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KUČERA ALEŠ, HOLÍK LADISLAV, MAROSZ KAREL, MARTINÍK ANTONÍN, VAVŘÍČEK DUŠAN: Changes in forms of available nitrogen and respiration in soil of beech forest as a reaction to a deforestation resulting from wind storm. Acta Universitatis Agriculturae et Silviculturae Mendelianae Brunensis, 2013, LXI, No. 1, pp. 107–113 The article deals with the reaction of soil environment to a violent deforestation resulting from a wind storm. As a material, permanent inventory plot located in Training Forest Enterprise Masaryk Forest Křtiny was selected. The plot represents beech high forest, where soil was sampled from four types of sample plots: (1) maternal forest representing situation before the storm; (2) zone of transition from the maternal forest to the open area; (3) reaff orested clearing; (4) natural evolution. From each sample plot type, 6 mixed samples of Ah horizon were analysed to assess N-ammonium (N-NH4 +) and N-nitrates (NO3 −) content and respiration activity. The results show a signifi cant diff erence between the respiration activities of the particular sample plots, as well as a signifi cant diff erence in the content of N-ammonium and N-nitrate forms, the maternal forest representing a site of the lowest biological (and respiration) activity on the one hand, and, on the other hand, site of high N-ammonium and low N-nitrate content, respectively. From the results, intensive nitrifi cation caused by the deforestation is evident. The results are to be used as a starting level for a long-term observation of reaction of the forest beech ecosystem to deforestation and selected types of forest management. European beech, N-ammonium, N-nitrates, nitrogen, wind storm, soil, clearing In August 2010, wind storm Antonín damaged many forest stands in the Czech Republic, also aff ecting several in the Training Forest Enterprise, Masaryk Forest Křtiny (TFE). The areas are used to establish permanent inventory plots (PIP) with the aim (1) to observe a reaction of forest ecosystem to development of clearings; (2) to observe a reaction of forest ecosystem to diff erent managements of forest restoration (Dobrovolný et al., 2011). One of the PIPs was established in the beech stand in autumn 2011. In the case of this PIP, changes of nitrogen forms acceptable by plants (NH4 + and NO3 −) and biological activity explained by respiration are observed, as a reaction to the development of a clearing. Numerous works has been written, dealing with the reaction of soil environment to deforestation, and focusing on the amount of nitrogen in soil (Bormann, Likens, 1994; Hruška, Ciencala, 2005; Vitousek, Jerry, 1979; Weis et al., 2006). Several articles focus on the infl uence of specifi c forest management or a er-clearing melioration on soil (Akselsson et al., 2004; Closa, Goicoechea, 2010; LeDuc, Rothstein, 2007; Prescott, 1997; Vitousek, Matson, 1985). Other works perceive the stormclearing as a natural disturbation and, hence, they observe autonomic evolution of forest ecosystems (Attiwill, 1993; Legout et al., 2009; Vitousek, Jerry, 1979). In general, stand climate changes, changes of water regime, soil biochemistry and physical chemistry all represent an immediate eff ect of deforestation (Smerthurst, Nambiar, 1990; Striegl, Wickland, 1998). Plant nutrition and soil nutrient regime, as well as nitrogen dynamics, belong among 108 Aleš Kučera, Ladislav Holík, Karel Marosz, Antonín Martiník, Dušan Vavříček soil properties with fast feedback as a reaction to a development of a clearing (Prescott, 1997). Disturbation can cause changes and fl ows of nitrogen in many forms: immobilization by decompositors, volatilization, denitrifi cation, loss to streamwater or groundwater, clay fi xation of ammonium, lags in nitrifi cation, nitrate reduction to ammonia, nitrate adsorption on soil colloids, lack of water for nitrate transport, or (once the plant regrowth is established) plant nitrogen uptake. In general, the change of acceptable nitrogen forms causes a change of nitrogen dynamic as a consequence of nitrifi cation (Weis et al., 2006; White, 2006; Šimek, 2003), which, means a change of N-ammonium form (N-NH4 +) to N-nitrates (NNO3 −). The principal result of the nitrifi cation process is an increase of nitrogen mobility and a risk of nitrogen losses with a groundwater. In the case of “non-extreme habitats”, the process of deforestation results in changes in water and temperature regime and light conditions which causes, rising of biological activity, intensifi cation of decomposition processes and nutrient cycles (Closa, Goicoechea, 2010; Marra, Edmonds, 1996; Marshall, 2000; Olsson et al., 1996). The hereinabove named parameters can be explained using soil respiration tests (Fleming et al., 2006). Except winter season, clear-cut areas represent sites with intensive respiration and CO2 fl ux (Striegl, Wickland, 1998). The present study deals with a content of two nitrogen forms (N-ammonium and N-nitrates) 1.5 year a er inception of the clearing caused by the wind storm. To explain reaction of soil biota, respiration tests were performed within the investigated area. The character of the article is a “pilot study” starting a long-term observation of soil reaction to deforestation. Original data representing the starting point, which is to be used for the long-term research on PIP, are presented. MATERIAL AND METHODS The PIP is located in the TFE close to village Vranov. The maternal forest is composed of European beech (Fagus sylvatica L.). The bedrock is composed of mixed substrate of granodiorite and loess, with a Cambisol soil type (Michéli et al., 2006). The research site is located on a medial slope with eastern exposition, with a potential risk of soil surface denudation resulting from the deforestation. The investigated forest was cleared in August 2010. In March 2012, the clearing was reaff orested with planting space of 10.000 pcs. per hectare using bare-rooted plants. The design of the study can be described as an area of four squares 25 × 25 m each, regularly deployed on the clearing. Between each two pairs of squares, a zone of natural evolution 20– 25 ms wide, oriented concurrently with contours, is placed. The soil was sampled in October 2011 and in April 2012 from four individual sampling plots. The sampling plots were marked as (M) adjacent maternal forest, which remained undamaged a er the storm; (T) transitional zone between the maternal forest and clearing; (P) plantation and (N) natural evolution with no a er-cleaning treatment. As the October sampling was performed before the reaff orestation, two slightly diff erent sample sets were provided: Sampling of October 2011 before plantation and sampling in April 2012 a er plantation. The dataset of October 2011 is composed of M, T and N sampling plots, the dataset of April 2012 is composed of M, T, P and N sampling plots. From each type of sampling plot, six mixed samples were provided from organomineral horizon Ah. Each mixed sample was composed of three individual sample sites randomly selected from the sample plot. Soil samples were analysed in a fresh condition, a er sieving through a sieve with meshes of 2 mm diameter. The leachate of N-ammonium (NH4 +) and N-nitrate (NO3 −) was analysed spectrophotometrically, basal and potential respiration was analysed by titration (Zbíral et al., 2004). N-ammonium and N-nitrates were assessed in leach of 1M KCl, in three repetitions for each soil sample. A er leaching, the sample was centrifuged. To assess N-ammonium, 4 ml of color reagent (130.0 g of sodium salicylate, 130.0 g of sodium citrate and 0.950 g of sodium nitroprusside, dihydrate dissolved in 1,000 ml of water), 4 ml of alkaline solution (32 g of sodium hydroxide and 2 g of sodium dichloroisocyanurate dihydrate dissolved in 1,000 ml of water) was added into 5 ml of soil eluate (ratio soil/1M KCl, 1/5, w/v). The total volume was supplied to 50 ml fl asks by demineralised water. Concentration of NH4 + (NNH4 +) [mg NH4 + * 1 g dry mass−1] was measured in wavelength of 655 nm (green coloured solution). The results were assessed according to a calibration curve. Nitrates were assessed in 20 ml of soil eluate (ratio soil/1M KCl, 1/5, w/v), into which 1 ml of 0.5% sodium salicylate was added. A er evaporating, 1 ml of concentrated sulfuric acid, 3 ml of demineralized water and 10 ml of alkaline solution was added. Total volume was supplied to 50 ml fl asks by demineralised water. Concentration of NO3 − (NNO3 −) [mg NO3 − * 1 g dry mass−1] was measured in wavelength of 410 nm (yellow coloured solution). The results were assessed according to a calibration curve. Respiration was assessed as basal (BR) and potential (with 2 mg of glucose per 1 g of dry soil) (PR), in three repetitions for each soil sample. 40 g of sample was being incubated in hermetic boxes for 6 hours in 22°C with 1 M NaOH put on petri dish. A er incubation, 2 ml of 12.5% BaCl2 was added to NaOH and the solution was titrated with 0,05M HCl using phenolphtalein indicator. Results are given in mg C-CO2*g −1*h−1. The data was processed using ANOVA, grouped according to the type of sampling plot (maternal – M, transitional – T, plantation – P, natural evolution – N). In the case of rejection of null-hypothesis (H0), a post-hoc analysis was performed in the form of Changes in forms of available nitrogen and respiration in soil of beech forest as a reaction to a deforestation 109 Turkey’s test. The signifi cance level  = 0.05. The calculations were performed in Statistica Cz 9.0. RESULTS AND DISCUSSION The average values of observed soil parameters are presented in Tab. I (each value represents the mean of three repetitions provided during analyses of soil samples). Respiration tests were performed in October 2011. The data gathered from the three types of sampling plots are processed (M, T, N). The results from ANOVA show rejection of H0 (p < 0.05) in the case of potential respiration (p = 0.0766 for basal respir