Effects of simulated acid rain on microbial activities and litter decomposition
Effects of simulated acid rain on microbial activities and litter decomposition
Journal of Ecology and Environment. 2011. Dec, 34(4): 401-410
Copyright ©2011, The Ecological Society of Korea
This is an Open Access article distributed under the terms of the Creative Commons Attribution Non-Commercial License ( which permits unrestricted non-commercial use,distribution, and reproduction in any medium, provided the original work is properly cited.
  • Received : September 06, 2011
  • Accepted : September 20, 2011
  • Published : December 01, 2011
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Sung-Min, Lim
Sang-Seob, Cha
Jae-Kuk, Shim

We assayed the effects of simulated acid rain on the mass loss, CO 2 evolution, dehydrogenase activity, and microbial biomass-C of decomposing Sorbus alnifolia leaf litter at the microcosm. The dilute sulfuric acid solution composed the simulated acid rain, and the microcosm decomposition experiment was performed at 23℃ and 40% humidity. During the early decomposition stage, decomposition rate of S. alnifolia leaf litter, and microbial biomass, CO 2 evolution and dehydrogenase activity were inhibited at a lower pH; however, during the late decomposition stage, these characteristics were not affected by pH level. The fungal component of the microbial community was conspicuous at lower pH levels and at the late decomposition stage. Conversely, the bacterial community was most evident during the initial decomposition phase and was especially dominant at higher pH levels. These changes in microbial community structure resulting from changes in microcosm acidity suggest that pH is an important aspect in the maintenance of the decomposition process. Litter decomposition exhibited a positive, linear relationship with both microbial respiration and microbial biomass. Fungal biomass exhibited a significant, positive relationship with CO 2 evolution from the decaying litter. Acid rain had a significant effect on microbial biomass and microbial community structure according to acid tolerance of each microbial species. Fungal biomass and decomposition activities were not only more important at a low pH than at a high pH but also fungal activity, such as CO 2 evolution, was closely related with litter decomposition rate.
Air pollution has developed into a serious environmen-tal crisis among modern human societies as a result of ex-tensive industrial developmental, rapid economic growth and an increased energy demand globally over the last century. Particularly increased anthropogenic emissions of combustibles and fossil fuels have induced the acidi-fication of rain and the soil. Observations from the Hub-bard Brook Experimental Forest (HBEF), starting in 1962, have produced the longest continuous record of precipi-tation and stream water chemistry (Moldan and Cerny 1994). Within these observations Likens (1972) highlight-ed the high acidity of rain and snow at HBEF, which have since been determined to mainly be due to the presence of sulfuric acid (Likens and Bormann 1995). As part of the International Biological Program, ecosystem research in Solling, a mountainous area in Germany, revealed high rates of deposition of various air pollutants, especially sul-furic acid (Mayer and Ulrich 1974). The increased acidity of precipitation is the result of anthropogenic emissions of SO 2 and NOx, which are hydrolyzed to become the strong acids H 2 SO 4 and HNO 3 in the atmosphere (Likens and Bormann 1995). Although it has been reported that acid rain tend to reduce the pH of the soil substrate, most studies of acid rain deposition have focused on sulfur and nitrogen deposition, the pH of precipitation and the high concentration of toxic metal ions (Pennanen et al. 1998, Jezierska-Tys 2004, Huang et al. 2010).
Acid rain has been shown to have a wide range of effects on the ecosystem, such as cation-loss or nutrient-leach-ing from leaves (Fairfax and Lepp 1975, Proctor 1983, Liu et al. 2007), alterations in the gas-exchange rate through leaf stomata (Evans et al. 1982, Hermle et al. 2007), and germination and plant growth (Wood and Bormann 1974, Neufold et al. 1985, Reich et al. 1987, Kim et al. 2008). Acid rain has also been responsible for soil acidification, which has resulted in soil fertility declines and in harmful ef-fects on plant growth resulting from leaching of soluble toxins (Wood et al. 1984, Matzner et al. 1986, Sakamoto et al. 2001, Monteith and Evans 2005). Moreover, acids can cause the release of nutrients such as Ca, Mg and K from their solid phases into solution (Batty and Younger 2007, Zhang et al. 2007).
In terrestrial ecosystems, acid rain has a significant effect on the decomposition process, which plays a par-ticularly important role in the cycle of materials and the maintenance of ecosystem stability. The increased acid-ity particularly affects the size, composition and activity of soil microbes (Fritze 1992, Myrold and Nason 1992, Bååth and Anderson 2003, Batty and Younger 2007, Rousk et al. 2009). Prescott and Parkinson (1985) suggested that microbe-mediated changes in soil processes, such as lit-ter decomposition, are the most important components of nutrient cycling. Particularly, low pH has been shown to reduce microbial activity (Bååth et al. 1979, Bewley and Parkinson 1985, Bååth and Anderson 2003, Batty and Younger 2007, Rousk et al. 2009). The studies of Hovland et al. (1980), Hovland (1981), Batty and Younger (2007), and Zhang et al. (2007) have all suggested that the low pH of acid rain accelerates the leaching of essential nutrients (K and Mg) from plant litter, as well as directly affecting the decomposition process. However, Ouyang et al. (2008) suggested that the mineralization of soil organic C was not related to low pH acid rain.
In South Korea, the rain in major cities has frequently been recorded as having a low pH year round (Ministry of Environment 2010). Lee (1998) examined the spatial distribution of precipitation acidity in the major cities of South Korea, and found that the almost area of major city exhibited low pH precipitation.
The aim of this study was to assess the effect of simu-lated acid rain on the plant litter decomposition process at the microcosm scale. Leaf litter samples were treated periodically with simulated acid rain, which included sul-furic acid, and retrieved for the determination of weight loss, microbial biomass, microbial community structure and microbial activities within the decomposing litter. The microbial activities measured were CO 2 evolution and the enzyme activities of the decomposing litter.
- Litter sample and experimental design
In the Korean Peninsula, Sorbus alnifolia tends to pre-dominate near big cities (Lee et al. 1998). We collected freshly fallen S. alnifolia leaf litter in October 2008, which was dried at 60° in a dry oven. Leaf litter samples were cut to a width of 2 cm for ease of use in the microcosm en-vironment. The initial leaf quality of the S. alnifolia leaf litter is presented in Table 1 .
The microcosm was created in 1 L colorless glass bot-tles with detachable lids. The bottles were filled with 300 g of quartz sand that had been cleaned of organic matter through repeated washing with distilled water. The quartz sand was used to control water content at 90% water holding capacity for the maintenance of a constant wa-ter content in the microcosm bottles. Approximately 4 g of litter was placed on top of the sand in each microcosm bottle. The microcosm bottles were covered with a piece of gauze to prevent too much evaporation and incubated at a constant 23℃ and 40% relative humidity.
After the first 16 days of conditioning, 10 mL of fresh soil suspension solution was applied to the litter samples.
Initial quality and chemical composition of Sorbus alnifolia leaf litterValues are mean ± standard deviation of four replicates (P< 0.005,N= 4).
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Initial quality and chemical composition of Sorbus alnifolia leaf litter Values are mean ± standard deviation of four replicates (P < 0.005, N = 4).
Additional artificial acid rain water, at the different pH levels, was applied twice a week from experimental day 24 until the end of experiment to compensate for water evaporation. The simulated acid rain was made up of di-luted sulfuric acid in deionized water at pH 6.5, 5, 4, and 3, respectively. Four replicated litter samples were carefully retrieved from four microcosm bottles for each pH treat-ment and analyzed after 80, 160, and 290 experimental days.
- Analysis of litter sample
- Mass loss
Litter samples retrieved from each microcosm were separated into two subsamples, one subsample was dried at 60℃ in a dry-oven for 48 h to determine moisture and dry matter contents for mass loss determination; the oth-er subsample was refrigerated at 4℃ before the biological activity analyses were performed.
- Nutrient content
One gram of oven dried and ground litter sample was mixed with 10 mL of HNO 3 (1 D.W :1 HNO3 ) and 3 mL of 60% HClO 4 . The sample was heated up slowly until the HNO 3 evaporated. When HClO 4 smoke went up, the sample was cooled to room temperature, mixed with 10 mL of HCl (1 D.W :1 HCl , v/v), and diluted with distilled water to 50 mL. The concentrations of Fe, Mg, Ca, P, Na, and K were mea-sured by inductively coupled plasma spectrometry (JY-ULTIMA-2, Jobin Yvon, Longjumeau, France), according to Helrich (1990), after filtration. More finely ground litter samples using a ball mill were used for the determination of C and N content with an element analyzer (Flash EA 1112, Thermo Electroncorporation, San Jose, U. S. A.).
- Cellulose and lignin content
Cellulose and lignin contents of each litter sample were determined according to Rowland and Roberts (1994). About 0.5 g of milled litter sample was weighed (W 1 ) and boiled for 1 h in 100 mL CTAB solution (1 g cetyltrimethyl ammonium bromide in 100 mL of 0.5 M H 2 SO 4 ) under continuous stirring. The solution was filtered through a heated and pre-weighed sinter (W 2 ) and washed three times with hot distilled water, then washed with acetone and dried for 2 h at 105℃ then weighed (W 3 ). About 10 mL of cool 72% H 2 SO 4 was added to the cooled sinter and the mixture was kept in 72% H 2 SO 4 for 3 h. Thereafter, the acid was filtered off under vacuum, and the residue was washed with hot distilled water until it was acid-free. The sinter was dried at 105℃ for 2 h, cooled, and weighed (W 4 ). The sinter was then heated at 500℃ for 2 h, cooled and weighed to determine the ash content of the residue (W 5 ). Acid detergent fiber (ADF), lignin (%) and cellulose (%) were calculated as;
  • % ADF = (W3- W2)/W1× 100
  • % Lignin = (W4- W5)/W1× 100
  • % Cellulose = (W3- W4)/W1× 100
- Respiration
The CO 2 evolution during decomposition was mea-sured with an infra-red gas analyzer (IRGA, modified LI-840; Li-Cor, Linclon, NE, USA). Measurements were performed twice a week until experimental day 80, after which they were performed once a week. The microcosm bottles were flushed with CO 2 -free air for 1 min through the hole in the lid and immediately sealed tightly with a rubber septum. The CO 2 concentration of air sample was measured with an IRGA after incubation at 23℃ for 2 h and is presented in μmol CO 2 g -1 h -1 .
- Dehydrogenase activity
Enzyme activity was determined using the method described by von Mersi and Schinner (1991). Each litter sample was mixed with 1.5 mL of tris buffer (1 M, pH 7) and 2 mL of substrate solution [2-(p-iodophenyl)-3-(p-nitrophenyl)-5-phenyltetrazoliumchloride, INT] in a test tube. The test tube was then sealed with stoppers and in-cubated at 40℃ in the dark for 2 h. The control sample was prepared as above. After incubation the samples were mixed with 10 mL of N,N-dimethylformamide:ethanol (1:1, v/v) and kept at room temperature in the dark for 1 h and shaken vigorously at 20 min intervals. After filtration, the developed idonitrotetrazolium formazan (INTF) was measured spectrophotometrically at 464 nm against a blank.
Dehydroganese activity was calculated as:
  • INTF (μg g-1dry litter2 h-1) = (S - C) × 100/% dm,
where S was the mean values of samples, C was the values of the control, and % dm was the factor for dry matter.
- Microbial biomass
Fungal, bacteria and total microbial biomass-C were determined by the substrate induced respiration (SIR) technique of Beare et al. (1990), which was modified from the Anderson and Domsch (1973, 1978) method.
0.5-1.0 g dry weight equivalent of litter sample was weighed in a serum bottle and incubated at 4℃ for 12 h with 2.5 mL of microbial respiration inhibitor per gram of litter sample. We used cyclohexamide (16.0 g/L) as a fungal respiratory inhibitor, and streptomycin (3.2 g/L) as a bacterial inhibitor. We then added 2.5 mL/g of glucose solution (16.0 g/L) as a substrate and immediately flushed the bottle with CO 2 -free air and sealed bottle tightly. We then incubated the bottle at 23℃ for 2 h. The CO 2 concen-tration in the bottle was measured by IRGA.
Microbial biomass-C was calculated according to the following equations.
  • Fungal biomass (μg C/gdry weight) = 231.5 + 17.3 (μg CO2- Cfungalg-1dry weighth-1)
  • Bacterial biomass (μg C/gdry weight) = 188.3 + 15.5 (μg CO2- Cbacterialg-1dry weighth-1)
  • Total microbial biomass-C (μg C/gdry weight) = -765.1+ 14.3 (μg CO2- Ctotalg-1dry weighth-1)
- Statistical analysis
Differences between samples, in regards to litter mass loss, CO 2 evolution, and microbial biomass were ana-lyzed statistically using a one-way ANOVA followed by a Turkey honestly significant difference test. For each value we provided linear correlation coefficients. All statistical work was performed with SPSS ver. 17.0 (SPSS Inc., Chi-cago, IL, USA).
- Litter mass loss
The changes in mass of the S. alnifolia leaf litter sam-ples during the experiment for the different pH treat-ments are illustrated in Fig. 1 . The mass of litter generally decreased as time elapsed, but there were differences in mass loss between different pH treatments during the early decomposition stage. In the early stage, mass loss at pH 3 was 26.7%, which represented the lowest rate of lit-ter decay; conversely, weight loss was 38.5% of initial lit-ter mass at pH 5, which represented the highest decaying rate. The difference between weight loss at pH 3 and pH 5 was 11.8%, which was statistically significant ( P = 0.001). However, litter decomposition rates were not significantly different between each pH treatment at the late decom-position stage, where mass loss was 46.5% and 48.1% at pH 3 and pH 4, respectively.
- Microbial biomass
Lager Image
Cumulative mass losses of Sorbus alnifolia leaf litter at 23℃ and in constant humidity from the different simulated acid rain pH treatments. Vertical lines indicate standard deviation (P < 0.05 N = 4).
Fig. 2 illustrates the changes in microbial biomass on the decomposing litter samples induced by the simulated acid rain. The different microbial groups reacted simi-larly in terms of biomass, which tended to decrease with increasing acidity; i.e., bacterial, fungal and total micro-bial biomasses were smallest at pH 3 and highest at pH 5; however, biomass at pH 6.5 was smaller than that at pH 5.
Microbial biomass changed greatly at the different lit-ter decomposition stages. Biomass tended to be highest at the mid decomposition stage, which is the stage that provided the greatest differences in microbial biomass at each pH level. In the late stage of litter decomposition, af-ter 290 experimental days, microbial biomass was small and there were small differences between each pH level. At day 80 of decomposition, total microbial biomass-C was 11.43 mg-C/g at pH 3, 14.3 mg-C/g at pH 4, 17.33 mg-C/g at pH 5, and 14.22 mg-C/g at pH 6.5. At the mid decomposion stage, total microbial biomass increased to 12.97 mg-C/g, 17.39 mg-C/g, 23.25 mg-C/g, and 19.44 mg-C/g at each pH treatment, respectively. However, the microbial biomass then decreased to 7.47 mg-C/g at pH 3, 8.49 mg-C/g at pH 4, 10.31 mg-C/g at pH 5, and 8.19 mg-C/g at pH 6.5, representing much smaller differences between the pH treatments.
Bacterial biomass on the decomposing S. alnifolia litter exhibited a similar pattern to total microbial biomass, but after the initial decomposition stage bacterial biomass decreased instead of increasing. Bacterial biomass at late stage of litter decay also presented smaller differences between the pH treatments; however, bacterial biomass was still lowest at pH 3. At the mid stage of decomposi-tion, fungal biomass conspicuously increased in all pH treatments and presented large differences between the
Lager Image
Total microbial biomass-C (mg-C/g) bacterial biomass and fungal biomass on the decaying Sorbus alnifolia leaf litter as measured by the substrate induced respiration method in combination with the selective inhibition technique at different pH levels. Vertical bars indicate standard deviation (P < 0.05 N = 4).
pH treatments in the low pH treatments.
The microbial community composition, i.e., the fungi/bacteria ratio, of the decomposing litter changed dra-matically between the initial and late litter decomposition stages. These differences were caused by the different responses of bacteria and fungi to the various pH levels at each litter decomposition stage ( Fig.3 ). At the initial
Lager Image
Changes in ratio of fungi:bacteria on the decaying Sorbus alnifolia leaf litter samples at different pH levels of simulated acid rain. Vertical bars indicate standard deviation (P < 0.05 N = 4).
Lager Image
Changes in CO2 evolution from decaying Sorbus alnifolia leaf litter at different pH levels of simulated acid rain. Vertical bars indicate standard deviation (P < 0.05 N = 4).
decomposition stage, 80 days after the start of decomposition, the fungi:bacteria ratio was higher than one at low pH, while it was smaller than one pH 5 and 6.5. The fungi:bacteria grew over the course of the experiment ( Fig.3 ). These results suggest that the bacterial commu-nity dominates the initial decomposition phase, espe-cially at high pH, while the fungal community was pre-dominant during the later stages of S. alnifolia leaf litter decomposition.
- Microbial respiration
CO 2 evolution from the decaying leaf litter was used as an indicator of microbial activity. CO 2 evolution rate was high during the early stages of decomposition ranging from 5.7 μmol CO 2 g -1 h -1 to 6.8 μmol CO 2 g -1 h -1 . However, microbial respiration rate gradually decreased over the course of the experiment ( Fig.4 ). In the early litter de-composition stage, CO 2 evolution was highest in the pH
Lager Image
Changes in dehydrogenase activity (mg INTF g-1 h-1) within decaying Sorbus alnifolia leaf litter at different pH levels of simulated acid rain (P < 0.05 N = 4). INTF idonitrotetrazolium formazan.
4 treatment at 0.68 μmol CO 2 g -1 h -1 . After this stage, CO 2 evolution decreased linearly with decreasing acidity. Dur-ing the late stages of decomposition (after 290 days), CO 2 evolution decreased to one third of its value during the early decomposition stages (2.3-2.6 μmol CO 2 g -1 h -1 ) and there were no significant differences between each pH treatment ( Fig.4 ).
- Dehydrogenase activity
Dehydrogenase activity, a measure of microbial meta-bolic activity, changed in a pH dependent manner. En-zyme activity decreased with increasing acidity, with the activity at low pH being 70-80% of the activity at high pH. Furthermore, dehydrogenase activity varied considerably between decomposition stages ( Fig.5 ). Dehydrogenase activities during the early decomposition stage ranged between 3.84-5.32 mg INTF g -1 h -1 , while they were be-tween 9.53- 13.27 mg INTF g -1 h -1 during the late decom-position stage. The two-fold increase in dehydrogenase activity during the late stage may have been attributable to the predominance of fungi during this stage.
Acid precipitation received considerable research at-tention during the 1970s and 1980s. And although the severity of acid precipitation has declined, it does con-tinue today with higher rates of deposition (Berg and McClaugherty 2008). Soil microbial activity and biomass play important roles in ecosystem processes such as litter decomposition and nutrient cycling, it has been shown that these microbial activities are influenced by the physi-cochemical environments and chemical contents of the decomposition substrate (Heal et al. 1997, Zimmer 2002, Sariyildiz and Anderson 2003, Berg and McClaugherty 2008). Especially, acid rain is thought of as one of the most serious anthropogenic impacts on ecosystem function and is a major component of the current environmental crisis facing modern society (Zhang et al. 2007, Berg and McClaugherty 2008, Wang et al. 2010).
The results of this study revealed a remarkable reduc-tion in leaf litter mass, a key indicator of microbial de-composition activity, during the early stages of decom-position even at low pH. Although, many studies have demonstrated a decrease in decomposition rates as a result of acidification (Rechcigl and Sparks 1985, Wolters 1991a, 1991b, Wang et al. 2010). But Batty and Younger (2007) found that the Phragmites australis leaf litter did not exhibit significant mass loss within a pH range of 3.0-6.5 in artificial mine water containing some metals, peat based compost and partially rotted cow manure over 6 month period. However, Wang et al. (2010) reported that simulated acid rain restrained the cumulative mass loss of Quercus acutissima litter in the field, with 15.28% mass loss at pH 4.5, 15.89% at pH 5 and 16.33% in the control over a six-month period.
In this study, plant litter mass loss rates were sig-nificantly different between pH treatments at the early decomposition stage but not during the late stages of decomposition. These results suggest that microbial community composition adapts to variations in pH as time lapses. The changes in fungi:bacteria ratio during the litter decomposition process demonstrated clear pat-terns of microbial succession over the experimental pe-riod. These succession patterns were previously detected by Bååth and Anderson (2003) by using SIR in combina-tion with the selective inhibition and phospholipid fatty acid (PLFA) techniques.
Microbial biomass was highest during the mid stage of decomposition and lowest during the late stage irrespec-tive of pH treatment; differences in biomass variation over time between the pH treatments showed the same pat-tern, with the largest differences evident during the mid stage of decomposition. Microbial biomass at each pH level exhibited similar responses as litter mass loss, with positive correlations between microbial biomass and lit-ter decomposition rates ( Table 2 ). Consequently, the re-duced rate of litter decomposition at low pH may have been due to the loss of microbial biomass resulting from acidification, especially during the early decomposition stages. However, decomposition process is more compli-cated as evidenced by the decomposer community com-position changing over the course of the decomposition cycle in a form of microbial succession (Abrahamsen et al. 1980, Bååth and Arnebrant 1994, Bååth and Anderson 2003). This study also found total microbial biomass-C, bacterial biomass, fungal biomass and fungi:bacteria ra-tio changed in response to pH and at the different decom-position stages. Fungal biomass was predominant at low pH while bacterial biomass dominated at higher pH lev-els, which is consistent with the results of the many other studies (Bååth et al. 1979, Bewley and Parkinson 1985, Esher et al. 1992, Fritze et al. 1992, Bååth and Arnebrant 1994, Arao 1999, Pennanen et al. 1999). Rousk et al. (2009) reported five-fold decreases in bacteria and five-fold in-creases in fungi, which resulted in an approximately 30-fold increase in fungal importance, as indicated by the fungal growth:bacterial growth ratio, when pH changing substrate from 8.5 to 4.5. Bååth and Anderson (2003) re-ported a positive correlation between microbial biomass and soil pH, and that the fungi:bacteria ratio decreased significantly with increasing pH (from about 9 at pH 3 to approximately 2 at pH 7) in beech/oak soil. They also found strong linear correlations between total microbial biomass and substrate pH, estimated with SIR in combi-nation with the selective inhibition and the PLFA tech-niques in a pH gradient (3.0-7.2).
CO 2 evolution and enzyme activity are good indicators of microbial activity in response to environmental chang-es such as pH of the substrate. In this study, CO 2 evolution peaked during the early litter decomposition stages and
The relationships between litter decomposition and three microbial biomass parameters present on the decaying leaf litter from the different simulated acid rain pH treatments taken at 23℃ and at constant humiditySIR, substrate induced respiration.*Significant correlation in theP-value range of 0.05.
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The relationships between litter decomposition and three microbial biomass parameters present on the decaying leaf litter from the different simulated acid rain pH treatments taken at 23℃ and at constant humidity SIR, substrate induced respiration. *Significant correlation in the P-value range of 0.05.
The relationships between microbial biomass and CO2evolution from the decaying litter from the different simulated acid rain pH treatments taken at 23℃ and at constant humiditySIR, substrate induced respiration.*Significant correlation in theP-value range of 0.05.
Lager Image
The relationships between microbial biomass and CO2 evolution from the decaying litter from the different simulated acid rain pH treatments taken at 23℃ and at constant humidity SIR, substrate induced respiration. *Significant correlation in the P-value range of 0.05.
decreased as time elapsed, resultantly differences in CO 2 evolution rates between the pH treatments were minimal during the late stages. CO 2 evolution showed significant pH dependent relationships in response to simulated acid rain and CO 2 evolution more strongly correlated with total microbial and fungal biomass. Fungal biomass ex-hibited a significant positive relationship with microbial biomass and with CO 2 evolution ( Table 3 ).
Dehydrogenase activity increased at the mid stage of decomposition and showed strong pH dependant rela-tionships, with activity being lowest at pH 3. Conversely, Killham et al. (1983) and Reddy (1995) suggested dehy-drogenase is unaffected by acidification; although, Wang et al. (2010) reported various inhibiting and catalytic ef-fects of simulated acid rain on many soil enzymes. This study did not find any significant relationships between dehydrogenase activity and CO 2 evolution. Burns (1978) reported that dehydrogenase activity did not consistent-ly correlate with the numbers of microorganisms in soil samples or with rates of oxygen consumption or evolu-tion of carbon dioxide.
The inhibiting effect of acid rain on litter mass loss in this study suggests that the substrate acidification seri-ously affects ecosystem functions. This study provides evidence that litter mass loss patterns in the different acidification treatments was the result of the responses of micro-decomposer growth rates or activities such as enzyme activities or microbial respiration. Consequently, there were complementary relationships among the microbial groups within the changing environment. Even though total microbial biomass on the decomposing litter samples was similar among the pH treatments, microbial species compositions were different due to the pH toler-ances of each microbial species. The results of this study and that of Bååth and Anderson (2003) suggest that the presence of a complementary microbial succession event between the bacterial and fungal groups, which occurs in such a manner that total mi-crobial biomass or total mi-crobial activities such as CO 2 evolution are constant along a pH gradient.
Abrahamsen G , Hovland J , Hagvar S , Hutchinson TC , Havas M 1980 Effects of artificial acid rain and liming on soil organisms and the decomposition of organic matters. In: Effects of Acid Precipitation on Terrestrial Ecosystems Plenum Press New York 341 - 362
Anderson JPE , Domsch KH 1973 Quantification of bacterial and fungal contributions to soil respiration. Arch Microbiol 93 113 - 127    DOI : 10.1007/BF00424942
Anderson JPE , Domsch KH 1978 A physiological method for the quantitative measurement of microbial biomass in soils. Soil Biol Biochem 10 215 - 221    DOI : 10.1016/0038-0717(78)90099-8
Arao T 1999 In situ detection of changes in soil bacterial and fungal activities by measuring13C incorporation into soil phospholipid fatty acids from13C acetate. Soil Biol Biochem 31 1015 - 1020    DOI : 10.1016/S0038-0717(99)00015-2
Bååth E , Anderson TH 2003 Comparison of soil fungal/bacterial ratios in a pH gradient using physiological and PLFA-based techniques. Soil Biol Biochem 35 955 - 963    DOI : 10.1016/S0038-0717(03)00154-8
Bååth E , Arnebrant K 1994 Growth rate and response of bacterial communities to pH in limed and ash-treated forest soils. Soil Biol Biochem 26 995 - 1001    DOI : 10.1016/0038-0717(94)90114-7
Bååth E , Lundgren B , Söderström B 1979 Effects of artificial acid rain on microbial activity and biomass. Bull Environ Contam Toxicol 23 737 - 740    DOI : 10.1007/BF01770034
Batty LC , Younger PL 2007 The effect of pH on plant litter decomposition and metal cycling in wetland meso-cosms supplied with mine drainage. Chemosphere 66 158 - 164    DOI : 10.1016/j.chemosphere.2006.05.039
Beare MH , Neely CL , Coleman DC , Hargrove WL 1990 A substrate-induced respiration (SIR) method for mea-surement of fungal and bacterial biomass on plant resi-dues. Soil Biol Biochem 22 585 - 594    DOI : 10.1016/0038-0717(90)90002-H
Berg B , McClaugherty C 2008 Plant Litter: Decomposition Humus Formation Carbon. Springer-Verlag Berlin.
Bewley RJF , Parkinson D 1985 Bacterial and fungal activity in sulphur dioxide polluted soils. Can J Microbiol 31 13 - 15    DOI : 10.1139/m85-003
Burns RG 1978 Enzyme activity in soil: some theoretical and practical considerations. In: Soil Enzymes (Burns RG, ed) Academic Press London 295 - 340
Esher RJ , Marx DH , Ursic SJ , Baker RL , Brown LR , Coleman DC 1992 Simulated acid rain effects in fine roots ec-tomycorrhizae microorganisms and invertebrates in pine forests of the southern United States. Water Air Soil Pollut 61 269 - 278    DOI : 10.1007/BF00482610
Evans LS , Gmur NF , Mancini D 1982 Effects of simulated acidic rain on yields of Raphanus sativus Lactuca sati-va Triticum aestivum and Medicago sativa. Environ Exp Bot 22 445 - 453    DOI : 10.1016/0098-8472(82)90055-7
Fairfax JAW , Lepp NW 1975 Effect of simulated ‘acid rain’ on cation loss from leaves. Nature 255 324 - 325    DOI : 10.1038/255324a0
Fritze H 1992 Effects of environmental pollution on forest soil microflora. Silva Fenn 26 37 - 48
Fritze H , Kiikkilä O , Pasanen J , Pietikäinen J 1992 Reaction of forest soil microflora to environmental stress along a moderate pollution gradient next to an oil refinery. Plant Soil 140 175 - 182    DOI : 10.1007/BF00010595
Heal OW , Anderson JM , Swift MJ 1997 Plant litter quality and decomposition: and historical overview. In: Driven by Nature: Plant Litter Quality and Decomposition (Cadisch G, Giller KE, eds) CAB International Walling-ford 3 - 45
Helrich K 1990 Official Methods of Analysis of the Associa-tion of Official Analytical Chemists. Association of Official Analytical Chemists Washington DC.
Hermle S , Vollenweider P , Günthardt-Goerg MS , McQuattie CJ , Matyssek R 2007 Leaf responsiveness of Popu-lus tremula and Salix viminalis to soil contaminated with heavy metals and acidic rainwater. Tree Physiol 27 1517 - 1531    DOI : 10.1093/treephys/27.11.1517
Hovland J 1981 The effect of artificial acid rain on respira-tion and cellulase activity in Norway spruce needle lit-ter. Soil Biol Biochem 13 23 - 26    DOI : 10.1016/0038-0717(81)90097-3
Hovland J , Abrahanmsen G , Ogner G 1980 Effects of artifi-cial acid rain on decomposition of spruce needles and on mobilisation and leaching of elements. Plant Soil 56 365 - 378    DOI : 10.1007/BF02143031
Huang DY , Xu YG , Zhou B , Zhang HH , Lan JB 2010 Wet deposition of nitrogen and sulfur in Guangzhou a sub-tropical area in South China. Environ Monit Assess 171 429 - 439    DOI : 10.1007/s10661-009-1289-7
Jezierska-Tys S 2004 Respiration activity and dehydroge-nase activity and number of proteolytic micro-organ-isms in soil contaminated with sulphur and amended with sewage sludge. Acta Agrophysica 106 501 - 508
Killham K , Firestone MK , McCall JG 1983 Acid rain and soil microbial activity: effects and their mechanisms. J Environ Qual 12 133 - 137
Kim YO , Rodriguez RJ , Lee EJ , Redman RS 2008 Phytolacca Americana from contaminated and noncontaminated soils of south Korea: effects of elevated temperature CO2and simulated acid rain on plant growth response. J Chem Ecol 34 1501 - 1509    DOI : 10.1007/s10886-008-9552-x
Lee CS , You YH , Kim JH 1998 Selection of tolerant species among Korean major woody plants to restore Yeocheon Industrial Complex Area. Korea J Ecol 21 337 - 344
Lee HY 1998 The spatial distribution of acid rain in Korea. J Korean Geogr Soc 33 455 - 468
Likens GE 1972 The Chemistry of Precipitation in the Cen-tral Finger Lakes Region. Cornell University Water Resources and Marine Science Center Ithaca NY.
Likens GE , Bormann FH 1995 Biogeochemistry of a Forest-ed Ecosystem. Springer-Verlag New York.
Liu J , Zhou G , Zhang D 2007 Simulated effects of acidic solutions on element dynamics in monsoon evergreen broad-leaved forest at Dinghushan China. Part 1: dy-namics of K Na Ca Mg and P. Environ Sci Pollut Res Int 14 123 - 129    DOI : 10.1065/espr2006.07.325
Matzner E , Murach D , Fortmann H 1986 Soil acidity and its relationship to root growth in declining forest stands in Germany. Water Air Soil Pollut 31 278 - 282
Mayer R , Ulrich B 1974 Conclusions on the filtering action of forests from ecosystem analysis. Oecol Plant 9 157 - 168
Ministry of Environment. 2010 Environmental Statistics Yearbook. Ministry of Environment Gwacheon.
Moldan B , Cerny J 1994 Biogeochemistry of Small Cach-ments: A Tool for Environmental Research. SCOPE 51. John Wiley & Sons New York.
Monteith DT , Evans CD 2005 The United Kingdom acid wa-ters monitoring network: a review of the first 15 years and introduction to the special issue. Environ Pollut 137 3 - 13    DOI : 10.1016/j.envpol.2004.12.027
Myrold DD , Nason GE 1992 Effect of acid rain on soil micro-bial processes. In: Environmental Microbiology (Mitchell R, ed) Wiley-Liss Inc. New York 59 - 82
Neufold HS , Jernstedt JA , Haines BL 1985 Direct foliar ef-fects of simulated acid rain I. Damage growth and gas exchange. New Phytol 99 389 - 405    DOI : 10.1111/j.1469-8137.1985.tb03667.x
Ouyang XJ , Zhou GY , Huang ZL , Liu JX , Zhang DQ , Li J 2008 Effect of simulated acid rain on potential carbon and nitrogen mineralization in forest soils. Pedosphere 18 503 - 514    DOI : 10.1016/S1002-0160(08)60041-7
Pennanen T , Fritze H , Vanhala P , Kiikkilä O , Neuvonen S , Bååth E 1998 Structure of a microbial community in soil after prolonged addition of low levels of simulated acid rain. Appl Environ Microbiol 64 2173 - 2180
Pennanen T , Liski J , Bååth E , Kitunen V , Uotila J , Westman CJ , Fritze H 1999 Structure of the microbial communi-ties in coniferous forest soils in relation to site fertility and stand development stage. Microbiol Ecol 38 168 - 179    DOI : 10.1007/s002489900161
Prescott CE , Parkinson D 1985 Effects of sulphur pollution on rates of litter decomposition in a pine forest. Can J Bot 63 1436 - 1443    DOI : 10.1139/b85-199
Proctor JTA 1983 Effect of simulated acid sulfuric rain on apple tree foliage nutrient content yield and fruit qual-ity. Environ Exp Bot 23 167 - 174    DOI : 10.1016/0098-8472(83)90036-9
Rechcigl JE , Sparks DL 1985 Effect of acid rain on the soil environment: a review. Commun Soil Sci Plant Anal 16 653 - 680    DOI : 10.1080/00103628509367636
Reddy MV 1995 Soil organisms and litter decomposition in the tropics. Oxford & IBH New Delhi.
Reich PB , Schoettle AW , Stroo HF , Troiano J , Amundson RG 1987 Effects of ozone and acid rain on white pine (Pinus strobus) seedlings grown in five soils. I. Net photosyn-thesis and growth. Can J Bot 65 977 - 987    DOI : 10.1139/b87-135
Rousk J , Brookes PC , Bååth E 2009 Contrasting soil pH ef-fects on fungal and bacterial growth suggest functional redundancy in carbon mineralization. Appl Environ Microbiol 75 1589 - 1596    DOI : 10.1128/AEM.02775-08
Rowland AP , Roberts JD 1994 Lignin and cellulose fraction-ation in decomposition studies using acid-detergent fi-bre methods. Commun Soil Sci Plant Anal 25 269 - 277    DOI : 10.1080/00103629409369035
Sakamoto K , Isobe Y , Dong X , Gao S 2001 Simulated acid rain leaching characteristics of acid soil amended with bio-briquette combustion ash. Water Air Soil Pollut 130 1451 - 1456    DOI : 10.1023/A:1013913014071
Sariyildiz T , Anderson JM 2003 Interactions between litter quality decomposition and soil fertility: a laboratory study. Soil Biol Biochem 35 391 - 399    DOI : 10.1016/S0038-0717(02)00290-0
von Mersi W , Schinner F 1991 An improved and accurate method for determining the dehydrogenase activity of soils with iodonitrotetrazolium chloride. Biol Fertil Soils 11 216 - 220    DOI : 10.1007/BF00335770
Wang C , Guo P , Han G , Feng X , Zhang P , Tian X 2010 Ef-fect of simulated acid rain on the litter decomposition of Quercus acutissima and Pinus massoniana in forest soil microcosms and the relationship with soil enzyme activities. Sci Total Environ 408 2706 - 2713    DOI : 10.1016/j.scitotenv.2010.03.023
Wolters V 1991a Effects of acid rain on leaf-litter decom-position in a beech forest on calcareous soil. Biol Fertil Soils 11 151 - 156    DOI : 10.1007/BF00336381
Wolters V 1991b Biological processes in two beech forest soils treated with simulated acid rain: a laboratory ex-periment with Isotoma tigrina (Insecta Collembola). Soil Biol Biochem 23 381 - 390    DOI : 10.1016/0038-0717(91)90195-P
Wood M , Cooper JE , Holding AJ 1984 Aluminum toxicity and nodulation of Trifolium repens. Plant Soil 78 381 - 391    DOI : 10.1007/BF02450371
Wood T , Bormann FH 1974 The effects of an artificial acid mist upon the growth of Betula alleghaniensis Britt. Environ Pollut 7 259 - 268    DOI : 10.1016/0013-9327(74)90035-4
Zhang JE , Ouyang Y , Ling DJ 2007 Impacts of simulated acid rain on cation leaching from the latosol in south China. Chemosphere 67 2131 - 2137    DOI : 10.1016/j.chemosphere.2006.12.095
Zimmer M 2002 Is decomposition of woodland leaf litter influenced by its species richness? Soil Biol Biochem 34 277 - 284    DOI : 10.1016/S0038-0717(01)00173-0