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Vegetation dynamics and carbon sequestration of Holocene alder (Alnus glutinosa) carrs of NE Germany
(2010)
Erlenwälder auf Moorstandorten werden oft als Zeichen von Moordegradation und Torfoxidation gewertet, aber erlenholzreiche Moorablagerungen (teilweise mehrere Meter tief) sind unter anderem in Nordostdeutschland weit verbreitet. Die Genese von Erlen-Holztorfen wurde bisher überwiegend durch das Konzept der „Verdrängungstorfbildung“ erklärt. Hierbei wird ein von gehölzfreier Vegetation akkumulierter Torf nach einer Grundwasserabsenkung durch nachträglich einwachsende Baumwurzeln verändert. Dieses Prinzip ist aber auf tiefgründige Erlen-Holztorfe nicht übertragbar, da Alnus glutinosa auf naturnahen Moorstandorten meist nur wenige Dezimeter tief wurzelt. Anliegen der vorliegenden Dissertation mit dem Titel „Vegetation dynamics and carbon sequestration of Holocene alder (Alnus glutinosa) carrs in NE Germany“ war die Identifizierung torfbildender Erlenwälder. Die torfbildende Vegetation, die Wasserstände während der Torfbildung und die Vegetationsdynamik dieser bewaldeten Niedermoore wurden durch Analysen von Makrofossilien, Pollen und sonstigen Mikrofossilien (u.a. Pilz-, Pflanzen-, und tierische Reste) rekonstruiert. Hierbei wurden in enger Kooperation mit dem Promotionsvorhaben von Frau Anja Prager (Non-pollen palynomorphs [NPPs] from modern alder carrs [NE Germany] - Tools for reconstructing past vegetation and site conditions) ca. 150 bisher unbekannte Mikrofossilien beschrieben und teilweise identifiziert. Die Datenauswertung wurde anhand von Fossilien-Diagrammen und statistischen Methoden (DCA, Clusteranalysis; Broken Stick Analysis) durchgeführt. Zur Altersbestimmung erfolgten 14C-AMS-Datierungen und der Kohlenstoffgehalt wurde über die Bestimmung der Trockenrohdichte ermittelt, wobei ein durchschnittlicher Kohlenstoffanteil von 56% angenommen wurde. Die untersuchten Erlen-Holztorfe wurden überwiegend direkt in Erlenwäldern abgelagert („Echter Bruchwaldtorf“); sind aber auch teilweise als Verdrängungstorfe aus vorherigen Seggentorfen entstanden oder in von Weiden dominierten Gehölzen gebildet worden. Die jährlichen Medianwasserstände der torfbildenden Erlenwälder lagen einerseits über Flur („sehr nass“-„very wet“) und zum anderen 0 bis 10 cm unter Flur („nass“ - „wet“). Die Vegetationszusammensetzung der sehr nassen Erlenwälder ähnelte teilweise dem Wasserfeder-Erlen-Wald und in einem Fall dem Zweizahn-Erlen-Bruchgehölz. Die nassen Erlenwälder konnten nicht auf der Ebene von Vegetationsformen rekonstruiert werden; charakteristisch war das häufige Auftreten von Urtica und eine Carex-dominierte Krautschicht. Über einen Vergleich der Mikrofossilien der Erlenholz-Tofe mit Mikrofossilien von Oberflächenproben aus rezenten Erlenwäldern konnten die Medianwasserstände nasser, torf-akkumulierender Erlenwälder auf 0-10 cm unter Flur festgelegt werden. Alle untersuchten Profile zeigten eine zyklische Bewaldung mit Zwischenphasen von Offenvegetation (meist Seggenriede). Als Bindeglieder zwischen Erlenwald und Seggenried traten teilweise Weidengebüsche auf, welche sich mitunter auch langfristiger etablieren konnten. Die zyklische Vegetationsentwicklung von Seggenrieden, Weidengebüschen und Erlenwäldern basierte fast ausschließlich auf einem schwankenden Wasserangebot im Moor. Dieses war fast immer die Folge von zyklischen Ent- und Wiederbewaldungen der umliegenden, grundwasserfernen Standorte durch den Menschen. Die „Echten Bruchwaldtorfe“ sind unter verschiedenen hydrologischen Bedingungen entstanden (Verlandungs-, Versumpfungs-, Überrieselungs- und Überflutungsmoor). Die Kohlenstoff-Akkumulationsraten („LORCA“-long-term apparent rate of carbon accumulation) liegen zwischen 31-44 g C m-2 yr-1 in sehr nassen und 50-81 g C m-2 yr-1 in nassen Erlenwäldern. Die höheren Akkumulationsraten in nassen Erlenwäldern können durch die deutlich steigende Produktivität von Erlen-Wäldern schon bei leicht sinkenden mittleren Wasserständen erklärt werden. Eine Verringerung der durchschnittlichen Wasserstände von über Flur zu leicht unter Flur führt annähernd zu einer Verdopplung der Primärproduktion von oberirdischem Holz und Wurzelholz. Dadurch gelangt auch ein größerer Anteil von Wurzelholz in den dauerhaft wassergesättigten Bereich. Da mit sinkenden Wasserständen auch die oxidative Zersetzung zunimmt, ist für die teilweise sehr hohen Torfakkumulationsraten in Erlenwäldern die Zersetzungsresistenz von Holz (Lignin) von zentraler Bedeutung. Die Akkumulationsraten nasser Erlenwälder übersteigen die borealer Waldmoore deutlich und erreichen die Größenordnung der Kohlenstoffakkumulation in den tropischen Waldmooren Süddostasiens. Die vorliegende Dissertation belegt die weitverbreitete und oft umfangreiche Torf- bzw. Kohlenstoffakkumulation in Holozänen Erlen-Wäldern Nordostdeutschlands.
To uncover the genetic structure of Populus euphratica forests along the Tarim River in Xinjiang, China, a PCR set of eight microsatellite markers was established. 18 primer pairs originally developed for P. tremuloides and P. trichocarpa were screened for amplification in P. euphratica. The eight most variable loci were selected for further genotyping experiments. Subsequently, two multiplex PCR assays, each containing four loci, were set up and optimized. Three populations containing altogether 436 trees were used to characterize the selected loci. The set was found to be moderately polymorphic (mean expected heterozygosity = 0.57). The resolution was sufficient to discriminate even siblings with high confidence (PID = 1.81x10-5). Cumulative exclusion probabilities were 0.89 (single parent), 0.98 (paternity), and 1.00 (parent pair) and proved the set’s suitability for parentage analysis. Practical and theoretical analysis of consequences of genotyping errors in this semi-clonal plant showed that the vast majority of errors (62.1%) lead to division of identical genotypes. Merging of different genotypes was found to be a very rare case (0.4%). This always leads to an overestimation of genotypes. A similarity threshold of one allele difference between two genotypes to be regarded as being identical lead to an underestimation of clonal richness and genotype number of one per cent compared to an overestimation of more than 20 per cent without such a threshold. Allowing a certain amount of variation is therefore expected to reflect the clonal structure better than an analysis that considers exact matches only. Using a combination of morphological and molecular analyses, a first study demonstrated that root suckers are clearly distinguished from seedlings in their root architecture. Root suckering starts when trees are 10–15 years old and bridges distances of up to 40 m at a time. Root suckers depend on their parent tree for at least five years and are expected to have a higher mortality than generatively grown trees. Molecular analysis of old growth stands revealed a highly variable proportion of clonal growth between different stands. In the study area, the proportion of clonality decreases with distance to the main river bed (R = 0.31 at the site closest to the main river, R = 0.97 at the site farthest away from the river). An analysis of the history of river movements at different sites indicates a dependency of clonal growth on the frequency of ground water replenishment by the yearly floods. Genetic differentiation among the stands in the study area is low (FST = 0.055), and isolation by distance was not detectable (P = 0.058). Also, the river does not function as a vector for directed gene flow in downstream direction (P > 0.11). The forests are therefore considered to be one large panmictic metapopulation with unrestricted gene flow. Clonal growth does not lead to higher final stand densities (P = 0.99) and is obviously not of crucial importance for stand survival. Furthermore, analysis of vitality measures and size differences indicate that root suckers are in disadvantage both in vitality and in survival rate compared to seedlings. In this light, a possible function of clonal growth as a luxury strategy to enhance a genetic individual’s reproduction success under good site conditions can be discussed. The genetic structure of the (meta)population bears direct implications for management and conversation of the Tugai forest in Xinjiang. Due to the low degree of differentiation and the unhindered gene flow even small, fragmented, or isolated populations have conservational value, thereby clearly answering the SLOSS question (a single large or several small protected areas) in the latter sense. More than that, non-clonal stands with the highest amount of genotypic diversity can be easily identified on satellite and aerial images. Selection of such stands for conservation is therefore possible without expensive and time-consuming molecular analyses.
Peatlands cover only about 3% of the terrestrial surface but are significant players in the global carbon (C) cycle and the climate system, since they store roughly one quarter of the global soil carbon (C) and are among the largest natural sources of methane (CH4). Since the resulting feedbacks on the climate system are uncertain, research efforts aim at identifying key processes and quantifying the C exchange from ecosystem to regional and global scales. To identify peatland ecosystem dynamics requires analysis of yet different scales. The key scale for their C dynamics is the microform scale, which is the smallest entity of the system. To estimate ecosystem dynamics, up-scaling from the microform scale is needed. Up-scaling demands (1) a correct estimation of the spatial heterogeneity and (2) the correct aggregation. In this thesis, the traditional spatial weighting of microform fluxes by the microform distribution is evaluated by (1) analyzing the flux calculation procedure, (2) investigating the effect of the resolution of the landcover maps on the up-scaling and by (3) cross-evaluating the up-scaling result with the directly measured ecosystem flux. Eventually, it is evaluated how these dynamics are considered in a mechanistic ecosystem model (LPJ-WHyMe). CH4 fluxes were measured on the microform scale with the closed chamber technique and on the ecosystem scale with the eddy covariance (EC) technique. The quantification of microform fluxes relies on the correct flux calculation. Since only few gas samples are taken during the closure period, traditionally the linear regression is applied when calculating CH4 fluxes from chamber measurements. Still, the chamber itself affects the diffusion gradient between peat and chamber atmosphere resulting in a theoretically non-linear concentration increase in the chamber. Using data with six data points per measurement from different microform types it is tested whether the linear or exponential regression fits the data better. In the majority of cases, the linear regression fits best. However, the exponential concentration change might still not be detectable resulting in an underestimation of the ’real‘ flux and the test of different techniqes to estimate the slope of a non-linear function with small sample amounts is recommended. To define the spatial heterogeneity of the peatland surface, the application of remote sensing techniques offer the advantage of supplying area-wide information with less uncertainty when compared to vegetation mapping along transects. However, the required resolution to resolve the microform distribution is <1m which in this study was derived from near-aerial photography. Besides for up-scaling, the resulting high-resolution landcover map was used in combination with a footprint model to analyze (1) the effect of landcover on the directly measured ecosystem flux and (2) its spatial representativeness. It was shown that fluctuations of the measured ecosystem flux over periods of several days could be explained by changes of the landcover composition in the source area of the EC measurements. The estimated budget was slightly biased towards the higher emissions from lawns which could be corrected. Still, the seasonal ecosystem CH4 budget was higher than the estimate derived from the up-scaling of microform fluxes. This is most likely due to an underestimation of microform fluxes by the chamber technique. Generally, the budget estimate derived from EC measurements was more accurate, i.e., characterized by less uncertainty than the up-scaled estimate. The developed approach depends on (1) identification and accurate measurements of all relevant microform types and (2) on spatial information which should be smaller than the footprint size of the EC measurements and available on the scale relevant for the studied process, i.e., the microform scale. The demonstrated effect of microform dynamics on the ecosystem flux highlights the importance of dealing with spatial heterogeneity of ecosystems in mechanistic modelling. For example, in LPJ-WHyMe, the ecosystem flux is simulated with mean input variables as water table level. To investigate its model performance, flux data from the rather homogeneous peatland margin and the more heterogeneous peatland centre were compared with the model output. At the homogeneous peatland margin, the ecosystem flux was clearly dominated (with a contribution of 91%) by one microform flux. In this case, one water table level as input variable could be used to estimate the ecosystem flux. However, for a heterogeneous site such as the peatland centre in this study, only one mean water table would simulate a mean microform flux but not the ecosystem flux. Consequently, it is recommended to incorporate at least one high-emitting and one low-emitting microform type in the model to increase the model performance.
This dissertation evaluates the effects of site conditions and livestock grazing on the vegetation of Azerbaijan’s winter pastures. We improved methods to estimate grazing intensity in vast rangelands and enhanced an approach to detect discontinuities in vegetation changes along environmental gradients. All analyses use field data from the semi-arid rangelands of Gobustan and Jeiranchel, at the foothills of the Greater Caucasus mountains. The data set comprises 313 vegetation relevés, each sized 100 m², based on a pre-stratification using topographical parameters. Additionally, we included data from farm transects and exclosure experiments. For each plot, selected site and soil variables were determined. VEGETATION AND SITE CONDITIONS: By means of cluster analysis, we derived 16 vegetation types with a total of 272 vascular plant species. Our vegetation classification, which is closely linked to site conditions, is an important groundwork for adapted rangeland management and monitoring. The study areas are dominated by semi-deserts with a high coverage of dwarf shrubs, and the mean number of vascular plant species was found to be about 28 per 100 m². According to ordination analysis (NMDS), species composition changes primarily along the altitudinal gradient, gradually proceeding from the Salsola nodulosa semi-deserts of the lowest parts (below 300 m a.s.l.) to the Salsola ericoides and Artemisia lerchiana semi-deserts of the upper regions (300–650 m a.s.l.). Soil salinity and carbonate concentration decrease as altitude increases. A second gradient reflects grazing intensity. One plant community that is typically found on intensively grazed sites in the vicinity of farmyards stands apart from the rest, which are subject to lower grazing and trampling pressures. A third factor that differentiates plant communities is the sand concentration of the soils. Additionally, communities that occur on steep slopes differ from communities that occur on level terrain. EXCLOSURE EXPERIMENTS: Exclosure experiments revealed that short-time abandonment of grazing leads to an increase in the number of annual species, in vegetation coverage, and in the heights of forbs and grasses. Clipping experiments indicated that the herbaceous species show hardly any compensatory growth in response to grazing. ESTIMATING GRAZING INTENSITY: A recurrent theoretical problem in rangeland research is the spatial modelling of grazing intensity around grazing hotspots like farms or watering places, the so called piospheres. In a widely used approach, grazing intensity is assumed to decrease in direct proportion to the distance from a hotspot. The resulting response patterns, which relate characteristics of the vegetation or site conditions to grazing intensity, are often nonlinear, and have been interpreted as indicating threshold changes or diff erent state-and-transitions along grazing gradients. However, we show that these ‘thresholds’ are usually geometrical artefacts. Taking into account the concentric structure of grazing hotspots, we suggest a new approach that approximates grazing intensity as the ratio of the total number of livestock kept at the farm to the distance between a given plot and the hotspot centre. Our approach is a simple yet significant improvement over current approaches because it enables us to merge or compare data from different sampling sites and because the approximation is in direct proportion to other grazing indicators like dung density or soil salinity. SPECIES TURNOVER PATTERNS: Combining our new grazing pressure model with species presence/absence data, we modelled vascular plant species responses, patterns of species richness and species turnover along grazing gradients on farm transects in Gobustan. The derived typical species response pattern along the finite grazing gradient is a sigmoid decrease. Species richness declines monotonically with increasing grazing intensity and thus conforms to generally acknowledged assumptions on the relationship between species richness and grazing pressure in semi-arid rangelands. Species turnover along the gradient was calculated using the slopes of species response curves. At first sight, the resulting pattern gives evidence for a discontinuous change. However, it ranges within the 95 % confidence interval of a null model based on assumptions of the individualistic continuum concept. Thus, species composition seems to change continuously along grazing gradients in Gobustan. This new null model approach can probably be adapted and applied to all ecological gradients and is useful for the validation of individualcontinuum or community concepts.
Carbon dioxide (CO2) is one of the most important factors of the Earth’s carbon cycle. Peatlands are well-known to be a long term sink for atmospheric carbon dioxide. Under changing environmental conditions, the carbon balance and hence the CO2 fluxes can be significantly changed, and peatlands may even become a significant atmospheric carbon source. To be able to predict the changes in climatic conditions and their effects on ecosystems, it is important to understand the contemporary CO2 exchange of the ecosystems. Many studies on peatland CO2 fluxes have been conducted in the boreal zone of North America and Scandinavia. Still little scientific evidence is available from peatland ecosystems of boreal Russia. This dissertation presents the detailed investigation of CO2 dynamics and the relevant processes and environmental factors from the boreal peatland site Ust-Pojeg (61°56'N, 50°13'E) in Komi Republic, northwest Russia. On the small spatial scale (microform), the investigated peatland was characterised by high variability in vegetation composition and coverage as well as in water table level which resulted in large variability in CO2 fluxes not only between the microform types but also within one microform type. The cumulative flux over the investigation period for the different microforms ranged from strong CO2 sources to CO2 sinks. An area-weighted estimate for the entire peatland showed that it was a CO2 source for the investigation period, which was characterised by average conditions in terms of precipitation and temperature. The CO2 fluxes were measured at different scales: by the closed chamber method at the microform scale and by the eddy covariance technique at the ecosystem scale. Three different upscaling methods were used to compare the fluxes. Irrespective of the upscaling methods, the discrepancies between the estimates based on the upscaled chamber measurements and estimates based on measurements by the eddy covariance technique were high. The high spatial heterogeneity of the vegetation and the water table level and thus of the CO2 fluxes were recognised as reasons for high potential errors when upscaling CO2 fluxes from the microform to the ecosystem level. Large discrepancies were also observed in comparison between measured CO2 fluxes and CO2 estimates based on the mechanistic ecosystem model LPJ-GUESS. Insufficient model forcing may have led to errors in the timing of the onset and the end of the growing season, and the modelled vegetation did not always reproduce the observed vegetation. These two factors may have led to the discrepancies in the model-measurement comparison. Although the closed chamber technique is widely used for measurements of CO2 fluxes between ecosystems and the atmosphere, the errors which might occur during the measurement itself or which are associated with the used measurement devices as well as the flux calculation from chamber-based CO2 concentration data are still under discussion. The study showed that the CO2 fluxes measured by the closed chamber method can be overestimated during low-turbulence nighttime conditions and can be seriously biased by inappropriate application of linear regression for the flux calculation. The methodological studies were conducted at the boreal peatland Salmisuo in eastern Finland (62°46'N, 30°58'E). The methods developed in this dissertation could contribute significantly to improved CO2 flux estimates. VI