神农架地区米心水青冈林和锐齿槲栎林的格局与过程

本文对神农架地区广泛分布的米心水青冈林和锐齿槲栎林的种群和群落学特征、干扰历史、更新策略、生物量、生产量及元素循环特征进行了研究。得到如下结论： 1 米心水青冈林是神农架地区山地垂直分布的地带性植被类型，主要群落学特征为：（1）建群种明显，该区域主要有2种类型，即米心水青冈林和米心水青冈、锐齿槲栎林;（2）群落结构简单，但物种组成丰富，在6600m~2样地中出现高等植物（不含苔藓植物）77科150属271种，组成种类以蔷薇科、百合科、忍冬科、虎耳草科、樟科、杜鹃花科和壳斗科为主;（3）群落乔木层（占重要值的12％）和灌木层（占盖度的15％）中含有一定比例的常绿树种;（4）群落生活型以高位芽植物（70.89%）占绝对优势，其次为地面芽植物（15.50%）和地下芽植物(12.92%)。 2 米心水青冈是多主干的树种，萌枝现象普遍，但萌枝数量不同地点差异较大。通过萌枝产生的枝群体平均密度为257 ± 99.3n•hm~(-2)。枝群体的年龄结构表现为“幼龄个体数目较多型”和“中国年龄阶段数目较多型”，并且有较多的枝群体表现出一致的年龄结构。从整个群落米心水青冈的年龄结构来看，表现出发展型种群的特点。枝群体的分布格局为随机分布。9丛米心水青冈完整的年轮分析结果表明，它们萌枝的时间不是边疆的，而与森林的受干扰有关。根据83个圆盘和生长锥芯资料，米心水青冈在萌枝后成长为乔木层或林冠层的过程中，径向生长表现为5种模式。这是丛株内竞争的结果。萌枝在米心水青冈林的维持和发展过程中，具有重要的生态学作用。 3 锐齿槲栎林是神农架地区山地垂地分布的地带性植被类型，主要群落学特征为：（1）建群种明显，该区域主要有2种类型，即锐齿槲栎林和锐齿槲栎、米心水青冈林;（2）群落乔木层和灌木层中含有一定比例的常绿树种，和暖温带的落叶栎林有较大差异;（3）群落物种组成丰富，不仅具有典型的温带科属，还有典型亚热带分布的科属，组成种类主要以蔷薇科、百合科、忍冬科、虎耳草科、山茱萸科、杜鹃花科、壳斗科和樟科;（4）生活型以高位芽植物（66.32%）占绝对优势，其次为地面芽（23.51%）和地下芽（9.47%）植物。 4 通过样地调查、树干解析及直径分析法，对米心水青冈林和锐齿槲栎林受压和释压历史及更新策略进行了研究。米心水青冈直径生长表现为5种模式。而锐齿槲栎只表现为2种模式。85.9 ± 6.9%的米心水青冈有过受压过程，平均受压2.1 ± 0.8次，平均受压时间为47 ± 24.1a，最长受压时间73a，平均释压次数为1.6 ± 0.7次，平均释压时间为23 ± 21.5a，而60.83%的锐齿槲栎都均有1次受压。平均受压时间为19 ± 14a，受压后没有表现出释压过程。结合高生长和径向生长，认为米心水青冈是耐阴树种，它的更新策略是在林下形成苗性萌枝，在有林窗形成时释压生长进入乔木层;而锐齿槲栎是不耐阴树种，它的更新策略是通过产生大量种子，当有大的林窗时，幼苗在林窗内生长逐步进入乔木层。 5 神农架地区102-130a成熟米心水青冈林的生物量在251.31-358.63T•hm~(-2)之间，平均为288.70 ± 48.30T•~(-2)，20-60a锐齿槲栎林群落生物量在134.85-301.20T•hm~(-2)，平均为231.60 ± 78.10T•hm~(-2)。虽然米心水青冈林和锐齿槲栎林灌木层草本层及藤本植物组成很丰富，但二种类型森林生物量的95％以上集中在乔木层。乔木层生物量主要集中在少数优势种中。在米心水青冈林生物量从大到小的序列中，前5种植物分别占乔木层总生物量58.67%-96.37%不等，同样锐齿槲栎林前5种植物占群落生物量的68.13%-95.26%。常绿植物占乔木层生物量的比例变化较大，米心水青冈林中占2.85-18.70%，锐齿槲栎林中一般常绿植物占0.8-9.98%，只有1个锐齿槲栎林样地常绿植物（主要是粉白杜鹃）占乔木层生物量的44.04%。米心水青冈林生物量根冠比为0.27 ± 0.05，锐齿槲栎林为0.21 ± 0.06。神农架地区米心水青冈林的生物量，在成熟的欧洲水青冈林及日本的水青冈林生物量范围之内，而锐齿槲栎林生物量远远大于我国温带落叶栎林的生物量。 6 神农架地区102-130a米心水青冈林生产量范围在1857-2786g•m~(-2)•a~(-1)，平均为2330 ± 397 g•m~(-2)•a~(-1)。20-60a锐齿槲栎林的生产量范围在1319-2521 g•m~(-2)•a~(-1)，平均为1930 ± 498 g•m~(-2)•a~(-1)。米心水青冈林和锐齿槲栎林乔木层生产量占群落总生产量的95％以上，乔木层各器官生产量大小顺序为叶> 树干> 枝和根，其中叶生产量占乔木层的一半以上，达53.87 ± 2.72%（米心水青冈林）和57.31 ± 6.23%（锐齿槲栎林）。在乔木层生产量从大到小的序列中，前5种植物平均占乔木层总生产量的81.03 ± 13.94%（米心水青冈林，范围在62.75%-92.66%）和84.23 ± 9.68%（锐齿槲栎林，范围在68.54-95.11%）。米心水青冈林和锐齿槲栎林群落地下部分生产量占总生产量的比例分别为11.29 ± 1.02%和9.22 ± 2.72。和我国其它地区地带性植被类型相比。米心水青冈林和锐齿槲栎生产量是较高的，和亚热带绿阔叶林生产量接近，但在器官分配上两者差异较大。 7 米心水青冈林和锐齿槲栎林土壤均呈酸性。其中锐齿槲栎林地土壤酸性更强。土壤元素特征表现为Al>C>K>Mg>Ca>N>S、P的特点，富铝化作用明显。8种元素在群落优势植物不同部位含量差异较大，N、P、K、Ca、Mg基本上是以叶片含量最高，树干或根中最低。仅从叶片来看，元素特征表现为C>Ca、N>K>Mg>S>P、Al。优势植物的C/N和C/P显著高于暖温带落叶阔叶林优势植物。8种元素在米心水青冈林和锐齿槲栎林中积累量分别为147.09 ± 25.60和116.00 ± 37.63 Mg hm~(-2)a~(-1)，其中97％以上积累在群落乔木层。两种森林类型各元素的积累量都表现为C>Ca, N> K> Mg> P> S> Al的特点。米心水青风林和锐齿槲栎林8种元素的年存留量分别为6263 ± 90.8和5946 ±246 kg hm~(-2)a~(-1),其中N、P、K、Ca、Mg 5种主要营养元素的存留量分别为179.7 ± 18.2和169.4 ± 23.5kg hm~(-2) a~(-1)。两种森林类型各元素的存留量都表现为C> N> Ca> K> Mg> S> P> Al。

Multiple environmental controls on phytoplankton growth strategies determine adaptive responses of the N : P ratio

The controls on the 'Redfield' N:P stoichiometry of marine phytoplankton and hence the N:P ratio of the deep ocean remain incompletely understood. Here, we use a model for phytoplankton ecophysiology and growth, based on functional traits and resource-allocation trade-offs, to show how environmental filtering, biotic interactions, and element cycling in a global ecosystem model determine phytoplankton biogeography, growth strategies and macromolecular composition. Emergent growth strategies capture major observed patterns in marine biomes. Using a new synthesis of experimental RNA and protein measurements to constrain per-ribosome translation rates, we determine a spatially variable lower limit on adaptive rRNA:protein allocation and hence on the relationship between the largest cellular P and N pools. Comparison with the lowest observed phytoplankton N:P ratios and N:P export fluxes in the Southern Ocean suggests that additional contributions from phospholipid and phosphorus storage compounds play a fundamental role in determining the marine biogeochemical cycling of these elements.

Availability and transfer to grain of As, Cd, Cu, Ni, Pb and Zn in a barley agri-system: Impact of biochar, organic and mineral fertilizers

With biochar becoming an emerging soil amendment and a tool to mitigate climate change, there are only a few studies documenting its effects on trace element cycling in agriculture. Zn and Cu are deficient in many human diets, whilst exposures to As, Pb and Cd need to be decreased. Biochar has been shown to affect many of them mainly at a bench or greenhouse scale, but field research is not available. In our experiment we studied the impact of biochar, as well as its interactions with organic (compost and sewage sludge) and mineral fertilisers (NPK and nitrosulfate), on trace element mobility in a Mediterranean agricultural field (east of Madrid, Spain) cropped with barley. At harvesting time, we analysed the soluble fraction, the available fraction (assessed with the diffusive gradients in thin gels technique, DGT) and the concentration of trace elements in barley grain. No treatment was able to significantly increase Zn, Cu or Ni concentration in barley grain, limiting the application for cereal fortification. Biochar helped to reduce Cd and Pb in grain, whereas As concentration slightly increased. Overall biochar amendments demonstrated a potential to decrease Cd uptake in cereals, a substantial pathway of exposure in the Spanish population, whereas mineral fertilisation and sewage sludge increased grain Cd and Pb. In the soil, biochar helped to stabilise Pb and Cd, while marginally increasing As release/mobilisation. Some of the fertilisation practises or treatments increased toxic metals and As solubility in soil, but never to an extent high enough to be considered an environmental risk. Future research may try to fortify Zn, Cu and Ni using other combinations of organic amendments and different parent biomass to produce enriched biochars.

Erosion rates and landscape evolution of the lowlands of the Upper Paraguay river basin (Brazil) from cosmogenic Be-10

Coordenação de Aperfeiçoamento de Pessoal de Nível Superior (CAPES)

Organic vs. Conventional Grassland Management: Do N-15 and C-13 Isotopic Signatures of Hay and Soil Samples Differ?

Distinguishing organic and conventional products is a major issue of food security and authenticity. Previous studies successfully used stable isotopes to separate organic and conventional products, but up to now, this approach was not tested for organic grassland hay and soil. Moreover, isotopic abundances could be a powerful tool to elucidate differences in ecosystem functioning and driving mechanisms of element cycling in organic and conventional management systems. Here, we studied the delta N-15 and delta C-13 isotopic composition of soil and hay samples of 21 organic and 34 conventional grasslands in two German regions. We also used Delta delta N-15 (delta N-15 plant - delta N-15 soil) to characterize nitrogen dynamics. In order to detect temporal trends, isotopic abundances in organic grasslands were related to the time since certification. Furthermore, discriminant analysis was used to test whether the respective management type can be deduced from observed isotopic abundances. Isotopic analyses revealed no significant differences in delta C-13 in hay and delta C-13 in both soil and hay between management types, but showed that delta C-13 abundances were significantly lower in soil of organic compared to conventional grasslands. delta C-15 values implied that management types did not substantially differ in nitrogen cycling. Only delta C-13 in soil and hay showed significant negative relationships with the time since certification. Thus, our result suggest that organic grasslands suffered less from drought stress compared to conventional grasslands most likely due to a benefit of higher plant species richness, as previously shown by manipulative biodiversity experiments. Finally, it was possible to correctly classify about two third of the samples according to their management using isotopic abundances in soil and hay. However, as more than half of the organic samples were incorrectly classified, we infer that more research is needed to improve this approach before it can be efficiently used in practice.

Factors controlling decomposition rates of fine root litter in temperate forests and grasslands

Background and aims Fine root decomposition contributes significantly to element cycling in terrestrial ecosystems. However, studies on root decomposition rates and on the factors that potentially influence them are fewer than those on leaf litter decomposition. To study the effects of region and land use intensity on fine root decomposition, we established a large scale study in three German regions with different climate regimes and soil properties. Methods In 150 forest and 150 grassland sites we deployed litterbags (100 μm mesh size) with standardized litter consisting of fine roots from European beech in forests and from a lowland mesophilous hay meadow in grasslands. In the central study region, we compared decomposition rates of this standardized litter with root litter collected on-site to separate the effect of litter quality from environmental factors. Results Standardized herbaceous roots in grassland soils decomposed on average significantly faster (24 ± 6 % mass loss after 12 months, mean ± SD) than beech roots in forest soils (12 ± 4 %; p < 0.001). Fine root decomposition varied among the three study regions. Land use intensity, in particular N addition, decreased fine root decomposition in grasslands. The initial lignin:N ratio explained 15 % of the variance in grasslands and 11 % in forests. Soil moisture, soil temperature, and C:N ratios of soils together explained 34 % of the variance of the fine root mass loss in grasslands, and 24 % in forests. Conclusions Grasslands, which have higher fine root biomass and root turnover compared to forests, also have higher rates of root decomposition. Our results further show that at the regional scale fine root decomposition is influenced by environmental variables such as soil moisture, soil temperature and soil nutrient content. Additional variation is explained by root litter quality.

Aboveground community and species-specific plant biomass from the Jena Experiment (Main Experiment, year 2004)

This data set contains aboveground community biomass (Sown plant community, Weed plant community, Dead plant material, and Unidentified plant material; all measured in biomass as dry weight) and species-specific biomass from the sown species of the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. Aboveground community biomass was harvested twice in 2004 just prior to mowing (during peak standing biomass in late May and in late August) on all experimental plots of the main experiment. This was done by clipping the vegetation at 3 cm above ground in four rectangles of 0.2 x 0.5 m per large plot. The location of these rectangles was assigned prior to each harvest by random selection of coordinates within the core area of the plots (i.e. the central 10 x 15 m). The positions of the rectangles within plots were identical for all plots. The harvested biomass was sorted into categories: individual species for the sown plant species, weed plant species (species not sown at the particular plot), detached dead plant material (i.e., dead plant material in the data file), and remaining plant material that could not be assigned to any category (i.e., unidentified plant material in the data file). All biomass was dried to constant weight (70°C, >= 48 h) and weighed. Sown plant community biomass was calculated as the sum of the biomass of the individual sown species. The data for individual samples and the mean over samples for the biomass measures on the community level are given. Overall, analyses of the community biomass data have identified species richness as well as functional group composition as important drivers of a positive biodiversity-productivity relationship.

Aboveground community and species-specific plant biomass from the Jena Experiment (Main Experiment, year 2007)

This data set contains aboveground community biomass (Sown plant community, Weed plant community, Dead plant material, and Unidentified plant material; all measured in biomass as dry weight) and species-specific biomass from the sown species of the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. Aboveground community biomass was harvested twice in 2007 just prior to mowing (during peak standing biomass in early June and in late August) on all experimental plots of the main experiment. This was done by clipping the vegetation at 3 cm above ground in four (May) or three (August) rectangles of 0.2 x 0.5 m per large plot. The location of these rectangles was assigned prior to each harvest by random selection of coordinates within the core area of the plots (i.e. the central 10 x 15 m). The positions of the rectangles within plots were identical for all plots. The harvested biomass was sorted into categories: individual species for the sown plant species, weed plant species (species not sown at the particular plot), detached dead plant material (i.e., dead plant material in the data file), and remaining plant material that could not be assigned to any category (i.e., unidentified plant material in the data file). All biomass was dried to constant weight (70°C, >= 48 h) and weighed. Sown plant community biomass was calculated as the sum of the biomass of the individual sown species. The data for individual samples and the mean over samples for the biomass measures on the community level are given. Overall, analyses of the community biomass data have identified species richness as well as functional group composition as important drivers of a positive biodiversity-productivity relationship.

Aboveground community and species-specific plant biomass from the Jena Experiment (Main Experiment, year 2006)

This data set contains aboveground community biomass (Sown plant community, Weed plant community, Dead plant material, and Unidentified plant material; all measured in biomass as dry weight) and species-specific biomass from the sown species of the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. Aboveground community biomass was harvested twice in 2006 just prior to mowing (during peak standing biomass in early June and in late August) on all experimental plots of the main experiment. This was done by clipping the vegetation at 3 cm above ground in four rectangles of 0.2 x 0.5 m per large plot. The location of these rectangles was assigned prior to each harvest by random selection of coordinates within the core area of the plots (i.e. the central 10 x 15 m). The positions of the rectangles within plots were identical for all plots. The harvested biomass was sorted into categories: individual species for the sown plant species, weed plant species (species not sown at the particular plot), detached dead plant material (i.e., dead plant material in the data file), and remaining plant material that could not be assigned to any category (i.e., unidentified plant material in the data file). All biomass was dried to constant weight (70°C, >= 48 h) and weighed. Sown plant community biomass was calculated as the sum of the biomass of the individual sown species. The data for individual samples and the mean over samples for the biomass measures on the community level are given. Overall, analyses of the community biomass data have identified species richness as well as functional group composition as important drivers of a positive biodiversity-productivity relationship.

Collection of data on plant height along the plant diversity gradient in the Jena Experiment (Main Experiment, time series since 2002)

This data set contains a time series of plant height measurements (vegetative and reproductive) from the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In addition, data on species specific plant heights for the main experiment are available from 2002. In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. 1. Plant height was recorded, generally, twice a year just before biomass harvest (during peak standing biomass in late May and in late August). Methodologies of measuring height have varied somewhat over the years. In earlier year the streched plant height was measured, while in later years the standing height without streching the plant was measured. Vegetative height was measured either as the height of the highest leaf or as the length of the main axis of non-flowering plants. Regenerating height was measured either as the height of the highest flower on a plant or as the height of the main axis of flowering. Sampled plants were either randomly selected in the core area of plots or along transects in defined distances. For details refer to the description of individual years. Starting in 2006, also the plots of the management experiment, that altered mowing frequency and fertilized subplots (see further details in the general description of the Jena Experiment) were sampled. 2. Species specific plant height was recorded two times in 2002: in late July (vegetative height) and just before biomass harvest during peak standing biomass in late August (vegetative and regenerative height). For each plot and each sown species in the species pool, 3 plant individuals (if present) from the central area of the plots were randomly selected and used to measure vegetative height (non-flowering indviduals) and regenerative height (flowering individuals) as stretched height. Provided are the means over the three measuremnts per plant species per plot.

Collection of data on soil carbon (particulate and dissolved) in the Jena Experiment (Main Experiment, time series since 2002)

This data set contains three time series of measurements of soil carbon (particular and dissolved) from the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. 1. Particulate soil carbon: Stratified soil sampling was performed every two years since before sowing in April 2002 and was repeated in April 2004, 2006 and 2008 to a depth of 30 cm segmented to a depth resolution of 5 cm giving six depth subsamples per core. Total carbon concentration was analyzed on ball-milled subsamples by an elemental analyzer at 1150°C. Inorganic carbon concentration was measured by elemental analysis at 1150°C after removal of organic carbon for 16 h at 450°C in a muffle furnace. Organic carbon concentration was calculated as the difference between both measurements of total and inorganic carbon. 2. Particulate soil carbon (high intensity sampling): In one block of the Jena Experiment soil samples were taken to a depth of 1 m (segmented to a depth resolution of 5 cm giving 20 depth subsamples per core) with three replicates per block ever 5 years starting before sowing in April 2002. Samples were processed as for the more frequent sampling. 3. Dissolved organic carbon: Suction plates installed on the field site in 10, 20, 30 and 60 cm depth were used to sample soil pore water. Cumulative soil solution was sampled biweekly and analyzed for dissolved organic carbon concentration by a high TOC elemental analyzer. Annual mean values of DOC are provided.

Soil carbon in the Jena Experiment (all blocks Main Experiment up to 30cm depth, year 2006)

This data set contains soil carbon measurements (Organic carbon, inorganic carbon, and total carbon; all measured in dried soil samples) from the main experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the main experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. Soil sampling and analysis: Stratified soil sampling was performed in April 2006 to a depth of 30 cm. Three samples per plot were taken using a split tube sampler with an inner diameter of 4.8 cm (Eijkelkamp Agrisearch Equipment, Giesbeek, the Netherlands). Sampling locations were less than 30 cm apart from sampling locations in 2002. Soil samples were segmented into 5 cm depth segments in the field (resulting in six depth layers) and made into composite samples per depth. Subsequently, samples were dried at 40°C. All soil samples were passed through a sieve with a mesh size of 2 mm. Because of much higher proportions of roots in the soil, samples in years after 2002 were further sieved to 1 mm according to common root removal methods. No additional mineral particles were removed by this procedure. Total carbon concentration was analyzed on ball-milled subsamples (time 4 min, frequency 30 s**-1) by an elemental analyzer at 1150°C (Elementaranalysator vario Max CN; Elementar Analysensysteme GmbH, Hanau, Germany). We measured inorganic carbon concentration by elemental analysis at 1150°C after removal of organic carbon for 16 h at 450°C in a muffle furnace. Organic carbon concentration was calculated as the difference between both measurements of total and inorganic carbon.

Plant height along the plant diversity gradient in the Jena Experiment (Main Experiment, year 2002)

This data set contains measurements of plant height: vegetative height (non-flowering indviduals) and regenerative height (flowering individuals) in 2002 from the Main Experiment plots of a large grassland biodiversity experiment (the Jena Experiment; see further details below). In the Main Experiment, 82 grassland plots of 20 x 20 m were established from a pool of 60 species belonging to four functional groups (grasses, legumes, tall and small herbs). In May 2002, varying numbers of plant species from this species pool were sown into the plots to create a gradient of plant species richness (1, 2, 4, 8, 16 and 60 species) and functional richness (1, 2, 3, 4 functional groups). Plots were maintained by bi-annual weeding and mowing. In 2002, plant height was recorded twice a year: in late June and just before biomass harvest during peak standing biomass in late August. For 3 target plant individuals (if present) per sown species from the central area of the plots, vegetative height (non-flowering indviduals) and regenerative height (flowering individuals) were measured as stretched height. Provided are the indivdiual measurements and the mean over the measured plants per plot (in June) and the mean over the measured plants per plot (in August).