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    As good as human experts in detecting plant roots in minirhizotron images but efficient and reproducible: the convolutional neural network “RootDetector”

    DatasetsImage acquisitionFor this study, we assembled three datasets: one for training of the RootDetector Convolutional Neural Network (Training-Set), one for a performance comparison between humans and RootDetector in segmenting roots in minirhizotron images (Comparison-Set), and one for the validation of the algorithm (Validation-Set). The Training-Set contained 129 images comprised of 17 randomly selected minirhizotron images sampled in a mesocosm experiment (see “Mesocosm sampling” Section), 47 randomly selected minirhizotron images sampled in a field study (see “Field sampling” Section) as well as the 65 minirhizotron images of soy roots published by Wang et al.15. The Comparison-Set contained 25 randomly selected minirhizotron images from the field-study which all were not part of the images included in the Training- and Validation-Sets. The Validation-Set contained 10 randomly selected minirhizotron images from the same field study, which had not been used in the Training-Set. All images were recorded with 2550 ✕ 2273 pixels at 300 dpi with a CI-600 In-Situ Root Imager (CID Bio-Science Inc., Camas, WA, USA) and stored as .tiff files to reduce compression loss. For all training and evaluation purposes we used raw, unprocessed output images from the CI-600.Mesocosm samplingThe mesocosm experiment was established in 2018 on the premises of the Institute for Botany and Landscape Ecology of the University of Greifswald (Fig. S1). It features 108 heavy duty plastic buckets of 100 l each, filled to two thirds of their height with moderately decomposed sedge fen peat. Each mesocosm contained one minirhizotron (inner diameter: 64 mm, outer diameter: 70 mm, length: 650 mm) installed at a 45°angle and capped in order to avoid penetration by light. The mesocosms were planted with varying compositions of plant species that typically occur in north-east German sedge fens (Carex rostrata, Carex acutiformis, Glyceria maxima, Equisetum fluviatile, Juncus inflexus, Mentha aquatica, Acorus calamus and Lycopus europaeus). The mesocosms were subjected to three different water table regimes: stable at soil surface level, stable at 20 cm below soil surface and fluctuating between the two levels every two weeks. The minirhizotrons were scanned weekly at two levels of soil depth (0–20 cm and 15–35 cm) between April 2019 and December 2021, resulting in roughly 9500 minirhizotron images of 216 × 196 mm. Manual quantification of root length would, based on own experience, take approximately three hours per image, resulting in approximately 28,500 h of manual processing for the complete dataset. Specimens planted were identified by author Dr. Blume-Werry, however no voucher specimen were deposited. All methods were carried out in accordance with relevant institutional, national, and international guidelines and legislation.Field samplingThe field study was established as part of the Wetscapes project in 201716. The study sites were located in Mecklenburg-Vorpommern, Germany, in three of the most common wetland types of the region: alder forest, percolation fen and coastal fen (Fig. S2). For each wetland type, a pair of drained versus rewetted study sites was established. A detailed description of the study sites and the experimental setup can be found in Jurasinski et al.16. At each site, 15 minirhizotrons (same diameter as above, length: 1500 mm) were installed at 45° angle along a central boardwalk. The minirhizotrons have been scanned biweekly since April 2018, then monthly since January 2019 at two to four levels of soil depth (0–20 cm, 20–40 cm, 40–60 cm and 60–80 cm), resulting in roughly 12,000 minirhizotron images of 216 × 196 cm, i.e. an estimated 36,000 h of manual processing for the complete dataset. Permission for the study was obtained from the all field owners. Figure 1Overview of the RootDetector system. The main component is a semantic segmentation network based on the U-Net architecture. The root length is estimated by skeletonizing the segmentation output and applying the formula introduced by Kimura et al.17. During training only, a weight map puts more emphasis on fine roots.Full size imageThe CNN RootDetectorImage annotationFor the generation of training data for the CNN, human analysts manually masked all root pixels in the 74 images of the Training-Set using GIMP 2.10.12. The resulting ground truth data are binary, black-and-white images in Portable Network Graphics (.png) format, where white pixels represent root structures and black pixels represent non-root objects and soil (Fig. 2b). All training data were checked and, if required, corrected by an expert (see “Selection of participants” for definition). The Validation-Set was created in the same way but exclusively by experts.Figure 2Example of segmentation and result of skeletonization. A 1000 by 1000 pixel input image (a), the manually annotated ground truth image (b), the RootDetector estimation image (c), the combined representation image (error map, d with green indicating true positives, red indicating false positive, blue indicating false negatives), the skeletonized RootDetector estimation image (e), and the skeletonized ground truth image (f).Full size imageArchitectureRootDetector’s core consists of a Deep Neural Network (DNN) based on the U-Net image segmentation architecture[27]nd is implemented in TensorFlow and Keras frameworks18. Although U-Net was originally developed for biomedical applications, it has since been successfully applied to other domains due to its generic design.RootDetector is built up of four down-sampling blocks, four up-sampling blocks and a final output block (Fig. 1). Every block contains two 3 × 3 convolutional layers, each followed by rectified linear units (ReLU). The last output layer instead utilizes Sigmoid activation. Starting from initial 64 feature channels, this number is doubled in every down-block and the resolution is halved via 2 × 2 max-pooling. Every up-block again doubles the resolution via bilinear interpolation and a 1 × 1 convolution which halves the number of channels. Importantly, after each up-sampling step, the feature map is concatenated with the corresponding feature map from the down-sampling path. This is crucial to preserve fine spatial details.Our modifications from the original architecture include BatchNormalization19 after each convolutional layer which significantly helps to speed up the training process and zero-padding instead of cropping as suggested by Ronneberger, Fischer, & Brox20 to preserve the original image size.In addition to the root segmentation network, we trained a second network to detect foreign objects, specifically the adhesive tape that is used as a light barrier on the aboveground part of the minirhizotrons. We used the same network architecture as above and trained in a supervised fashion with the binary cross-entropy loss. During inference, the result is thresholded (predefined threshold value: 0.5) and used without post-processing.TrainingWe pre-trained RootDetector on the COCO dataset21 to generate a starting point. Although the COCO dataset contains a wide variety of image types and classes not specifically related to minirhizotron images, Majurski et al.22 showed, that for small annotation counts, transfer-learning even from unrelated datasets may improve a CNNs performance by up to 20%. We fine-tuned for our dataset with the Adam optimizer23 for 15 epochs and trained on a total of 129 images from the Training-Set (17 mesocosm images, 47 field-experiment images, 65 soy root images). To enhance the dataset size and reduce over-fitting effects, we performed a series of augmentation operations as described by Shorten & Khoshgoftaar24. In many images, relatively coarse roots ( > 3 mm) occupied a major part of the positive (white) pixel space, which might have caused RootDetector to underestimate fine root details overall. Similarly, negative space (black pixels) between tightly packed, parallel roots was often very small and might have impacted the training process to a lesser extent when compared to large areas with few or no roots (Fig. 2). To mitigate both effects, we multiplied the result of the cross-entropy loss map with a weight map which emphasizes positive–negative transitions. This weight map is generated by applying the following formula to the annotated ground truth images:$$omega left( x right) = 1 – left( {tanh left( {2tilde{x} – 1} right)} right)^{2}$$
    (1)
    where ω(x) is the average pixel value of the annotated weight map in a 5 × 5 neighborhood around pixel x. Ronneberger, Fischer, & Brox20 implemented a similar weight map, however with stronger emphasis on space between objects. As this requires computation of distances between two comparatively large sets of points, we adapted and simplified their formula to be computable in a single 5 × 5 convolution.For the loss function we applied a combination of cross-entropy and Dice loss 25:$${mathcal{L}} = {mathcal{L}}_{CE} + lambda {mathcal{L}}_{Dice} = – frac{1}{N}sumnolimits_{i} {wleft( {x_{i} } right)y_{i} log left( {x_{i} } right) + lambda frac{{2sumnolimits_{i} {x_{i} y_{i} } }}{{sumnolimits_{i} {x_{i}^{2} sumnolimits_{i} {y_{i}^{2} } } }}}$$
    (2)

    where x are the predicted pixels, y the corresponding ground truth labels, N the number of pixels in an image and λ a balancing factor which we set to 0.01. This value was derived empirically. The Dice loss is applied per-image to counteract the usually high positive-to-negative pixel imbalance. Since this may produce overly confident outputs and restrict the application of weight maps, we used a relatively low value for λ.Output and post-processingRootDetector generates two types of output. The first type of output are greyscale .png files in which white pixels represent pixels associated with root structures and black pixels represent non-root structures and soil (Fig. 2c). The advantage of .png images is their lossless ad artifact-free compression at relatively small file sizes. RootDetector further skeletonizes the output images and reduces root-structures to single-pixel representations using the skeletonize function of scikit-image v. 0.17.1 (26; Fig. 2e,f). This helps to reduce the impact of large diameter roots or root-like structures such as rhizomes in subsequent analyses and is directly comparable to estimations of root length. The second type of output is a Comma-separated values (.csv) file, with numerical values indicating the number of identified root pixels, the number of root pixels after skeletonization, the number of orthogonal and diagonal connections between pixels after skeletonization and an estimation of the physical combined length of all roots for each processed image. The latter is a metric commonly used in root research as in many species, fine roots provide most vital functions such as nutrient and water transport3. Therefore, the combined length of all roots in a given space puts an emphasis on fine roots as they typically occupy a relatively smaller fraction of the area in a 2D image compared to often much thicker coarse roots. To derive physical length estimates from skeletonized images, RootDetector counts orthogonal- and diagonal connections between pixels of skeletonized images and employs the formula proposed by Kimura et al.17 (Eq. 3).$$L = left[ {N_{d}^{2} + left( {N_{d} + N_{o} /2} right)^{2} } right]^{{1/2}} + N_{o} /2$$
    (3)
    where Nd is the number of diagonally connected and No the number of orthogonally connected skeleton pixels. To compute Nd we convolve the skeletonized image with two 2 × 2 binary kernels, one for top-left-to-bottom-right connections and another for bottom-left-to-top-right connections and count the number of pixels with maximum response in the convolution result. Similarly, No is computed with a 1 × 2 and a 2 × 1 convolutional kernels.Performance comparisonSelection of participantsFor the performance comparison, we selected 10 human analysts and divided them into three groups of different expertise levels in plant physiology and with the usage of digital root measuring tools. The novice group consisted of 3 ecology students (2 bachelor’s, 1 master’s) who had taken or were taking courses in plant physiology but had no prior experience with minirhizotron images or digital root measuring tools. This group represents undergraduate students producing data for a Bachelor thesis or student assistants employed to process data. The advanced group consisted of 3 ecology students (1 bachelor’s, 2 master’s) who had already taken courses in plant physiology and had at least 100 h of experience with minirhizotron images and digital root measuring tools. The expert group consisted of 4 scientists (2 PhD, 2 PhD candidates) who had extensive experience in root science and at least 250 h of experience with digital root measuring tools. All methods were carried out in accordance with relevant institutional, national, and international guidelines and legislation and informed consent was obtained from all participants.Instruction and root tracingAll three groups were instructed by showing them a 60 min live demo of an expert tracing roots in minirhizotron images, during which commonly encountered challenges and pitfalls were thoroughly discussed. Additionally, all participants were provided with a previously generated, in-depth manual containing guidelines on the identification of root structures, the correct operation of the root tracing program and examples of often encountered challenges and suggested solutions. Before working on the Comparison-Set, all participants traced roots in one smaller-size sample image and received feedback from one expert.Image preparation and root tracingBecause the minirhizotron images acquired in the field covered a variety of different substrates, roots of different plant species, variance in image quality, and because tracing roots is very time consuming, we decided to maximize the number of images by tracing roots only in small sections, in order to cover the largest number of cases possible. To do this, we placed a box of 1000 × 1000 pixels (8.47 × 8.47 cm) at a random location in each of the images in the Comparison-Set and instructed participants to trace only roots within that box. Similarly, we provided RootDetector images where the parts of the image outside the rectangle were occluded. All groups used RootSnap! 1.3.2.25 (CID Bio-Science Inc., Camas, WA, USA;27), a vector based tool to manually trace roots in each of the 25 images in the comparison set. We decided on RootSnap! due to our previous good experience with the software and its’ relative ease of use. The combined length of all roots was then exported as a csv file for each person and image and compared to RootDetector’s output of the Kimura root length.ValidationWe tested the accuracy of RootDetector on a set of 10 image segments of 1000 by 1000 pixels cropped from random locations of the 10 images of the Validation-Set. These images were annotated by a human expert without knowledge of the estimations by the algorithm and were exempted from the training process. As commonly applied in binary classification, we use the F1 score as a metric to evaluate the performance RootDetector. F1 is calculated from precision (Eq. 4) and recall (Eq. 5) and represents their harmonic mean (Eq. 6). Ranging from 0 to 1, higher values indicate high classification (segmentation) performance. As one of the 10 image sections contained no roots and thus no F1 Score was calculable, it was excluded from the validation. We calculated the F1 score for each of the nine remaining image sections and averaged the values as a metric for overall segmentation performance.$$Precision;(P) = frac{{tp}}{{tp + fp}}$$
    (4)
    $$Recall;(R) = frac{{tp}}{{tp + fn}}$$
    (5)
    $$F1 = 2*frac{{P*R}}{{P + R}}$$
    (6)
    where P = precision, R = recall, tp = true positives; fp = false positives, fn = false negatives.Statistical analysisWe used R Version 4.1.2 (R Core Team, 2021) for all statistical analyses and R package ggplot2 Version 3.2.128 for visualizations. Pixel identification-performance comparisons were based on least-squares fit and the Pearson method. Root length estimation-performance comparisons between groups of human analysts (novice, advanced, expert) and RootDetector were based on the respective estimates of total root length plotted over the minirhizotron images in increasing order of total root length. Linear models were calculated using the lm function for each group of analysts. To determine significant differences between the groups and the algorithm, 95% CIs as well as 83% CIs were displayed and RootDetector root length outside the 95% CI were considered significantly different from the group estimate at α = 0.0529. The groups of human analysts were considered significantly different if their 83% CIs did not overlap, as the comparison of two 83% CIs approximates an alpha level of 5%30,31.This study is approved by Ethikkommission der Universitätsmedizin Greifswald, University of Greifswald, Germany. More

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    Marine protected areas, marine heatwaves, and the resilience of nearshore fish communities

    Lauchlan, S. S. & Nagelkerken, I. Species range shifts along multistressor mosaics in estuarine environments under future climate. Fish Fish. 21, 32–46 (2020).Article 

    Google Scholar 
    Gao, G., Zhao, X., Jiang, M. & Gao, L. Impacts of marine heatwaves on algal structure and carbon sequestration in conjunction with ocean warming and acidification. Front. Mar. Sci. 8, 758651 (2021).Article 

    Google Scholar 
    Asch, R. G. Climate change and decadal shifts in the phenology of larval fishes in the California Current ecosystem. Proc. Natl. Acad. Sci. 112, E4065–E4074 (2015).Article 
    ADS 
    CAS 

    Google Scholar 
    Lonhart, S. I., Jeppesen, R., Beas-Luna, R., Crooks, J. A. & Lorda, J. Shifts in the distribution and abundance of coastal marine species along the eastern Pacific Ocean during marine heatwaves from 2013 to 2018. Mar. Biodivers. Rec. 12, 13 (2019).Article 

    Google Scholar 
    Morley, J. W. et al. Projecting shifts in thermal habitat for 686 species on the North American continental shelf. PLoS ONE 13, e0196127 (2018).Article 

    Google Scholar 
    Vergés, A. et al. The tropicalization of temperate marine ecosystems: Climate-mediated changes in herbivory and community phase shifts. Proc. R. Soc. B 281, 20140846 (2014).Article 

    Google Scholar 
    Wernberg, T. et al. Climate-driven regime shift of a temperate marine ecosystem. Science 353, 169–172 (2016).Article 
    ADS 
    CAS 

    Google Scholar 
    Cheung, W. W. L. et al. Marine high temperature extremes amplify the impacts of climate change on fish and fisheries. Sci. Adv. https://doi.org/10.1126/sciadv.abh0895 (2021).Article 

    Google Scholar 
    Ling, S. D., Johnson, C. R., Frusher, S. D. & Ridgway, K. R. Overfishing reduces resilience of kelp beds to climate-driven catastrophic phase shift. Proc. Natl. Acad. Sci. 106, 22341–22345 (2009).Article 
    ADS 
    CAS 

    Google Scholar 
    Pessarrodona, A. et al. Tropicalization unlocks novel trophic pathways and enhances secondary productivity in temperate reefs. Funct. Ecol. 36, 659–673 (2022).Article 

    Google Scholar 
    Hobday, A. J. et al. A hierarchical approach to defining marine heatwaves. Prog. Oceanogr. 141, 227–238 (2016).Article 
    ADS 

    Google Scholar 
    Holbrook, N. J. et al. A global assessment of marine heatwaves and their drivers. Nat. Commun. 10, 2624 (2019).Article 
    ADS 

    Google Scholar 
    Smale, D. A. et al. Marine heatwaves threaten global biodiversity and the provision of ecosystem services. Nat. Clim. Chang. 9, 306–312 (2019).Article 
    ADS 

    Google Scholar 
    Cheung, W. W. L. & Frölicher, T. L. Marine heatwaves exacerbate climate change impacts for fisheries in the northeast Pacific. Sci. Rep. 10, 6678 (2020).Article 
    ADS 
    CAS 

    Google Scholar 
    Garrabou, J. et al. Marine heatwaves drive recurrent mass mortalities in the Mediterranean Sea. Glob. Change Biol. 28, 5708–5725 (2022).Article 
    CAS 

    Google Scholar 
    Wernberg, T. et al. An extreme climatic event alters marine ecosystem structure in a global biodiversity hotspot. Nat. Clim. Change 3, 78–82 (2013).Article 
    ADS 

    Google Scholar 
    Cure, K. et al. Distributional responses to marine heat waves: insights from length frequencies across the geographic range of the endemic reef fish Choerodon rubescens. Mar. Biol. 165, 1 (2018).Article 

    Google Scholar 
    Jacox, M. G., Tommasi, D., Alexander, M. A., Hervieux, G. & Stock, C. A. Predicting the evolution of the 2014–2016 California current system marine heatwave from an ensemble of coupled global climate forecasts. Front. Mar. Sci. https://doi.org/10.3389/fmars.2019.00497 (2019).Article 

    Google Scholar 
    Gentemann, C. L., Fewings, M. R. & García-Reyes, M. Satellite sea surface temperatures along the West Coast of the United States during the 2014–2016 northeast Pacific marine heat wave. Geophys. Res. Lett. 44, 312–319 (2017).Article 
    ADS 

    Google Scholar 
    Cavanaugh, K. C., Reed, D. C., Bell, T. W., Castorani, M. C. N. & Beas-Luna, R. Spatial variability in the resistance and resilience of giant kelp in southern and baja California to a multiyear heatwave. Front. Mar. Sci. https://doi.org/10.3389/fmars.2019.00413 (2019).Article 

    Google Scholar 
    Cavole, L. M. et al. Biological impacts of the 2013–2015 warm-water anomaly in the Northeast Pacific: Winners, losers, and the future. Oceanography 29, 273–285 (2016).Article 

    Google Scholar 
    Sen Gupta, A. et al. Drivers and impacts of the most extreme marine heatwave events. Sci. Rep. 10, 19359 (2020).Article 
    ADS 
    CAS 

    Google Scholar 
    Rykaczewski, R. R. & Checkley, D. M. Influence of ocean winds on the pelagic ecosystem in upwelling regions. Proc. Natl. Acad. Sci. 105, 1965–1970 (2008).Article 
    ADS 
    CAS 

    Google Scholar 
    Thompson, A. R. et al. Putting the Pacific marine heatwave into perspective: The response of larval fish off southern California to unprecedented warming in 2014–2016 relative to the previous 65 years. Glob. Change Biol. 28, 1766–1785 (2022).Article 
    CAS 

    Google Scholar 
    Suryan, R. M. et al. Ecosystem response persists after a prolonged marine heatwave. Sci. Rep. 11, 6235 (2021).Article 
    ADS 
    CAS 

    Google Scholar 
    Bates, A. E. et al. Resilience and signatures of tropicalization in protected reef fish communities. Nat. Clim. Change 4, 62–67 (2014).Article 
    ADS 

    Google Scholar 
    Behrens, M. & Lafferty, K. Effects of marine reserves and urchin disease on southern Californian rocky reef communities. Mar. Ecol. Prog. Ser. 279, 129–139 (2004).Article 
    ADS 

    Google Scholar 
    Bernhardt, J. R. & Leslie, H. M. Resilience to climate change in coastal marine ecosystems. Ann. Rev. Mar. Sci. 5, 371–392 (2013).Article 

    Google Scholar 
    Caselle, J. E., Davis, K. & Marks, L. M. Marine management affects the invasion success of a non-native species in a temperate reef system in California, USA. Ecol. Lett. 21, 43–53 (2018).Article 

    Google Scholar 
    Micheli, F. et al. Evidence that marine reserves enhance resilience to climatic impacts. PLoS ONE 7, e40832 (2012).Article 
    ADS 
    CAS 

    Google Scholar 
    Olds, A. D. et al. Marine reserves help coastal ecosystems cope with extreme weather. Glob. Change Biol. 20, 3050–3058 (2014).Article 
    ADS 

    Google Scholar 
    Freedman, R. M., Brown, J. A., Caldow, C. & Caselle, J. E. Marine protected areas do not prevent marine heatwave-induced fish community structure changes in a temperate transition zone. Sci. Rep. 10, 21081 (2020).Article 
    ADS 
    CAS 

    Google Scholar 
    Bates, A. E. et al. Climate resilience in marine protected areas and the ‘Protection Paradox’. Biol. Cons. 236, 305–314 (2019).Article 

    Google Scholar 
    Kirlin, J. et al. California’s Marine Life Protection Act Initiative: Supporting implementation of legislation establishing a statewide network of marine protected areas. Ocean Coast. Manag. 74, 3–13 (2013).Article 

    Google Scholar 
    Saarman, E. T. et al. An ecological framework for informing permitting decisions on scientific activities in protected areas. PLoS ONE 13, e0199126 (2018).Article 

    Google Scholar 
    Caselle, J. E., Rassweiler, A., Hamilton, S. L. & Warner, R. R. Recovery trajectories of kelp forest animals are rapid yet spatially variable across a network of temperate marine protected areas. Sci. Rep. 5, 14102 (2015).Article 
    ADS 
    CAS 

    Google Scholar 
    Hamilton, S. L., Caselle, J. E., Malone, D. P. & Carr, M. H. Incorporating biogeography into evaluations of the Channel Islands marine reserve network. PNAS 107, 18272–18277 (2010).Article 
    ADS 
    CAS 

    Google Scholar 
    Wendt, D. E. & Starr, R. M. Collaborative research: An effective way to collect data for stock assessments and evaluate marine protected areas in California. Mar. Coast. Fish. 1, 315–324 (2009).Article 

    Google Scholar 
    Côté, I. M. & Darling, E. S. Rethinking ecosystem resilience in the face of climate change. PLoS Biol. 8, e1000438 (2010).Article 

    Google Scholar 
    Holling, C. S. Resilience and stability of ecological systems. Annu. Rev. Ecol. Syst. 4, 1–23 (1973).Article 

    Google Scholar 
    Li, L. et al. Subregional differences in groundfish distributional responses to anomalous ocean bottom temperatures in the northeast Pacific. Glob. Change Biol. 25, 2560–2575 (2019).Article 
    ADS 

    Google Scholar 
    Dawson, M. N. Phylogeography in coastal marine animals: A solution from California?. J. Biogeogr. 28, 723–736 (2001).Article 

    Google Scholar 
    Horn, M. H., Allen, L. G. & Lea, R. N. Biogeography. In The Ecology of Marine Fishes: California and Adjacent Waters (ed. Allen, L.) 3–25 (University of California Press, 2006). https://doi.org/10.1525/california/9780520246539.003.0001.Chapter 

    Google Scholar 
    Horn, M. H. & Allen, L. G. A distributional analysis of California coastal marine fishes. J. Biogeogr. 5, 23–42 (1978).Article 

    Google Scholar 
    Garrabou, J. et al. Mass mortality in Northwestern Mediterranean rocky benthic communities: Effects of the 2003 heat wave. Glob. Change Biol. 15, 1090–1103 (2009).Article 
    ADS 

    Google Scholar 
    Smale, D. A. & Wernberg, T. Extreme climatic event drives range contraction of a habitat-forming species. Proc. R. Soc. B 280, 20122829 (2013).Article 

    Google Scholar 
    O’Leary, B. C. et al. Addressing criticisms of large-scale marine protected areas. Bioscience 68, 359–370 (2018).Article 

    Google Scholar 
    California Department of Fish and Wildlife. California Sheephead, Bodianus (formerly Semicossyphus) pulcher, Enhanced Status Report. (2021).Pinsky, M. L., Selden, R. L. & Kitchel, Z. J. Climate-driven shifts in marine species ranges: Scaling from organisms to communities. Ann. Rev. Mar. Sci. 12, 153–179 (2020).Article 

    Google Scholar 
    Francour, P., Mangialajo, L. & Pastor, J. Mediterranean marine protected areas and non-indigenous fish spreading. In Fish Invasions of the Mediterranean Sea: Change and Renewal (eds Golani, D. & Appelbaum-Golani, B.) 127–144 (Pensoft Publisher, 2010).
    Google Scholar 
    Couce, E., Ridgwell, A. & Hendy, E. J. Future habitat suitability for coral reef ecosystems under global warming and ocean acidification. Glob. Change Biol. 19, 3592–3606 (2013).Article 
    ADS 

    Google Scholar 
    Bennett, S., Wernberg, T., Harvey, E. S., Santana-Garcon, J. & Saunders, B. J. Tropical herbivores provide resilience to a climate-mediated phase shift on temperate reefs. Ecol. Lett. 18, 714–723 (2015).Article 

    Google Scholar 
    Trainer, V. L. et al. Pelagic harmful algal blooms and climate change: Lessons from nature’s experiments with extremes. Harmful Algae 91, 101591 (2020).Article 

    Google Scholar 
    Gliwicz, Z. M., Babkiewicz, E., Kumar, R., Kunjiappan, S. & Leniowski, K. Warming increases the number of apparent prey in reaction field volume of zooplanktivorous fish. Limnol. Oceanogr. 63, S30–S43 (2018).Article 
    ADS 

    Google Scholar 
    Nielsen, J. M. et al. Responses of ichthyoplankton assemblages to the recent marine heatwave and previous climate fluctuations in several Northeast Pacific marine ecosystems. Glob. Change Biol. 27, 506–520 (2021).Article 
    ADS 

    Google Scholar 
    du Pontavice, H., Gascuel, D., Reygondeau, G., Stock, C. & Cheung, W. W. L. Climate-induced decrease in biomass flow in marine food webs may severely affect predators and ecosystem production. Glob. Change Biol. 27, 2608–2622 (2021).Article 
    ADS 

    Google Scholar 
    Arimitsu, M. L. et al. Heatwave-induced synchrony within forage fish portfolio disrupts energy flow to top pelagic predators. Glob. Change Biol. 27, 1859–1878 (2021).Article 
    ADS 
    CAS 

    Google Scholar 
    Oken, K. L., Essington, T. E. & Fu, C. Variability and stability in predation landscapes: A cross-ecosystem comparison on the potential for predator control in temperate marine ecosystems. Fish Fish. 19, 489–501 (2018).Article 

    Google Scholar 
    Baum, J. K. & Worm, B. Cascading top-down effects of changing oceanic predator abundances. J. Anim. Ecol. 78, 699–714 (2009).Article 

    Google Scholar 
    Jacox, M. G. et al. Impacts of the 2015–2016 El Niño on the California current system: Early assessment and comparison to past events. Geophys. Res. Lett. 43, 7072–7080 (2016).Article 
    ADS 

    Google Scholar 
    Brodeur, R. D., Auth, T. D. & Phillips, A. J. Major shifts in pelagic micronekton and macrozooplankton community structure in an upwelling ecosystem related to an unprecedented marine heatwave. Front. Mar. Sci. https://doi.org/10.3389/fmars.2019.00212 (2019).Article 

    Google Scholar 
    Field, J. C. et al. Spatiotemporal patterns of variability in the abundance and distribution of winter-spawned pelagic juvenile rockfish in the California Current. PLoS ONE 16, e0251638 (2021).Article 
    CAS 

    Google Scholar 
    Schroeder, I. D. et al. Source water variability as a driver of rockfish recruitment in the California current ecosystem: Implications for climate change and fisheries management. Can. J. Fish. Aquat. Sci. 76, 950–960 (2019).Article 
    CAS 

    Google Scholar 
    Echeverria, T. W. Thirty-four species of California rockfishes: Maturity and seasonality of reproduction. Fish. Bull. 85, 229–250 (1987).
    Google Scholar 
    Miller, A. & Sydeman, W. Rockfish response to low-frequency ocean climate change as revealed by the diet of a marine bird over multiple time scales. Mar. Ecol. Prog. Ser. 281, 207–216 (2004).Article 
    ADS 

    Google Scholar 
    Johnson, K. F. et al. Status of lingcod (Ophiodon elongatus) along the southern U.S. west coast in 2021. 195 p. (2021).Winemiller, K. O. & Rose, K. A. Patterns of life-history diversification in North American fishes: Implications for population regulation. Can. J. Fish. Aquat. Sci. 49, 2196–2218 (1992).Article 

    Google Scholar 
    Stuart-Smith, R. D., Brown, C. J., Ceccarelli, D. M. & Edgar, G. J. Ecosystem restructuring along the great barrier reef following mass coral bleaching. Nature 560, 92–96 (2018).Article 
    ADS 
    CAS 

    Google Scholar 
    Starr, R. M. et al. Variation in responses of fishes across multiple reserves within a network of marine protected areas in temperate waters. PLoS ONE 10, e0118502 (2015).Article 

    Google Scholar 
    Ziegler, S. L. et al. External fishing effort regulates positive effects of no-take marine protected areas. Biol. Cons. 269, 109546 (2022).Article 

    Google Scholar 
    Jarvis, E. T. & Lowe, C. G. The effects of barotrauma on the catch-and-release survival of southern California nearshore and shelf rockfish (Scorpaenidae, Sebastes spp.). Can. J. Fish. Aquat. Sci. 65, 1286–1296 (2008).Article 

    Google Scholar 
    Brooks, R. et al. Nearshore Fishes Abundance and Distribution Data, California Collaborative Fisheries Research Program (CCFRP). (2022).García-Reyes, M. & Sydeman, W. J. California multivariate ocean climate indicator (MOCI) and marine ecosystem dynamics. Ecol. Ind. 72, 521–529 (2017).Article 

    Google Scholar 
    R Development Core Team. R: A language and environment for statistical computing. R Foundation for Statistical Computing. (2021).Oksanen, J. et al. vegan: Community Ecology Package. (2020).Pinheiro, J., Bates, D., DebRoy, S., Sarkar, D. & R Core Team. nlme: Linear and Nonlinear Mixed Effects Models. (2021). More

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    Response of cyanobacterial mats to ambient phosphate fluctuations: phosphorus cycling, polyphosphate accumulation and stoichiometric flexibility

    Our findings highlight the critical role of polyP in Sodalinema stali-formed cyanobacterial mats, as it was dynamically accumulated and recycled during acclimation to P fluctuations.Cellular response to progressive P starvationAnalogous to planktonic cyanobacteria, growth under low P availability could be sustained by recycling polyP, which acted as a primary P source (Fig. 2a) [16, 23, 24]. We further attribute the rapid reduction of easily dispensable cellular P-containing compounds to the substitution of cellular phospholipids with S- or N-containing membrane lipids to maintain growth at the onset of P stress (Fig. 2a) [15, 23]. However, the exhaustion of this easily dispensable P pool limited proliferation in Phase 2, and the metabolic strategy switched from a focus on growth towards maintenance (Fig. 5). The interpretation of prevailing cellular processes based on our results is graphically summarized and explained in detail below (Fig. 5).Fig. 5: Schematic interpretation of cellular phosphorus (P) cycling in a cyanobacterial mat, based on significant changes of the monitored parameters (arbitrary units).a At low P availability, initially contained polyphosphate (polyP) was recycled simultaneously with phosphate uptake to sustain growth at constant C:N:P ratios. Further proliferation at the onset of P stress in Phase 1 was sustained by mobilization of cellular P, e.g. phospholipids, which led to rapidly increasing C:N:P ratios. Severe P stress in Phase 2, indicated by increasing APase activity, prevented proliferation and photosynthesis, indicated by a loss of green chlorophyll pigments. PolyP accumulation by deficiency response occurs with severely increasing P stress, whereby globular DNA accumulation indicates the allocation of P contained in DNA into polyP. P re-addition to the P-stressed cells in Phase 3 triggered overplus uptake and narrow C:N:P ratios, transitioning to luxury uptake at higher C:N:P ratios following polyP recycling. b At high P availability, polyP in Phase 1 was accumulated by overplus uptake at narrow C:N:P ratios, transitioning to luxury uptake at higher C:N:P ratios during polyP recycling in Phase 2. P-deprivation in Phase 3 did not affect the cells, which we attributed to a sufficient amount of phosphate in the residual medium or within the biofilm matrix. Arrows indicate phosphorus transformation processes, whereby arrows pointing towards DNA represent cell growth. Yellow granules = polyP, blue granules = globular DNA spheres, P = phospholipids, S = substitute lipids.Full size imageSevere P stress in Phase 2 was indicated by the colour change from green towards yellow-green (Fig. S1) and increasing APase activity (Fig. 2a). The colour change suggested the loss of photosynthetic pigments [40], but we could not clarify whether this occurred through active cellular pigment reduction or degradation of available chlorophyll e.g., by oxidation. The increasing APase activity (Fig. 2a) suggested that Sodalinema stali is capable of hydrolysing organic P [14]. Even though APase expression did not trigger proliferation, it likely hydrolysed a potentially available organic P pool, as increasing DIC, NH4 and decreasing pH indicated progressive decay and remineralisation of organic matter (Fig. 1a). This suggests that in analogous oligotrophic environments with often fluctuating conditions, the strategy has to be maximizing the utilization of external P sources contained in organic and inorganic sediment particles that get trapped in the EPS [41]. The sediment can contain large amounts of organic P [42] and the fluctuating physico-chemical gradients in the EPS matrix due to high daytime pH and low oxygen conditions at night, facilitate P desorption from metal oxides, leading to higher dissolved phosphate concentrations within the mat, compared to the overlying water body [3]. However, alternating redox conditions at the SWI could also trigger polyP release from benthic microorganisms to the sediments, where it could act as a P source for the benthic food-chain, or ultimately trigger the formation of mineral P phases [32], to sustainably remove P from the aquatic cycle. Either way, we suggest that polyP-containing cyanobacterial mats critically impact P fluxes at the SWI.With persisting severe P stress and increasing APase activity in Phase 2, polyP accumulation as a deficiency response was observed (Fig. 2a), which has been reported from planktonic cyanobacteria of different habitats [24, 29, 23], as well as stream periphyton [28]. However, the reasons causing this deficiency response remain unresolved. In marine phytoplankton of the oligotrophic Sargasso Sea, Martin et al. [23] excluded that polyP-rich cells were in a perpetual overplus state with ‘undetectable’ pulses driving this state and suggested that polyP accumulation occurred as a cellular stress response. In other studies, reduced biosynthesis of P-rich rRNA coincided with deficiency responses [26, 28] and led to the suggestion that polyP accumulation at P concentrations below a certain threshold required for growth occurs because of P allocation changes away from growth and towards storage. Further, APase can hydrolytically cleave phosphate groups from nucleic acids and convert DNA-lipid-P to DNA-lipids, which were shown to self-assemble into globular lipid-based DNA micelles [43]. These preferentially anchor on cell membranes [44], and indeed, such DNA spheres were found to accumulate at the cell’s polar membranes in our experiments adjacent to polyP during deficiency response (Fig. 4a: Phase 2,c). Therefore, we suggest that intracellular P recovery by cleavage from P-rich DNA and reallocation to polyP, and potentially reduced rRNA synthesis [31], is also a strategy in benthic mats of Sodalinema stali as a response to severe P stress when P availability is too low to sustain growth. This supports the theory of a reallocation of resources away from growth towards flexibly available P and energy storage. Such direct intracellular P cycling could be beneficial to help retain P within the cyanobacterial population; while external P moieties such as dissolved organic P within the matrix can act as an additional P source, they are also likely to be subject to nutrient competition between cyanobacteria and other organisms inhabiting the matrix.Such effects of potential interactions in terms of nutrient competition or provision between cyanobacteria and mutualistic microorganisms contained within the same EPS matrix are difficult to assess and we cannot exclude some potential effects on our results. However, mutualistic microorganisms that are naturally contained in many cyanobacterial or algal cultures are often critical for metacommunity functioning and hence, working with axenic mat-forming strains may even further falsify any obtained results. Furthermore, microscopic analyses revealed that Sodalinema always dominated the biomass and hence, it is here considered reasonable to work with a non-axenic culture.Cellular response to a simulated P pulseIn P-deficient cells, the affinity of the P uptake system is typically increased to maximize P uptake for future pulses [13, 45]. The simulated P pulse to the P-stressed cells in Phase 3 led to a rapid increase of the cellular P content by 1260% relative to C within 3 days (Fig. 2a), whereby P was accumulated to a significant part as polyP, which is characteristic for overplus uptake [25]. Many different types of oligotrophic aquatic habitats experience only temporal P pulses, e.g., from redox changes at the benthic interface leading to P release from the sediment [32], storm run-off [28], upwelling [46], or excretions of aquatic animals [47]. The capability of microorganisms to immediately take up, store, and efficiently re-use this P by overplus uptake is hence of critical importance for a population to sustain a potential subsequent period of low P availability. Overplus uptake is typically accompanied by the overall slow growth of the population and cellular recovery from P starvation, including ultrastructural organization and recovery of the photosynthetic apparatus [48]. This took one week after re-feeding of P-starved Nostoc sp. PCC 7118 cells [48]—a timeframe very similar to the delayed onset of photosynthesis observed in our study, indicated by the elevated pH at day 9 (Fig. 1a). Regarding overplus-triggering mechanisms following P pulses, Solovochenko et al. [48] suggested that overplus uptake occurs due to a delayed down-regulation of high-affinity Pi transporters, which are active during P starvation, and emphasized the simultaneous advantage of osmotically inert polyP accumulation as a response to dramatically high phosphate concentrations in the cells. Even though APase levels declined following our experimental P re-addition, they were significantly elevated for at least 9 days (Fig. 2a). As our experimental design involved replacing the medium with APase-free, BG11 + medium after Phase 2, we assume that the APase detected in Phase 3 was actively produced, and we conclude that previously relevant, low-P response mechanisms are slowly disengaged with some sort of lag, even when ambient P is repleted. Following cellular recovery, Sodalinema now recycled stored polyP instead of further accumulating it during the transition from overplus-to luxury uptake, which was reflected in the increasing C:N:P molar ratios and decreasing polyP levels without significant additional phosphate uptake (Figs. 1a, 2a, 5).Qualitative observations on polyP distributionMost methods applied to analyse polyP in microorganisms are quantitative and do not contain information on its spatial distribution within a population. The here observed variable distribution of polyP between the cells during luxury uptake and deficiency response, as well as the retention of polyP in few individual filaments during polyP recycling in Phase 1 of the low P experiment (Fig. 4) suggests strategies of either slow growth with a retention of polyP, or of high growth with polyP recycling. This was also suggested for cells of a unicellular Synechocystis sp. PCC 6803 population during overplus uptake [47]. In contrast, polyP in our experiment was distributed homogeneously between all cyanobacterial cells during overplus uptake (Fig. 4a: Phase 3, Fig. 4b: Phase 1). Yet, we are unaware of any polyP distribution study in multicellular or mat-forming cyanobacteria and hence, further mechanisms of interactions, e.g., cell-to-cell communication [49, 50], might also contribute to purposeful differentiation of cells or filaments within a common matrix.In summary, our study shows that the mat-forming Sodalinema stali (1) is capable of luxury uptake, overplus uptake and deficiency response with a heterogenous polyP distribution during polyP recycling, luxury uptake and deficiency response, while (2) dynamically adjusting cellular P content to changing phosphate concentrations. (3) Proliferation is sustained under the expense of polyP, followed by P acquisition from other easily dispensable cellular P-containing compounds under the onset of P stress. (4) Further, biosynthetic allocation changes away from growth towards maintenance with relative polyP accumulation at the expense of P-rich DNA are conducted under severe P stress. Our findings demonstrate the extraordinary capabilities of mat-forming cyanobacteria to adapt their P acquisition strategies to strong P fluctuations. While lasting proliferation under P limitation requires the mobilization of additional P sources through regeneration of P from particulate matter, the transition to net P accumulation under excess ambient P is rapid and effective. Since current projections of climate and land use change include intensified pulses of P load to aquatic ecosystems [50], e.g., through external input from surplus of agriculture fertilizer, inefficient wastewater treatment plants, and internal loads via the mobilization of legacy P, these P ‘bioaccumulators’ could form an important component in P remediation by temporarily accumulating P within the mat, and synthesizing polyP that could ultimately stimulate the formation of mineral P phases to sustainably remove P from the aquatic cycle. More

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    Fine-resolution global maps of root biomass carbon colonized by arbuscular and ectomycorrhizal fungi

    To calculate total root biomass C colonized by AM and EcM fungi, we developed a workflow that combines multiple publicly available datasets to ultimately link fine root stocks to mycorrhizal colonization estimates (Fig. 1). These estimates were individually derived for 881 different spatial units that were constructed by combining 28 different ecoregions, 15 land cover types and six continents. In a given spatial unit, the relationship between the proportion of AM- and EcM-plants aboveground biomass and the proportion of AM- and EcM-associated root biomass depends on the prevalence of distinct growth forms. Therefore, to increase the accuracy of our estimates, calculations were made separately for woody and herbaceous vegetation and combined in the final step and subsequently mapped. Below we detail the specific methodologies we followed within the workflow and the main assumptions and uncertainties associated.Fig. 1Workflow used to create maps of mycorrhizal fine root biomass carbon. The workflow consists of two main steps: (1) Estimation of total fine root stock capable to form mycorrhizal associations with AM and EcM fungi and (2) estimation of the proportion of fine roots colonized by AM and EcM fungi.Full size imageDefinition of spatial unitsAs a basis for mapping mycorrhizal root abundances at a global scale, we defined spatial units based on a coarse division of Bailey’s ecoregions23 After removing regions of permanent ice and water bodies, we included 28 ecoregions defined according to differences in climatic regimes and elevation (deposited at Dryad-Table S1). A map of Bailey’s ecoregions was provided by the Oak Ridge National Laboratory Distributed Active Archive Center24 at 10 arcmin spatial resolution. Due to potential considerable differences in plant species identities, ecoregions that extended across multiple continents were split for each continent. The continent division was based upon the FAO Global Administrative Unit Layers (http://www.fao.org/geonetwork/srv/en/). Finally, each ecoregion-continent combination was further divided according to differences in land cover types using the 2015 Land Cover Initiative map developed by the European Space Agency at 300 m spatial resolution (https://www.esa-landcover-cci.org/). To ensure reliability, non-natural areas (croplands and urban areas), bare areas and water bodies were discarded (Table 1). In summary, a combination of 28 ecoregions, 15 land cover types and six continents were combined to define a total of 881 different spatial units (deposited at Dryad-Table S2). The use of ecoregion/land cover/continent combination provided a much greater resolution than using a traditional biome classification and allowed to account for human-driven transformations of vegetation, the latter based on the land cover data.Table 1 List of land cover categories within the ESA CCI Land Cover dataset, used to assemble maps of mycorrhizal root biomass.Full size tableMycorrhizal fine root stocksTotal root C stocksEstimation of the total root C stock in each of the spatial units was obtained from the harmonized belowground biomass C density maps of Spawn et al.20. These maps are based on continental-to-global scale remote sensing data of aboveground biomass C density and land cover-specific root-to-shoot relationships to generate matching belowground biomass C maps. This product is the best up-to-date estimation of live root stock available. For subsequent steps in our workflow, we distinguished woody and herbaceous belowground biomass C as provided by Spawn et al.20. As the tundra belowground biomass C map was provided without growth form distinction, it was assessed following a slightly different workflow (see Section 2.2.3 for more details). To match the resolution of other input maps in the workflow, all three belowground biomass C maps were scaled up from the original spatial resolution of 10-arc seconds (approximately 300 m at the equator) to 10 arc‐minutes resolution (approximately 18.5 km at the equator) using the mean location of the raster cells as aggregation criterion.As the root biomass C maps do not distinguish between fine and coarse roots and mycorrhizal fungi colonize only the fine fractions of the roots, we considered the fine root fraction to be 88,5% and 14,1% of the total root biomass for herbaceous and woody plants, respectively. These constants represent the mean value of coarse/fine root mass ratios of herbaceous and woody plants provided by the Fine-Root Ecology Database (FRED) (https://roots.ornl.gov/)25 (deposited at Dryad-Table S3). Due to the non-normality of coarse/fine root mass ratios, mean values were obtained from log-transformed data and then back-transformed for inclusion into the workflow.Finally, the belowground biomass C maps consider the whole root system, but mycorrhizal colonization occurs mainly in the upper 30 cm of the soil18. Therefore, we estimated the total fine root stocks in the upper 30 cm by applying the asymptotic equation of vertical root distribution developed by Gale & Grigal26:$$y=1-{beta }^{d}$$where y is the cumulative root fraction from the soil surface to depth d (cm), and β is the fitted coefficient of extension. β values of trees (β = 0.970), shrubs (β = 0.978) and herbs (β = 0.952) were obtained from Jackson et al.27. A mean value was then calculated for trees and shrubs to obtain a woody vegetation β value of 0.974. As a result, we estimated that 54.6% of the total live root of woody vegetation and 77.1% of herbaceous vegetation is stored in the upper 30 cm of the soil. In combination, this allowed deriving fine root C stocks in the upper 30 cm of woody and herbaceous vegetation.The proportion of root stocks colonized by AM and EcMThe proportion of root stock that forms associations with AM or EcM fungi was obtained from the global maps of aboveground biomass distribution of dominant mycorrhizal types published by Soudzilovskaia et al.14. These maps provide the relative abundance of EcM and AM plants based on information about the biomass of grass, shrub and tree vegetation at 10arcmin resolution. To match with belowground root woody plants biomass data, proportions of AM trees and shrubs underlying the maps of Soudzilovskaia et al.14 were summed up to obtain the proportion of AM woody vegetation. The same was done for EcM trees and shrubs.Our calculations are subjected to the main assumption that, within each growth form, the proportion of aboveground biomass associated with AM and EcM fungi reflects the proportional association of AM and EM fungi to belowground biomass. We tested whether root:shoot ratios were significantly different between AM and EcM woody plants (the number of EcM herbaceous plants is extremely small17). Genera were linked to growth form based on the TRY database (https://www.try-db.org/)19 and the mycorrhizal type association based on the FungalRoots database17. Subsequently, it was tested whether root:shoot ratios of genera from the TRY database (https://www.try-db.org/)19 were significantly different for AM vs EcM woody plants. No statistically significant differences (ANOVA-tests p-value = 0.595) were found (Fig. 2).Fig. 2Mean and standar error of root to shoot ratios of AM and EcM woody plant species.Full size imageEstimation of mycorrhizal fine root stocksWe calculated the total biomass C of fine roots that can potentially be colonized by AM or EcM fungi by multiplying the total woody and herbaceous fine root C biomass in the upper 30 cm of the soil by the proportion of AM and EcM of woody and herbaceous vegetation. In the case of tundra vegetation, fine root C stocks were multiplied by the relative abundance of AM and EcM vegetation without distinction of growth forms (for simplicity, this path was not included in Fig. 1, but can be seen in Fig. 3. As tundra vegetation consists mainly of herbs and small shrubs, the distinction between woody and herbaceous vegetation is not essential in this case.Fig. 3Workflow used to create mycorrhizal fine root biomass C maps specific for tundra areas.Full size imageFinally, we obtained the mean value of mycorrhiza growth form fine root C stocks in each of the defined spatial units. These resulted in six independent estimations: AM woody, AM herbaceous, EcM woody, EcM herbaceous, AM tundra and EcM tundra total fine root biomass C (Fig. 4).Fig. 4Fine root biomass stocks capable to form association with AM (a) and EcM (b) fungi for woody, herbaceous and tundra vegetation. Final AM and EcM stock result from the sum of the growth form individual maps. There were no records of fine root biomass of EcM herbaceous vegetation.Full size imageThe intensity of root colonization by mycorrhizal fungiColonization databaseThe FungalRoot database is the largest up-to-date compilation of intensity of root colonization data, providing 36303 species observations for 14870 plant species. Colonization data was filtered to remove occurrences from non-natural conditions (i.e., from plantations, nurseries, greenhouses, pots, etc.) and data collected outside growing seasons. Records without explicit information about habitat naturalness and growing season were maintained as colonization intensity is generally recorded in the growing season of natural habitats. When the intensity of colonization occurrences was expressed in categorical levels, they were converted to percentages following the transformation methods stated in the original publications. Finally, plant species were distinguished between woody and herbaceous species using the publicly available data from TRY (https://www.trydb.org/)19. As a result, 9905 AM colonization observations of 4494 species and 521 EcM colonization observations of 201 species were used for the final calculations (Fig. 5).Fig. 5Number of AM (a) and EcM (b) herbaceous and woody plant species and total observations obtained from FungalRoot database.Full size imageThe use of the mean of mycorrhizal colonization intensity per plant species is based on two main assumptions:

    1)

    The intensity of root colonization is a plant trait: It is known that the intensity of mycorrhizal infections of a given plant species varies under different climatic and soil conditions28,29, plant age30 and the identity of colonizing fungal species31. However, Soudzilovskaia et al.9 showed that under natural growth conditions the intraspecific variation of root mycorrhizal colonization is lower than interspecific variation, and is within the range of variations in other plant eco-physiological traits. Moreover, recent literature reported a positive correlation between root morphological traits and mycorrhizal colonization, with a strong phylogenetic signature of these correlations32,33. These findings provide support for the use of mycorrhizal root colonization of plants grown in natural conditions as a species-specific trait.

    2)

    The percentage of root length or root tips colonized can be translated to the percentage of biomass colonized: intensity of root colonization is generally expressed as the proportion of root length colonized by AM fungi or proportion of root tips colonized by EcM fungi (as EcM infection is restricted to fine root tips). Coupling this data with total root biomass C stocks requires assuming that the proportion of root length or proportion of root tips colonized is equivalent to the proportion of root biomass colonized. While for AM colonization this equivalence can be straightforward, EcM colonization can be more problematic as the number of root tips varies between tree species. However, given that root tips represent the terminal ends of a root network34, the proportion of root tips colonized by EcM fungi can be seen as a measurement of mycorrhizal infection of the root system and translated to biomass independently of the number of root tips of each individual. Yet, it is important to stress that estimations of fine root biomass colonized by AM and EcM as provided in this paper might not be directly comparable.

    sPlot databaseThe sPlotOpen database21 holds information about the relative abundance of vascular plant species in 95104 different vegetation plots spanning 114 countries. In addition, sPlotOpen provides three partially overlapping resampled subset of 50000 plots each that has been geographically and environmentally balanced to cover the highest plant species variability while avoiding rare communities. From these three available subsets, we selected the one that maximizes the number of spatial units that have at least one vegetation plot. We further checked if any empty spatial unit could be filled by including sPlot data from other resampling subsets.Plant species in the selected subset were classified as AM and EcM according to genus-based mycorrhizal types assignments, provided in the FungalRoot database17. Plant species that could not be assigned to any mycorrhizal type were excluded. Facultative AM species were not distinguished from obligated AM species, and all were considered AM species. The relative abundance of species with dual colonization was treated as 50% AM and 50% ECM. Plant species were further classified into woody and herbaceous species using the TRY database.Estimation of the intensity of mycorrhizal colonizationThe percentage of AM and EcM root biomass colonized per plant species was spatially upscaled by inferring the relative abundance of AM and EcM plant species in each plot. For each mycorrhizal-growth form and each vegetation plot, the relative abundance of plant species was determined to include only the plant species for which information on the intensity of root colonization was available. Then, a weighted mean intensity of colonization per mycorrhizal-growth form was calculated according to the relative abundance of the species featuring that mycorrhizal-growth form in the vegetation plot. Lastly, the final intensity of colonization per spatial unit was calculated by taking the mean value of colonization across all plots within that spatial unit. These calculations are based on 38127 vegetation plots that hold colonization information, spanning 384 spatial units.The use of vegetation plots as the main entity to estimate the relative abundance of AM and EcM plant species in each spatial unit assumes that the plant species occurrences and their relative abundances in the selected plots are representative of the total spatial unit. This is likely to be true for spatial units that are represented by a high number of plots. However, in those spatial units where the number of plots is low, certain vegetation types or plant species may be misrepresented. We addressed this issue in our uncertainty analysis. Details are provided in the Quality index maps section.Final calculation and maps assemblyThe fraction of total fine root C stocks that is colonized by AM and EcM fungi was estimated by multiplying fine root C stocks by the mean root colonization intensity in each spatial unit. This calculation was made separately for tundra, woody and herbaceous vegetation.To generate raster maps based on the resulting AM and EcM fine root biomass C data, we first created a 10 arcmin raster map of the spatial units. To do this, we overlaid the raster map of Bailey ecoregions (10 arcmin resolution)24, the raster of ESA CCI land cover data at 300 m resolution aggregated to 10 arcmin using a nearest neighbour approach (https://www.esa-landcover-cci.org/) and the FAO polygon map of continents (http://www.fao.org/geonetwork/srv/en/), rasterized at 10 arcmin. Finally, we assigned to each pixel the corresponding biomass of fine root colonized by mycorrhiza, considering the prevailing spatial unit. Those spatial units that remained empty due to lack of vegetation plots or colonization data were filled with the mean value of the ecoregion x continent combination.Quality index mapsAs our workflow comprises many different data sources and the extracted data acts in distinct hierarchical levels (i.e plant species, plots or spatial unit level), providing a unified uncertainty estimation for our maps is particularly challenging. Estimates of mycorrhizal fine root C stocks are related mainly to belowground biomass C density maps and mycorrhizal aboveground biomass maps, which have associated uncertainties maps provided by the original publications. In contrast, estimates of the intensity of root colonization in each spatial unit have been associated with three main sources of uncertainties:

    1)

    The number of observations in the FungalRoot database. The mean species-level intensity of mycorrhizal colonization in the vegetation plots has been associated with a number of independent observations of root colonization for each plant species. We calculated the mean number of observations of each plant species for each of the vegetation plots and, subsequently the mean number of observations (per plant species) from all vegetation plots in each spatial unit. These spatial unit averaged number of observations ranged from 1 to 14 in AM and from 1 to 26 in EcM. A higher number of observations would indicate that the intraspecific variation in the intensity of colonization is better captured and, therefore, the species-specific colonization estimates are more robust.

    2)

    The relative plant coverage that was associated with colonization data. From the selected vegetation plots, only a certain proportion of plant species could be associated with the intensity of colonization data in FungalRoot database. The relative abundance of the plant species with colonization data was summed up in each vegetation plot. Then, we calculated the average values for each spatial unit. Mean abundance values ranged from 0.3 to 100% in both AM and EcM spatial units. A high number indicates that the dominant plant species of the vegetation plots have colonization data associated and, consequently, the community-averaged intensity of colonization estimates are more robust.

    3)

    The number of vegetation plots in each spatial unit. Each of the spatial units differs in the number of plots used to calculate the mean intensity of colonization, ranging from 1 to 1583 and from 1 to 768 plots in AM and EcM estimations, respectively. A higher number of plots is associated with a better representation of the vegetation variability in the spatial units, although this will ultimately depend on plot size and intrinsic heterogeneity (i.e., a big but homogeneous spatial unit may need fewer vegetation plots for a good representation than a small but very heterogeneous spatial unit).

    We provide independent quality index maps of the spatial unit average of these three sources of uncertainty. These quality index maps can be used to locate areas where our estimates have higher or lower robustness. More

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    Multifunctionality of temperate alley-cropping agroforestry outperforms open cropland and grassland

    Foley, J. A. et al. Global consequences of land use. Science 309, 570–574 (2005).Article 
    CAS 

    Google Scholar 
    Rockström, J. et al. A safe operating space for humanity. Nature 461, 472–475 (2009).Article 

    Google Scholar 
    Geiger, F. et al. Persistent negative effects of pesticides on biodiversity and biological control potential on European farmland. Basic Appl. Ecol. 11, 97–105 (2010).Article 
    CAS 

    Google Scholar 
    Zhang, W., Ricketts, T. H., Kremen, C., Carney, K. & Swinton, S. M. Ecosystem services and dis-services to agriculture. Ecol. Econ. 64, 253–260 (2007).Article 

    Google Scholar 
    Tilman, D., Cassman, K. G., Matson, P. A., Naylor, R. & Polasky, S. Agricultural sustainability and intensive production practices. Nature 418, 671–677 (2002).Article 
    CAS 

    Google Scholar 
    Helming, K. et al. Managing soil functions for a sustainable bioeconomy-assessment framework and state of the art. Land Degrad. Dev. 29, 3112–3126 (2018).Article 

    Google Scholar 
    Rockström, J. et al. Sustainable intensification of agriculture for human prosperity and global sustainability. Ambio 46, 4–17 (2017).Article 

    Google Scholar 
    Lehmann, J., Bossio, D. A., Kögel-Knabner, I. & Rillig, M. C. The concept and future prospects of soil health. Nat. Rev. Earth Environ. 1, 544–553 (2020).Article 

    Google Scholar 
    Smith, J., Pearce, B. D. & Wolfe, M. S. Reconciling productivity with protection of the environment: Is temperate agroforestry the answer? Renew. Agric. Food Syst. 28, 80–92 (2013).Article 

    Google Scholar 
    European Commission. A Greener and Fairer CAP (EC, 2021).Grass, I. et al. Trade-offs between multifunctionality and profit in tropical smallholder landscapes. Nat. Commun. 11, 1186 (2020).Article 
    CAS 

    Google Scholar 
    Mayer, S. et al. Soil organic carbon sequestration in temperate agroforestry systems – a meta-analysis. Agric. Ecosyst. Environ. 323, 107689 (2022).Article 
    CAS 

    Google Scholar 
    Pardon, P. et al. Juglans regia (walnut) in temperate arable agroforestry systems: effects on soil characteristics, arthropod diversity and crop yield. Renew. Agric. Food Syst. 35, 533–549 (2020).Article 

    Google Scholar 
    Schmidt, M. et al. Nutrient saturation of crop monocultures and agroforestry indicated by nutrient response efficiency. Nutr. Cycl. Agroecosyst. 119, 69–82 (2021).Article 
    CAS 

    Google Scholar 
    Beule, L. & Karlovsky, P. Tree rows in temperate agroforestry croplands alter the composition of soil bacterial communities. PLoS ONE 16, e0246919 (2021).Article 
    CAS 

    Google Scholar 
    Palma, J. H. N. et al. Modeling environmental benefits of silvoarable agroforestry in Europe. Agric. Ecosyst. Environ. 119, 320–334 (2007).Article 

    Google Scholar 
    Kay, S. et al. Spatial similarities between European agroforestry systems and ecosystem services at the landscape scale. Agroforest Syst. 92, 1075–1089 (2018).Article 

    Google Scholar 
    Swieter, A., Langhof, M., Lamerre, J. & Greef, J. M. Long-term yields of oilseed rape and winter wheat in a short rotation alley cropping agroforestry system. Agroforest Syst. 93, 1853–1864 (2019).Article 

    Google Scholar 
    Ivezić, V., Yu, Y. & van der Werf, W. Crop yields in European agroforestry systems: a meta-analysis. Front. Sustain. Food Syst. 5, 606631 (2021).Article 

    Google Scholar 
    Cardinael, R. et al. High organic inputs explain shallow and deep SOC storage in a long-term agroforestry system – combining experimental and modeling approaches. Biogeosciences 15, 297–317 (2018).Article 
    CAS 

    Google Scholar 
    Smith, P. Carbon sequestration in croplands: the potential in Europe and the global context. Eur. J. Agron. 20, 229–236 (2004).Article 
    CAS 

    Google Scholar 
    Kay, S. et al. Agroforestry creates carbon sinks whilst enhancing the environment in agricultural landscapes in Europe. Land Use Policy 83, 581–593 (2019).Article 

    Google Scholar 
    Cardinael, R. et al. Impact of alley cropping agroforestry on stocks, forms and spatial distribution of soil organic carbon — a case study in a Mediterranean context. Geoderma 259–260, 288–299 (2015).Article 

    Google Scholar 
    Cardinael, R. et al. Spatial variation of earthworm communities and soil organic carbon in temperate agroforestry. Biol. Fertil. Soils 55, 171–183 (2019).Article 
    CAS 

    Google Scholar 
    Boinot, S. et al. Alley cropping agroforestry systems: reservoirs for weeds or refugia for plant diversity? Agric. Ecosyst. Environ. 284, 106584 (2019).Article 

    Google Scholar 
    Barnes, A. D. et al. Direct and cascading impacts of tropical land-use change on multi-trophic biodiversity. Nat. Ecol. Evol. 1, 1511–1519 (2017).Article 

    Google Scholar 
    Kehoe, L. et al. Biodiversity at risk under future cropland expansion and intensification. Nat. Ecol. Evol. 1, 1129–1135 (2017).Article 

    Google Scholar 
    DuPont, S. T., Culman, S. W., Ferris, H., Buckley, D. H. & Glover, J. D. No-tillage conversion of harvested perennial grassland to annual cropland reduces root biomass, decreases active carbon stocks, and impacts soil biota. Agric. Ecosyst. Environ. 137, 25–32 (2010).Article 
    CAS 

    Google Scholar 
    Bengtsson, J. et al. Grasslands-more important for ecosystem services than you might think. Ecosphere 10, e02582 (2019).Article 

    Google Scholar 
    Beule, L. et al. Conversion of monoculture cropland and open grassland to agroforestry alters the abundance of soil bacteria, fungi and soil-N-cycling genes. PLoS ONE 14, e0218779 (2019).Article 
    CAS 

    Google Scholar 
    Borrelli, P., Ballabio, C., Panagos, P. & Montanarella, L. Wind erosion susceptibility of European soils. Geoderma 232–234, 471–478 (2014).Article 

    Google Scholar 
    Amundson, R. et al. Soil and human security in the 21st century. Science 348, 12610711–12610716 (2015).Article 

    Google Scholar 
    Olson, K. R., Al-Kaisi, M., Lal, R. & Cihacek, L. Impact of soil erosion on soil organic carbon stocks. J. Soil Water Conserv. 71, 61A–67A (2016).Article 

    Google Scholar 
    Larney, F. J., Bullock, M. S., Janzen, H. H., Ellert, B. H. & Olson, E. C. S. Wind erosion effects on nutrient redistribution and soil productivity. J. Soil Water Conserv. 53, 133–140 (1998).
    Google Scholar 
    de Jong, E. & Kowalchuk, T. E. The effect of shelterbelts on erosion and soil properties. Soil Sci. 159, 337–345 (1995).Article 

    Google Scholar 
    Deutsch, M. & Otter, V. Nachhaltigkeit und förderung? Akzeptanzfaktoren im Entscheidungsprozess deutscher Landwirte zur Anlage von Agroforstsystemen. Berichte über Landwirtschaft – Zeitschrift für Agrarpolitik und Landwirtschaft Aktuelle Beiträge (2021).Tsonkova, P., Böhm, C., Quinkenstein, A. & Freese, D. Ecological benefits provided by alley cropping systems for production of woody biomass in the temperate region: a review. Agroforest Syst. 85, 133–152 (2012).Article 

    Google Scholar 
    Lehmann, J., Weigl, D., Droppelmann, K., Huwe, B. & Zech, W. Nutrient cycling in an agroforestry system with runoff irrigation in Northern Kenya. Agroforestry Syst. 43, 49–70 (1998).Article 

    Google Scholar 
    Shao, G. et al. Impacts of monoculture cropland to alley cropping agroforestry conversion on soil N2O emissions. GCB Bioenergy https://doi.org/10.1111/gcbb.13007 (2022).Isaac, M. E. & Borden, K. A. Nutrient acquisition strategies in agroforestry systems. Plant Soil 444, 1–19 (2019).Article 
    CAS 

    Google Scholar 
    Cannell, M. G. R., van Noordwijk, M. & Ong, C. K. The central agroforestry hypothesis: the trees must acquire resources that the crop would not otherwise acquire. Agroforestry Syst. 34, 27–31 (1996).Article 

    Google Scholar 
    Beule, L., Vaupel, A. & Moran-Rodas, V. E. Abundance, diversity, and function of soil microorganisms in temperate alley-cropping agroforestry systems: a review. Microorganisms 10, 616 (2022).Article 
    CAS 

    Google Scholar 
    Thevathasan, N. V. & Gordon, A. M. in New Vistas in Agroforestry, Vol. 1 (eds Nair, P. K. R., Rao, M. R. & Buck, L. E.) 257–268 (Springer Netherlands, 2004).Veldkamp, E. & Keller, M. Fertilizer-induced nitric oxide emissions from agricultural soils. Nutr. Cycling Agroecosyst. 48, 69–77 (1997).Article 
    CAS 

    Google Scholar 
    Luo, J., Beule, L., Shao, G., Veldkamp, E. & Corre, M. D. Reduced soil gross N2O emission driven by substrates rather than denitrification gene abundance in cropland agroforestry and monoculture. JGR Biogeosciences 127, e2021JG006629 (2022).Article 
    CAS 

    Google Scholar 
    Langenberg, J., Feldmann, M. & Theuvsen, L. Alley cropping agroforestry systems: using Monte-Carlo simulation for a risk analysis in comparison with arable farming systems. German J. Agric. Econ. 67, 95–112 (2018).
    Google Scholar 
    Otter, V. & Langenberg, J. Willingness to pay for environmental effects of agroforestry systems: a PLS-model of the contingent evaluation from German taxpayers’ perspective. Agroforest Syst. 94, 811–829 (2020).Article 

    Google Scholar 
    Zhang, X. et al. Quantification of global and national nitrogen budgets for crop production. Nat. Food 2, 529–540 (2021).Article 

    Google Scholar 
    Markwitz, C., Knohl, A. & Siebicke, L. Evapotranspiration over agroforestry sites in Germany. Biogeosciences 17, 5183–5208 (2020).Article 

    Google Scholar 
    Pardon, P. et al. Trees increase soil organic carbon and nutrient availability in temperate agroforestry systems. Agric. Ecosyst. Environ. 247, 98–111 (2017).Article 
    CAS 

    Google Scholar 
    European Commission. Commission regulation (EC) No 1120/2009 (EC, 2009).Piñeiro, V. et al. A scoping review on incentives for adoption of sustainable agricultural practices and their outcomes. Nat. Sustain. 3, 809–820 (2020).Article 

    Google Scholar 
    Kay, S. et al. Agroforestry is paying off – economic evaluation of ecosystem services in European landscapes with and without agroforestry systems. Ecosyst. Serv. 36, 100896 (2019).Article 

    Google Scholar 
    European Council. Council agrees its position on the next EU common agricultural policy. Press release. https://www.consilium.europa.eu/en/press/press-releases/2020/10/21/council-agrees-its-position-on-the-next-eu-common-agricultural-policy/ (2020).IUSS Working Group WRB. World Reference Base for Soil Resources 2014. International Soil Classification System for Naming Soils and Creating Legends for Soil Maps (FAO, 2014).Garland, G. et al. A closer look at the functions behind ecosystem multifunctionality: a review. J. Ecol. 109, 600–613 (2021).Article 

    Google Scholar 
    Naumann, C. & Bassler, R. Die Chemische Untersuchung von Futtermitteln 3. Auflage (Chemical Analysis of Feedstuff 3rd Edition) (VDLUFA-Verlag, 1976).Beule, L., Lehtsaar, E., Rathgeb, A. & Karlovsky, P. Crop diseases and mycotoxin accumulation in temperate agroforestry systems. Sustainability 11, 2925 (2019).Article 
    CAS 

    Google Scholar 
    Verwijst, T. & Telenius, B. Biomass estimation procedures in short rotation forestry. For. Ecol. Manag. 121, 137–146 (1999).Article 

    Google Scholar 
    Harris, D., Horwáth, W. R. & van Kessel, C. Acid fumigation of soils to remove carbonates prior to total organic carbon or carbon-13 isotopic analysis. Soil Sci. Soc. Am. J. 65, 1853–1856 (2001).Article 
    CAS 

    Google Scholar 
    Blake, G. & Hartge, K. in Methods of Soil Analysis: Part 1 – Physical and Mineralogical Methods 363–375 (Americal Society of Agronomy, Inc., 1995).Davidson, E. A., Hart, S. C., Shanks, C. A. & Firestone, M. K. Measuring gross nitrogen mineralization, and nitrification by 15N isotopic pool dilution in intact soil cores. J. Soil Sci. 42, 335–349 (1991).Article 
    CAS 

    Google Scholar 
    Tiessen, H. & Moir, J. O. in Soil Sampling and Methods of Analysis Ch. 25 (CRC Press, 1993).Beule, L. et al. Poplar rows in temperate agroforestry croplands promote bacteria, fungi, and denitrification genes in soils. Front. Microbiol. 10, 3108 (2020).Article 

    Google Scholar 
    Ando, S. et al. Detection of nifH sequences in sugarcane (Saccharum officinarum L.) and pineapple (Ananas comosus [L.] Merr.). Soil Sci. Plant Nutr. 51, 303–308 (2005).Article 
    CAS 

    Google Scholar 
    Singh, J., Singh, S. & Vig, A. P. Extraction of earthworm from soil by different sampling methods: a review. Environ. Dev. Sustain. 18, 1521–1539 (2016).Article 

    Google Scholar 
    Brookes, P. C., Landman, A., Pruden, G. & Jenkinson, D. S. Chloroform fumigation and the release of soil nitrogen: a rapid direct extraction method to measure microbial biomass nitrogen in soil. Soil Biol. Biochem. 17, 837–842 (1985).Article 
    CAS 

    Google Scholar 
    Shen, S. M., Pruden, G. & Jenkinson, D. S. Mineralization and immobilization of nitrogen in fumigated soil and the measurement of microbial biomass nitrogen. Soil Biol. Biochem. 16, 437–444 (1984).Article 
    CAS 

    Google Scholar 
    Marx, M.-C., Wood, M. & Jarvis, S. C. A microplate fluorimetric assay for the study of enzyme diversity in soils. Soil Biol. Biochem. 33, 1633–1640 (2001).Article 
    CAS 

    Google Scholar 
    Matson, A. L., Corre, M. D., Langs, K. & Veldkamp, E. Soil trace gas fluxes along orthogonal precipitation and soil fertility gradients in tropical lowland forests of Panama. Biogeosciences 14, 3509–3524 (2017).Article 
    CAS 

    Google Scholar 
    Wen, Y., Corre, M. D., Schrell, W. & Veldkamp, E. Gross N2O emission and gross N2O uptake in soils under temperate spruce and beech forests. Soil Biol. Biochem. 112, 228–236 (2017).Article 
    CAS 

    Google Scholar 
    McKenzie, N. J., Green, T. W. & Jacquier, D. W. in Soil Physical Measurement and Interpretation for Land Evaluation 150–162 (Csiro Publishing, 2002).Priesack, E. Expert-N model library documentation. https://expert-n.uni-hohenheim.de/en/documentation (2005).Formaglio, G., Veldkamp, E., Duan, X., Tjoa, A. & Corre, M. D. Herbicide weed control increases nutrient leaching compared to mechanical weeding in a large-scale oil palm plantation. Biogeosciences 17, 5243–5262 (2020).Article 
    CAS 

    Google Scholar 
    Kroetsch, D. & Wang, C. in Soil sampling and methods of analysis (eds Angers, D. A. & Larney, F. J.) 713–725 (CRC Press, 2008).Kurniawan, S. et al. Conversion of tropical forests to smallholder rubber and oil palm plantations impacts nutrient leaching losses and nutrient retention efficiency in highly weathered soils. Biogeosciences 15, 5131–5154 (2018).Article 
    CAS 

    Google Scholar 
    Markwitz, C. Micrometeorological Measurements and Numerical Simulations of Turbulence and Evapotranspiration over Agroforestry (University of Göttingen, 2021).Jarrah, M., Mayel, S., Tatarko, J., Funk, R. & Kuka, K. A review of wind erosion models: data requirements, processes, and validity. Catena 187, 104388 (2020).Article 

    Google Scholar 
    van Ramshorst, J. G. V. et al. Reducing wind erosion through agroforestry: a case study using large eddy simulations. Sustainability 14, 13372 (2022).Article 

    Google Scholar 
    Kanzler, M., Böhm, C., Mirck, J., Schmitt, D. & Veste, M. Microclimate effects on evaporation and winter wheat (Triticum aestivum L.) yield within a temperate agroforestry system. Agroforest Syst. 93, 1821–1841 (2019).Article 

    Google Scholar 
    Clough, Y. et al. Land-use choices follow profitability at the expense of ecological functions in Indonesian smallholder landscapes. Nat. Commun. 7, 13137 (2016).Article 
    CAS 

    Google Scholar  More

  • in

    Status does not predict stress among Hadza hunter-gatherer men

    Sapolsky, R. M. The influence of social hierarchy on primate health. Science 308, 648–652 (2005).Article 
    ADS 
    CAS 

    Google Scholar 
    Snyder-Mackler, N. et al. Social status alters immune regulation and response to infection in macaques. Science 354, 1041–1045 (2016).Article 
    ADS 
    CAS 

    Google Scholar 
    Levy, E. J. et al. Higher dominance rank is associated with lower glucocorticoids in wild female baboons: A rank metric comparison. Horm. Behav. 125, 104826 (2020).Article 
    CAS 

    Google Scholar 
    Sapolsky, R. M. Social status and health in humans and other animals. Annu. Rev. Anthropol. 33, 393–418 (2004).Article 

    Google Scholar 
    Goymann, W. & Wingfield, J. C. Allostatic load, social status and stress hormones: the costs of social status matter. Anim. Behav. 67, 591–602 (2004).Article 

    Google Scholar 
    Cavigelli, S. A. & Chaudhry, H. S. Social status, glucocorticoids, immune function, and health: Can animal studies help us understand human socioeconomic-status-related health disparities?. Horm. Behav. 62, 295–313 (2012).Article 
    CAS 

    Google Scholar 
    Meyer, J. S. & Hamel, A. F. Models of stress in nonhuman primates and their relevance for human psychopathology and endocrine dysfunction. ILAR J. 55, 347–360 (2014).Article 
    CAS 

    Google Scholar 
    Saltzman, W., Schultz-Darken, N. J., Scheffler, G., Wegner, F. H. & Abbott, D. H. Social and reproductive influences on plasma cortisol in female marmoset monkeys. Physiol. Behav. 56, 801–810 (1994).Article 
    CAS 

    Google Scholar 
    Abbott, D. H. et al. Are subordinates always stressed? A comparative analysis of rank differences in cortisol levels among primates. Horm. Behav. 43, 67–82 (2003).Article 
    CAS 

    Google Scholar 
    Sadoughi, B., Lacroix, L., Berbesque, C., Meunier, H. & Lehmann, J. Effects of social tolerance on stress: Hair cortisol concentrations in the tolerant Tonkean macaques (Macaca tonkeana) and the despotic long-tailed macaques (Macaca fascicularis). Stress 1, 1–9 (2021).
    Google Scholar 
    Kawachi, I. & Berkman, L. Social cohesion, social capital, and health. Social Epidemiol. 174, 290–314 (2000).
    Google Scholar 
    Dong, M. et al. Insights into causal pathways for ischemic heart disease: adverse childhood experiences study. Circulation 110, 1761–1766 (2004).Article 

    Google Scholar 
    Galobardes, B., Lynch, J. W. & Davey Smith, G. Childhood socioeconomic circumstances and cause-specific mortality in adulthood: Systematic review and interpretation. Epidemiol. Rev. 26, 7–21 (2004).Article 

    Google Scholar 
    Lockwood, K. G., John-Henderson, N. A. & Marsland, A. L. Early life socioeconomic status associates with interleukin-6 responses to acute laboratory stress in adulthood. Physiol. Behav. 188, 212–220 (2018).Article 
    CAS 

    Google Scholar 
    Taylor, S. E. Mechanisms linking early life stress to adult health outcomes. Proc. Natl. Acad. Sci. 107, 8507–8512 (2010).Article 
    ADS 
    CAS 

    Google Scholar 
    Uchino, B. N. Social Support and Physical Health: Understanding the Health Consequences of Relationships (Yale University Press, 2004).Book 

    Google Scholar 
    Holt-Lunstad, J. & Uchino, B. N. Social support and health. Health Behav. Theory Res. Pract. 1, 183–204 (2015).
    Google Scholar 
    Gurven, M., Allen-Arave, W., Hill, K. & Hurtado, A. M. Reservation food sharing among the Ache of Paraguay. Hum. Nat. 12, 273–297 (2001).Article 
    CAS 

    Google Scholar 
    Hill, K. & Hurtado, A. M. Ache Life History: The Ecology and Demography of a Foraging People (Routledge, 2017).Book 

    Google Scholar 
    Kraft, T. S., Venkataraman, V. V., Tacey, I., Dominy, N. J. & Endicott, K. M. Foraging performance, prosociality, and kin presence do not predict lifetime reproductive success in Batek hunter-gatherers. Hum. Nat. 30, 71–97 (2019).Article 

    Google Scholar 
    Venkataraman, V. V., Kraft, T. S., Dominy, N. J. & Endicott, K. M. Hunter-gatherer residential mobility and the marginal value of rainforest patches. Proc. Natl. Acad. Sci. 114, 3097–3102 (2017).Article 
    ADS 
    CAS 

    Google Scholar 
    Woodburn, J. Egalitarian societies. Man 1, 431–451 (1982).Article 

    Google Scholar 
    Marlowe, F. The Hadza: Hunter-Gatherers of Tanzania Vol. 3 (University of California Press, 2010).
    Google Scholar 
    Fedurek, P. et al. Status does not predict stress: Women in an egalitarian hunter–gatherer society. Evol. Hum. Sci. 2, 1–10 (2020).
    Google Scholar 
    Kornienko, O. & Santos, C. E. The effects of friendship network popularity on depressive symptoms during early adolescence: Moderation by fear of negative evaluation and gender. J. Youth Adolesc. 43, 541–553 (2014).Article 

    Google Scholar 
    Smelser, N. J. & Baltes, P. B. International Encyclopedia of the Social & Behavioral Sciences Vol. 11 (Elsevier, 2001).
    Google Scholar 
    Kim, D. A., Benjamin, E. J., Fowler, J. H. & Christakis, N. A. Social connectedness is associated with fibrinogen level in a human social network. Proc. R. Soc. B Biol. Sci. 283, 20160958 (2016).Article 

    Google Scholar 
    Kindermann, T. A. & Gest, S. D. Assessment of the peer group: Identifying naturally occurring social networks and capturing their effects. In Handbook of peer interactions, relationships, and groups, 100–117 (2009).Kornienko, O., Clemans, K. H., Out, D. & Granger, D. A. Friendship network position and salivary cortisol levels. Soc. Neurosci. 8, 385–396 (2013).Article 

    Google Scholar 
    La Greca, A. M. & Lopez, N. Social anxiety among adolescents: Linkages with peer relations and friendships. J. Abnorm. Child Psychol. 26, 83–94 (1998).Article 

    Google Scholar 
    Okamoto, J. et al. Social network status and depression among adolescents: An examination of social network influences and depressive symptoms in a Chinese sample. Res. Hum. Dev. 8, 67–88 (2011).Article 

    Google Scholar 
    Ulset, V. S. et al. Are unpopular children more likely to get sick? Longitudinal links between popularity and infectious diseases in early childhood. PLoS ONE 14, e0222222 (2019).Article 
    CAS 

    Google Scholar 
    Hawkes, K. Showing off: Tests of an hypothesis about men’s foraging goals. Ethol. Sociobiol. 12, 29–54 (1991).Article 

    Google Scholar 
    Smith, E. A. Why do good hunters have higher reproductive success?. Hum. Nat. 15, 343–364 (2004).Article 

    Google Scholar 
    Apicella, C. L., Feinberg, D. R. & Marlowe, F. W. Voice pitch predicts reproductive success in male hunter-gatherers. Biol. Lett. 3, 682–684 (2007).Article 
    CAS 

    Google Scholar 
    Apicella, C. L. Upper-body strength predicts hunting reputation and reproductive success in Hadza hunter–gatherers. Evol. Hum. Behav. 35, 508–518 (2014).Article 

    Google Scholar 
    Smith, K. M., Olkhov, Y. M., Puts, D. A. & Apicella, C. L. Hadza men with lower voice pitch have a better hunting reputation. Evol. Psychol. 15, 1474704917740466 (2017).Article 

    Google Scholar 
    MacDougall-Shackleton, S. A., Bonier, F., Romero, L. M. & Moore, I. T. Glucocorticoids and “stress” are not synonymous. Integr. Organ. Biol. 1, 017 (2019).
    Google Scholar 
    Ouellette, S. J. et al. Hair cortisol concentrations in higher-and lower-stress mother–daughter dyads: A pilot study of associations and moderators. Dev. Psychobiol. 57, 519–534 (2015).Article 
    CAS 

    Google Scholar 
    Stalder, T. et al. Stress-related and basic determinants of hair cortisol in humans: A meta-analysis. Psychoneuroendocrinology 77, 261–274 (2017).Article 
    CAS 

    Google Scholar 
    Heimbürge, S., Kanitz, E. & Otten, W. The use of hair cortisol for the assessment of stress in animals. Gen. Comp. Endocrinol. 270, 10–17 (2019).Article 

    Google Scholar 
    Fedurek, P. et al. Relationship between proximity and physiological stress levels in hunter-gatherers: The Hadza. Horm. Behav. 147, 105294 (2023).Article 

    Google Scholar 
    Bowers, K. et al. Maternal distress and hair cortisol in pregnancy among women with elevated adverse childhood experiences. Psychoneuroendocrinology 95, 145–148 (2018).Article 
    CAS 

    Google Scholar 
    Wells, S. et al. Associations of hair cortisol concentration with self-reported measures of stress and mental health-related factors in a pooled database of diverse community samples. Stress 17, 334–342 (2014).Article 
    CAS 

    Google Scholar 
    Faresjö, T. et al. Elevated levels of cortisol in hair precede acute myocardial infarction. Sci. Rep. 10, 1–8 (2020).Article 

    Google Scholar 
    Fuchs, A. et al. Link between children’s hair cortisol and psychopathology or quality of life moderated by childhood adversity risk. Psychoneuroendocrinology 90, 52–60 (2018).Article 
    CAS 

    Google Scholar 
    Staufenbiel, S. M., Penninx, B. W., Spijker, A. T., Elzinga, B. M. & van Rossum, E. F. Hair cortisol, stress exposure, and mental health in humans: A systematic review. Psychoneuroendocrinology 38, 1220–1235 (2013).Article 
    CAS 

    Google Scholar 
    Davison, B., Singh, G. R. & McFarlane, J. Hair cortisol and cortisone as markers of stress in Indigenous and non-Indigenous young adults. Stress 22, 210–220 (2019).Article 
    CAS 

    Google Scholar 
    Kim, E., Bolkan, C., Crespi, E. & Madigan, J. The relationship between hair cortisol, chronic stress, and well-being among older adults with dementia. Innov. Aging 3, S468 (2019).Article 

    Google Scholar 
    Woodburn, J. Egalitarian societies revisited. Proper. Equal. 1, 18–31 (2005).
    Google Scholar 
    Berbesque, J. C., Wood, B. M., Crittenden, A. N., Mabulla, A. & Marlowe, F. W. Eat first, share later: Hadza hunter–gatherer men consume more while foraging than in central places. Evol. Hum. Behav. 37, 281–286 (2016).Article 

    Google Scholar 
    Marlowe, F. W. & Berbesque, J. C. Tubers as fallback foods and their impact on Hadza hunter-gatherers. Am. J. Phys. Anthropol. 140, 751–758 (2009).Article 

    Google Scholar 
    Berbesque, J. C. & Marlowe, F. W. Sex differences in food preferences of Hadza hunter-gatherers. Evol. Psychol. 7, 147470490900700400 (2009).Article 

    Google Scholar 
    Hawkes, K., O’Connell, J. F. & Blurton Jones, N. G. Hunting income patterns among the Hadza: Big game, common goods, foraging goals and the evolution of the human diet. Philos. Trans. R. Soc. Lond. B 334, 243–251 (1991).Article 
    ADS 
    CAS 

    Google Scholar 
    Hawkes, K. Hunting and the evolution of egalitarian societies: Lessons from the Hadza. Hierarch. Action Cui Bono 27, 1–10 (2000).
    Google Scholar 
    Stibbard-Hawkes, D. N., Attenborough, R. D. & Marlowe, F. W. A noisy signal: To what extent are Hadza hunting reputations predictive of actual hunting skills?. Evol. Hum. Behav. 39, 639–651 (2018).Article 

    Google Scholar 
    Smith, K. M. & Apicella, C. Partner choice in human evolution: The role of character, hunting ability, and reciprocity in Hadza campmate selection. (2019).Smith, K. M. & Apicella, C. L. Hadza hunter-gatherers disagree on perceptions of moral character. Soc. Psychol. Pers. Sci. 11, 616–625 (2020).Article 

    Google Scholar 
    Gurven, M., Allen-Arave, W., Hill, K. & Hurtado, M. “It’s a wonderful life”: Signaling generosity among the Ache of Paraguay. Evol. Hum. Behav. 21, 263–282 (2000).Article 
    CAS 

    Google Scholar 
    Aktipis, A. et al. Cooperation in an uncertain world: For the Maasai of East Africa, need-based transfers outperform account-keeping in volatile environments. Hum. Ecol. 44, 353–364 (2016).Article 

    Google Scholar 
    Cronk, L. et al. Managing risk through cooperation: Need-based transfers and risk pooling among the societies of the Human Generosity Project. in Global Perspectives on Long Term Community Resource Management, 41–75 (Springer, 2019).Cronk, L. & Aktipis, A. Design principles for risk-pooling systems. Nat. Hum. Behav. 1, 1–9 (2021).
    Google Scholar 
    Jones, N. B. Demography and Evolutionary Ecology of Hadza Hunter-Gatherers Vol. 71 (Cambridge University Press, 2016).
    Google Scholar 
    Crittenden, A. N. et al. Oral health in transition: The Hadza foragers of Tanzania. PLoS ONE 12, e0172197 (2017).Article 

    Google Scholar 
    Bennett, F. J., Barnicot, N. A., Woodburn, J. C., Pereira, M. S. & Henderson, B. E. Studies on viral, bacterial, rickettsial and treponemal diseases in the Hadza of Tanzania and a note on injuries. Hum. Biol. 1, 243–272 (1973).
    Google Scholar 
    Ibar, C. et al. Evaluation of stress, burnout and hair cortisol levels in health workers at a University Hospital during COVID-19 pandemic. Psychoneuroendocrinology 128, 105213 (2021).Article 
    CAS 

    Google Scholar 
    Rajcani, J., Vytykacova, S., Solarikova, P. & Brezina, I. Stress and hair cortisol concentrations in nurses during the first wave of the COVID-19 pandemic. Psychoneuroendocrinology 129, 105245 (2021).Article 
    CAS 

    Google Scholar 
    Hill, K. R., Wood, B. M., Baggio, J., Hurtado, A. M. & Boyd, R. T. Hunter-gatherer inter-band interaction rates: Implications for cumulative culture. PLoS ONE 9, e102806 (2014).Article 
    ADS 

    Google Scholar 
    Bird, D. W., Bird, R. B., Codding, B. F. & Zeanah, D. W. Variability in the organization and size of hunter-gatherer groups: Foragers do not live in small-scale societies. J. Hum. Evol. 131, 96–108 (2019).Article 

    Google Scholar 
    Fedurek, P. et al. Social status does not predict in-camp integration among egalitarian hunter-gatherer men. Behav. Ecol. 33, 65–76 (2022).Article 

    Google Scholar 
    Ponzi, D., Muehlenbein, M. P., Geary, D. C. & Flinn, M. V. Cortisol, salivary alpha-amylase and children’s perceptions of their social networks. Soc. Neurosci. 11, 164–174 (2016).Article 

    Google Scholar 
    Marlowe, F. W. Mate preferences among Hadza hunter-gatherers. Hum. Nat. 15, 365–376 (2004).Article 

    Google Scholar 
    Von Rueden, C. R. & Jaeggi, A. V. Men’s status and reproductive success in 33 nonindustrial societies: Effects of subsistence, marriage system, and reproductive strategy. Proc. Natl. Acad. Sci. 113, 10824–10829 (2016).Article 

    Google Scholar 
    Townsend, C. Egalitarianism, Evolution Of (Wiley, 2018).Book 

    Google Scholar 
    Winterhalder, B. Diet choice, risk, and food sharing in a stochastic environment. J. Anthropol. Archaeol. 5, 369–392 (1986).Article 

    Google Scholar 
    Cornell, T. & Allen, T. B. War and Games Vol. 3 (Boydell Press, 2002).
    Google Scholar 
    Smáradóttir, S. Health and Wellbeing in the Arctic: The Critical Issues of Food Insecurity and Suicide Among Indigenous People.Finkler, H. W. Violence and the administration of justice: A focus on inuit communities in Northern Canada. BC Third World LJ 4, 137 (1983).
    Google Scholar 
    Bowles, S. Did warfare among ancestral hunter-gatherers affect the evolution of human social behaviors?. Science 324, 1293–1298 (2009).Article 
    ADS 
    CAS 

    Google Scholar 
    Fry, D. P. & Söderberg, P. Lethal aggression in mobile forager bands and implications for the origins of war. Science 341, 270–273 (2013).Article 
    ADS 
    CAS 

    Google Scholar 
    Gat, A. Proving communal warfare among hunter-gatherers: The quasi-rousseauan error. Evol. Anthropol. 24, 111–126 (2015).Article 

    Google Scholar 
    Kreyszig, E. Bernstein polynomials and numerical integration. Int. J. Numer. Meth. Eng. 14, 292–295 (1979).Article 
    MATH 

    Google Scholar 
    Meyer, D. et al. Misc functions of the department of statistics, probability theory group (formerly: E1071). Package e1071. TU Wien (2015).R Development Core. A Language ans Environment for Statistical Computing. (R Found Stat Comput Vienna, 2018).Wennig, R. Potential problems with the interpretation of hair analysis results. Forensic Sci. Int. 107, 5–12 (2000).Article 
    CAS 

    Google Scholar 
    Kumari, M., Shipley, M., Stafford, M. & Kivimaki, M. Association of diurnal patterns in salivary cortisol with all-cause and cardiovascular mortality: Findings from the Whitehall II study. J. Clin. Endocrinol. Metab. 96, 1478–1485 (2011).Article 
    CAS 

    Google Scholar 
    Marmot, M. G. & Sapolsky, R. Of baboons and men: Social circumstances, biology, and the social gradient in health. in Sociality, hierarchy, health: Comparative biodemography: Papers from a workshop (2014).Hoffman, M. C., Karban, L. V., Benitez, P., Goodteacher, A. & Laudenslager, M. L. Chemical processing and shampooing impact cortisol measured in human hair. Clin. Investig. Med. 37, E252 (2014).Article 
    CAS 

    Google Scholar 
    Sauvé, B., Koren, G., Walsh, G., Tokmakejian, S. & Van Uum, S. H. Measurement of cortisol in human hair as a biomarker of systemic exposure. Clin. Investig. Med. 30, E183–E191 (2007).Article 

    Google Scholar 
    Slominski, R., Rovnaghi, C. R. & Anand, K. J. Methodological considerations for hair cortisol measurements in children. Ther. Drug Monit. 37, 812 (2015).Article 
    CAS 

    Google Scholar 
    Xiang, L., Sunesara, I., Rehm, K. E. & Marshall, G. D. Jr. A modified and cost-effective method for hair cortisol analysis. Biomarkers 21, 200–203 (2016).Article 
    CAS 

    Google Scholar 
    Tukey, J. Exploratory Data Analysis (Addison-Wesley, 1977).MATH 

    Google Scholar 
    Mangiafico, S. & Mangiafico, M. S. Package ‘rcompanion’. Cran Repos 1–71 (2017).Kuznetsova, A., Brockhoff, P. B. & Christensen, R. H. lmerTest package: Tests in linear mixed effects models. J. Stat. Softw. 82, 1–26 (2017).Article 

    Google Scholar 
    Bates, D. M. lme4: Mixed-Effects Modeling with R. (2010).Lüdecke, D. ggeffects: Tidy data frames of marginal effects from regression models. J. Stat. Softw. 3(26), 772. https://doi.org/10.21105/joss.00772 (2018).Article 

    Google Scholar 
    Nowok, B., Raab, G. M. & Dibben, C. synthpop: Bespoke creation of synthetic data in R. J. Stat. Softw. 74, 1–26 (2016).Article 

    Google Scholar  More

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    COP15: escalating tourism threatens park conservation

    At December’s United Nations Convention on Biological Diversity summit (COP15), an insidious threat emerged to national parks — even as scientists argued for expanding protected areas. The World Travel & Tourism Council wants commercial tourism to be allowed to build developments in national parks globally, without obligation to help finance park conservation (see go.nature.com/3x2fsi9). This would undermine existing private tourism developments that do support conservation.
    Competing Interests
    The authors declare no competing interests. More

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    Scientists petition UCLA to reverse ecologist’s suspension

    The University of California, Los Angeles, suspended ecologist Priyanga Amarasekare without salary or benefits for one year, and will cut her salary by 20% for two more years.Credit: Al Seib/Los Angeles Times via Getty

    In April of last year, the Ecological Society of America awarded Priyanga Amarasekare one of the highest honours in the field of ecology: the Robert H. MacArthur Award. A little over two months later, the University of California, Los Angeles (UCLA), placed Amarasekare on a one-year suspension without pay or benefits, and forbid her from accessing her laboratory, maintaining her insect colonies, managing her grants or contacting students. Now scientists from around the world, who call Amarasekare a “highly distinguished ecologist”, “a committed teacher and outstanding mentor” and a “tireless advocate for under-represented groups”, are calling for her reinstatement.
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    The precise allegations that led to her suspension are unknown. UCLA has declined to release them, and barred Amarasekare from discussing the matter publicly. But long-standing tensions between Amarasekare and the university are no secret. A native of Sri Lanka and one of two women of colour who have tenure in the ecology and evolution department, she has previously accused the university of discrimination for repeatedly denying her promotions that were granted to colleagues. Former students and faculty members who are familiar with the situation think that Amarasekare’s suspension was retaliation for speaking out.Some 315 scientists raised concerns about her suspension in a petition that was delivered to the university on 23 January, arguing that Amarasekare “has long been denied significant advancement within her department, out of keeping with her contributions to the field”. Moreover, the sanctions levied against Amarasekare — including the one-year suspension and 20% salary reduction for an additional two years — represent “the kind of punishment normally applied only to the most egregious wrongdoings”, including scientific misconduct and sexual harassment violations, the petitioners write.In the absence of compelling evidence to the contrary, the scientists ask that UCLA rescind the disciplinary actions and fully compensate Amarasekare.Officials with UCLA say that the university “supports freedom of expression and does not condone retaliation of any sort”. They declined to discuss the accusations against or in support of Amarasekare, saying the university is “bound to respect the privacy of the numerous individuals involved in this matter”. Amarasekare also declined to comment.A confusing decisionColleagues told Nature that Amarasekare is the rare ecologist whose research spans the theoretical, computational and experimental realms. One project in her laboratory that touches on all of these areas focuses on the impact of climate change on insect communities. “She’s really several years ahead of everybody else,” says Andy Dobson, an ecologist at Princeton University in New Jersey who led the petition. Dobson has written letters to support Amarasekare’s various applications for promotion at UCLA and says he has been baffled by the university’s decisions. “She complained, and most of what’s happened seems to be a reaction against that,” he says.
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    Nature spoke to several former students and faculty members who defended Amarasekare in administrative hearings in September 2021. Although none knew the specific details of the charges against her, they all thought she had been targeted for speaking out against what she saw as discrimination within the department. In particular, they said Amarasekare vented about her own experience at UCLA on a departmental e-mail listserve created to discuss issues of racism and discrimination in the aftermath of the killing of George Floyd, whose death in May 2020 sparked national protests.“That’s why she got into trouble. She ended up criticizing pretty much the entire department — with good reason,” says Marcel Vaz, an ecologist at Wilkes University in Wilkes-Barre, Pennsylvania, who was a graduate student in the department at the time. He and other students came forward to support her. “We demanded some explanation,” Vaz says, “but we never got any feedback.”Peter Kareiva, a former UCLA faculty member who spoke on Amarasekare’s behalf during the administrative proceedings, calls her a brilliant scientist as well as a terrific teacher and student mentor. Kareiva witnessed Amarasekare raise uncomfortable issues and challenge internal policies in faculty meetings. He says she might have made mistakes in terms of “facilitating harmony” among fellow faculty members, but that her goal was always to improve the department.
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    “I am still incredulous by the punishment levied,” says Kareiva, who now serves as president of the Aquarium of the Pacific in Long Beach, California.It is unclear what happens next, but scientists and former students and faculty members contacted by Nature are concerned about the impact on Amarasekare’s current students, the disruption of federally funded research and the potentially irretrievable loss of time-sensitive experiments that could provide insights regarding the ecological impacts of climate change.As the recipient of the MacArthur award, Amarasekare is expected to discuss this research when she delivers her keynote address at the Ecological Society of America’s annual meeting in Portland, Oregon, in August. More