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This dataset contains statistics of the sonnendach.ch dataset at the national level. See README.md for more information.

Abstract Secondary concentrators are used in solar concentrating systems to redirect solar beams reflected by the primary concentrators to the focal point or line. These components allow to increase the concentrated solar flux density and hence to lower thermal radiation losses. Solar reflectors for secondary concentrators are permanently exposed to environmental conditions, high radiation fluxes and elevated temperatures that potentially cause stress and degradation throughout the time. Therefore, analyzing solar reflectors of secondary concentrators by simulating these conditions is crucial. No previous research works about the durability of solar reflector materials for secondary concentrators have been reported. The present work is focused on studying the degradation of the reflector materials by simulating accelerated aging, caused by several ambient parameters and the effect of concentrated radiation. Both cooled and uncooled systems for secondary concentrators are included in this study. According to results obtained, aluminum reflectors and thin silvered-glass reflectors glued to an aluminum structure showed minimum reflectance losses and structural degradation under the operation conditions of cooled 3D secondary concentrators (tower systems). Following critical aspects to avoid reflector degradation were identified: to select a suitable adhesive material to glue the thin silvered-glass reflector to the support aluminum structure, to properly protect reflectors edges, to design a suitable cooling system and to avoid the combination of high radiation fluxes with mechanical stress. In addition, laminated silvered-glass reflectors have shown to be suitable for uncooled 2D secondary concentrators (Fresnel collectors). Furthermore, a comparison with naturally aged secondary concentrators using silvered-glass reflectors glued to an aluminum structure revealed that the simulated degradation under accelerated conditions performed in this work did reproduce the most frequent degradation patterns suffered in real operating conditions.

The Social-Ecological Systems (SES) framework serves as a valuable framework to explore and understand social and ecological interactions, and pathways in water governance. Yet, it lacks a robust understanding of change. We argue an analytical and methodological approach to engaging global changes in SES is critical to strengthening the scope and relevance of the SES framework. Relying on SES and resilience thinking, we propose an institutional and cognitive model of change that institutions and natural resources systems co-evolve to provide a dynamic understanding of SES that stands on three causal mechanisms: institutional complexity trap, rigidity trap, and learning processes. We illustrate how Data Cube technology could overcome current limitations and offer reliable avenues to test hypothesis about the dynamics of social-ecological systems and water security by offering to combine spatial and time data with no major technical requirements for users.

Laboratory corrosion and scaling testing of metallic materials exposed in high temperature and pressure environments generally involves complex, multi-instrument measurement setups. Here, we present a setup including an autoclave that is instrumented for in-situ electrochemical testing and that contains a ZrO2-based solid-state pH electrode and devices for temperature control and solution stirring. We show results highlighting the importance of adequate pre-calibration of the pH measurement, due to the hysteresis depending on temperature sweep. Additionally, we illustrate how interfacing the autoclave and the electrochemical cell to measuring and controlling instruments, using different data communication interfaces, can create ground loops. These ground loop interferences can introduce significant errors in the measurement, such as a potential shift of >100 mV. In complex, multi-instrument setups, a complete understanding of ground loops may often be difficult. Thus, we recommend systematic checks to identify the ground loops and we propose measures to avoid them. Measurement, 155 ISSN:0263-2241 ISSN:1873-412X

Abstract. Reliable quantification of the sources and sinks of greenhouse gases, together with trends and uncertainties, is essential to monitoring the progress in mitigating anthropogenic emissions under the Paris Agreement. This study provides a consolidated synthesis of CH4 and N2O emissions with consistently derived state-of-the-art bottom-up (BU) and top-down (TD) data sources for the European Union and UK (EU27+UK). We integrate recent emission inventory data, ecosystem process-based model results, and inverse modelling estimates over the period 1990–2018. BU and TD products are compared with European National GHG Inventories (NGHGI) reported to the UN climate convention secretariat UNFCCC in 2019. For uncertainties, we used for NGHGI the standard deviation obtained by varying parameters of inventory calculations, reported by the Member States following the IPCC guidelines recommendations. For atmospheric inversion models (TD) or other inventory datasets (BU), we defined uncertainties from the spread between different model estimates or model specific uncertainties when reported. In comparing NGHGI with other approaches, a key source of bias is the activities included, e.g. anthropogenic versus anthropogenic plus natural fluxes. In inversions, the separation between anthropogenic and natural emissions is sensitive to the geospatial prior distribution of emissions. Over the 2011–2015 period, which is the common denominator of data availability between all sources, the anthropogenic BU approaches are directly comparable, reporting mean emissions of 20.8 Tg CH4 yr−1 (EDGAR v5.0) and 19.0 Tg CH4 yr−1 (GAINS), consistent with the NGHGI estimates of 18.9 ± 1.7 Tg CH4 yr−1. TD total inversions estimates give higher emission estimates, as they also include natural emissions. Over the same period regional TD inversions with higher resolution atmospheric transport models give a mean emission of 28.8 Tg CH4 yr−1. Coarser resolution global TD inversions are consistent with regional TD inversions, for global inversions with GOSAT satellite data (23.3 Tg CH4yr−1) and surface network (24.4 Tg CH4 yr−1). The magnitude of natural peatland emissions from the JSBACH-HIMMELI model, natural rivers and lakes emissions and geological sources together account for the gap between NGHGI and inversions and account for 5.2 Tg CH4 yr−1. For N2O emissions, over the 2011–2015 period, both BU approaches (EDGAR v5.0 and GAINS) give a mean value of anthropogenic emissions of 0.8 and 0.9 Tg N2O yr−1 respectively, agreeing with the NGHGI data (0.9 ± 0.6 Tg N2O yr−1). Over the same period, the average of the three total TD global and regional inversions was 1.3 ± 0.4 and 1.3 ± 0.1 Tg N2O yr−1 respectively, compared to 0.9 Tg N2O yr−1 from the BU data. The TU and BU comparison method defined in this study can be operationalized for future yearly updates for the calculation of CH4 and N2O budgets both at EU+UK scale and at national scale. The referenced datasets related to figures are visualized at https://doi.org/10.5281/zenodo.4288969 (Petrescu et al., 2020).

Historic seeds were acquired for 32 species from stored collections in ex-situ seed banks at The Australian PlantBank and the Australian National Botanic Garden. This included four herbaceous species, ten shrubs, seven shrub-trees and eleven trees where all shrubs, shrub-trees and trees were evergreen species (See Everingham et al 2021, Ecology and Dryad dataset https://doi.org/10.5061/dryad.4f4qrfj83 for more information of seed collection). Matched modern seeds from the same species as the historic seeds were collected in the same location, at the same time of year as their historic counterparts. The amount of time between the historic and modern seed collections ranged from 29 years to 40 years. Seeds were germinated on water agar (0.7% w.v.) in controlled incubators. Most species were germinated at 20°C with a 12-hour light, 12-hour dark cycle, but some species required specific germination treatments such as gibberellic acid (GA3), smoke water (1%) or specific temperature and light treatments (see Everingham et al 2021, Ecology and Dryad dataset https://doi.org/10.5061/dryad.4f4qrfj83 for full germination treatment methods). Treatments were always kept constant for modern and historic seeds of each species. After germination, we transferred up to 50 germinated seeds to trays made up of 24-cells each measuring 4 cm (depth) by 2 cm2 (square area) cells. The seedlings grew for two weeks in the trays to ensure early seedling survival before being transferred to individual 1.9 L pots. Potting soil comprised of 33% Australian Native Landscape supply of “Organic Garden Mix”, 33% washed river sand and 33% Cocopeat as well as a general slow-release fertiliser added at 200 mL per 75 L of soil. Plants were grown in a glasshouse at UNSW, Sydney for six months with an overhead irrigation system. Pots were randomised each month to reduce position effects. After the six-month growing period, we measured a range of morphological leaf traits including leaf area, leaf roundness, leaf margin complexity and leaf thickness following standard protocols from Perez-Harguindeguy 2013, Australian Journal of Botany. To measure leaf shape, leaf area and leaf mass per unit area (LMA), we collected three fresh leaves (excluding the petiole) from each individual plant at the end of the six-month growing period. For two species (Acacia georgensis and Acacia concurrens), due to their seedling size, we were not able to measure area on three leaves and one to two leaves were sampled. Images of these fresh leaves were captured on a Flatbed Scanner and their area and shape metrics were calculated using values measured in image analysis software, ImageJ. Leaf surface area was calculated as the average of the three leaves’ total surface area. ImageJ provided a measurement for each leaf of the maximum length (longest axis of the smallest possible rectangle drawn around the leaf) and width (longest axis perpendicular to the determined maximum length). From these measurements we calculated leaf roundness as the average ratio of width to length of the three leaves whereby the leaves with roundness measurements closer to zero would be longer, thinner leaves and the leaves closer or equal to 1 would be rounder leaves. We calculated the margin complexity as the average of the ratio of perimeter length (cm) to surface area (cm2) from the perimeter of the leaf and the area analysed in ImageJ. To calculate leaf mass per unit area we used the leaf surface area calculations measured in ImageJ. The leaves were then dried to a constant temperature using a drying oven at 60° C for 72 hr. Oven dry mass (g) for the leaves was measured by weighing on a microbalance (Mettler Toledo© AG204 microbalance, 1 x 10-4 accuracy). LMA was calculated as oven-dry mass divided by fresh area. We measured leaf thickness by sampling one leaf from each individual modern and historic plant from all species (the third leaf from the growing tip, counted from the first fully developed/unfolded leaf). On these leaves we measured fresh leaf thickness (mm) at two points on adjacent sides of the mid-vein using a micrometer. An average for leaf thickness was taken from the two measurements for each individual plant. Finally, we calculated stomatal density using the clear nail polish peel method. Clear nail polish peels were performed on the first mature leaf closest to the growing apical tip from each plant. Clear nail polish was painted on the top and underside of the leaf on fresh tissue, away from the mid-vein or any prominent veins. We allowed the nail polish to dry for approximately 60 seconds before removing and mounting on a microscope slide with a coverslip. The peels were then imaged using a Leica© microscope. Stomata in each image were counted manually for the top of the leaf and the bottom of the leaf and the average stomatal density (stomata.cm-2) was calculated for each plant and use in further analysis. We measured physiological variables including leaf photosynthetic rate, intrinsic water use efficiency (iWUE) and leaf nitrogen content. To obtain photosynthetic measurements, we used portable infrared gas analysers (LICOR 6400XT, Lincoln, Nebraska) on well-watered, non-root-bound, non-flowering individuals. We randomly selected a subset of ten historic plants and ten modern plants from each species. Some species had fewer than ten plants available, and some species were excluded from photosynthetic measurements because their leaves were not large enough to fit into the gas chamber without damage to the majority of the seedling. We took infrared gas measurements on the youngest fully expanded mature leaf following standard protocols [66] between the hours of 10:00 to 14:00 (Australian Eastern Standard Time) on days with no visible cloud cover. We ensured that for each species, infrared gas exchange measurements were taken on historic and modern plants at random within a 30-minute period to minimise changes in light or temperature. Our measurements were made under constant saturating light conditions (1800 μmol m-2 s-1) provided from a constant light source in the LICOR chamber. The chamber CO2 concentration was set at 400ppm and the temperature set at 25° C. We took five consecutive measurements approximately two seconds apart and used the average of these five measurements. We recorded the light-saturated photosynthetic rate (Asat; μmol CO2 m-2 s-1) and the stomatal conductance (gs; mol H2O m-2 s-1), and then calculated the intrinsic water use efficiency (iWUE) as the ratio between photosynthetic rate and stomatal conductance. To quantify leaf nitrogen, we harvested leaves at six months, dried them for 72 hr at 60°C, pooled and homogenised each species’ individual modern leaves and individual historic leaves separately and then ground the dried leaf tissue. For each species we sent a pooled sample of historic ground leaf tissue and a pooled sample of modern ground leaf tissue to the Environmental Analysis Laboratory at Southern Cross University, Lismore, Australia for nitrogen analysis. Climate change metrics were determined for each species’ historic and modern seed collection based geographically on modern seed collection site location data (which was collected typically at the same location as the historic data or within a 1 km radius) and were obtained from the Australian Gridded Climate Data at 5 km2 resolution following methods from Everingham et al. 2021, Ecology. The processing code is freely available at https://github.com/SEveringham/ClimateData. The amount of change in all climate metrics was calculated across the five years before historic and modern seed collection to capture longer-term climate change responses of the species without extending to a period of climate that may become non-meaningful or overlap with modern climate data. The amount of change in precipitation metrics and heatwave duration were calculated using the log-transformed ratio of means. Change in all temperature metrics was calculated as the difference between the modern and historic climate metrics. We used different scaling methods because a difference of a few degrees Celsius of temperature has a much higher biological impact than a difference of a few millimetres of precipitation as precipitation has a much larger range of measurement than temperature. None of the climate change metrics were significantly correlated with one another (as all correlation coefficients were below 0.6) and therefore no climate metrics were excluded from our analyses. The climate change metrics we used included the change between the modern and historic seed collections in mean monthly temperature (calculated as the daily median temperature in the month prior to the seed collection and averaged across the previous five years before the seed collection was made) and mean monthly precipitation (an average of precipitation from the month prior to seed collection and then averaged across the 5 years prior to collection). Both the change in the range of temperature and the range of precipitation were calculated as the change (between historic to modern collections) in the difference between the yearly maximum and minimum temperature or precipitation averaged across the five years prior to each seed collection. We also used metrics for change in temperature variability and change in precipitation variability, both of which were calculated as the coefficient of variation (standard deviation divided by the mean) of the temperature or precipitation of the month prior to seed collection averaged across the five years prior. The change in maximum and minimum precipitation of the season before collection were calculated to determine the effects of seasonal rainfall and these were an average across five prior years of collection of the maximum rainfall in the 4 months prior to seed collection (bound by wet season in the subtropics or autumn, winter, spring, summer seasons in the mid-latitudes). We used the change in vapour pressure deficit (VPD) as an indication of the change in atmospheric aridity between the historic and modern seed collections. Finally, metrics of change in extreme climate events included the calculation of maximum heatwave duration (the longest heatwave across all seasons in the 5 years prior to collection whereby heatwaves were defined based on exceptionally high air temperature following the relative extreme heat index metric) and maximum dry spell duration (following the same protocol as maximum heatwave duration but instead with dry spells as calculated from an “extreme dryness index” using VPD measurements). All of the above raw data is available in the leaf measurement file and the climate variable file. We performed all data transformation analysis in R, version 3.6.0 with code freely available at https://github.com/SEveringham/leaf-trait-responses-to-climate-change. All transformed data is available in the full leaf analysis data file provided. Change in traits or gas exchange variables was calculated for all morphological, photosynthetic and leaf economic traits or variables using the log-transformed ratio of means per species using the escalc function in the metafor package. To determine if leaf economic spectra were related to changes in climate, we used a Principal Components Analysis (PCA) to obtain metrics that combined the change in inverse LMA, photosynthetic rate and nitrogen content. The inverse of LMA (specific leaf area [SLA]) was used as it is negatively related to leaf economy (i.e. leaves that have a larger surface area per unit mass will have a lower LMA and are typically on the ‘faster' end of the leaf economic spectrum). The PCA was achieved using the prcomp function in base R and used imputed data as not all species had measurements for all three variables (imputation was done using the imputePCA function in the missMDA package). Adaptation to changing conditions is one of the strategies plants use to survive climate change. Here, we ask whether plants’ leaf morphological and physiological traits/gas exchange variables have changed in response to recent, anthropogenic climate change. We grew seedlings from resurrected historic seeds from ex-situ seed banks and paired modern seeds in a common-garden experiment. Species pairs were collected from regions that had undergone differing levels of climate change using an emerging framework – Climate Contrast Resurrection Ecology, allowing us to hypothesise that regions with greater changes in climate (including temperature, precipitation, climate variability and climatic extremes) there would be greater trait responses in leaf morphology and physiology over time. Our found that in regions where there were greater changes in climate, there were greater changes in average leaf area, leaf margin complexity, leaf thickness and leaf intrinsic water use efficiency. Changes in leaf roundness, photosynthetic rate, stomatal density and the leaf economic strategy of our species were not correlated with changes in the climate. Our results show that leaves do have the ability to respond to changes in climate, however, there are greater inherited responses in morphological leaf traits than in physiological traits/variables, and greater responses to extreme measures of climate than gradual changes in climatic means. It is vital for accurate predictions of species’ responses to impending climate change to ensure that future climate change ecology studies utilise knowledge about the difference in both leaf trait and gas exchange responses, and the climate variables that they respond to. # Data from: Leaf morphological traits show greater responses to changes in climate than leaf physiological traits and gas exchange variables These are the data available for the study pertaining to the manuscript Leaf morphological traits show greater responses to changes in climate than leaf physiological traits and gas exchange variables by Everingham et al. The methods for data collection are available here on Dryad and also in the methods section of the manuscript. There are four datasets available: 1.Leaf_trait_measurement_data.xlsx: the raw data of all leaf trait measurements in the study 2.Climate_Data.xlsx: the raw data of all climate data used in the study 3.growthform.csv: the raw growth form data of each species in the study 4.LeafDataFullUsedinAnalyses.csv: transformed data from the raw data which is then used in all main analyses in the study All datasets have a tab for metadata ("Metadata") where each variable in each dataframe is explained in detail with units provided. Datasets 1,3 and 4 contain NA values - this NA indicates a value that was not measured on the given species due to survival constraints or measurements constraints. The code used to transform the raw data (datasets 1,2,3) to create data 4 are openly available at: [https://github.com/SEveringham/leaf-trait-responses-to-climate-change](https://github.com/SEveringham/leaf-trait-responses-to-climate-change) For more information contact the corresponding author/data collector Suz Everingham ([suz.everingham@gmail.com](mailto:suz.everingham@gmail.com)) Data files can be opened in microsoft excel or any program that can read xlsx files

The syntheses of 4,4′-bis(4-dimethylaminophenyl)-6,6′-dimethyl-2,2′-bipyridine (1), 4,4′-bis(4-dimethylaminophenylethynyl)-6,6′-dimethyl-2,2′-bipyridine (2), 4,4′-bis(4-diphenylaminophenyl)-6,6′-dimethyl-2,2′-bipyridine (3), and 4,4′-bis(4-diphenylaminophenylethynyl)-6,6′-dimethyl-2,2′-bipyridine (4) are reported along with the preparations and characterisations of their homoleptic copper(I) complexes [CuL2][PF6] (L = 1–4). The solution absorption spectra of the complexes exhibit ligand-centred absorptions in addition to absorptions in the visible region assigned to a combination of intra-ligand and metal-to-ligand charge-transfer. Heteroleptic [Cu(5)(Lancillary)]+ dyes in which 5 is the anchoring ligand ((6,6′-dimethyl-[2,2′-bipyridine]-4,4′-diyl)bis(4,1-phenylene))bis(phosphonic acid) and Lancillary = 1–4 have been assembled on fluorine-doped tin oxide (FTO)-TiO2 electrodes in dye-sensitized solar cells (DSCs). Performance parameters and external quantum efficiency (EQE) spectra of the DSCs (four fully-masked cells for each dye) reveal that the best performing dyes are [Cu(5)(1)]+ and [Cu(5)(3)]+. The alkynyl spacers are not beneficial, leading to a decrease in the short-circuit current density (JSC), confirmed by lower values of EQEmax. Addition of a co-absorbent (n-decylphosphonic acid) to [Cu(5)(1)]+ lead to no significant enhancement of performance for DSCs sensitized with [Cu(5)(1)]+. Electrochemical impedance spectroscopy (EIS) has been used to investigate the interfaces in DSCs; the analysis shows that more favourable electron injection into TiO2 is observed for sensitizers without the alkynyl spacer and confirms higher JSC values for [Cu(5)(1)]+.