyst (CexV1/W8Ti) has a poor hydrothermal stability (750 ◦ C,
10% H2 O, 12 h). Addition of zirconia (10%) significantly reinforces the stability of the ceriapromoted catalyst. Ceria also has a great influence on the reaction mechanism. Ce-doped
catalysts (CeVZr/WTi) are extremely sensitive to the presence of NO2 in the reaction gases
and are much more active in fast SCR conditions (Equation (5)) than in standard conditions
(Equation (6)). The influence of NO2 is limited on the cerium-free catalysts (VZr/WTi),
suggesting that NO2 does not readily react via the fast SCR reaction in absence of ceria.
NO + NO2 + 2NH3 → 2N2 + 3H2 O
(5)
1
O2 + 2NH3 → 2N2 + 3H2 O
(6)
2
The group of Tianjin University investigated the method of introduction of cerium
and vanadium on the commercial 10% WO3 /TiO2 support [201]. Ceria was introduced
either by impregnation of cerium nitrate (IMP) or by deposition–precipitation of cerium
nitrate in the presence of ammonia (DP). Characteristics and performances of the catalysts
are reported in Table 5.
NO +
Table 5. Comparison of VCe/WTi DP, VCe/WTi IMP and cerium-free catalyst in NH3 -SCR. Vanadium
was introduced by impregnation on the support (VWTi) or on the Ce-doped support using the
VO(CO2 )2 complex (prepared by reaction of V2 O5 powder with oxalic acid). SCR conditions: 500 ppm
NO, 500 ppm NH3 , 5% O2 and 4% H2 O. From [201].
BET Area
Ce3+ (%)
NO Conv.
N2 O
(m2 g−1 )
(from XPS Data)
at 250 ◦ C (%)
at 550 ◦ C (ppm)
VWTi
80
-
35
14
VCeWTi IMP
80
44
42
8
VCeWTi DP
83
53
67
5
Catalyst
The catalyst prepared by deposition–precipitation shows higher performances for the
NH3 -SCR reaction. This is not due to changes in the textural properties but to specific
properties of ceria, more reducible in VCeWTi DP. This catalyst also possesses more acidic
sites (mainly Lewis sites) associated with surface wolframyl and ceria species. Youn et al.
studied the role of the order of impregnation of vanadium and cerium–tungsten [202]. They
showed that vanadium impregnated first (CeW/V/Ti) gave better performances. Similar
topics were recently explored by Liu et al. [203], who demonstrated that the impregnation
sequence of W and Ce influence the NH3 adsorption capacity and the Ce3+ /(Ce4+ + Ce3+ )
ratio in correlation with catalytic results. Addition of copper to ceria (Cu-Ce-W-V/Ti)
reinforces the beneficial effect of ceria at low temperature [204].
The specific role of ceria on the sulfur resistance of V2 O5 -WO3 /TiO2 catalysts was
investigated by Liang et al. [205]. Ceria helps to improve DeNOx activity and sulfur
resistance. A 3% loading of ceria is optimal for better performances. Higher loadings
of ceria are detrimental: they provoke a decrease in surface area and partial covering of
vanadia by ceria. Complex formulae combining Ce and Mn doping were described by
Zhao et al. Ce and Mn coaddition confers excellent H2 O and SO2 resistance on V2 O5 WO3 /TiO2 catalysts [206]. SO2 is mainly adsorbed on Mn4+ and Ce4+ cations, making the
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active surface of V2 O5 -WO3 free. A multiplicity of valence states of the elements would be
beneficial to a high NO conversion. Additionally, codoping of Ce4+ and Zr4+ enhances the
tolerance to alkali metals of V2 O5 -WO3 /TiO2 catalysts, as K-poisoning resistance occurs by
blocking potassium in the form of Ce-O-K structure [207].
4.4.2. Ceria Added to WO3 /TiO2 (Without Vanadium)
A number of works were carried out on vanadium-free catalysts to better study the
interaction between ceria and tungsten and its role in the SCR reaction. Chen et al. prepared
CeO2 /TiO2 and CeO2 -WO3 /TiO2 catalysts by an ultrasonic method and investigated the
reactivity of adsorbed ammonia with NO + O2 by DRIFT [208]. Comparison of CeO2 /TiO2
and CeO2 /WO3 /TiO2 catalysts shows that tungsten has a dramatic effect on the SCR
reaction: (i) it allows conversion of NO at lower temperatures (50% conversion is reached
at 165 ◦ C on CeWTi instead of 225 ◦ C on CeTi); (ii) it increases the selectivity for N2 at high
temperature (less N2 O). Tungsten increases the number of Brønsted sites (virtually absent
on CeTi) and tends to accelerate the cerium reduction (more Ce3+ in CeWTi). Another report
by Chen et al. confirmed the important role of tungsten by increasing the oxidation activity
of NO to NO2 , allowing the catalyst to work in fast SCR conditions [209]. Interaction
between ceria and tungsta seems to play a decisive role in SCR activity and selectivity.
Geng et al. compared WTi and CeWTi catalysts and showed that ceria is effective for the
inhibition of N2 O formation when it is added to WO3 -TiO2 [210].
Great efforts were made in the last decade to improve the preparation of cerium-based
tungsten catalysts. Michalow-Mauke et al. developed a preparation method based on flamespray (FS) pyrolysis of Ce, W and Ti precursors in tetrahydrofuran [211,212]. Compared
to catalysts prepared by impregnation, catalysts prepared by FS synthesis show superior
performances. This is due to a better dispersion of ceria and tungsta and to a greater
interaction of these elements with titania leading to highly active Ce–O–W (especially Ce3+ –
O–W6+ ) and Ce–O–Ti sites [212]. The fact that FS synthesis mainly produces rutile instead
of anatase does not seem to hamper the performance of the catalysts prepared by this
technique. Sol–gel techniques were also used by Jiang et al. to prepare CeO2 -WO3 /TiO2
catalysts [213]. Butyl titanate was dissolved in a solution of ethanol/water/nitric acid and
then mixed with cerium nitrate and ammonium metatungstate. Different catalysts were
prepared with 10% WO3 and various loadings of ceria (from 0 to 40%). DeNOx activity of
these materials is visualized in Figure 18.
Figure 18. SCR activity of CexW10Ti catalysts prepared by a sol–gel method using butyl titanate as Ti
precursor. Effect of cerium loading on NO conversion. Reaction conditions: 1000 ppm NO, 1000 ppm
NH3 , 3% O2 . From Jiang et al. [213] with permission from Elsevier.
The catalyst with 20% CeO2 shows the best performance in NH3 -SCR. It has also a
good resistance to SO2 /H2 O when 500 ppm SO2 and 10% H2 O are added to the reactant
mixture. The same optimal composition (20% CeO2 ) had already been observed on a
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series of Cex W20 TiO2 catalysts prepared by homogeneous precipitation with urea aqueous
solution [214]. In every case, these CeO2 -WO3 -TiO2 catalysts show exceptional resistance
to SO2 .
Improved methods
of preparation of CeO2 -WO3 /TiO2 catalysts were recently re−δ
ported, either using H2 O2 as a promoter of active sites [215] or leading to 2D materials
(Ce0.184 W0.07 Ti0.748 O2−δ nanofibers prepared by electrospinning) [216]. H2 O2 modification
improves both the BET surface area and the number of Brønsted sites, while nanofibers
seem ideal for a good performance at low temperature owing to the formation of a great
number of oxygen vacancies. Salazar et al. investigated the method of impregnation of
Ce and W on TiO2 [217]. They showed that successive impregnation (with intermediary
calcinations) of Ce on W/Ti led to higher performances than when catalysts were prepared
by coimpregnation. Successive impregnation favors the formation of Ce-O-W bridges,
which play an essential role in the SCR reaction. No clear correlation was observed between
the SCR activity and the degree of Ce reduction or the number of Brønsted sites, even
though these parameters are probably important for a good DeNOx activity.
Monolithic catalysts were prepared and tested by Cao et al. [218]. A TiO2 -SiO2 powder
was mixed with aqueous solutions of ammonium paratungstate and cerium nitrate. Ammonia was added up to pH = 10 to form a slurry which was extruded, dried and calcined at
550 ◦ C. Silica was added to titania to increase its thermal stability. Excellent performances
were obtained, superior to those of powder catalysts especially at high temperatures.
4.4.3. Ceria Added to WO3 (Without Vanadia or Titania)
In order to avoid complex interactions between Ce, W, V and Ti, CeO2 -WO3 catalysts
were prepared and tested in NH3 -SCR. Zhang et al. compared the behavior of ceria
doped with various acid promoters: phosphotungstic, silicotungstic and phosphomolybdic
acids or ammonium sulfate [219]. Ceria doped with phosphotungstic (CeO2 -P-W) or
silicotungstic acid (CeO2 -Si-W) showed the highest NOx conversion (Figure 19). However,
CeO2 -P-W exhibited the best N2 selectivity over the whole temperature range, especially
at T > 450 ◦ C where N2 O could be formed.
Figure 19. NOx conversion over acid-promoted ceria catalyst. Ceria promoted by tungstic acids
is much more active (800 ppm NH3 + 800 ppm NO + 5% O2 , GHSV = 60,000 h−1 ). From Zhang
et al. [219] with permission from Elsevier.
The mode of preparation of ceria for the synthesis of P-W/CeO2 catalysts was further
investigated by Song et al. [220]. They compared hydrothermal (cerium nitrate + glucose
+ acrylic acid aged at 160 ◦ C in autoclave), sol–gel (cerium nitrate in citric acid) and
precipitation (cerium nitrate solution + ammonium carbonate) techniques. The P-W/CeO2
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catalyst with ceria prepared by hydrothermal technique gave the highest performances. It
combined the highest BET area, the highest Ce3+ concentration and an adequate balance
between Brønsted and Lewis acid sites. Wang et al. showed that the ceria morphology
(cubes, particles, rods) would have a great impact on the performance of W-CeO2 catalysts
for the NH3 -SCR reaction [221]. Ceria supports were prepared by hydrothermal methods
according to the synthesis procedures developed by Peng et al. [222]. Ceria nanorods
were prepared from cerium acetate, while nanoparticles and nanocubes were synthesized
using cerium nitrate. Nanocubes expose preferentially (100) planes while nanorods expose
both (110) and (100) planes. Contrasting with these surface structures, (111) planes are
essentially found with nanoparticles. Nanoparticles are more active than nanocubes and
nanorods for the NH3 -SCR reaction, which tends to prove that WO3 attached to (111) faces
of ceria gives the best performances for NOx abatement.
Modification of ceria by manganese shows that N2 O can be avoided by the incorporation of WO3 into the catalyst. Better performances, with a good SO2 and CO2 resistance,
were obtained with W0.1 Mn0.4 Ce0.5 composition [223]. One of the roles of ceria is to promote redox properties by oxygen mobility improvement. As cerium–zirconium oxides
have superior properties of reduction [194,224,225], it was logical to replace pure ceria with
cerium–zirconium oxides in the preparation of supported WO3 catalysts. These formulations were explored by Ning et al. [226]. Methods of preparation of CeO2 -ZrO2 -WO3 (CZW)
catalysts were similar to those developed by Song et al. for tungsten catalysts supported on
ceria [220]. Catalysts prepared by hydrothermal methods show the best performance for
the NH3 -SCR reaction. This is due to a higher tungsten dispersion and to the coexistence of
Brønsted and Lewis acid sites, while CZW catalysts prepared by other techniques possess
only Lewis sites. Acid properties of CeO2 -ZrO2 -WO3 catalysts are greatly influenced by the
state of tungsten oxide [227]. Moreover, the formation of amorphous W species resulted in
the abundance of Ce3+ and oxygen vacancies with a correlative increase in the NO oxidation
activity. Recently, great efforts were devoted to reinforcing the stability of SCR catalysts.
Liu et al. showed that doping WO3 /Ce0.68 Zr0.32 O2 with silica significantly improved the
thermal stability of the catalyst (10% H2 O, 800 ◦ C) [228]. Silica allows maintaining the
acidity of the catalyst after thermal treatment. Moreover, it inhibits the formation of cerium
tungstate Ce2 (WO4 )3 , which is detrimental to the catalyst performances. Similar effects
were obtained by doping the CeZrOx support with alumina in monolithic catalysts [229].
The Cex Zr1−x O2 composition also impacts the WO3 /Cex Zr1−x O2 behaviors. The characterization of 9% WO3 /Cex Zr1−x O2 catalysts with various ZrO2 weight ratios in Cex Zr1−x O2
(30%, 42%, 60% and 80%) indicated that the increase in the zirconium content enhanced
the acidity (number and strength of acidic sites). Accordingly, the NH3 -SCR activity also
increased [230]. Note that after WO3 addition, the basic NOx storage sites of Cex Zr1−x O2
were fully altered while the oxygen storage capacities (OSC) were dramatically decreased
for all samples.
4.5. Iron-Promoted WO3 Catalysts for NH3 -SCR
Iron catalysts being promising SCR catalysts, especially when Fe is inserted in zeolites [231], it was logical that researchers attempt to associate Fe and W for the DeNOx
reaction. Fe-W mixed oxides were studied for this application by Li et al. [232] and Wang
et al. [233]. Catalysts were prepared by ammonia precipitation of ammonium paratungstate
(APT) and iron nitrate [232], or by urea precipitation of ammonium metatungstate (AMT)
and iron nitrate [233], which may explain some differences in performances for the two
series of catalysts. Activity maximum was observed by Li et al. with the FeW5 sample (i.e.,
having a Fe/W molar ratio of 5), while the optimal performances were found by Wang et al.
for a Fe/W ratio of 3 (Fe0.75 W0.25 Ox sample). Location of acid sites would also be different:
B sites on tungsten (W-OH) and L sites on iron (Li et al.), or B sites on FeWO4 and L sites on
Fe2 O3 , i.e., Fe oxide not associated with tungsten (Wang et al.). In fact, Wang et al. proposed
that the good performances of Fe0.75 W0.25 Ox would be due to a fine interaction between
Fe2 O3 and FeWO4 with an easier electron transfer from W6+ sites to Fe3+ sites, which favors
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the formation of NO2 . Wang et al. also reported that their mixed oxide catalysts were
extremely resistant to SO2 poisoning, especially at high temperature (T > 300 ◦ C) [234].
Similar conclusions were reported for tungsten-free catalysts, where Fe0.1 V0.1 TiOx catalyst
showed the optimal NH3 -SCR performance and excellent SO2 resistance [174].
Direct impregnation of tungsten on hematite Fe2 O3 was reported by Liu et al. [235].
Hematite was first prepared by urea precipitation of Fe nitrate. The solid (dried and
calcined at 500 ◦ C) was then impregnated with ammonium metatungstate solution in
oxalic acid. Optimal performances were observed with the 5% WO3 /Fe2 O3 sample. The
reverse impregnation (iron on WO3 nanorods) was studied by Li et al. [236]. It is difficult
to compare the two methods of preparation. Nevertheless, both led to comparable DeNOx
activity with a 50% NO conversion around 275 ◦ C, even though the catalyst evaluation was
carried out in somewhat different conditions.
Iron–tungsten was also supported on zirconia [237] or cerium–zirconium oxide for
monolith preparation [238]. In absence of iron, supported tungsten shows a good ammonia
oxidation activity but virtually no SCR activity. The presence of iron is required to create
SCR catalysts whose activity is linked to the formation of Fe3+ Lewis sites. The main
role of these sites would be to promote NO oxidation to NO2 , the first step in the SCR
mechanism. These studies on ZrO2 and CeZrOx were carried out with relatively high
W loading (Fe/W molar ratio close to 1). Magnetic iron oxides doped with tungsten
and cerium were also prepared as SCR catalysts [239]. In these materials, iron is mainly
in the form of γ-Fe2 O3 and α-Fe2 O3 , but other forms can be present since W and Ce
tend to create highly dispersed iron species. Compared to previous catalysts synthesized
over zirconia or CeZrOx , higher iron loadings were used to prepare FeCeWOx catalyst
(most active material: Fe0.90 Ce0.05 W0.05 and Fe0.85 Ce0.10 W0.05 ). Copper being an active
component of SCR catalysts, it was tempting to promote iron catalysts with copper. Ma et al.
reported a one-pot preparation of Cu0.02 Fe0.2 Wx TiO2 materials (x varying from 0.01 to 0.03),
which were tested in the SCR reaction [240]. A moderate amount of tungsten significantly
improves stability and acid and redox properties, leading to superior performances for the
SCR reaction, even in the presence of water and SO2 (best formula: Cu0.02 Fe0.2 W0.02 TiO2 ).
Complex catalysts including several promoters (Fe, V, Mn, W, Ce) were also developed [241].
It appears that multiple redox pairs (Fe2+ /Fe3+ , V4+ /V5+ , Mn2+ -Mn3+ /Mn4+ ) would play
an important role in the reaction.
4.6. Manganese-Promoted WO3 Catalysts for NH3 -SCR
Titania-supported manganese tungstate catalysts were prepared by Kong et al. in
order to replace the standard V-W/TiO2 catalyst for the NH3 -SCR reaction [242]. The
solution combustion method with Mn, W and Ti precursors mixed with glycine is suitable
for preparing high-surface-area materials (up to 280 m2 g−1 ). Mn/TiO2 without W showed
a high activity at low temperature, which declined rapidly above 300 ◦ C. Tungsten allowed
enlarging the activity window up to 400 ◦ C. The highest performance was obtained with
the Mn0.1 W0.05 Ti0.85 O2−δ catalyst. Similar materials were reported by Shin et al. [243] and
Wang et al. [244]. In these studies, high tungsten contents were used (15% in [243] and
25% in [244]), which seems beneficial to improve the performance at low temperature. For
instance, Wang et al. obtained a 50% NO conversion at 40–50 ◦ C and 100% NO conversion
from 80 to 280 ◦ C over the W0.25 Mn0.25 Ti0.5 O2 catalyst. The role of tungsten is to facilitate
Mn redox capacity, leading to high concentration of Mn4+ and reactive oxygen species
(Figure 20).
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Figure 20. Characterization of Mn/TiO2 and W-Mn/TiO2 catalysts by XPS: Mn (a) and O (b)
photopeaks. Presence of tungsten favors Mn oxidation to Mn 4+ and formation of O reactive species
α
(Oα ). NO oxidation to NO2 is improved on W-Mn/TiO2 favoring the fast SCR reaction. From Wang
et al. [244] with permission from Elsevier.
Additionally, a study investigating the vanadium loss from V-W/TiO2 catalysts was
conducted in [245] and reports that manganese is the best candidate to make up for the
loss of SCR activity caused by the decrease in V2 O5 loading (50%), in opposition to other
transient metals as Nb, Co, Cr, Cu or Ce. Note that similar behaviors are denoted for
tungsten-free catalysts: Mn-loaded catalyst (Mn5 V1 Mo3 Ce7 /Ti) exhibits the optimal SCR
performance associated with a large number of acid sites and high redox properties [246].
Many studies were devoted to the promotion by cerium of manganese-based SCR
catalysts. Nie et al. investigated the effect of several acidic oxides (Nb2 O5 , WO3 and
MoO3 ) on the performance of MnOx -CeO2 catalysts [247]. NbCeTi and WCeTi are very
active at 200 ◦ C, while MoCeTi is active only at high temperature. WO3 -promoted catalyst
has the broadest operation window with significant NO conversion above 300 ◦ C. Ma
et al. investigated the effect of WO3 doping on the performances of MnOx -CeO2 catalysts
for the SCR reaction [223]. The concentration of manganese in ceria was kept constant
(Mn/Ce = 0.4) while the concentration of tungsten was varied from 0.03 to 0.2. Undoped
Mn0.4 Ce was active only at low temperature: its activity decreased sharply above 200 ◦ C.
WO3 -doped catalysts showed far better activity above 200 ◦ C, with an optimum for the
W0.1 Mn0.4 Ce sample. Mn0.4 Ce has only Lewis acid sites. Doping with tungsten generates
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Brønsted sites allowing activity at high temperature. Moreover, High SO2 resistance is
also achieved on W0.1 Mn0.4 Ce by suppression of SO2 oxidation activity. Promotion by
tin of MnOx -CeO2 support seems to favor low-temperature SCR activity [248]. High NO
conversion is obtained on the SnMnCeOx support (50% at 60 ◦ C but only 50% at 300 ◦ C).
Addition of tungsten shifts the conversion profile to higher temperatures with good activity
and excellent N2 selectivity up to 300 ◦ C.
In several studies by the group of Hong (South Korea), WMnCe-based catalysts were
supported on titania [249–251]. In the first two studies, WMnCeTi samples were prepared
by wet impregnation without any control of the pH, while in the third study, a strict control
of the pH between 2.8 and 1.7 was applied by addition of oxalic acid. Controlling the pH of
the slurry around 1.7 leads to catalysts more active for the NH3 -SCR. This result is linked
to the fact that an acidic pH increases the formation of surface Mn4+ and Ce3+ , while NO
would be less strongly adsorbed. A good synergetic effect was observed with zirconia
as support for manganese. Increasing the concentration of tungsten on MnZrOx allows
obtaining catalysts more active and more selective for N2 up to 400 ◦ C [252]. XPS results
and DRIFT studies on the most active catalyst (15%W/MnZrOx ) showed that the redox
cycle (Equation (7)) would promote the electron transfer between W and Mn, contributing
to NH3 activation.
Mn4+ − O2− −− W5+ ⇔ Mn3+ − O−2− − W6+
−
−
−
−
(7)
Developing active catalysts over a wide range of temperatures is a challenge for the
NH3 -SCR reaction. Combining two catalysts (MnOx -CeO2 /TiO2 (MnCeTi) and V2 O5 WO3 /TiO2 (VWTi)), Zhang et al. were able to obtain high NO conversion from 150 to
400 ◦ C [253]. The best configuration was obtained when VWTi was set at the fore part and
MnCeTi at the rear part of the catalyst bed (Figure 21, CC-B curve). MnCeTi is much more
active than VWTi for the NO oxidation reaction, allowing work in fast SCR conditions over
a wide range of temperatures. MnCeTi is also more active for the NH3 oxidation reaction,
which has a less detrimental effect in CC-B configuration (VWTi + MnCeTi).
Figure 21. Combination of MnOx -CeO2 /TiO2 (MnCeTi) and V2 O5 -WO3 /TiO2 (VWTi) catalysts
for the NH3 -SCR reaction. Configuration CC-A: MnCeTi first and then VWTi; configuration CC-B:
reverse position; configuration CC-C: physical mixture of the two catalysts. From Zhang et al. [253]
with permission from John Wiley and Sons.
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5. Other DeNOx Applications of WO3 -Doped Catalysts
5.1. Tungsten Catalysts for the NOx Trap–SCR Coupled System
One of the technologies for NOx abatement in diesel engine exhausts is the NOx trap
system, also called NOx storage reduction (NSR) or lean NOx trap (LNT) [254]. The catalyst
(typically Pt/BaO-Al2 O3 ) works according to a sequential operation: (i) during one or two
minutes, NOx from the exhaust gases is stored on the catalyst as nitrate and nitrite species;
(ii) during a few seconds, hydrocarbons are added to the exhaust gases for the reduction
step, and adsorbed nitrates and nitrites are reduced to N2 . However, some ammonia may
also be produced (ammonia slip), which should be eliminated on an ammonia oxidation
catalyst. An alternative solution would be to use this in situ produced ammonia on an
SCR catalyst to transform the residual NOx not yet converted. This is the NOx trap–SCR
coupled system [255]. Several studies considered the coupling of Pt-BaO-Al2 O3 (NSR
catalyst) with Cu-zeolites (SCR catalyst) [256–259] or with Fe-zeolites [260,261]. Can et al.
investigated the use of WO3 /CeZrOx (as SCR material) coupled to a usual Pt/BaO/Al2 O3
catalyst [230]. The effect of adding an SCR catalyst (WO3 /Ce0.58 Zr0.42 O2 ) downstream of
the NSR catalyst is depicted in Figure 22. SiC being inert for all the reactions, NSR + SiC
represents the performance of the NSR catalyst alone. The effect of adding an SCR catalyst
to the NSR material is clearly visible in the figure: more NOx is converted and more NH3
produced on the first bed is consumed. N2 O is never produced on the NSR catalyst alone or
on the coupled system NSR+SCR. In fact, a part of the ammonia produced on the NOx -trap
catalyst reacts with oxygen (NH3 oxidation reaction or SCO). Fortunately, both SCR and
SCO are selective for N2 on these materials.
Figure 22. Analyses of nitrogen-containing gases during lean/rich oscillations. The catalysts were
exposed to 500 ppm NO, 10% O2 , 10% H2 O and 10% CO2 during the lean period (60 s) and to 3% H2 ,
10% H2 O and 10% CO2 during the rich period (3 s). From Can et al. [230] with permission from the
American Chemical Society.
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Other tungsten catalysts (WO3 /Al0.2 Ce0.4 Ti0.4 , WO3 /Al0.2 Ce0.16 Zr0.32 Ti0.32 and WO3 /
Al0.1 Si0.1 Ce0.16 Zr0.32 Ti0.32 , selected among 30 formulations) were also tested in the NOx
trap–SCR coupled process [262]. Ammonia release and its use in oxidation (SCO) or
reduction (SCR) is shown in Figure 23 for four configurations of NOx trap–SCR coupled
systems. Configuration 4 with silica-containing SCR catalyst offers the best performances,
especially at 300 ◦ C. Presence of silica increases Lewis acidity and more strongly increases
Brønsted acidity, which can explain the good behavior of the Si-doped catalyst.
Figure 23. Ammonia release and use in SCO or SCR on different NOx trap–SCR systems. In
on corresponds
Configuration
every case, 1%Pt/10%BaO-Al2 O3 (Pt-BaAl) is used as NOx trap catalyst.
corre
to P
alone),
to
0.4
,
trap
alone),
to
Pt-BaAl
+
WO
/Al
Ce
Ti
,
to
Pt-BaAl
+
sponds to
Pt-BaAl
+
SiC
(NO
x
3
0.2
0.4 0.4
WO3 /Al0.2 Ce0.16 Zr0.32 Ti0.32 and to Pt-BaAl + WO3 /Al0.1 Si0.1 Ce0.16 Zr0.32 Ti0.32 . The catalysts were
exposed to the same lean/rich oscillations as in Figure 22. From Can et al. [262] with permission
from Elsevier.
5.2. Tungsten Catalysts for NOx Reduction by Other Reductants
5.2.1. Reduction by Hydrogen (H2 -SCR)
NOx reduction by hydrogen is well adapted to depollution of sites where hydrogen
is available (e.g., refineries, H2 plants) [263]. The authors of [263] investigated the H2 SCR over WOx -ZrCe (zirconium rich) and WOx -CeZr (cerium rich) catalysts. Reaction
conditions were 520 ppm NO + NO2 (NO/NO2 = 9), 5% O2 and 10% CO2 . The reaction
can be written as follows (Equation (8)):
NO + H2 →
1
N2 + H2 O
2
(8)
However, formation of nitrous oxide (Equation (9)) and undesired hydrogen oxidation
(Equation (10)) may be observed:
2NO + H2 → N2 O + H2 O
(9)
1
O2 → H2 O
(10)
2
Maximum activity is obtained at 250 ◦ C over WOx -CeZr and at 300 ◦ C over WOx -ZrCe.
The Zr-rich catalyst WOx -ZrCe shows better performances if the whole 150–600 ◦ C temperature range is considered. This could be due to a higher concentration of acid sites on
WOx -ZrCe than on WOx -CeZr (about twice). Selectivity for N2 is close to 80–90%, with
maximum formation of N2 O around 20 ppm over WOx -CeZr and 15 ppm over WOx -ZrCe.
Addition of 7% water slightly decreases the NOx conversion but improves the N2 selectivity.
H2 +
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Platinum is one of the most active metals for the NO reduction by H2 at low temperature [264–266]. Platinum activity and selectivity are extremely sensitive to the nature of
support. For instance, Pt/ZrO2 is superior to Pt-Al2 O3 (more active and more selective for
N2 ), and promotion by WO3 improves the performances of Pt/ZrO2 [267]. NO2 and nitrate
species are thought to be essential intermediates in the reaction [265]. However, other
authors found that NO adsorption and decomposition on Pt would be the most important
step of the reaction [268,269]. Maximum NO conversion is observed between 90 and 130 ◦ C.
Zhang et al. reported a NO conversion of 91% at 110 ◦ C over 0.1%Pt-1%W-HZSM-5 in
the following reaction conditions: 910 ppm NO + 90 ppm NO2 + 5000 ppm H2 + 10% O2 .
Tungsten oxide is thought to maintain Pt in the metallic state even in highly oxidizing
conditions. It suppresses NO2 adsorption on Pt and inhibits the formation of nitrate species.
It accelerates the dissociation of NO and H2 on Pt. The main drawback of H2 -SCR is the
lack of N2 selectivity due to ammonia formation. Platinum being a poor NH3 -SCR catalyst,
this ammonia cannot be used for increasing the selective conversion of NO to N2 . By
contrast, Pt-WO3 is an excellent catalyst for selective oxidation of NH3 (SCO), but only at
higher temperatures (250–300 ◦ C) [270]. Replacing Pt by Ru does not significantly improve
the SCO reaction at lower temperatures [271], which does not allow selective conversion of
ammonia formed in H2 -SCR.
5.2.2. Reduction by Ethanol (C2 H5 OH-SCR)
Alumina-supported silver catalysts are very active for the NOx reduction by oxygenated compounds, especially ethanol or acetone [272]. It seems that the formation of isocyanate species (-NCO) is a key step of the ethanol-SCR reaction over Ag/Al2 O3 [273,274]
even though many other species may be detected [275,276]. This remarkable activity of
silver catalysts for ethanol-SCR prompted Barreau et al. to imagine a combination between
Ag/Al2 O3 and a NH3 -SCR catalyst (WO3 /CeZrO2 ) using C2 H5 OH-NH3 mixture for NOx
reduction [277,278]. The effect of silver alone for the C2 H5 OH-SCR and for the C2 H5 OHNH3 -SCR and finally the effect of adding WO3 /CeZrO2 are illustrated in Figure 24.
Figure 24. NOx conversion and NH3 outlet concentration in C2 H5 OH-SCR (blue) and C2 H5 OH
+ NH3 -SCR (red) on 2%Ag/Al2 O3 and effect of adding 6%WO3 /Cex Zry O2 to Ag/Al2 O3 in the
C2 H5 OH + NH3 -SCR reaction (green). Mixture: 400 ppm NO + 1200 ppm C2 H5 OH + 400 ppm NH3
(when present) + 10% O2 + 10% CO2 + 8% H2 O. From [277] with permission from Elsevier.
Silver alumina alone possesses a significant activity for the ethanol-SCR reaction (blue
curve). The activity is enhanced by the presence of ammonia (red curve). In the dual
bed (Ag + W) system (green curve), an increased conversion of NOx is observed, and
simultaneously the outlet concentration of ammonia is decreased.
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The respective roles of Ag/Al2 O3 and WO3 /CeZrO2 in this complex reaction were
summarized in the review by Barreau et al. [279]. Figure 25 illustrates the reaction pathway identified in the ethanol-NH3 SCR reaction over the Ag/W dual bed. Note that
WO3 /CeZrO2 is then more suitable than a copper-exchanged zeolite (2.5% Cu–FER) as
an SCR catalyst. Despite a significantly higher ammonia conversion rate using the zeolite, NOx abatement is lower because ammonia and ethanol strongly interact together
on Cu2.5–FER [278].
Figure 25. Reaction pathway identified in the ethanol-NH3 SCR reaction over Ag/Al2 O3 + WO3 /CeZrOx
dual bed. Hydrogen species are key intermediates in the reduction of NO on Ag. The fast SCR is the
main reaction over WO3 /CeZrOx , but acetaldehyde formed over Ag tends to produce undesired
reactions. Oxidation of NH3 is observed at high temperature. Fortunately, this reaction is totally
selective for N2 over the tungsten catalyst. From Barreau et al. [279] with permission from Elsevier.
5.3. Conclusions
Tungsten-based catalysts are highly referenced as active samples in NOx reduction
abatement for a wide range of reducers or processes. Commonly used in V-W/TiO2
catalysts for NH3 -SCR application, WO3 is known to increase the activity, widen the
temperature window, improve the resistance to various poisons and lower ammonia
oxidation activity by O2 . Tungsten is also involved in V-O-V species formation by confining
vanadia in small clusters leading to oligomeric vanadia (V2 O5 ) sites, demonstrating higher
NH3 -SCR activity than monomeric vanadyl compounds. WO3 is also associated with ceria
as redox support, with or without vanadia or titania, for low-temperature activity and N2 O
limitation emission. Tungsten increases the number of Brønsted sites, favors the formation
of Ce-O-W bridges and tends to accelerate the cerium reduction.
6. Total Oxidation of Volatile Organic Compounds in Gas Phase and Gas Sensors
Owing to the multiple oxidation states of tungsten and rapid diffusion of surface
oxygen, WO3 is also a candidate for oxidation reaction in gas phase [280], VOC oxidation
(Section 6.1) and gas sensor application (Section 6.2).
6.1. VOC Oxidation in Gas Phase on Tungsten Catalysts
The first part of this section is focused on the non-photocatalyzed reactions. However,
WO3 is response-sensitive to light up to 480 nm, which also makes it a good candidate
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for photoassisted VOC oxidation (Section 6.1.2). Note that WO3 -based photacatalysts for
liquid phase applications are depicted in Section 7.
6.1.1. VOC Oxidation on Tungsten Catalysts (Non-Photocatalyzed Reactions)
Balzer et al. showed that WO3 alone (7.5 m2 g−1 ) can efficiently catalyze BTX oxidation [281]. The reactivity of the different hydrocarbons is as follows: benzene (T50 = 250 ◦ C)
> toluene (T50 = 340 ◦ C) > m-xylene (T50 = 420 ◦ C) ≈ p-xylene (T50 = 430 ◦ C). Oxidation
activity of WO3 is linked to the presence of W6+ , W5+ and W4+ surface species generating
reactive oxygen species.
However, WO3 is generally used in supported catalysts. Pansare et al. investigated NH3
and toluene decomposition on tungsten carbide (WC) and tungstated zirconia (WZ) [282].
Both WC and WZ catalysts were active for the simultaneous decomposition of NH3 and
toluene at 700 ◦ C in the presence of H2 , CO, CO2 and H2 O. Benzene is formed by steam
dealkylation of toluene. The WO3 -V2 O5 -TiO2 catalyst usually employed for NH3 -SCR reaction
(see Section 4) was proven to possess good oxidation activity for VOC abatement. Debecker
et al. studied the total oxidation of benzene and chlorobenzene on a catalyst containing 3%
WO3 (or MoO3 ) supported on titania variously loaded with vanadia (3 to 10% V2 O5 ) [283].
The main results of this study are summarized in Table 6.
Table 6. Total oxidation of benzene and chlorobenzene (CB) at 300 ◦ C on V2 O5 -TiO2 , 3%WO3 -V2 O5 TiO2 or 3%MoO3 -V2 O5 -TiO2 catalysts. Reaction conditions: 100 ppm benzene or chlorobenzene, 20%
O2 in He. VVH = 37,000 h−1 . Adapted from [283].
Benzene Conversion @ 300 ◦ C (%)
CB Conversion @ 300 ◦ C (%)
Vanadium Loading
3% V2 O5
5% V2 O5
10% V2 O5
10% V2 O5
No promoter
23
71
86
75
WO3 -promoted
34
77
98
93
MoO3 -promoted
43
83
95
93
Vanadium oxide was then the active phase for VOC oxidation. However, tungsten and
molybdenum oxides significantly increased V2 O5 activity. It is worth noting that promotion
by WO3 allowed reaching almost 100% conversion of benzene with the 10% V2 O5 catalyst.
WO3 and MoO3 promotion were also beneficial for chlorobenzene conversion, even though
total oxidation cannot be reached at 300 ◦ C. Benzene oxidation over WO3 -V2 O5 -TiO2
catalysts was also investigated by Lu et al. [284]. Traces of benzene (1–10 ppm) were treated
in a gas containing CO2 , CO, O2 and H2 O, simulating a flue gas issued from a methane
burner. HCl (50 ppm), SO2 (400 ppm), NO (300 ppm) and NH3 (360 ppm) were added
to simulate a waste incineration flue gas atmosphere. Due to the very low concentration
of benzene, its conversion was measured by resonance-enhanced multiphoton ionization
time-of-flight MS (REMPI-TOFMS), a technique well adapted to analyze minute traces
of hazardous air pollutants [285]. The most active catalyst was supported on a highsurface-area TiO2 (166 m2 g−1 , quasipure anatase) with a low loading of vanadia (0.8 wt.%)
promoted by 6 wt.% WO3 . About 80% of benzene could be eliminated with little variation
of efficiency when other pollutants (NO, NH3 , HCl, SO2 ) were present.
Other tungsten-based catalysts were employed for VOC abatement. For instance, magnesium tungstate (MgWO4 )-based catalysts were evaluated by Gancheva et al. in CO
and hydrocarbon oxidation [286]. Four catalysts were tested: pure MgWO4 (5.2 m2 g−1 ),
MgWO4– 3%WO3 (4.0 m2 g−1 ) and these materials promoted by 0.5% Pd. Without palladium,
pure MgWO4 was more active than the same support enriched in WO3 . With Pd-promoted
catalysts, two opposite behaviors were observed: MgWO4 /3%WO3 /0.5%Pd was the most
active catalyst in hydrocarbon combustion (toluene, n-hexane) while MgWO4 /0.5%Pd (with
no tungstate) was much more active for CO oxidation. Gancheva et al. proposed that CO and
HC would be activated on MgWO4 and WO3 by two different mechanisms depending on
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the nature of the reactant CO or HC. The role of palladium would be to favor O2 adsorption
and activation.
Catalytic abatement of trichloroethane (TCE) was performed on complex materials
consisting of W-Mo bronzes (W-Mo/Nb/V/P) [287]. The best performances were obtained
on the mixed W-Mo bronze with a W/Mo ratio close to 1. Complete composition (based on
W + Mo = 1) was Mo(0.54)/W(0.46)/Nb(0.41)/V(0.20)/P(0.08). A 50% decomposition of
TCE was achieved at 300 ◦ C on this material, while a reference zeolite (HMOR) gave 50%
conversion at 470 ◦ C. The performance of this bronze catalyst was linked to its acidity (B
sites only present on W-containing materials) and to its high oxygen mobility in the bulk,
as revealed by 16 O/18 O exchange.
Tungsten oxide is also a good promoter of diesel oxidation catalyst (DOC) allowing increasing activity of noble meta—alumina catalyst: a gain of 20 ◦ C on the light-off
conversion of HCs was attained with 1% WO3 on the reference PtPd/Al2 O3 catalyst [288].
For ambient air purification, the very mild operating conditions require the development of fine structures/morphologies to improve the number of surface oxygen vacancies.
With this aim, formaldehyde oxidation can be performed at room temperature by 1%
Pt-doped WO3 nanoflakes assembled into hollow microspheres (23 m2 g−1 ), in which
the porous architecture promotes diffusion and adsorption of HCHO [289]. However,
photoassisted catalysis appears more suitable for the very mild operating conditions.
6.1.2. WO3 -Based Photocatalysts for VOC Oxidation
WO3 -based materials as photocatalysts are mostly dedicated to reactions occurring
in liquid phase (Section 7, in which general information about WO3 -based photocatalysts
is provided). However, few recent studies reported that such catalysts also demonstrated
intersecting behaviors in gas phase, especially for ambient air purification. To overcome
drawbacks of bare WO3 , such as photocorrosion and unsuitable bandgap structure for the
reduction of molecular oxygen, improvement can be obtained by structure/morphology
control and/or doping. For instance, WO3 nanoparticles obtained by gas phase method
and annealing at 600 ◦ C were reported to be much more active than commercial WO3 in
acetaldehyde oxidation. Oxidation rate can be further significantly improved by addition
of ZrO2 , which acts as a sorbent for the acetic acid intermediate species to release the
WO3 surface. Moreover, Pt or Ru addition allowed the total mineralization into CO2 and
H2 O [290,291]. A physical mixture of WO3 and CeO2 also exhibited excellent photocatalytic activity in acetaldehyde oxidation, which was attributed to the electron scavenging
property of CeO2 aiding charge carrier separation [292]. WO3 can be also associated with
the other usual photocatalyst, namely TiO2 . To improve the visible light sensitivity of WO3
nanoparticles impregnated into a commercial TiO2 powder, Balayeva et al. successfully
added Fe(III) nanoclusters. The observed enhancement in acetaldehyde photooxidation
was then attributed to the promotion of multielectron reduction processes [293]. However,
Caudillo-Flores et al. pointed out that a cautious approach must be adopted when interpreting the results. They prepared TiO2 /WO3 samples with various W/Ti atomic ratios from 0
to 0.5, leading to various structures ranging from truly doped samples in which tungsten
was exclusively located in lattice positions of the anatase structure to composite catalysts
where nanosized tungsten species were supported over TiO2 . The authors highlighted that
both the reaction rate (in toluene and styrene photo-oxidation) and the apparent quantum
efficiency can lead to misleading results in terms of the most active TiO2 /WO3 sample(s) as
well as the (positive/negative) magnitude in comparison with bare titania reference [294].
Implementation of photocatalysts in building windows is of major interest in air
purification. Li et al. proposed a g-C3 N4 @Csx WO3 heterostructure as a coating for a
multifunctional smart window for UV-isolating, Vis-penetrating, NIR-shielding and photocatalytic activity. These composites display excellent formaldehyde and toluene decomposition properties. The shielded NIR light is used instead of wasted as heat, while the
C3 N4 @Csx WO3 structure promotes the separation of charge carriers and then enhances
photocatalytic oxidation. Moreover, the small polaron can jump from localized states to
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the conduction band of Csx WO3 under NIR irradiation (730–1100 nm), resulting in an
NIR-catalytic reduction [295]. Note that this kind of structure was also proposed as a
photocatalyst for water purification (see Sections 7.6.3 and 7.6.4).
6.2. Gas Sensors Using Tungsten-Based Catalytic Materials
Since the mid-1950s, gas sensors have experienced great development for environmental and safety applications. Gas sensors are based on the measurement of electrical
behaviors caused by chemical changes. Expected properties are sensibility, selectivity,
stability, repeatability and response time. To build low-cost sensors, the measurement of
the resistivity of heated semiconductor oxides is suitable thanks to the cost of raw materials
and the convenience of microelectronic integration. Details of the internal structure of
the sensors, including the heater, electrodes and external circuit, are out of the scope of
this review.
The sensing is related to changes in the electrical conductivity, which are mainly
attributable to changes in the oxygen concentration at the oxide surface. Many oxides
exhibit conductivity changes in presence of gases, but most of the commercialized sensors
are based on SnO2 , WO3 or ZnO. As reported in the recent review by Dong et al., a huge
number of works have been devoted to tungsten oxide based sensors [296]. Tungsten oxide
is sensitive to many gases such as O2 , O3 , CH4 , CO, H2 , NH3 , C3 H8 , NO, NO2 and H2 S, with
operating temperature in the 250–450 ◦ C range [297,298]. WO3 is an n-type oxide; i.e., the
adsorption of surface oxygen atoms form an electron depletion region (Equations (11)–(13)),
depending on the temperature of the material, leading to a potential barrier. Consequently,
the adsorption of an oxidizing gas increases the resistivity of WO3 [299,300].
O2 + e− → O2 − (low temperature)
(11)
O2 − + e− → 2O− (medium temperature)
(12)
O− + e− → O2− (high temperature)
(13)
The formation of oxygen anions (Equation (13)) should be avoided (via the temperature
control of the sensor) because of their tendency to be incorporated in the bulk of the material.
Recent studies about WO3 -based sensors are mainly dedicated to NO2 detection
(Section 6.2.1), but other gases are also considered (Section 6.2.2).
6.2.1. WO3 -Based Sensor for NO2 Detection
Since WO3 is an n-type semiconductor, NO2 adsorption leads to anionic adsorbates
on the surface of WO3 according to reaction (14):
NO2 (gas) + e− (from surface) ⇋ NO2−
(14)
Han and Yin performed density functional theory (DFT) calculations to study the adsorption characteristics and electron transfer of nitrogen dioxide on O- and WO-terminated
WO3 (001) surfaces with oxygen vacancies [301]. It was found that NO2 is (i) oxidized into
nitrate on the bridging oxygen atom from an oxygen defect of the O-terminated WO3 (001)
surface and (ii) dissociated on a WO-terminated (001) surface: one oxygen atom from NO2
fills the oxygen vacancy, and the resulting NO fragment is adsorbed onto a W atom. Both
of these adsorption models are responsible for an increase in the electrical resistance of
WO3 . In a very recent study, Yang et al. showed by in situ DRIFT spectroscopy that NO2
and NO exhibit similar interaction with the surface of tungsten oxide; both nitrogen oxides
were detected as oxidizing gases [302].
The structure/morphology of WO3 is a key factor in the sensor response, and this topic
is particularly developed in the recent literature. For instance, comparison of Ni-doped
WO3 nanowires and nanosheets shows that nanowires exhibited a rapid response time
(66 s) but a slow recovery time (204 s) due to a low NO2 desorption rate from the internal
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porous structure of nanowires. On the contrary, the recovery time over nanosheets was
shorter (126 s), thanks to a lower surface area and a less porous structure [303].
The effect of the structure on the sensor response for undoped WO3 was also evidenced
by Li et al. [304]. An enhancement of the gas sensing properties was obtained by the
formation of self-assembled hierarchical hollow spheres. Such structure enhances the
sensitivity to NO2 . At 140 ◦ C, a response was recorded for NO2 concentration of 18 ppb.
This was attributed to a high specific surface area (7 m2 g−1 ) and to a wide range of pore size
distribution (from 3 to 60 nm) that promotes the gas diffusion. Table 7 summarizes the latest
developments in the synthesis of controlled undoped WO3 structures for high-sensitivity
NO2 gas sensors (papers published in 2019–2020).
Table 7. Latest developments in the synthesis of controlled undoped WO3 structures for highsensitivity NO2 gas sensors (papers published in 2019–2020).
WO3 Structure/
Morphology
Detection Limit
@ Optimal T
Remarks
Ref.
Nanoparticles
(~40 nm)
100 ppb
@ 25–50 ◦ C
Ionic liquid-assisted synthesis,
samples calcined at 500 ◦ C for 2 h.
[305]
Microflowers
assembled from
nanoplates
125 ppb
@ 105 ◦ C
Outer diameters of ~2 µm,
composed of nanoplates with the
average pore size of 10.9 nm
[306]
Nanowire-assembled
WO3 nanomesh
50 ppb
@ 160 ◦ C
WO3 nanomesh, assembled from
single-crystalline WO3 nanowires
[307]
Nanowires (2 nm)
930 ppb
@ 100 ◦ C
Nanosheets
300 ppb
@ 100 ◦ C
Comparison of monoclinic,
triclinic and hexagonal WO3
nanosheets; best performances
obtained with triclinic WO3
[309]
Mesoporous WO3
60 ppb
@ 500 ◦ C
Diameter: 7 nm; specific surface
area: 209 m2 g−1 , prepared from
SBA-15 as the hard template
[310]
[308]
Improvement in NO2 detection can also be obtained by both tuning the tungsten
morphology and creating interactions with a support. For instance, Ma et al. showed that
tungsten oxide nanorods (diameters of 50–150 nm and lengths of 5–20 mm) supported on
porous silicon (PS) had a good response to NO2 and good recovery characteristics at room
temperature. The lowest detected NO2 concentration was 250 ppb [311]. The same authors
also synthesized nanowires with diameters of 20–30 nm and lengths of 1–2 µm which were
grown directly on the porous silicon through thermal annealing of tungsten film. The
sensor responded well to NO2 compared to other gases since the NO2 response was three
times higher for 2 ppm NO2 than for 50 ppm NH3 , 100 ppm ethanol or 100 ppm acetone
at 150 ◦ C [312]. Modulations of the potential barriers at both homo- and heterojunctions
between porous silicon and tungsten oxide were proposed to be responsible for the good
sensibility at a low operating temperature (100 ◦ C) [313]. Excellent gas-sensing behaviors
were obtained with n-WO3−x /n-PS nanocomposite prepared by sputtering tungsten oxide
films on a high specific surface area porous silicon substrate [314]. This sensor exhibited
an anomalistic p-type semiconducting behavior, which was supposed to improve the
amplification effect of the heterojunction between WO3 nanowires and the PS composites
(PS forms p–n heterointerface with n-type WO3 nanowires). The XPS analysis indicated
the presence of large amounts of surface oxygen vacancies that directly contributed to the
sensor response. NO2 concentration as low as 30 ppb was then detected, and Figure 26
illustrates that the NO2 selectivity vs. other gases was especially interesting. To improve
the control of the WO3 nanowire synthesis on silicon microelectromechanical systems
(MEMS), Lee et al. recently developed a fabrication process by stress-induced method, in
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which the growth position of the WO3 nanowires can be controlled by patterning of the
WO3 seed film [315]. Finally, note that competition between different gases may influence
the recovery time. For instance, WO3 film demonstrated a longer recovery time towards
NO2 compared to NH3 [316].
Figure 26. n-WO−3−x /n-porous silicon sensor responses to various gases at RT. From Li et al. [314]
with permission from Elsevier.
Doped WO3 sensors: Sensor improvement can also be obtained by WO3 doping. The
addition of precious metals to WO3 is performed to improve the gas–sensor interaction,
as well as the response and recovery times, and decrease the operating temperature.
Gold is the most represented metal in the recently reported works, probably because
Au-doped WO3 -based sensors exhibit overall enhancement in NO2 sensing performances
(response, detection limit and response/recovery times) [317,318] but also because they
are only slightly affected by humidity. In fact, measurement in a humid atmosphere is one
drawback of the semiconductor oxide-based sensors, and WO3 is no exception [319]. Water
adsorption leads to the oxidation of the WO3 lattice because water fills the oxygen vacancies
(operando DRIFT experiments), and consequently the resistance of the WO3 -based sensor
increases [320]. The selectivity of the sensor is then affected, with lower signals toward NO2
and higher sensor signals to CO. Sevastyanov et al. showed that water dependency can be
virtually avoided by gold addition in the bulk and on the surface of WO3 . The conductivity
in pure air of such Au/WO3 :Au material increased only 1.1–1.2 times when the absolute
humidity raised from 2 to 16 g m3 (it increases 6–7 times for Pt/SnO2 :Sb films in the same
humidity range). Measurements with 0.45–10 ppm NO2 showed that the Au/WO3 :Au
sensor response did not depend on humidity [321]. This behavior toward humidity was
confirmed on Au-WO3 core–shell-structured nanospheres, associated with excellent NO2
selectivity and long-term stability [322]. The significant performance improvement in NO2
detection of Au/WO3 compared to bare WO3 was attributed by Hang et al. to a combined
sensing mechanism: the surface Au nanoparticles dominated chemical sensitization while
interbedded Au nanoparticles induced electronic sensitization [323]. An activation of
Au/WO3 :Au thin films by laser diode radiation instead of constant heating was proposed
by Almaev et al. [324] to reduce the response time to NO2 by photodesorption. Moreover,
holes generated in the near-surface region of WO3 film by optical transitions were supposed
to favor the photodesorption of chemisorbed O2 - species, leading to the absence of response
to reducing gases and change in oxygen concentration.
Results obtained with platinum-doped WO3 appear possibly contradictory. Chmela
et al. reported that platinum addition to WO3 nanowires (<100 nm) caused detrimental
effects, with lower sensitivity and selectivity toward NO2 compared with the unfunction-
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alized systems, associated with better sensing properties toward C2 H5 OH [325]. On the
opposite, with nitrided WO3 (WOx Ny nanofibers), platinum addition enhanced the gas
sensing characteristics by (i) lowering the operating temperature; (ii) enhancing the sensor
reversibility at 50 ◦ C; and (iii) exhibiting an exceptional selectivity toward NO2 against
interfering molecules such as C2 H5 OH, C7 H8 , CH4 , CO, NH3 and NO [326].
Silver was also recently reported as a promising dopant. The optimal calcination
temperature was found at 500 ◦ C to obtain the larger response, better selectivity, faster response/recovery time and better long-term stability for NO2 [327]. With 0.5%Ag-WO3 [328],
the sensor shows higher NO2 sensing response at 200 ◦ C and higher selectivity for NO2 in
the presence of different interfering gases (NH3 , acetone, SO2 , methanol, CO2 , NO). Significant decreases in gas responses were observed with high silver loading (5 and 10 mol%)
because the silver crystallite size became too large and hindered their catalytic effects [329].
Comparing Ag-, Pd- and Pt-doped WO3 nanoplates, Li et al. showed that Pd-WO3
exhibited the highest response to NO2 while Ag-WO3 exhibited the fastest response
speed [330]. The promotional effect of palladium was attributed by Liu et al. to the
Schottky barrier between Pd and WO3 [331].
WO3 -based sensors doped with other oxides have attracted little attention in the
recent literature. Only a few recent studies report improvements of WO3 -based sensors
by doping with oxides such as Sn, Sb and Fe. The main characteristics of these studies
are summarized in Table 8. The observed improvements were generally attributed to an
increase in the oxygen vacancies on the sensing surface.
Table 8. Oxide-doped WO3 -based sensors for NO2 detection.
Sensor Material
Detection Limit
@ Optimal T
RuO2 /WO3 nanowires
Remarks
Ref.
Improved selectivity by enhancement of
the electron depletion layer due to the
formation of RuO2 /WO3 Schottky
junctions
[332]
(2014)
Fe-doped WO3 hollow
nanospheres.
10 ppb
@ 120 ◦ C
The light distortion in the WO3 crystal
lattice by Fe doping produced interesting
defects for gas sensing, with more
oxygen vacancies
[333]
(2018)
WO3 -In2 O3
nanocomposites
@ 140 ◦ C
Sol–gel preparation method; also active
for CO detection at 240 ◦ C
[334]
(2019)
@ 30 ◦ C
Improvement in NO2 detection
attributed to abundant structural defects
derived from Sb doping, reduced
bandgap and the 3D hierarchical
microstructure
[335]
(2018)
5 ppb NO2
@ 100 ◦ C
Optimal loading: 2 wt.% Sn; introduction
of Sn ions resulted in shorter response
and recovery times, attributed to the
increased number of oxygen vacancies on
the sensing surface
[336]
(2018)
3D hierarchical
structured Sb-doped
WO3
Sn-doped WO3
nanoplates
6.2.2. WO3 -Based Sensors for Detection of Gasses Other Than NO2
WO3 -based sensors were also investigated for the detection of gases other than NO2 .
With this aim, only a few studies have dealt with undoped WO3 . Nanostructured WO3 was
evaluated for H2 S [337] or Cl2 [338] detection, while thin film was found to be sensitive to
acetone [339]. However, for this latest gas, a comparative study showed that SnO2 is the
best thin film compared to tungsten oxide or tin-doped tungsten oxide [340].
As described in Section 6.2.1, water adsorption on semiconductor oxides usually
affects the measurements. However, this behavior can be used to develop sensors for
relative humidity measurement. With this aim, WO3 is usually associated with TiO2
in the recently published studies. Zanettia et al. examined the influence of the WO3
loading (0–10 mol%) on nanopowdered samples prepared by the polymeric precursor
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method [341]. Best results in humidity measurements (in the 15–85% relative humidity
range) were obtained with 2 mol% WO3 . This was attributed to the best compromise
between the increase in acid sites and the mean pore size and pore size distribution. Faia
et al. studied the influence of V2 O5 doping for TiO2 -WO3 sensors [342]. A p- to n-type
transition still occurred for the doped sensors with the lower V2 O5 content, while the
sensor with the higher V2 O5 content exhibited a typical n-type behavior with humidity
increase. In addition, the electrical response to the relative humidity (10–100%) depended
on the changes in the fabrication route (sintering temperature), which influences the final
structure.
Section 6.2.1 also shows that NO2 detection can be improved by the addition of precious metals to WO3 -based sensors. Nevertheless, these modifications are rather dedicated
to the detection of reductant gases such as NH3 , H2 , H2 S and CO.
Palladium–WO3 samples were prepared by spray pyrolysis by Gobole et al. The
optimal palladium loading was found to be 3 wt.% Pd in WO3 for the detection of NO2 ,
SO2 and NH3 at 100, 200 and 225 ◦ C, respectively. For all of the studied gases, the response
and recovery times for concentrations up to 750 ppm were fast, in the ranges of 0.5–1.25 s
and 1–6.7 s respectively [343]. Tungsten trioxide nanowires decorated with iridium oxide
nanoparticles resulted in remarkable changes in the morphology and defects of tungsten
oxide nanowires. Such a sensor was found to be sensitive towards ethanol, NH3 , H2 , H2 S
and NO2 [344]. Tungsten oxide functionalized with gold or platinum nanoparticles was
synthesized by Vallejos et al. using a single-step method via aerosol-assisted chemical vapor
deposition. The metal additions allow the discrimination of C2 H5 OH, H2 and CO gases,
which are present in proton-exchange fuel cells. Particularly, Pt-functionalized tungsten
oxide films allow H2 detection at 250 ◦ C, whereas nonfunctionalized tungsten oxide films
detected low CO concentration (100 ppm) at a lower temperature (150 ◦ C) [345]. Platinum–
tungsten oxide can also be used to improve the CO electro-oxidation activity employed
in the electrochemical sensor [346]. The interaction between platinum and tungsten oxide
was enhanced by a reductive heat treatment, leading to a significant negative shift in CO
oxidation potential. A portable CO sensor device built with Pt/WOx /C exhibited a higher
sensitivity, faster response time and good linearity within 50 ppm CO, compared with a
usual Pt/C-based sensor.
Xu et al. showed that triethylamine vapor is efficiently detected by Ag/Pt/W18 O49
hybrid nanowire sensor, with a detection limit of 71 ppb. The ternary hybrid showed
better behavior in detecting triethylamine than the binary Ag/W18 O49 and Pt/W18 O49
nanowires [347]. This excellent performance was attributed to the dual sensitization
mechanism, i.e., a synergy of both electronic and chemical interactions.
Pt-catalyst-loaded tungsten oxide is also a good candidate for optical hydrogen gas
sensor applications due to its gasochromic behavior (Pt/WO3 turns blue in H2 atmosphere
while its electrical conductivity also changes). Yamaguchi et al. investigated the influence of
partial pressures of hydrogen and oxygen gases on a Pt/WO3 -based sensor prepared by a
sol–gel method [348]. Unfortunately, the optical absorbance of the film exhibited a nonlinear
relationship with the H2 concentration in absence of oxygen. However, the absorbance and
electrical conductivity increased proportionally with the H2 concentration in presence of
oxygen, but both parameters strongly depended on the oxygen partial pressure. According
to the relationship between the gasochromism and the oxygen concentration, the authors
demonstrated that Pt/WO3 is able to detect hydrogen gas concentrations in a low oxygen
gas concentration atmosphere.
6.3. Conclusions
In summary, WO3 is active in catalytic or photocatalytic oxidation of volatile organic
compounds. Catalytic oxidation activity of WO3 is linked to the presence of W6+ , W5+
and W4+ surface species generating reactive oxygen compounds. In supported catalysts,
tungsten oxides promote the activity of the V2 O5 active phase. Many pollutants are reported
in studies considering the catalytic abatement of VOCs, such as formaldehyde, hexane,
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trichloroethane, chlorobenzene, benzene, toluene and xylene. W-based samples are also
largely studied for gas sensors, mainly in NO2 detection. WO3 is an n-type semiconductor,
and its electrical conductivity varies with the oxygen concentration at the oxide surface.
In addition, great recent efforts have been made in the development of the synthesis of
controlled WO3 structure/morphology for high-sensitivity gas sensors.
7. Pollutant Remediation in Liquid Phase (Photocatalysis)
The use of WO3 -based catalyst for pollutant remediation in liquid phase mainly
concerns the oxidation of organic compounds via photocatalytic processes. Only a
few recent studies have dealt with WO3 -based catalysts for non-photocatalytic application, such as H2 O2 electrogeneration over WO2.72 /Vulcan XC72 gas diffusion electrode [349], hydrolysis of waste bottle PET in supercritical CO2 assisted by acidic catalysis over WO3 -TiO2 [350] or heavy metal ion adsorption on inorganic–organic hybrid
WOx –ethylenediamine nanowires [351]. However, this section is focused on the main use
of tungsten-based catalysts in liquid phase, namely photocatalysis.
Compared to TiO2 , which responds only to UV light, WO3 is visible-light-responsive.
The bandgap between the valence band (VB) and the conduction band (CB) is 2.6–2.8 eV.
However, bare WO3 is not very active due to the fast recombination of photogenerated
electrons and holes. Fortunately, the photocatalytic activity of WO3 can be improved in
five main ways: (i) the control of the WO3 structure/morphology to obtain nanoporous
structures with large surface area and fast pollutant diffusion; (ii) surface hybridization
with graphene to obtain large specific surface areas and improvement in the charge transfer; (iii) coupling with other semiconductors (TiO2 ) to enhance the photoinduced charge
separation efficiency; (iv) doping by noble metal, which works as an electron pool and
catalyzes O2 activation.
WO3 as a photocatalyst has been the subject of three recent reviews (“WO3 -based
photocatalysts: morphology control, activity enhancement and multifunctional applications” by Dong et al. (2017) [352]; “Adsorptive removal and photocatalytic degradation
of organic pollutants using metal oxides and their composites: A comprehensive review”
by Gusain et al. (2019) [353]; “Tungsten oxide-based visible light-driven photocatalysts:
crystal and electronic structures and strategies for photocatalytic efficiency enhancement”
by Quan et al. (2020) [354]). Consequently, the section is mainly focused on the more recent
studies. Evaluated molecules are mainly dyes, but other organics that are of major interest
for water treatment are also considered, such as active molecules (medicinal and plant
protection products) or pathogens.
7.1. Undoped WO3 Photocatalysts
As previously introduced, bare WO3 is poorly active as a photocatalyst, but structured/hierarchized WO3 exhibits interesting behaviors. Monoclinic WO3 phase was often
reported as a suitable structure for photocatalysis. Noticeably, Xie et al. showed in 2012 that
monoclinic WO3 exhibits preferentially the suitable high-surface-energy {002} facet [355].
Indeed, the simple thermodecomposition of H2 WO4 leads first to the cubic phase, but
the monoclinic structure is formed with increasing time and/or temperature. After 30
min at 450 ◦ C, the resulting WO3 oxide shows 90% monoclinic phase [356]. The phase
transformation is associated with a decrease in the specific surface area and an increase
in oxygen vacancies. The electron transport is then improved, favoring the photocatalytic
activity (ibuprofen removal by ozonation under visible-light radiation).
Various preparation methods have been developed to improve the WO3 photocatalyst.
Chen et al. evaluated different fuels (glycine, urea, urea and citric acid) to synthesize
nanoscale tungsten oxides (nanoparticles, nanorods and nanoneedles) by the solution combustion synthesis method. Monoclinic WO3 was obtained with urea, while a mixture of
monoclinic W18 O49 and WO3 structures was obtained with glycine when the molar ratio
glycine/ammonium paratungstate was 10 or higher. Such W18 O49 + WO3 mixture was
also obtained with improved porosity using a mixture of urea and citric acid because the
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reactants generated more gases and the combustion reaction was more vigorous (production
of larger holes). Accordingly, this sample exhibited the best activity in methylene blue
degradation [357]. Nanoparticles of monoclinic WO3 can be also synthesized from Na2 WO4
and PVP 70,000 (polyvinylpyrrolidone) as surfactant and template [358]. The synthesis was
carried out at 180 ◦ C in a Teflon autoclave. The best morphology for the photocatalytic
efficiency in degradation of rhodamine B (RhB) under visible light was the block-shaped
morphology. The authors proposed that the high photocatalytic efficiency could be attributable to the reducing activity of PVP which led to the formation of oxygen vacancies,
beneficial for the capture of photoelectrons and the generation of superoxide radicals.
Monoclinic WO3 nanoplates (100–170 nm in side length and 30–50 nm in thickness)
can be also obtained by a one-step template-free hydrothermal route, from a mixture of
aqueous solutions of Na2 WO4 · and HCl maintained at 180 ◦ C for 12 h in an autoclave [359].
The optimal calcination set-up was found to be 600 ◦ C for 2 h. The resulting catalyst
allowed the degradation of rhodamine B with an activity 5 times higher than that of a
commercial WO3 powder. It was proposed that the high concentration of -OH species was
responsible for the enhancement of photocatalysis.
However, the superiority of the monoclinic phase has been questioned very recently by
Zhang et al. [360]. They studied the photocatalyzed degradation of rhodamine B (RhB) over
monoclinic (m-WO3 ) and hexagonal (h-WO3 ) tungsten oxide. Samples were synthesized
via acid precipitation process and decomposition of H2 WO4 at different temperatures in air
or N2 to obtain oxidized or partially reduced oxidation states. After irradiation, the RhB removal efficiency classification was as follows: m-WO3 (22%) < m-WO3−x (48%) < h-WO3−x
(76%) ≤ h-WO3 (80%). It is important to note that the specific surface areas of the hexagonal
samples (52–55 m2 g−1 ) were approximately twice those of m-WO3 . It also appeared that
the impact of the oxidation state of tungsten was more significant for the monoclinic phase
than for the hexagonal one. In fact, the impact of the hexagonal/monoclinic-WO3 ratio
(h/m) in the photocatalytic activity was clearly pointed out by Lu et al. [361]. To tune the
h/m ratio, they used a sol–gel preparation method with K2 SO4 as stabilizing agent and
controlled calcination time and temperature. The observed optimal h/m ratio was close to
70/30, for which the activity in rhodamine B degradation was multiplied by a factor of 7.4
compared to pure m-WO3 . This improvement was attributed to the formation of a phase
junction between h-WO3 and m-WO3 , which exhibits high efficiency for the separation and
transfer of photoexcited electron–hole pairs (electrochemical impedance measurements).
New innovative designs are also a way to produce efficient WO3 photocatalysts. For
instance, monoclinic nanocuboids, synthesized by hydrothermal treatment of commercial
WO3 with H2 O2 , showed high amounts of coordinative unsaturated W sites suitable for
the photocatalytic degradation of methylene blue [362]. Other morphologies such as diskshaped WO3 (D-WO3 , monoclinic phase) were recently reported as attractive for acetic
acid mineralization (after 0.1% Pt addition). To obtain such samples, aqueous solution of
(NH4 )10 W12 O41 · was mixed with HNO3 at 75 ◦ C. After maturation, the resulting powder
was calcined 3 h at various temperatures to vary the physical properties. As expected, the
crystallinity of D-WO3 increased with the calcination temperature while the specific surface
area decreased. The highest photocatalytic activity was obtained with the sample calcined
at 600 ◦ C [363]. Another recent approach was to design a single tungsten atom oxide
photocatalyst, supported on poly(ethylene oxide), as shown in Figure 27a [364]. In this
case, the photogenerated electron transfer process is enabled by an electron in the spin-up
channel excited from the highest occupied molecular orbital to the lowest unoccupied
molecular orbital +1 state, which can only occur with single tungsten atom oxide with W5+
(Figure 27b). The resulting catalyst exhibited a degradation rate of 0.24 s−1 for dyes (methyl
orange, methyl red, dimethyl yellow; mechanism illustrated in Figure 27c for methyl
orange), which is two orders of magnitude higher than those of available photocatalysts.
Additionally, the reactions between oxygen with photogenerated electrons (e− + O2ads
→ O2 − •) and between adsorbed water and photogenerated holes (h+ + H2 Oads → H+ +
OHads •) produce reactive oxidizing species such as superoxide anions (O2 − •), hydrogen
−
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→
−
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→
−
peroxide (H2 O2 ) and hydroxyl radicals (OH•). Reactive oxidizing species are responsible
for the degradation of aqueous organic compounds, besides the direct decomposition of
organic compounds with photogenerated holes.
Figure 27. (a) A Cs-corrected STEM-HAADF image showing monodispersed single tungsten atoms.
(b) TD-DFT calculated the occupations and transitions between states in W6+ (left part) and separately
↑ spins.
↓ Dashed lines connect spin-up and -down channels
in W5+ (middle part). Arrows ↑ and ↓ denote
in the same band. The HOMO, LUMO and LUMO+1 bands for W5+ have been decomposed (right
part) according to the tungsten atomic orbitals. (c) Photocatalytic degradation reaction (methyl
orange): upon photoexcitation, the hole dissociates an H2 O into H+ and ·OH. The electron⋅ cleaves a
C-N bond in the azo-benzenesulfonic group. The resulting H+ then reacts with 4-(2λ2-diazenyl)-N,Nλ
⋅
dimethylaniline (green) to form N,N-dimethylaniline, while the ·OH reacts with benzenesulfonic
acid radical (blue) to form p-hydroxy benzene sulfonic acid. From [364] with permission from John
Wiley and Sons.
It is important to note here that dye decolorization and mineralization have to be
distinguished. This point is highlighted for instance in the paper of Cheng et al. about the
treatment of effluent from oil palm agroindustry with tungsten oxide photocatalysts [365].
With the optimum catalyst loading (at 0.5 g/L), the decolorization reached 96.2% but the
mineralization reached only 51.1%.
To improve the efficiency of treatment by photocatalysis, tungsten oxide can be also
used as a photoelectrocatalyst, i.e., implemented at the surface of a photoanode. The idea
is to promote the photoelectron transfer to dissolved oxygen, which is a drawback of
WO3 photocatalysis. To enhance charge separation, electrochemical and photocatalytic
techniques can be used together. Zheng et al. synthetized nanoporous, monoclinic WO3
photoanodes from a tungsten foil (0.1 mm thickness) that was anodized at 50 V in 0.25 wt.%
HF electrolyte and subsequently annealed at 500 ◦ C. It was showed that methyl orange
mineralization rate was higher in photoelectrocatalysis (at E = 1 V vs. SCE in NaH2 PO4
electrolyte) than in photocatalysis or electrocatalysis [366], as illustrated in Figure 28. The
high efficiency of the WO3 photoelectrocatalyst was also demonstrated for the abatement
of pathogens such as Escherichia coli [367].
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Figure 28. Methyl orange degradation rate by different processes. Experimental set-up: nanoporous
−
lamp), oxidation potential of 1 V
monoclinic WO3 anode, irradiating intensity of 0.1 W cm−2 (xenon
vs. SCE (NaH2 PO4 electrolyte). From Zheng et al. [366] with permission from Elsevier.
7.2. WO3 –Carbon Photocatalysts
As previously mentioned, the fast electron–hole recombination is a major drawback
of WO3 for photocatalysis application. In addition to the synthesis of structured WO3
with controlled morphology, another way to improve the photocatalysis efficiency is to
associate WO3 with carbon-based materials that exhibit interesting high specific surface
areas. Among the various possible structures of carbon-based materials, graphene appears
the most popular. Preparation of WO3 –graphene composite can be performed by different
methods. Recent studies reported techniques such as the electrospinning technique to
obtain a porous tungsten oxide nanoframework with graphene film [368]; a one-pot synthesis, first mixing sodium tungstate and nitric acid and then adding tetraphenylporphyrinn,
graphene and citric acid (final calcination in the 350–550 ◦ C temperature range) [369]; or
a method based on pulsed laser ablation in liquid phase: WO3 nanoparticles suspended
in water were mixed with a suspension of monolayer graphene and irradiated for 30
min by the pulsed laser beam of 355 nm. During the laser irradiation, the photoinduced
electrons in the WO3 reduced graphene, and WO3 nanoparticles were anchored on the
graphene sheets [370].
The synthesized film reported in [368] showed the ability to adsorb aromatic molecules,
extensive light absorption range, significant light trapping and efficient charge carrier
separation properties. Consequently, this sample allowed a high activity in the photodegradation of rhodamine B compared to bare WO3 and TiO2 nanomaterials.
The in situ prepared nanocomposites made of tetraphenylporphyrin/WO3 /reduced
graphene [369] showed specific surface areas around 450 m2 g−1 and spherically shaped
nanoparticles of monoclinic WO3 when the appropriate tetraphenylporphyrin loading
and calcination temperature of 350 ◦ C were used. The visible radiation absorption was
confirmed with a bandgap energy of 2.14 eV. The photocatalytic degradation rate of 20 ppm
Acid Blue 25 was 85% in 3 h at pH = 4 (UV–Vis and TOC analyses). This behavior was
attributed to the visible-light absorption properties and to the high separation rate of photogenerated charge carriers. Similar conclusions were obtained with the samples prepared
by the pulsed laser ablation evaluated in methyl blue degradation [370]: WO3 -reduced
graphene samples showed much better visible-light absorption and less photogenerated
charge recombination than pure WO3 .
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Other carbon-based materials were also recently developed. Amorphous carboncoated tungsten oxide was obtained via pyrolysis of hybrid polyoxometalates (hybrid
POMs) in nitrogen atmosphere [371]. Compositions, microstructures and concentrations
of oxygen vacancies were closely related to the species of organic amines in the hybrid
POMs. The presence of defects (oxygen vacancy) was responsible for the improvement in
the degradation of dyes (methylene blue, methyl orange and rhodamine B) compared with
WO3 or TiO2 photocatalysts.
WO3 /carbon nanotube (CNT) nanocomposites were proposed by Isari et al. for the
abatement of tetracycline (antibiotic) and other pharmaceutical wastes in water [372]. Samples were synthesized via a sol–gel method (aqueous sodium tungstate + lactic acid + CNT+
HCl; the obtained gel was then transferred in an autoclave for 30 h at 190 ◦ C). The characterization techniques demonstrated the incorporation of CNTs into the WO3 framework and
an efficient reduction in charge carrier recombination rate compared to the corresponding
WO3 catalyst without CNT. The pollutant remediation was performed coupling visible
light and ultrasound (US) irradiations (sono-photocatalysis). Ultrasonic irradiation favors
HO• formation, mainly via water decomposition. It was found that 60 mg/L tetracycline
could be perfectly degraded with the following set-up: WO3 /CNT: 0.7 g L−1 ; pH = 9; US
power: 250 W m−2 ; light intensity: 120 W m−2 ; duration: 60 min. Trapping experiment
results verified that HO• radicals and h(+) were the main oxidative species.
7.3. WO3 Photocatalysts Doped by Precious Metals or Silver
As previously mentioned, the restricted application of tungsten oxide (WO3 ) is due
to its low conduction band. Tungsten trioxide (WO3 ) is an n-type semiconductor with
a small bandgap (Eg 2.6–2.8 eV). Consequently, WO3 has a limited ability to react with
electron acceptors such as oxygen and has a high recombination rate of the photogenerated
electron–hole pairs. Therefore, great attention has been paid to develop novel visible-lightdriven WO3 -based photocatalysts, and special attention has been paid to the crystal facet
engineering of WO3 nanocrystals (Section 7.1). Additionally, doping with noble metal
(Section 7.3.1) or silver (Section 7.3.2) is an effective way to enhance the absorption of sunlight and improve the photocatalytic efficiency together with material phase/morphology
design to generate oxygen vacancies.
7.3.1. WO3 Photocatalysts Doped by Precious Metals
Abe et al. [373] proposed the enhancement of photocatalytic properties of WO3 by
loading Pt, which can trap electrons photogenerated from WO3 . The use of Pt as an electron
scavenger on WO3 nanorods was also investigated in [374]. Platinum nanoparticles were
loaded on WO3 nanorods with various mass ratios (0.1, 0.2 and 0.3) via a photoreduction
process (PRP). The photocatalytic activity in aerobic oxidation of alcohols reached up to 98%
for Pt/WO3 and 69% for WO3 , while no oxidation was observed in the absence of light. The
highest photocatalytic performance was obtained for the mass ratio of 0.2. This enhancement in the photocatalytic activity after platinum loading was attributed to an extended
lifetime of the generated electron–hole pairs compared to WO3 support. Additionally,
Gunji et al. [375] reported the importance of controlling the metal deposition site on the
photocatalyst surfaces to optimize the use of the photoexcited electrons and holes without
the recombination of photogenerated carriers during the photochemical decomposition of
organic pollutants. The authors proposed a cocatalyst based on the site-selective deposition
of PtPb nanoparticles on oxidation sites and deposition of Pt nanoparticles on reduction
sites. The synthesized PtPb/Pt/WO3 exhibited higher photocatalytic performance for the
decomposition of acetic acid under visible-light irradiation (λ > 420 nm) than that observed
using the conventional photodeposited Pt/WO3 or chemically deposited PtPb/WO3 .
Platinum doping was also evaluated on tungsten trioxide for catalyzed oxidation
reaction [289] or as an electrode for direct methanol fuel cells (DMFCs) [376]. Pt/WO3
catalyst layers were prepared by electrosynthesis of WO3 on a graphite (Gr) support. It
was reported that the corresponding Pt/WO3 /Gr electrode has higher catalytic activity for
λ
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methanol oxidation than a commercial Pt/C catalyst. Interestingly, methanol oxidation is
enhanced under visible-light illumination, which is attributed to both a synergy between
Pt and WO3 active sites and the simultaneous occurrence of methanol photooxidation at
WO3 sites.
7.3.2. WO3 Photocatalysts Doped by Silver
The surface plasmon resonance (SPR) effect greatly contributes to enhancing the
visible-light absorbance of catalysts by allowing resonant photons at the metal–dielectric
interface to resist the restoring force of positive nuclei [377]. The SPR effect of silver was
investigated by Ding et al. [378]. By studying the relationships between the locations of
silver nanoparticles on different facets of hexagonal WO3 nanorods and the photocatalytic
performance of the photocatalyst, Ding et al. reported that both the intrinsic nature of
charge separation on the {001} facets of WO3 -110 nanorods and the SPR effect contribute to
the enhancement of visible-light absorption and the decrease in the recombination of the
photogenerated electron−hole
− pairs. The highest efficiency in the degradation of methyl
orange (MO) was obtained with 4.5 wt.% Ag/WO3 photocatalyst presenting dominant
exposed {001} facets compared to {100} or {010} ones. A mechanism was proposed where
photons are absorbed under visible-light irradiation and photogenerated electrons and
holes are subsequently produced by a facet surface transfer, as summarized in Figure 29.
Figure 29. Possible degradation mechanism of MO over 4.5 wt.% Ag/WO3 photocatalyst under
visible-light irradiation. From [378] with permission from the American Chemical Society.
The crucial role of oxygen defects was investigated by Wei et al. [379]. Tungsten
oxide (WO3−X ) is a transition metal oxide that has rich substoichiometric compositions and
possesses oxygen defects involved in photon–electron interactions. In combination with
silver nanowires (Ag NWs) presenting surface plasmon resonance properties, the incident
photon-to-electron conversion efficiency is enhanced together with the methylene blue
(MB) photodegradation performance. In fact, the electron concentration in WO3−X depends
mainly on the stoichiometric defect concentration. This means that oxygen deficiencies
play a critical role in the decay of localized SPR phenomena.
Morphology and properties of Ag-WO3 hierarchical materials were also investigated
by Capeli et al. [380] for the degradation of rhodamine B (RhB) dye under 467 nm LED light
irradiation. Three-dimensional WO3 catalysts decorated with silver nanoparticles (Ag NPs)
−
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were prepared by a one-step hydrothermal method in the absence of surfactant (WO3 •Ag).
The amount
of Ag NPs is an important factor in the formation of various novel and
complex WO3 3D hierarchical architectures, from 3D irregular-platelet-like building blocks,
which evolve into 3D hexagonal building blocks, to three-dimensional hexagonal-footballlike and finally to 3D multibranched spiky ball-like microcrystals. The WO3 •0.20Ag 3D
hierarchical
structure presented higher photodegradation of RhB dye solution compared to
the individual WO3 3D material. This result was assigned to an engineering heterojunction
between Ag NPs and WO3 semiconductor, which could enhance the light absorption (more
photoexcited electrons) and suppress the photogenerated electron–hole pair recombination.
Ag NPs act as an electron reservoir. Under light, photogenerated electrons (e– ) in the
valence band (VB) are excited to the conduction band (CB), and electrons from the reservoir
on the Ag NPs could be trapped by O2 molecules to generate superoxide radical (•O2 – )
species. Concurrently, a similar number of holes (h+ ) are generated in the valence band
(VB), which are able to react with H2 O or OH– molecules to generate OH• radicals. Similar
results were achieved by Gao et al. [381], who used silver to improve the properties
of the WO3 . Ag nanoparticles (Ag NPs) were reported to enhance the production of
negative oxygen ions (•O2 – radicals) under visible light by the prepared Ag/WO3 catalysts
supported on wood. More precisely, Ag NPs redistribute the charge carriers, which could
trap the photogenerated electrons and inhibit the recombination of excited electrons and
holes (Figure 30).
Figure 30. Schematic illustration of the mechanism of negative oxygen ion production upon the
Ag/WO3 –wood. From [381] with permission from Elsevier.
Promising plasmonic Ag/AgCl photocatalysts have been recently investigated. The
SPR effect of silver is responsible for the broadened absorption in the visible-light region, and these properties were expanded to WO3 . For instance, Ma et al. [382] prepared
Ag–AgCl/WO3 hollow spheres with a flowerlike structure that had superior visible photocatalytic activity because of their unique morphology. Adhikari et al. [383] also observed a
photocatalytic activity enhancement of Ag/AgCl/WO3 powder prepared by a microwaveassisted hydrothermal method. However, most WO3 /Ag/AgCl photocatalysts reported
were in powder form, thus having limited use in practical applications because tedious
regeneration is required. Consequently, Fang et al. [384] prepared WO3 /Ag/AgCl films on
a conventional glass substrate to reduce the regeneration cost. The WO3 film was prepared
on a glass substrate by calcination of spin-coated W precursor. Ag/AgCl particles were
then deposited on WO3 film by an impregnation–precipitation–photoreduction method.
Excellent photocatalytic performances were obtained in the degradation of methyl orange
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(MO) and rhodamine B (RhB) under visible light. It is proposed that Ag and AgCl greatly
promoted the separation of photogenerated electron–hole pairs and improved the charge
transfer efficiency of WO3 . Based on the photoelectrochemical test and radical trapping
measurement, a Z-scheme mechanism for WO3 /Ag/AgCl is proposed where •O2 – and
h+ play the major roles in photodegradation, while the effect of OH• could be neglected
(Figure 31a). Consequently, Z-scheme composite photocatalysts have to be considered as
an effective way to enhance the photocatalytic performance of catalysts. Li et al. [385] proposed plasmonic Ag/Ag2 WO4 /WO3 Z-scheme visible-light composite photocatalyst for
the degradation of rhodamine B, methylene blue and methyl orange. A possible Z-scheme
mechanism of the ternary composite was proposed under visible light where Ag particles
produce SPR effect but also work as the charge transmission bridge (Figure 31b).
Figure 31. (a) The possible photocatalytic mechanism of organic pollutant degradation on
WO3 /Ag/AgCl film under visible-light illumination. From [383] with permission from Elsevier.
(b) Schematic illustrating the proposed photocatalytic mechanism over the Ag/β-Ag2 WO4 /WO3
photocatalyst. From [385] with permission from Elsevier.
Sahoo et al. [386] designed a Z-scheme WO3−X -Ag-ZnCr layered double hydroxide
(LDH) photocatalyst for tetracycline degradation, based on the SPR effect of metallic Ag as
redox electron mediator. The defects created by surface oxygen vacancy in WO3−X and the
existence of Ag as electron transfer conductor facilitate the charge pair separation efficiency
and enhance the photocatalytic activity.
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7.4. WO3 –TiO2 -Based Photocatalysts
Because of the poor activity of WO3 due to its rapid electron–hole recombination,
coupling with other semiconductors to use the sunlight as a free light source is an attractive
research area. Concomitantly, titanium dioxide (TiO2 ) is an interesting material for applications in the purification of air and water by removal of recalcitrant organic and inorganic
pollutants such as synthetic dyes, phenols and chlorophenols, volatile organic compounds,
detergents, solvents, heavy metals or pharmaceutical antibiotics.
Unfortunately, due to the size of TiO2 bandgap (Eg 3.0–3.2 eV), bare TiO2 only works
in conjunction with irradiation of limited wavelength (λirr < 385 nm) corresponding to
ultraviolet (UV) light that accounts for only 6.8% of the solar spectrum, thus limiting its
photocatalytic activity. The visible (Vis) range (400–760 nm) accounts for about 38.9%, and
infrared radiation (IR, 760–3000 nm) makes up most of the remaining 54.3% [387]. In addition to the ability of materials to absorb solar spectrum, the effectiveness of photocatalytic
systems also depends on the sample capacity to separately collect photogenerated electrons
and holes. The high electron–hole recombination rate limits the photocatalytic performance
of bare TiO2 . Consequently, several approaches were devoted to improving the photocatalytic performance of titania, especially by coupling with other semiconductors. The
objective is to increase the separation of charge carriers by doping titania with metal oxide
presenting both conducting band (CB) and valance band (VB) of higher or equal energy
compared to TiO2 . Among the many possibilities, the addition of crystalline tungsten
oxide (WO3 ) has interesting advantages. Its shorter bandgap (Eg 2.6–2.8 eV) compared
to TiO2 (Eg 3.0–3.2 eV) requires longer wavelengths for the excitation and extends the
photoresponse of TiO2 to the visible light region. The coupling with WO3 also induces
energy levels enabling the electrons photogenerated in the conducting band of TiO2 to
transfer into the CB of WO3 . Consequently, the photopromoted holes can diffuse from the
CB of WO3 into the valence band of TiO2 . The surface acidity of the TiO2 catalyst can also
be increased by adding WO3 , which facilitates the adsorption of OH− or H2 O molecules
and targeted molecules on TiO2 and thereby improves the photocatalytic activity of TiO2 .
WO3 –TiO2 combination also induces dark activity due to the energy storage ability of
tungsten oxide.
WO3 –TiO2 -based systems exist as (i) tungsten oxide doping of supported or hybrid
materials (Section 7.4.1) and (ii) metal doping of WO3 –TiO2 materials (Section 7.4.2).
7.4.1. WO3 –TiO2 -Based Systems as Supported and Composite Photocatalysts
The photocatalytic activity of a WO3 –TiO2 system is largely determined by its structure,
which is significantly influenced by the preparation method of the catalyst. Consequently,
both WO3 supported (WO3 /TiO2 ) and composite (TiO2 /WO3 ) materials are described.
Supported photocatalysts. Dyes such as methylene blue, rhodamine B or methyl orange
are often chosen as model pollutants, but the degradation of several other contaminants
has also been evaluated. For instance, Gao et al. [388] obtained WO3 /TiO2 material with
high surface area and unique morphology by synthesizing heterostructured photocatalysts
from wood fibers through a two-step hydrothermal method and a calcination process.
The wood fibers acted as carbon substrates, allowing the recombination probability of
photoexcited charge carriers to be reduced, and also increased the transport of charges.
It results in high performance of the WO3 /TiO2 –wood fibers as a UV-light or a visiblelight photocatalyst for degradation of rhodamine B, methylene blue, methyl orange or
phenol. Ding et al. [389] also observed a photoinduced electron–hole separation effect over
tungsten oxide (WO3 )/TiO2 core–shell nanowires for the degradation of rhodamine B. The
degradation of RhB was also undertaken over WO3 /TiO2 and MoO3 /TiO2 composites [390].
The reduction of the electron–hole recombination rate by coupling TiO2 with tungsten
oxide or molybdenum oxide led to high photocatalytic activity. The 5 wt.% WO3 /TiO2
composite was the more efficient sample due to the more efficient separation of charge
carriers. The electron migration from the conduction band (CB) of TiO2 to the WO3 CB can
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be offset by O2 and produces superoxide radical (O2 •) and hydrogen peroxide (H2 O2 ) and
finally hydroxyl radical (OH•) to decompose RhB (Figure 32).
Figure 32. Proposed mechanism of dye degradation in visible light by WO3 /TiO2 composite.
From [390] with permission from Elsevier.
Yang et al. [391] synthesized porous WO3 /TiO2 hollow microspheres by a spray drying
method. The authors observed that the tungsten oxides mainly existed in a highly dispersed
amorphous form on anatase when the loading amount of tungsten oxide was below 3 mol%.
The improved photocatalytic activity in methylene blue and phenol photodegradation
under UV-light irradiation over the WO3 /TiO2 catalyst mainly arises from the enhanced
charge separation efficiency provided by the acidity induced by WO3 addition, rather than
the improved light absorbance by highly dispersed amorphous tungsten oxides.
WO3 /TiO2 materials, designed as nanocomposites, mixed oxides or supported photocatalysts, were also used to degrade malathion pesticide [392], imazapyr [393], sulfamethoxazole [394] or formic acid [395]. For instance, 2% WO3 /TiO2 prepared by sol–gel method
showed excellent photocatalytic performance, achieving complete malathion degradation
after 2 h [392]. Synthesis of mesoporous WO3 –TiO2 nanocomposites presented interesting
behavior for imazapyr herbicide degradation under visible light and UV illumination. The
overall photocatalytic efficiency of the 3% WO3 –TiO2 nanocomposite was 3.5 higher than
for mesoporous TiO2 [393]. The WO3 –TiO2 nanocomposite showed both monoclinic and
triclinic WO3 structures. Tungsten-promoted composite catalysts were also envisaged by
Ioannidou et al. [394]. Experiments showed that the 4% W-TiO2 catalyst calcined at 700 ◦ C
was the most active for sulfamethoxazole degradation (350 µg/L) under simulated solar
irradiation, enhancing the rate of pristine TiO2 by 50%. Tungsten is believed to act as a
trap of electrons, thus reducing the rate of electron–hole recombination and, consequently,
increasing degradation rates. The addition of electron acceptors, such as hydrogen peroxide and sodium persulfate, in the reaction mixture also improved the catalyst activity.
Photoactivity of WO3 –TiO2 mixed oxides prepared by a sol–gel method was tested under
UV–visible irradiation in both the mineralization of formic acid in aqueous suspension and
the gas phase oxidation of acetaldehyde [395]. The catalyst containing a 3% W/Ti molar
ratio gave the best results, due to the formation of an intimately mixed oxide resulting
in a better charge separation due to the migration of photoproduced holes from WO3 to
TiO2 . WO3 supported samples were also synthesized using liquid phase plasma process for
degradation of diethyl phthalate [396]. The best degradation performance was observed for
bare TiO2 photocatalyst under UV light source, but modified TiO2 photocatalysts showed
a 1.7–6.2 times higher degradation rate under blue light.
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Composite photocatalysts. Composite (or hybrid) TiO2 /WO3 materials are another
strategy to obtain an enhancement in the photon absorption and a dark activity due to both
the storage of photogenerated electrons and a redox process. Khan et al. [397] prepared
microsized hybrid TiO2 /WO3 samples (TWx; x is 0.025, 0.5, 0.075, 0.1 molar ratio of W
precursor) by sol–gel and crash precipitation methods followed by spray drying. Evaluated
in the photocatalytic degradation of methylene blue (MB), the hybrid TW0.075 was reported
as the most active material, with 90% of dye degradation reached in 100 min with dark runs.
It was reported that TiO2 and WO3 acted in synergy to increase the lifetime of electron–hole
pairs and to decrease the recombination rate by electron diffusion from CB of TiO2 to WO3 .
The authors proposed a mechanism for the transfer pathways of the photogenerated charge
carriers in the hybrid powders (TWx) (Figure 33) where both hydroxyl radicals (OH•) and
superoxide anions (O2 – ) play a major role.
Figure 33. Proposed mechanism illustrating the transfer pathways of the produced charge carriers
and various oxidizing species contributing to the degradation of MB. From [397] with permission
from Elsevier.
TiO2 /WO3 systems (TW) were also studied by Rimaldi et al. for ethanol and tetracycline (TC) degradation [398]. Analyses supported the parallel occurrence of several TC
degradation pathways in the case of TW samples in which OH• radicals are involved,
as previously mentioned in [397] for MB conversion. TiO2 -WO3 composites were also
evaluated for bisphenol A (BPA) oxidation under simulated solar light [399]. A core–shell
system composed of a layer of TiO2 nanoparticles on the surface of WO3 nanowires was
also evaluated as an effective photocatalyst in the degradation of RhB [389]. Again, the
photoinduced electron–hole separation effect between WO3 and TiO2 contributed to the
improvement of the photocatalytic activity.
WO3 -TiO2 photocatalytic systems can be also associated with other processes to obtain
overall improvements. With the aim to associate photocatalysis with electrochemistry, WO3
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was associated with a TiO2 nanotube array to obtain a photoanode designed to improve
photoelectrocatalytic (PEC) performance for the degradation of methylene blue [400]. A
synergistic vacancy-induced self-doping effect and localized surface plasmon resonance
(LSPR) effect were observed, confirming the importance of oxygen vacancies in improving
PEC performance.
WO3 –TiO2 -based catalysts were also evaluated for photocatalytic-assisted ozonation
of pollutants. A 4% WO3 /titanate nanotube composite catalyst allowed the complete
removal of emerging contaminants such as caffeine, metoprolol and ibuprofen in municipal
wastewater in less than 40 min with TOC removal up to 64% after 2 h. Compared to bare
TiO2 , WO3 addition induced a higher activity under visible-light radiation and an increase
in the adsorption capacity of organic compounds [401].
7.4.2. Metal-Doped WO3 –TiO2 -Doped Systems
To decrease the fast electron–hole recombination and improve the interfacial charge
transfer process of WO3 –TiO2 materials, the addition of noble metals or heteropolyoxometallates (POMs) has been successfully explored.
Noble metals act as a sink of conduction band photoinduced electrons, avoiding their
recombination and enhancing the photocatalytic process. Thus, TiO2 –WO3 –Au systems
were evaluated by several authors. X-ray diffraction (XRD) data and Raman spectroscopy
measurements usually indicated that TiO2 is mainly in anatase structure, while the WO3
can be amorphous or crystallized. Gold nanoparticles improve the material’s response
in the visible domain [402]. Kovács et al. [403,404] studied the structural peculiarities
of TiO2 /WO3 /Au materials. It was shown that each minor structural change in bulk or
surface has a significant impact on the photocatalytic activity and intermediate formation
dynamics, using phenol as a model pollutant. However, the gold deposition mode was
found crucial over structural peculiarities, especially for W species. The resulting sample
presented three WO3 forms in different proportions: amorphous, crystalline and doped.
These forms manifested in different species (W6+ , W4+ , Wdefects ), which critically influenced
the activity and the intermediate formation during the photodegradation. Consequently,
gold-containing samples resulted in a modification of structural particularities, but the
correlation between structural features and PCA or intermediate formation was strongly
dependant on the synthesis pathway [404].
Platinum addition is reported to enhance the electron storage ability, the visible
activity and the electron–hole separation of photocatalysts by the creation of Schottky-type
junctions, thus facilitating the charge transfer at the catalyst–environment interface [405].
By varying the platinum amount from 0.2 to 1 wt.% in Pt/TiO2 -WO3 materials prepared
through the spray drying method, the optimum amount for the degradation of methylene
blue (MB) was found at 0.8 wt.% Pt. Hydrogen peroxide (H2 O2 ) and hydroxyl radicals
(OH•) were found as the main species responsible for the aqueous degradation of the
model pollutant. TiO2 maintained its tetragonal anatase phase and WO3 maintained its
monoclinic structure. The corresponding Pt0.8 TW sample presented the lowest electron–
hole recombination rate (photoluminescence measurements) and the highest amount of
surface hydroxyl groups (FTIR experiments).
The use of heteropolyoxometallates (POMs) is another interesting way to decrease the
fast electron–hole recombination on TiO2 . POMs act as effective traps of photoinduced
electrons, leading to visible-light-absorbing materials with high photocatalytic activity.
Tungstosilicic acid (TSA; H4 SiW12 O40 ) was successfully used by Rengifo-Herrera et al. [406]
to obtain the formation of a surface complex between the Keggin structure of TSA and
the TiO2 surface, or the formation of Keggin–TSA/TiO2 composites. It resulted in visiblelight absorption of modified catalysts. The photocatalytic activity in the degradation
of 4-chlorophenol depends on the TSA amount. FT-IR and FT-Raman characterizations
indicated that the main heteropolyoxometallate species presented in the composites was
the [SiW12 O40 ]4− anion, which exhibited a strong interaction with the TiO2 surface.
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7.5. WO3 Associated with Transition Metal Oxides Other Than TiO2 (Zn, Fe, Sn, Mn, Ni, Mo, Co, Nb)
In view of photocatalytic activity enhancement of WO3 catalysts, doped materials
have attracted much attention, and the present section focuses on the modification of
tungsten(VI) oxide by transition metal oxides (MOs). In fact, by coupling WO3 with
another semiconductor, an improvement of charge separation in photoinduced charge
transfer processes of n-type semiconductor is expected, leading to a drop in electron–hole
(e− /h+ ) pair recombination and an increase in photocatalytic activities.
7.5.1. ZnO–WO3
Among the multitude of oxides considered, zinc receives great attention owing to its
high light sensitivity and wide bandgap energy (3.37 eV). However, the photocatalytic
activity of zinc oxide is limited to the ultraviolet light range of the solar energy spectrum,
representing only 5–7% of the total sunlight energy. Another limitation is the rapid recombination of the electron–hole (e− /h+ ) cavity. To overcome these issues, surface modification
of the structures of the ZnO nanoparticles has been proposed. The aim is to alter the
bandgap energy, thus shifting the absorption band to the visible region in semiconductor
systems. Doping ZnO by WO3 enables the electrons produced from ZnO to be trapped,
thus preventing the fast recombination of electron–hole pairs and increasing the photocatalytic activity. WO3 has the advantage of narrow bandgap energy (2.2–2.8 eV), which
could activate the zinc oxide. Such ZnO-WO3 materials can act as good candidates for
the degradation of Direct Blue 15 (DB15) or methylene blue (MB) dye, organophosphorus
pesticides such as diazinon, diclofenac and bacterial or fungal strains.
Zinc oxide nanoparticles doped with 0.5% to 2% WO3 were synthesized by hydrothermal method to obtain samples where W was added into ZnO structure [407]. Photocatalytic
activity for diazinon removal was reported to reach 99% for 2% WO3 -doped ZnO catalyst
after 180 min of contact time. This result was attributed to a reduction in the network
constant. Similar tungsten oxide doped ZnO nanoparticles were evaluated in the photocatalytic degradation of Direct Blue 15 [408]. Numerous parameters, namely pH, light
intensity, dopant percentage, dye concentration and contact time, affect the process. It
appeared that acidic pH resulted in higher efficiencies of the photocatalytic process. In
addition, increasing the concentration of the WO3 dopant percentage from 1 to 5% w/v increased the degradation rate from 30.7 to 73.1%. Tungsten acted as a recombinant mediator
of interfacial charge transfer, which resulted in a change in the photocatalytic efficiency
of the doped ZnO. Sajjad et al. [409] revealed that the formation of Zn-O-W linkage was
responsible for a redshift of the absorption peak to the visible region, resulting in a lower
bandgap and a promotion of the separation of photogenerated carriers. In fact, the proposed energy state configuration showed dissimilar locations of conduction and valence
bands of both semiconductor oxides in ZnO/WO3 composites. Due to a narrowing of the
bandgap, the charge separation is facilitated and the rate of recombination is significantly
reduced, resulting in improved photodegradation efficiency. In addition, the transfer of
charge carriers due to the narrow bandgap can be confirmed by OH• radical measurement
as proposed by Mugunthan et al. [410] for the degradation of diclofenac with ZnO-WO3
mixed oxide catalysts. Authors observed higher hydroxyl radical (OH•) generation when
coupling ZnO and WO3 compared to bare ZnO. The benefit of the coupled system is mainly
due to optimal loading of WO3 since good dispersion of WO3 in coupled oxides promotes
the formation of heterojunction structures between the two coupled oxides. The optimal
molar ratio of Zn:W = 10:1 was found for the degradation of diclofenac.
Photocatalytic activity of Zn-doped WO3 (Zn-d-WO3 ) nanoparticles for antifungal
and antibacterial degradation was studied by Arshad et al. [411]. Zn loading from 0.1 to
0.3% had a significant impact on both antibacterial/antifungal photocatalytic degradation
and structural/morphological properties. Characterizations showed that the Zn-d-WO3
structure was triclinic, the particle shape was a mix of spheres and rods and the particle
size was decreased as the Zn concentration increased from 0.1 to 0.3%. Photocatalytic
activity of Zn-WO3 was evaluated in methylene blue (MB) dye degradation. Again, Zn
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loading impacted the activity. The maximum dye degradation rate was achieved with
Zn(0.3%)-WO3 sample, at 78% and 92% with 120 min of contact time for visible and UV
irradiation, respectively. Again, it was proposed that after the generation of electron–hole
pairs (e− /h+ ), the electronic vacancies or holes in the valence band are promoted due to the
migration of electrons from the valence band to the conduction band. As a consequence,
electron–hole pairs generate hydroxyl radicals (OH•) and superoxide ions (•O2 – ) that act
as powerful oxidizing agents to mineralize the dye into CO2 and H2 O.
Novel Pd/ZnWO4 nanocomposite materials for photocatalytic degradation of atrazine
were evaluated by Al-Amshany et al. [412]. Photocatalytic activity of ZnWO4 was highly
affected by the insertion of Pd into the composition. Palladium was reported to replace W
in the ZnWO4 lattice leading to a sample presenting low bandgap, low electron–hole pair
(e− /h+ ) recombination rate and high BET surface area. Consequently, high photocatalytic
activity for atrazine degradation was obtained for 1.65 wt.% Pd/ZnWO4 nanocomposite,
with 100% of degradation after 60 min of reaction time.
7.5.2. MO–WO3 (MO: Metal Oxides = Fe, Sn, Mn, Ni, Mo, Co)
Other transition metal oxides such as Fe, Sn, Mn, Ni, Mo and Co were evaluated in the
past few years to improve the photocatalytic activity of WO3 . Metal oxides act as electron
sinks to capture the photoinduced electrons through their low energy trapping sites; they
then reduce the electron–hole recombination and enhance charge separation.
Fe2 O3 is a visible-light-driven material with a bandgap energy of 2.0–2.3 eV and a
CB of 0.46–0.77 eV. Wang et al. [413] proposed a new active FeWO4 /Fe2 O3 di-modified
WO3 for the degradation of methylene blue (MB), toluidine blue (TB), azure I (AI) and
acridine orange (AO) under visible-light irradiation. Beneficially, Fe2+ , which is classically
involved in the Fenton reaction favors the generation of OH• radicals and subsequent
organic dye degradation. Over FeWO4 /Fe2 O3 -modified WO3 sample, FeWO4 and Fe2 O3
acted as electron traps. Consequently, a valence decrease of Fe3+ to Fe2+ led to the capture
of photoexcited electrons of WO3 and enabled the Fenton reaction in the presence of
trace H2 O2 . Consequently, di-modified WO3 samples showed high photocatalytic activity
compared to bare WO3 . This assisted Fenton process was also described by Mwangl Ngigi
et al. [414] for photocatalytic degradation of Methylparaben (MeP) over Fe-doped WO3
nanoparticles in presence of H2 O2 . The best formulation was 5 wt.% Fe-WO3, with 50.8%
MeP degradation in the presence of H2 O2 . A hydroxyl radical mechanism was advanced
to explain the efficiency and enhancement of iron-doped WO3 on visible-light activity of
the organic pollutant removal.
SnO2 is also used for bandgap tuning of nanomaterials to transform UV-light-active
catalysts into visible-light-driven catalysts. Nevertheless, tin dioxide has a wider bandgap
of 3.6 eV (UV-light-driven catalyst) with a high recombination rate of its photogenerated
electron–hole pairs, which limits its use. These drawbacks can be overcome by tungsten
doping to serve as a photogenerated charge trap, thus decreasing the recombination rate of
e− /h+ pairs by the reduction of the bandgap. In this way, Ullah et al. [415] reported that
tungsten-doped SnO2 (W@SnO2 ) nanospheres can be a preferred choice for visible light
photocatalytic degradation compared to standard TiO2 (Degussa-P25). With the increase in
the W content from 0 to 6 mol %, the bandgap of SnO2 was tuned from 3.6 to 2.8 eV, and the
degradation of crystal violet dye reached 100% after 40 min of contact time.
The formation of a nanocomposite of WO3 with manganese oxides is also a way to
reduce the bandgap of tungsten oxide. The constitution of composite with Mn, indigo dye
and reduced graphene oxide (RGO) was investigated by Ahmad et al. [416] as visible light
photocatalyst for methylene blue (MB) dye removal. A synergetic association between
WO3 and RGO was observed which increased the rate of charge transfer and limited the
recombination of electron–hole pairs in the nanosized composite. As a consequence, the socalled Mn/indigo/RGO/WO3 presented improved photocatalytic performance compared
to Mn/indigo/WO3 .
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Well-crystalline NiO-WO3 nanoparticles were synthesized by Rosaline et al. [417] for
the photocatalytic degradation of eosin yellow (EY) dye. A photocatalytic degradation rate
of 95% was obtained after 180 min under visible-light irradiation. The authors proposed
that photogenerated electrons of NiO possibly migrate into the conduction band of WO3 .
Simultaneously, the holes move in the opposite direction, which greatly decreases the
recombination of electron–hole pairs.
Mo-doped WO3 nanowires for adsorbing methylene blue (MB) dye from wastewater
were evaluated by Silveira et al. [418]. Samples presented hexagonal structure (h-WO3 ),
and the Mo doping led to a change in morphology of h-WO3 nanowires from large bundles
to narrow bundles when Mo loading increased from 4 to 15 at %. In fact, Mo6+ and W6+ have
similar ionic radii and electron structures, which enables Mo to directly incorporate the
crystalline lattice of WO3 to form a Mox W1−x O3 structure. As a consequence, the bandgap
of WO3 can be reduced by substituting W by Mo in order to improve the photocatalytic
activity with visible light, as demonstrated in [419]. In addition, Mo-doped WO3 samples
also exhibited a considerable improvement in MB adsorption capacity [418].
The reduction in electron and hole recombination of WO3 can also occur with nanocomposites of cobalt(II, III) oxide and tungsten(VI) oxide. The synthesis of p–n heterojunction
catalysts, such as Co3 O4 /WO3 , was claimed to enhance the photoactivity under UV- or
visible-light radiation [420]. The strong reduction in photoexcited electrons and holes
resulted in the enhancement in diclofenac sodium degradation. The highest degradation
efficiency was obtained for 0.02 M of cobalt acetate (CW2), with 98.7% achieved for the
degradation of 15 ppm diclofenac sodium at pH 10.7. Higher generation of hydroxyl
radicals (OH•) associated with the enhancement of effective charge separation was still
advanced to explain the high photocatalytic activity of the CW2 sample. Figure 34 shows
the charge transfer proposed by Malefane et al. [420] and the p–n heterojunction formed to
minimize photoexcited electron and hole recombination in CW2 nanocomposite.
Figure 34. Proposed degradation mechanism in Co3 O4 /WO3 p–n heterojunction. From [420] with
permission from Elsevier.
7.6. WO3 Associated with Other Systems (Post-Transition Metal Oxides and Metalloids, Rare
Earths, Nitrides)
7.6.1. Post-Transition Metal or Metalloid–WO3 Systems
Among the post-transition metals, bismuth and gallium were evaluated in recently
published works.
Bi2 WO6 /perylene diimide (PDI) composite photocatalyst was prepared and evaluated
in phenol oxidation (and water decomposition to produce oxygen) under visible light [421].
Compared to the self-assembled perylene diimide and Bi2 WO6 , the composite showed an
enhancement in the phenol degradation because the positions of conduction and valence
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bands between Bi2 WO6 and perylene diimide favored the separation of the photogenerated
carriers. The Bi2 WO6 /PDI composite exhibited an n–n-type heterojunction.
BiFeWO6 /WO3 nanocomposites were studied by Priya et al. [422]. Various BiFeWO6
loadings from 1 to 3 wt.% deposited on WO3 nanorods were prepared by simple coprecipitation and hydrothermal treatment. Pure BiFeWO6 bandgap was measured at 2.0 eV, and
the best photodegradation of rhodamine B under visible-light illumination was obtained
with 1% BiFeWO6 /WO3 This sample exhibited a bandgap of 2.3 eV, while the bandgap
increased to 2.9 eV for 3% BiFeWO6 /WO3 .
The influence of the partial substitution of gallium by tungsten in a Ga2 Zr2 O7
fluorite-type nanosized material was recently examined in crystal violet degradation [423].
Ga2 Zr2−x Wx O7 samples with x = 0, 0.05, 0.1, 0.15 and 0.2 were prepared using the citrate
technique. W0.15 substitution (optimal loading) allowed the shift of the absorption range
to the visible-light range by decreasing the bandgap from 4.95 eV for Ga2 Zr2 O7 to 1.7 eV
for Ga2 Zr0.85 W0.15 O7 . The crystal violet photocatalytic degradation rate was then multiplied by 20 (optimum operating conditions: pH = 9, 1 g L−1 catalyst, reaction duration
of 300 min). Complete degradation was obtained with the addition of 25 mmol L−1
hydrogen peroxide. O2 center dot and holes were found to have a more important role
in Ga2 Zr2−x Wx O7 systems compared with HO center dot.
The excellent semiconductor tungsten selenide WSe2 was recently used as quantum
dots (particle size: 7–8 nm) and associated with nitrogen-doped graphene oxide to prepare
a composite photocatalyst by the mechanical stripping method [424]. The degradation of
methylene blue under visible light with the composite (optimal WSe2 loading: 4.7 wt.%)
was better than WSe2 and nitrogen-doped graphene oxide (N-GO) alone. The photocatalytic
degradation rate of 50 mL at 1 × 10–4 mol·L−1 dye with only 0.01 g catalyst reached 93%
after 1 h light exposure (300 W Xe lamp with a cutoff wavelength of 420 nm; reaction was
monitored by a total organic carbon analysis).
7.6.2. Rare Earth–WO3 Systems
Cerium is a very popular component in redox catalysis thanks to its ability to vary
between CeIII and CeIV . Impregnation of 1 to 25 wt.% of Ce3+ ions onto WO3 led to
a better absorption cross-section and a redshift in the band edges [425]. The decrease
in the photoluminescence emission intensity and the suppression of the Raman active
bands of WO3 indicated the recombination quenching ability of Ce surface states. For low
cerium loading (≤5%), cerium was mainly found as CeIII , while CeIV was predominant for
higher loadings. An enhancement in the charge retention ability was observed with the
Ce loading increase. In comparison to pure WO3 , Ce-doped catalysts exhibited superior
activity for 2-nitrophenol and 2-chlorophenol removal in natural sunlight exposure. For
low cerium loadings, the surface oxygen bonded with CeIII serves as electron trapping and
transfer centers, while the synergic composite mechanism is the dominating mode for high
Ce loading [425].
Tahir et al. evaluated various other rare earths (REs) by doping WO3 with La, Gd and
Er (RE molar contents of 2, 4 and 6%). Samples were obtained by coprecipitation at 80 ◦ C
in acidified aqueous solution. Photocatalytic activity was measured in degradation of dyes
(methyl orange, methyl blue, crystal violet), antibiotic (tetracycline) and antimetabolite
(methotrexate) and compared to a 10% carbon nanodots–WO3 reference sample [426]. La,
Gd and Er did not enter into the crystal lattice of WO3 (monoclinic and hexagonal phases)
but were positioned in the interstitial sites, with La-O-W, Gd-O-W and Er-O-W bonds. The
photocatalytic activity order was as follows: 2% Gd-WO3 > carbon nanodots–WO3 > 4%
Er-W > 4% La-W > undoped WO3 . The best photocatalytic performance achieved with
2% Gd-WO3 could be attributed to its higher surface area, the inhibition of the chargecarrier recombination, the high surface hydroxyl content and the extended visible-light
absorption region.
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7.6.3. Nitride–WO3 Systems
The graphite-like carbon nitride (g-C3 N4 ) is a metal-free polymer that is an n-type
semiconductor. Its structural and physiochemical behaviors give it interesting properties in
electrical and optical fields. The g-C3 N4 -based nanostructures are emerging materials for
energy and environmental photocatalytic applications (e.g., photocatalytic water reduction
and oxidation, degradation of pollutants, carbon dioxide reduction) [427].
Xiao et al. prepared Z-scheme WO3 /g-C3 N4 composite hollow microspheres by
controlled in situ hydrolysis and a polymerization process (Na2 WO4 in deionized water
with the addition of dicyandiamide C2 H4 N4 and glucose; the homogenized solution was
then transferred into an autoclave and heated 200 ◦ C; for 20 h; after centrifugation and
washing, the product was finally annealed at 550 ◦ C; for 3 h in air (Figure 35)) [428].
The shell of the hollow microspheres consisted of well-distributed WO3 and g-C3 N4
nanoparticles, favoring heterojunctions with numerous interfaces and highly exposed
oxidation–reduction active sites. Various contents of g-C3 N4 were evaluated, and the
best results were obtained with a molar loading of 4% dicyandiamide with respect to
W. The lifetime of the charge carriers reached 2.23 ns, which is obviously prolonged
compared to WO3 . This optimized Z-scheme system maintained the redox potential of the
components. Combined with the long lifetime of holes and electrons, this photocatalyst
showed enhanced degradation rates towards tetracycline hydrochloride (antibiotic agent)
and ceftiofur sodium (antibacterial agent).
Figure 35. Scheme of the in situ construction of WO3 /g-C3 N4 composite hollow microspheres (CHMs). From [428] with
permission from Elsevier.
g-C3 N4 /WO3 materials can be also shaped as thin films for water purification [429].
A bilayered structure has to be formed to ensure an enhanced charge carriers’ separation. Trapping experiments performed under UV illumination revealed that the activation of the photocatalytic oxidation of methylene blue (MB) came from both holes and
superoxide radicals.
Other nitrides such as tantalum nitride (Ta3 N5 ) were also recently evaluated in dye
degradation. Ta3 N5 is one of the few visible-light-absorbing photocatalysts capable of
overall water splitting (OWS). Ta3 N5 /W18 O49 nanocomposite fibers were prepared by the
solvothermal technique to obtain a catalyst made of orthorhombic Ta3 N5 nanoparticles and
monoclinic W18 O49 nanowires. This sample showed a doubled degradation rate of rhodamine B under white light compared to Ta3 N5 nanoparticles alone [430]. In fact, W18 O49
allowed dye adsorption before illumination. Using tert-butanol and p-benzoquinone as
scavenger agents, it was demonstrated both hydroxyl and superoxide radicals contributed
to the cleavage of rhodamine B. The superoxide species were involved in N-deethylation of
the dye. The generation of both radical species on W18 O49 was due to the electronic transfer
between W18 O49 and Ta3 N5 . Taking into account the recycling ability of the catalyst and
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the simplicity of the synthesis process, the authors propose that this catalyst is a good
candidate for the scale-up.
7.6.4. Photoreduction over WO3 Based Systems
Photocatalytic water treatment is mainly focused on the oxidation of organic pollutants.
However, due to its high toxicity, CrVI species reduction into CrIII is also a major concern.
g-C3 N4 /WO3 thin-film materials presented in the previous section also exhibited Cr6+
elimination behavior under UV illumination [429]. The Cr6+ reduction rate was 6% and
93% after 120 min illumination for WO3 and g-C3 N4 /WO3 , respectively. In opposition with
photocatalytic oxidation of methylene blue for which active species came from both holes
and superoxide radicals, the main active species for chromium reduction are electrons.
For the same chromium reduction, Thwala et al. evaluated the doping of WO3 by
1, 3 and 5 mol % of magnesium (one-pot preparation method) [431]. A slight increase
(0.0069 nm) of d spacing was observed by HRTEM imagery after Mg addition, according
to a decrease in the bandgap energy and a shift in the edge positions, also confirmed
by XPS analysis (0.08 eV). The rate of recombination was greatly reduced upon doping
(photoluminescence analysis). DFT calculations supported the recombination reduction
rate due to the introduction of the Mg orbital. With 500 mL at 9.5 ppm CrVI maintained
at pH = 1 and a catalyst weight of 0.1 g, 97% CrVI reduction rate was reached with 3 mol %
Mg-WO3 after one hour under visible-light irradiation (990 W Xe lamp).
7.7. Conclusions
WO3 -based photocatalysts benefit from a visible-light response due to a 2.6–2.8 eV
bandgap between the valence band (VB) and the conduction band (CB). The challenge is
to avoid the fast recombination of the photogenerated electrons and holes of bare WO3
by doping or promotion (with carbon, metal(s), TiO2 , etc.). Depending on the reaction
conditions, the formation of reactive oxidizing species such as superoxide anions (O2 − •),
hydrogen peroxide (H2 O2 ) and hydroxyl radicals (OH•) is reported. The WO3 -TiO2 system
is of great interest for extending the photoresponse of TiO2 (Eg 3.0–3.2 eV) to the visible
light region since the electrons photogenerated in the conducting band of TiO2 can transfer
into the CB of WO3 . The photopromoted holes can thereafter diffuse from the CB of WO3
into the valence band of TiO2 .
8. Conclusions
Tungsten oxide materials exhibit suitable behaviors for surface reactions and catalysis
such as acidic properties (mainly Brønsted sites), redox and adsorption properties (due to
the presence of oxygen vacancies) and a photostimulation response under visible light. The
bandgap of WOx is commonly stressed to 2.6–2.8 eV for crystallized WO3 3D structures
but grows up to 5.5 eV for isolated WO4 species (such as bi-grafted, di-oxo WO4 surface
sites) or supported WOx catalysts depending on the loading. From the operating conditions of the catalytic process, each of these behaviors is tunable by (i) controlling structure
and morphology (nanoplates, nanosheets, nanorods, nanowires, nanomesh, microflowers,
hollow nanospheres, etc.), (ii) thermal treatment under controlled atmosphere and (iii) interactions with other compounds (such as conductors (carbon), semiconductors (e.g., TiO2 )
and precious metals); WOx particles can be also dispersed on high specific surface area
support. Based on these behaviors, WO3 -based catalysts were developed for environmental
applications. One of the major advantages of the acidic and redox behaviors of WO3−x is
their suitability for the abatement of NOx from stationary sources, associated mainly with
TiO2 and V2 O5 (nitric acid plants first; treatment of incinerator and other combustion gases
nowadays). WO3 -based catalysts also promote the abatement of some VOCs. Moreover,
surface oxygen vacancies are also useful in the development of gas sensors, especially
for NO2 detection. Modifications are suitable to improve sensibility, selectivity, stability,
repeatability and response time. Besides, the recent literature shows a high interest in
WO3 -based materials for photocatalysis applications. Bare WO3 is not very active due
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to the fast recombination of photogenerated electrons and holes, but the photocatalytic
activity of WO3 can be significantly improved by numerous associations to obtain suitable
reactivity. Generally evaluated in dye degradation, WO3 -based photocatalysts are also
valuable for the treatment of wastewater polluted with medicinal molecules and plant
protection products. This topic should continue to retain considerable attention in the
near future.
Author Contributions: Conceptualization, D.D. and X.C.; resources, D.D., F.C. and X.C.; writing—
review and editing, D.D., F.C. and X.C. All authors have read and agreed to the published version of
the manuscript.
Funding: This research was funded by the Regional Council of Nouvelle Aquitaine, the French
Ministry of Research and the European Regional Development Fund (ERDF).
Data Availability Statement: Not applicable.
Conflicts of Interest: The authors declare no conflict of interest.
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