Removal of Acetone and Methyl Isopropyl Ketone in a Composite Bead
Biofilter
Wu-Chung Chan and Kang-Hong Peng
Department of Civil Engineering and Engineering Informatics
Chung-Hua University
No.707, Sec. 2, Wufu Rd., Hsinchu City 300, Taiwan (R.O.C.)
Tel.: +886-3-5186725 Fax.: +886-3-5372188
Email: wcchan@chu.edu.tw
Abstract
Removal of acetone and methyl isopropyl ketone (MIPK) in a composite bead biofilter was investigated.
Both microbial growth rate kg and biochemical reaction rate kd would be inhibited at higher inlet concentration.
For the microbial growth process, the kg value of MIPK was greater than that of acetone and the inhibitive effect
for MIPK was more sensitive than that for acetone in the average inlet concentration range of 100-150 ppm. The
kg value of acetone was greater than that of MIPK and the inhibitive effect was almost the same sensitivity for
two ketone compounds in the average inlet concentration range of 200-300 ppm. The zero-order kinetic with the
diffusion rate limitation was regarded as the most adequate biochemical reaction model. For the biochemical
reaction process, the kd value of acetone was greater than that of MIPK and the inhibitive effect for MIPK was
more sensitive than that for acetone in the average inlet concentration range of 100-300 ppm. The maximum
elimination capacity of acetone and MIPK were 54.68 and 35.18 gC h-1 m-3 bed volume, respectively. The
compound with less number of carbons or no side group in the main chain was easier biodegraded by the
microbial.
Keywords: acetone; methyl isopropyl ketone; microbial growth rate; biochemical reaction rate; composite bead
biofilter
1.
dioxide). Biofiltration involves the passage of a
Introduction
The removal of volatile organic compounds
(VOCs) from a polluted air stream using a biological
process is highly efficient and has low installation
and
operation/maintenance
costs.
Biofiltration
technology offers environmental advantages: it does
not generate undesirable byproducts by converting
many
organic
and
inorganic
compounds
into
harmless oxidation products (e.g., water and carbon
polluted air stream through a packed bed containing
microorganisms
immobilized
within
a
biofilm
attached to the bed-packing material. Contaminants
are transferred to the interface between the gas and
biofilm and are subsequently absorbed into the
biofilm. Contaminants are then used as carbon and/or
energy sources for the microorganisms within the
biofilm. The solid filter material provides a nutrient
source
and
matrix
for
the
attachment
of
process.
in the biofiltration process in our previous works [6,
Therefore, the filter material property is an important
7]. The diffusivity of nutrient within this filter
factor to obtain optimal pollutant removal. The
material would be an important control factor for
optimal filter material should have the following
achieving good biofilter performance.
microorganisms
in
the
biofiltration
characteristics: high moisture holding capacity,
Acetone, methyl ethyl ketone (MEK), methyl
porosity, available nutrients, and pH buffer capacity
isobutyl ketone (MIBK) and methyl isopropyl ketone
[1].
(MIPK) are widely used industrial chemicals. These
A wide range of filter materials including
ketone compounds were designed high-priority toxic
compost, peat, and soil have been studied and found
chemicals.
to be effective bed material for specific contaminants
compounds are released into the atmosphere during
and gas streams [2-4]. However, these natural
manufacturing processes every year, leading to the
materials appear cracking and compaction as the
endangerment of air quality and public health. Some
filter bed is operated over a period of time. These
reports
phenomena cause a rise in the bed’s head loss and
compounds. MEK biodegradation by Pseudomonas
uneven flow distribution to reduce the efficiency of
sp. KT-3 was suppressed as the addition of MIBK or
the removal of VOC. Carbon, nitrogen, and
acetone in liquid culture. The phenomenon was due
phosphorus
for
to the solubility of acetone was higher than that of
microbial growth and metabolism. Carbon can be
MEK, and MIBK and MEK could compete with each
provided by the VOCs in the air stream, but both
other for enzyme binding [8]. MEK degradation by
nitrogen and phosphorus must be provided by the
using biofilters with a pure strain of Rhodococcus sp.
filter material. Nitrogen is a major constituent of
or a mixed culture of microbes showed no advantage
microorganism proteins and nucleic acids because it
of a pure culture; and the mass-transfer mechanism is
can make up approximately 15% of microbial cell dry
macropore controlled in both the granular activated
weight [5]. Consequently, nitrogen can be a limiting
carbon and compost media [9]. The maximum
nutrient if adequate amounts are not available in the
elimination capacity achieved were 50g/m3-h for
biofilter material. Inorganic nitrogen (i.e., ammonia,
MEK and 20g/m3-h for MIBK at the inlet
nitrate, or nitrite) is water-soluble and can be
concentration of two pollutants mixture 300 mg/m3
considered
for
MEK and 330 mg/m3 MIBK [10]. Although the lag
microorganisms. Inorganic nitrogen is generally not
phase for MIBK removal was shorter than that for
initially present in the filter material. It is formed by
MEK removal, the biodegradation rate of MEK was
the mineralization of organic nitrogen in the filter
significantly higher than that of MIBK. Both MEK
material and by recycling nitrogen through the
and MIBK biodegradation rates were reduced as
mineralization of cells. Granular activated carbon
MEK was pulsed into the air stream containing MEK
(GAC) has large surface area and porosity, so adding
and MIBK mixtures, but both rates were not
GAC into the biofilter would enhance the adsorption
influenced as MIBK was pulsed [11]. Various
capacity, moisture holding capacity, and porosity of
responses were observed when hexane, acetone,
filter
alcohol
1-propanol and MIBK were introduced in a step pulse
was
manner to biofilter degrading MEK. Hexane was
prepared and was proven suitable as a filter material
neither adsorbed to the packing nor biodegraded to a
are
as
material.
three
the
important
available
A spherical
(PVA)/peat/KNO3/GAC
nutrients
nitrogen
polyvinyl
composite
bead
Large
concerned
volumes
the
of
these
biofiltration
of
ketone
ketone
significant extent. Acetone was subject to important
operating and design on the biofiltration. However,
sorption and well degraded. 1-Propanol was better
details of the kinetic of such biodegradation
removed even though the biofilter had never been
processes in biofilter are scant in the relevant
exposed to 1-propanol vapors before the experiment.
literature. This article investigates the biochemical
MIBK showed the most inhibitive effect on the
kinetic behaviors of ketone compounds in a
degradation of the base feed of MEK [12]. The
composite bead biofilter. The ketone compounds are
maximum elimination capacity of MEK was 5.82 kg
acetone and MIPK. The composite bead is the
/m3day.
backwashing
and
spherical PVA/peat/KNO3/GAC composite bead. The
long-term
stable
relationships between the microbial growth rate and
removal efficiency over 99% was retained for loading
biochemical kinetic rate with ketone compounds and
COD
starvation/stagnant
Using
strategies,
3
rate up to 3.52-5.63 kg COD/m -day [13]. The
maximum elimination capacity of MIBK was 4.82 kg
COD /m3-day. Combination of backwashing and
inlet VOCs concentration are also investigated.
2.
Experimental
intermittent operations, long-term stable removal
Peat (industrial grade from KekkilaOyj, Tuusula,
efficiency over 99% was retained for loading rate up
Finland) was dried at 105℃ before use. It has a dry
to 5.43 kg COD/m3-day. The pseudo-first-order
density of 90 kg m-3, a pH of 5.5, a pore volume of
removal rate constant decreased with increase in
96%, and an organic substance content of 91%. Boric
volumetric loading rate for MEK and MIBK [14].
acid, sodium monobasic phosphate, sodium dibasic
The biofilter performance was evaluated under
phosphate, potassium nitrate, acetone and methyl
interchanging the feed VOCs in the sequence MEK,
isopropyl ketone (extra pure grade from Union
toluene, MIBK and styrene, and then back to MEK.
Chemical, Hsinchu, Taiwan) were used as received.
The biofilter provided high removal efficiency within
Poly(vinyl alcohol) (PVA) powder (industrial grade
the critical loading of each VOCs. The biofilter easily
from Chung Chun Petrochemical, Hsinchu, Taiwan)
acclimated to the oxygenated compounds (MEK and
and granular activated carbon (GAC) (industrial
MIBK), but re-acclimation was delayed for the
grade from Taipei Chemical, Hsinchu, Taiwan) were
aromatic compounds (toluene and styrene). The
also used as received.
destructed aromatic compounds were eliminated
The
procedures
for
preparing
exclusively by aerobic biodegradation; however, the
PVA/peat/GAC/KNO3 composite beads and the
destructed oxygen compounds were eliminated by
apparatus and operation of the biofilter system were
aerobic biodegradation and possible denitrification
described in our previous work [7]. Acetone and
[15].
methyl isopropyl ketone were used as VOCs. Acetone
Recently, we had indicated that the process for
and metyl isopropyl ketone were individually in each
degradation of VOCs in a composite bead biofilter
air stream which flowed through the biofilter column
could be divided into lag, log growth and maximum
in downward mode. Before packing, the filter
stationary three phases, and the log growth and
material was immersed in 0.384 M KNO3 aqueous
maximum stationary phases were important for
solution to adsorb KNO3 and to reach equilibrium
controlling the removal efficiency of biofilter [6,7].
(approximately 12 h). The bead moisture content was
Therefore, studies the kinetic of log growth and
humidified to more than 1.5 g water g-1 dry solid and
maximum stationary phases was very important for
the seeding was performed with activated sludge. The
VOCs concentration in the inlet and exit air streams
Both phase II and III are important for controlling the
of each section was taken by auto-sampling and
removal efficiency of biofilter, so the effect of inlet
analyzed using gas chromatography (GC) (Model
concentration and type of ketone compounds on the
GC-8A from Shimadzu, Tokyo, Japan). The VOCs
microbial growth rate and biochemical reaction rate
removal efficiency was calculated by the difference
was studied.
of the VOCs concentration between the inlet and exit
air streams. The relative standard deviation and
relative error of the experimental measurements were
less than 2% and 5%, respectively.
3.
3.1 Microbial growth
In the log growth phase (phase II), the
microbial growth rate increased exponentially and
was represented by the following equation [17].
Results and discussion
dX/dt = kg X
(1)
The variation in the percentage of removed
where X is the number of viable cells per unit volume,
VOCs over operation time in an air stream with flow
kg is the microbial growth rate and t is the operation
rate 0.102 m3 h-1, two ketone compounds average
time. More amount of viable cell per unit volume in
inlet concentration in the range of 100 to 300 ppm, an
the bed could consume more amount of contaminant
operation temperature 30℃ and a relative humidity
because contaminant degradation was the result of
of more than 95 % through a composite bead filter
microbial activity. Therefore, the concentration of
bed is shown in Figure 1. (only the average inlet
VOCs in the exit stream (C) was inversely
concentration of 200 ppm is shown because the data
proportional to the number of viable cells per unit
for the other concentrations were visually similar).
volume in the bed. The kinetic of contaminant
degradation is closely related to the kinetics of
100
microbial growth [1], so Eq. 1 can be converted into
Percentage of removed VOCs, %
III
II
dC/dt = – kg C
80
Integration of Eq. 2 yields
60
I
ln(C/C0) = – kg t
40
(3)
where C0 is the concentration of VOCs in the inlet air
stream. A plot of ln(C/C0) versus t should correspond
20
0
(2)
to a straight line and kg can be determined. Therefore,
0
50
100
150
200
250
300
Operation time, t , h
the microbial growth rate kg of two ketone
compounds at various inlet concentrations was
Figure 1. Percentage of removed VOCs over
operation time (t) for the biofilter at the average inlet
concentration 200 ppm: (■) acetone, (▲) methyl
isopropyl ketone.
calculated from the data in phase II and Eq. 3. The
calculated kg values were listed in Table 1.
The variations of the kg values with average
inlet concentration C0 for two ketone compounds are
shown in Figure 2. It was found that the kg value
It is found that the variation in the percentage of
decreased with increasing average inlet concentration
removed VOCs over operation time appeared in three
in the concentration range of 100-300 ppm. An
phases: lag phase (phase I), log growth phase (phase
increase in the inlet concentration generally would
II) and maximum stationary phase (phase III) [6, 16]
enhance the transfer rate of the VOCs from the gas
phase to the biofilm. This phenomenon leads more
atm-m3 mol-1, respectively [19], so the amount of
microorganisms to participate in the biodegradation
acetone dissolved in the biofilm was greater than that
activity.
of MIPK dissolved. Thus, the result indicated that
Table 1. The values of kg (h-1) at various average inlet
concentrations and compounds
Average inlet
such amount of acetone would produce toxic effect to
the microorganism at the average inlet concentration
100 ppm. To compare the order of kg value between
Compounds
concentration, ppm
Acetone
Methyl isopropyl ketone
100
0.0558
0.1634
150
0.0347
0.0498
200
0.0262
0.0134
250
0.0204
0.0103
300
0.0150
0.0024
two compounds, it was found that the order of kg
value was MIPK > acetone in the average
concentration range of 100-150 ppm, it was acetone >
MIPK in the average concentration range of 200-300
ppm, and it was a transition region in the average
concentration range of 150-200 ppm.
The kg value decreased from 0.0558 to 0.0347
However, high concentrations of some recalcitrant
VOCs may produce inhibitive effects on the
metabolic activity of the microbial population [18].
Therefore, the result indicated that the inhibitive
effect predominated and the microbial growth rate
was inhibited at higher inlet concentration.
h-1 for acetone, and from 0.1634 to 0.0498 h-1 for
MIPK as the average inlet concentration increased
from 100 to 150 ppm. The slope of the linear profiles
in this concentration range for acetone and MIPK
were 0.42x10-3 and 2.27x10-3 h-1ppm-1, respectively.
These results indicated that the inhibitive effect,
resulting from increased inlet concentration, for
MIPK was more sensitive than that for acetone in this
0.2
concentration range. The kg value decreased from
0.0262 to 0.0150 h-1 for acetone, and from 0.0134 to
kg, h
-1
0.0024
h-1
for
MIPK
as
the
average
inlet
concentration increased from 200 to 300 ppm. The
0.1
slope of the linear profiles in this concentration range
for acetone and MIPK were 1.12x10-4 and 1.10x10-4
h-1ppm-1, respectively. The result indicated that the
0.0
0
100
200
300
Average inlet concentration, C0, ppm
Figure 2. The variations of kg with average inlet
concentration (C0) for two ketone compounds: (■)
acetone, (▲) methyl isopropyl ketone.
inhibitive effect, resulting from increased inlet
concentration, for two ketone compounds was almost
the same sensitivity in this concentration range.
3.1 Biochemical reaction
In the maximum stationary phase, the
The kg value of acetone was much smaller than
population of viable cells was at a relatively constant
that of MIPK about 65.8% at the average inlet
value. Under the steady-state conditions, the substrate
concentration 100 ppm. The Henry’s law constant of
utilization rate by microbial was proposed by
acetone and MIPK was 5.5320x10-5 and 9.2561x10-5
Ottengraf [1]. Three situations may be encountered in
a biochemical reaction system. These corresponding
equations
could
be
derived
from
the
Michaeilis-Menten relationship to express the rates of
biochemical reaction for each situation as follows:
derived from the Michaelis-Menten equation [17]
(C0-C)/ln(C0/C) = Vm (θ/ln(C0/C)) - Ks
(8)
where Ks is half-saturation constant and Vm is
1. First-order kinetic
maximum reaction rate. A plot of (C0-C)/ln(C0/C)
ln(C/C0) = – k1θ
(4)
2. Zero-order kinetic with reaction limitation
versus θ/ln(C0/C) should correspond to a straight line,
and Ks and Vm can be determined. The plot of
C0-C = k0θ
(5)
3. Zero-order kinetic with diffusion limitation
1/2 2
C = C0 [1-θ(a k0De /2mC0δ) ]
(C0-C)/ln(C0/C) versus θ/ln(C0/C) for two ketone
compounds is shown Figure 4.
(6)
where a is the interfacial area per unit volume, De is
the
effective
diffusion
coefficient,
m
is
the
distribution coefficient of the component, θis the
empty bed residence time (EBRT), δ is the biofilm
thickness, k0 is the zero-order reaction rate coefficient
with reaction limitation and k1 is
the
first-order
reaction rate coefficients. However, for convenience
of use, it is necessary to define a new parameter, kd =
(ak0De/2mC0δ)1/2. It can be seen that kd is a function
of the operating conditions of the biofilter system,
and kd is constant under steady-state conditions.
Therefore, Eq. 6 can be rewritten as
1-(C/C0)1/2 = kdθ
(7)
where kd is the zero-order reaction rate coefficients
with diffusion limitation.
The plots of ln(C/C0) versusθ, C0-C versusθand
1-(C/C0)1/2 versusθcalculated from the data in phase
III are shown in Figure 3 (only the average inlet
concentration 200 ppm of acetone is shown since the
data for other concentrations and compounds were
visually similar). It was found that three plots had
high
correlation
coefficient.
The
correlation
Figure 3. Plots of (a) C0-C versus θ, (b) ln(C/C0)
coefficient values for linearized profiles developed
versus θ, (c) 1-(C/C0)1/2 versus θ for acetone at the
from three kinetic models for acetone and MIPK
average inlet concentration 200 ppm.
were range from 0.9373-0.9930, and 0.9253-0.9998,
respectively. Therefore, all three plots almost follow a
linear relationship.
In order to verify the biochemical reaction
kinetic model, assume there was a plug air flow in the
biofilter column and the following equation was
The calculated Ks for acetone and MIPK were
26.80 and 22.96 ppm, respectively. The calculated Vm
for acetone and MIPK were 8.55 and 7.55 g-C h-1 kg-1
packed material, respectively.
According to the Michaelis-Menten concept, (I)
as the substrate concentration was very low (Ks >>
faster than that of MIPK in this concentration range.
The variation of kd with average inlet
C0), the reaction rate expression could be simplified
to
first-order
kinetic;
substrate
concentration C0 for two ketone compounds is shown
concentration was very high (Ks << C0), the reaction
in Figure 5. It was found that the kd value decreased
rate expression could be simplified to zero-order
with increasing average inlet concentration in the
kinetic; (III) as the substrate concentration C0 was
concentration range of 100-300 ppm. The result
comparable with Ks, the reaction rate expression
indicated that the biochemical reaction rate was also
could not be simplified and it was followed
inhibited at the higher inlet concentration. The result
fractional-order
was closely corresponding to the result reported that
kinetic
(II)
as
as
Eq.7
the
derived
by
Ottengraf’s diffusion limiting model [20].
the
pseudo-first-order
removal
rate
constant
decreased as the employed loading rate increased for
the removal of MEK from waste gas in a trickle-bed
air filter [13].
0 .0 6
kd, s
-1
0 .0 4
0 .0 2
Figure 4. Plot of (C0-C)/ln(C0/C) versus θ/ln(C0/C)
0 .0 0
for two ketone compounds: (■) acetone, (▲) methyl
0
50
100
150
200
250
300
A verage inlet concnetration, C 0 , ppm
isopropyl ketone.
The ratio of C0/Ks for acetone and MIPK were
Figure 5. The variations of kd with average inlet
3.73-11.2 and 4.36-13.07, respectively. Therefore,
concentration (C0) for two ketone compounds: (■)
zero-order kinetic with diffusion rate limitation could
acetone, (▲) methyl isopropyl ketone.
be regarded as the most adequate biochemical
reaction kinetic model because the values of Ks and
C0 were comparable for two ketone compounds in
this study. The result was corresponding to the result
reported that biodegradation of acetone follows zero
order kinetics with mass transfer resistance in a
compost biofilter [21]. Thus, the kd value of two
ketone compounds at various inlet concentrations
could be calculated from Eq. 7 and was list in Table 2.
The kd value of acetone was approximately 1.07-5.14
times greater than that of MIPK in the average inlet
concentration range of 100-300 ppm. The result
indicated that the biodegraded rate of acetone was
The kd value decreased from 0.0512 to 0.0279
s
-1
for acetone, and from 0.0472 to 0.0137 s-1 for
MIPK as the average inlet concentration increased
from 100 to 200 ppm. The slope of the linear profiles
in this concentration range for acetone and MIPK
were 2.33x10-4 and 3.35x10-4 s-1ppm-1, respectively.
The result indicated that the inhibitive effect,
resulting from increased inlet concentration, for
MIPK was more sensitive than that for acetone in this
concentration range. The kd decreased from 0.0279 to
0.0216s-1 for acetone, and from 0.0137 to 0.0042 s-1
for MIPK as the average inlet concentration increased
from 200 to 300 ppm. The slope of the linear profiles
capacity will eventually be reached. This maximum
in this concentration region for acetone and MIPK
overall elimination capacity is independent of
-5
-5
-1
-1
were 6.30x10 and 9.50x10 s ppm , respectively.
contaminant concentration and residence time within
These results indicated that the inhibitive effect,
a reasonable range of operating conditions [1]. The
resulting from increased inlet concentration, for
relationship of elimination capacity (EC) of biofilter
MIPK was also more sensitive than that for acetone
versus load for two ketone compounds is shown in
in this concentration range. Thus, the inhibitive effect
Figure 6. It was found that elimination capacity
for MIPK was more pronounced in the concentration
increased and tended towards a constant value with
range of 100-300 ppm.
increasing inlet load. The maximum elimination
Table 2. The values of kd (s-1) at various average inlet
concentrations and compounds.
Average inlet
capacity of actone and MIPK were 54.68 and 35.18 g
C h-1m-3 bed volume, respectively. The result
indicated that the maximum elimination capacity of
Compounds
concentration, ppm
Acetone
Methyl isopropyl ketone
100
0.0512
0.0472
150
0.0381
0.0355
200
0.0279
0.0137
250
0.0257
0.0103
300
0.0216
0.0042
acetone was greater than that of MIPK. Thus, the
compound with less number of carbons or no side
group in the main chain was easier biodegraded by
the microbial. This result was closely corresponding
to the result reported that the maximum elimination
capacity (50 g m-3 h-1) of MEK was larger than that
(20 g m-3h-1) of methyl isobutyl ketone (MIBK) [10].
3.3 Elimination capacity
60
EC, g-C h m bed volume
Elimination capacity (EC) is the mass of
contaminant degraded per unit mass of filter material
40
-3
per unit time and is always equal to or less than the
50
-1
load. Elimination capacity and load could be
expressed as
EC = Q (C0-C)/V
Load = Q C0/V
(9)
0
where Q is the flow rate of inlet air steam and V is
100% of the removal efficiency. By increasing the
reached. Beyond that point the removal efficiencies
will be less than 100%. This point is typically called
the critical elimination capacity. As the load
continues to increase, a maximum overall elimination
50
100
150
200
250
300
350
-3
Load, g-C h m bed volume
Figure 6. The variations of elimination capacity (EC)
with load for two ketone compounds biofilters: (■)
acetone, (▲) methyl isopropyl ketone.
load on a system, a point where the overall load will
exceed the overall elimination capacity will be
0
-1
the volume of filter material as packed. Under low
equals the load and the system is calculated to be at
20
10
(10)
load conditions, the elimination capacity essentially
30
4.
Conclusions
The biochemical kinetic behaviors of acetone
and methyl isopropyl ketone (MIPK) in a composite
bead biofilter were investigated. Both microbial
growth rate kg and biochemical reaction rate kd would
be inhibited at higher inlet concentration. For the
[2]. Williams, T.O., Miller, F.C., Biofilters and
microbial growth process, the order of kg value was
facility operations, Biocycle, Vol. 33 pp. 75-79
MIPK > acetone and the inhibitive effect for MIPK
(1992).
was more sensitive than that for acetone in the
[3]. Hodge, D.S., Tahatabai, F., Winer, A.M.,
average inlet concentration range of 100-150 ppm.
Treatment of hydrocarbon fuel vapors in
The order of kg value was acetone > MIPK and the
biofilters,
inhibitive effect for two ketone compounds had
pp.655-662 (1991).
almost the same sensitivity in the average inlet
Environ.
Technol,
VOl.
12,
[4]. Bohn, H.L., Biofiltration: design principles and
The
pitfalls, in: Proceedings of the 86th Annual
half-saturation constant Ks values of acetone and
Meeting & Exhibition of the Air & Waste
MIPK were 26.80 and 22.96 ppm, respectively. The
Management Association, Denver, Coloado,
maximum reaction rate Vm values of acetone and
(1993).
concentration
range
of
200-300
-1
ppm.
-1
MIPK were 8.55 and 7.55 gC h kg packed material,
[5]. Carlson, D.A., Leiser, C.P., Soil beds for the
respectively. The zero-order kinetic with the diffusion
control of sewage odors, J. Water Pollut.
rate limitation could be regarded as the most adequate
Control Fed., Vol. 38 pp.829-840 (1966).
biochemical reaction model. For the biochemical
[6]. Chan, W.C., Lin, Z.Y., A process to prepare a
reaction process, the kd value of acetone was
synthetic filter material containing nutrients for
approximately 1.07-5.14 times greater than that of
biofiltration, Bioresour. Technol., Vol. 26 pp.
MIPK in the average inlet concentration range of
223-230 (2006).
100-300 ppm. The inhibitive effect for MIPK was
[7]. Chan, W.C., Chang, L.Y., Kinetic behaviors
more sensitive than that for acetone in the average
between acetone and composite bead in
inlet concentration range of 100-300 ppm. The
biofilter, Appl. Microbiol. Biotechnol., Vol. 72
maximum elimination capacity of acetone and MIPK
pp.190-196 (2006).
were 54.68 and 35.18 gC h-1 m-3 bed volume. The
[8]. Lee, T.H., Kim, J., Kim, M.J., Ryu, H.W.,
compound with less number of carbons or no side
Degradation characteristic of methyl ethyl
group in the main chain was easier biodegraded by
ketone by Pseudomonas sp. KT-3 in liquid
the microbial.
culture and biofilter, Chemosphere, Vol. 3
Acknowledgements
pp.315-322 (2006).
[9]. Amanullah, M., Viswanathan, S., Farooq, S.,
The authors wish to thank the National Science
Equilibrium, kinetics and column dynamics of
Council of the Republic of China for financial aid
methyl ethyl ketone biodegration, Ind. Eng.
through the project, NSC 95-2211-E-216-019.
Chem. Res., Vol. 39 pp. 3387-3396 (2000).
[10]. Deshusses, M.A., Hamer, G., The removal of
Volatile ketone mixtures from air in biofilters,
References
[1]. Deviney, J.S., Deshusses, M.A., and Webster,
T.S., Biofiltration for air pollution control,
Lewis publishers, New York, (1999).
Bioprocess Eng., Vol. 9 pp. 141-146 (1993).
[11]. Deshusses, M.A., Hamer, G., Dunn, I.J.,
Transient-sstate
behaviors
of
a
biofilter
removing mixtures of vapors of MEK and
MIBK from air, Biotechnol. Bioeng., Vol. 49 pp.
performance, and maintenance, J. Air Waste
587-598 (1996).
[12]. Deshusses, M.A., Transient behaviors of
Manag. Assoc., Vol. 44 pp. 1315-1321 (1994).
and
[21]. Hwang, S.J., Tang, H.M., Wang, W.C.,
interactions between pollutants, J. Environ Eng.,
Modeling of acetone biofiltration process,
June, pp. 563-568 (1997).
Environ. Porg., Vol. 16 pp. 187-192 (1997).
biofilters:start-up,
carbon
balance,
[13]. Cai, Z., Kim, D., Sorial, G.A., Evaluation of
trickle-bed air biofilter performance for MEK
removal,
J.
Hazard
Mater.,
Vol.
B114,
pp.153-158 (2004).
[14]. Cai, Z., Kim, D., Sorial, G.A., Removal of
methyl isobutyl ketone from contaminated air
by trickle-bed air biofilter, J. Environ Eng.,
Vol.131, pp. 1322-1329 (2005).
[15]. Cai, Z., Kim, D., Sorial, G.A., Saikaly, P, Zein,
M.M, Oerther, D.B. Performance and microbial
diversity of a trickle-bed air biofilter under
interchanging contaminants, Eng Life Sci., Vol.
6, pp. 37-42 (2006).
[16]. Reynold, T.D., Unit operation and process in
environmental
engineering,
Wadsorth
Inc,
California, (1982).
[17]. Valsaraj, K.T., Elements of environmental
engineering: thermodynamics and kinetics,
Lewis publishers, New York, (1995).
[18]. Yaws, C.L., Sheth, S.D., Han, M., Using
solubility and Henry’s law constant data for
ketones in water, Pollut. Eng., Vol.44 pp. 44-46
(1998).ketones in water, Pollut. Eng., Vol.44 pp.
44-46 (1998).
[19]. Leson., G., Winer, A.M., Biofiltration: an
innovative air pollution control technology for
VOC emissions, J. Air Waste Manag. Assoc.,
Vol. 41 pp. 1045-1054 (1991).
[20]. Yang, Y., Allen, E.R., Biofiltration control of
hydrogen
sulfide.
2.
Kinetics,
biofilter