More stories

  • in

    Plateaus, rebounds and the effects of individual behaviours in epidemics

    The Thau lagoon dataThe measurement campaign concerned four wastewater treatment plants (WWTP) in the Thau lagoon area in France, serving the cities of Sète, Pradel-Marseillan, Frontignan and Mèze. The measurements were obtained by using digital PCR20 (dPCR) to estimate the concentration of SARS-CoV-2 virus in samples taken weekly from 2020-05-12 to 2021-01-12. We provide further details about the measurement method in the “Methods” section.Figure 1Concentrations of SARS-CoV-2 (genome units per litre in logarithmic scale) from four WWTPs in Thau lagoon, measured weekly with dPCR technology from May 12th 2020 to January 12th, 2021. Note that there are some missing points.Full size imageFigure 1 shows the outcomes in a logarithmic scale over a nine months period. We summarise now their main features.

    1.

    An exponential phase starts simultaneously in Mèze and Frontignan WWTPs in early June.

    2.

    The genome units concentration curves in these two places reach, again simultaneously, a plateau. It has stayed essentially stable or slightly decreasing since then.

    3.

    The evolution at Sète and Pradel-Marseillan remarkably followed the previous two zones in a parallel way, with a two weeks lag. The measurements at Sète and Pradel-Marseillan continued to grow linearly (recall that this is in log scale, thus exponentially in linear scale), while the Mèze and Frontignan figures have stabilised ; then, after two weeks, they too stabilised at a plateau with roughly the same value as for the other two towns.

    4.

    The measurements seem to show a tendency to increase over the very last period.

    The epidemiological model with heterogeneity and natural variability of population behaviourThe appearance of such plateaus and shoulders need not be explained either by psychological reactions or by public health policy effects. Indeed, the regulations were roughly constant during the measurement campaign and awareness or fatigue effects do not seem to have altered the dynamics over this long period of time. Witness to this is the fact that two groups of towns saw the same evolution, but two weeks apart one from the other. To understand this phenomena we propose a new model.Given the complexity and multiplicity of behavioural factors favouring the spread of the epidemic, we assume that the transmission rate involves a normalised variable (a in (0,1)) that defines an aggregated indicator of risky behaviour within the susceptible population. Thus, we represent the heterogeneity of individual behaviours with this variable. We take a as an implicit parameter that we do not seek to calculate. The classical SIR model is macroscopic and the type of model we discuss here can be viewed as intermediate between macroscopic and microscopic.The initial distribution of susceptible individuals (S_0(a)) in the framework of a SIR-type compartmental description of the epidemic can be reasonably taken as a decreasing function of a. We take the infection transmission rate (a mapsto beta (a)) to be an increasing function of a. In the Supplementary Information (SI) Appendix, the reader will find a more general version of this model involving a probability kernel of transition from one state to another. The model here can be derived as a limiting case of that more general version.Likewise, the behaviour of individuals usually changes from one day to another21. Many factors are at work in this variability: social imitation, public health campaigns, opportunities, outings, the normal variations of activity (e.g. work from home certain days and use of public transportation and work in office on others) etc. Therefore, the second key feature of our model is variability of such behaviours: variations of the population density for a given a do not only come from individuals becoming infected and leaving that compartment but also results from individuals moving from one state a to another21. In the simplest version of the model, variability is introduced as a diffusion term in the dynamics of susceptible individuals.The modelWe denote by S(t, a) the density of individuals at time t associated with risk parameter a, by I(t) the total number of infected, and by R(t) the number of removed individuals. We are then led to the following system:$$begin{aligned} frac{{partial S(t,a)}}{{partial t}} & = d{mkern 1mu} frac{{partial ^{2} S(t,a)}}{{partial a^{2} }} – beta (a)S(t,a)frac{{I(t)}}{N} \ frac{{{text{d}}I(t)}}{{{text{d}}t}} & = frac{{I(t)}}{N}{mkern 1mu} intlimits_{0}^{1} beta (a)S(t,a);da – gamma I(t), \ frac{{{text{d}}R(t)}}{{{text{d}}t}} = & gamma I(t), \ end{aligned}$$
    (1)
    where (gamma) denotes the inverse of typical duration (in days) of the disease and d a positive diffusion coefficient. System (1) is supplemented with initial conditions$$begin{aligned} S(0,a) = S_0(a), quad I(0) = I_0, quad hbox {and} quad R(0) = 0, end{aligned}$$
    (2)
    and with zero flux condition in a at (a=0, 1). In the “Methods” section below, we discuss the relation of this model with other current works.A more general modelIn a more general version of our model, we can consider the population of infected as also structured by the parameter a. The equations are as before but now we keep track of the class a in the infected population. The mechanism here is that a susceptible individual from class a can be infected by infectious from any class I(t, b) but then gives rise to an individual I(t, a) of the same parent class. We also assume that there is a diffusion of the infected behaviours. We denote by ({mathfrak {B}}(a,b)) the transmission rate of S(t, a) by I(t, b). For simplicity and because it is natural, we will assume that it is of the form$$begin{aligned} {mathfrak {B}}(a,b)= beta (a) beta (b) end{aligned}$$where (beta) is as before. For full generality, we can also envision multi-dimensional parameters (ain {mathbb {R}}^d), with (a_iin (0,1)). We are then led to the system:$$begin{aligned} frac{{partial S(t,a)}}{{partial t}} & = d;Delta _{a} S(t,a) – S(t,a)frac{{beta (a)}}{N}intlimits_{0}^{1} beta (b)I(t,b);db \ frac{{partial I(t,a)}}{{partial t}} & = d^{prime}Delta _{a} I(t,a) + S(t,a)frac{{beta (a)}}{N}intlimits_{0}^{1} beta (b)I(t,b)db – gamma I(t,a), \ frac{{{text{d}}R(t)}}{{{text{d}}t}} & = gamma intlimits_{0}^{1} I (t,b){mkern 1mu} db, \ end{aligned}$$
    (3)
    In the SI we write further, more general, forms of this model, with ({mathfrak {B}}(a,b)) and more general diffusion of behaviours, that can include jumps or non-local variations. The type of models we discuss here may also shed light on the initial phase of the epidemic. We plan to investigate these questions in future work.Patterns generated by the modelIn the next section, we will discuss how the model fits the data observed in the Thau lagoon measurements. But before that, we start by showing that the above model (1) can generate the different patterns we mentioned. For this we rely on numerical simulations without fitting real data. And indeed we obtain plateaus, shoulders, and oscillations. The latter can be interpreted as epidemic rebounds.The key parameter here is the diffusion coefficient d, which controls the amplitude of behavioural variability (see Fig. 2). Large values of d rapidly yield homogenised behaviours, leading to classical SIR-like dynamics of infectious individuals. For very small values of d, the system also has a simple dynamics, in the sense that I(t) has a unique maximum, and therefore has no rebounds. We derive this in the limit (d=0) for which we show in the SI that there are neither plateaus nor rebounds.For some intermediate range of the parameter d, plateaus may appear after an exponential growth, like in the initial phase of the SIR model. A small amplitude oscillation, called “shoulder”, precedes a temporary stabilisation on a plateau, followed by a large time convergence to zero of infectious population. We also show that for small enough d, time oscillations of the infectious population curve, i.e. epidemic rebounds, may be generated by Model (1). Such oscillations also appear after a plateau, in a similar way to what one can see in observations.Simulations in Fig. 2 illustrate the various patterns obtained on the dynamics of infected population as a function of the diffusion parameter. For small enough d, in the top left graph of Fig. 2, one can see oscillations of the fraction of infectious individuals. These oscillations cannot be achieved in the classical SIR model. In fact, the two lower graphs of that figure, for somewhat larger values of d, exhibit the SIR model outcomes. Indeed, for sufficiently large d, the system becomes rapidly homogeneous (i.e. constant with respect to a). Yet, such oscillations are standard in the dynamics of actual epidemics, like the current Covid-19 pandemic. The intermediate value of d, represented in the upper right corner of Fig. 2 shows the typical onset of a plateau at a rather high value of I. Note that this plateau is preceded by a first small dip and then a characteristic “shoulder-like” oscillation.Figure 2Model behaviour depending on diffusion parameter values: infected rate dynamics in logarithmic scale. From left to right and then top to bottom, graphs are associated with (d=10^{-5}), (d=5times 10^{-5}), (d=10^{-3}) and (d=5times 10^{-3}) (in (day^{-1}) unit).Full size imageSecondary epidemic peaks are of lower amplitude than the first one, as shown in the top graphs of Fig. 2. This empirical observation leads us to conjecture that, at least in many cases, it is a general property of this model (with (beta) independent of time). This property would then reflect a kind of dissipative nature of Model (1). It is natural to surmise that a change of behaviours in time may generate oscillations with higher secondary peaks. Such changes result for instance from lifting social distancing measures or from fatigue effects in the population.We illustrate this with numerical simulations in Fig. 3. We assume a collective time modulation of the (beta (a)) transmission profile. That is, we replace (beta (a)) by (beta (a)varphi (t)) for some time dependent function (varphi), the other parameters are the same as in the simulations shown in Fig. 2. We look at the effect of a “lockdown exit” type effect. Then, (varphi (t)) takes two constant values, 1 from (t=0) to (t={1000}) and 1.2 after (t={1100}). In between, that is, for (tin ({1000}, {1100})), (varphi (t)) changes linearly from the value 1 to 1.2.Figure 3Multiple epidemic rebounds: susceptible individuals are divided into 50 discrete groups in the case where relaxation of social distancing measures starts on Day (t=1000) and ends up on Day (t=1100). The fraction of infected individuals in the population is represented in the left graph in logarithmic scale and in linear scale in the right graph.Full size imageOne can clearly see a secondary peak with higher amplitude than the first one. Note that after this peak, a third one occurs, with a lower amplitude than the second one. This third peak happens in the regime when (beta) is again constant in time.The effect of variantsAnother important factor that yields secondary peaks with higher amplitudes is the appearance of variants. Consider the situation with two variants. We denote by (I_1(t)) and (I_2(t)) the corresponding infected individuals. The first variant, which we call the historical strain, is associated with (beta _1) and (I_1(0)) and starts at (t=0). The variant strain corresponds to (beta _2) and (I_2) and starts at Day (t=1000). In this situation, the system (1) is extended by the following system:$$begin{aligned} frac{{partial S(t,a)}}{{partial t}} & = d{mkern 1mu} frac{{partial ^{2} S(t,a)}}{{partial a^{2} }} – left( {beta _{1} (a)I_{1} (t) + beta _{2} (a)I_{2} (t)} right)frac{{S(t,a)}}{N}, \ frac{{{text{d}}I_{2} (t)}}{{{text{d}}t}} & = frac{{I_{2} (t)}}{N}{mkern 1mu} intlimits_{0}^{1} {beta _{2} } (a)S(t,a){mkern 1mu} da – gamma _{2} I_{2} (t), \ frac{{{text{d}}I_{1} (t)}}{{{text{d}}t}} & = frac{{I_{1} (t)}}{N}{mkern 1mu} intlimits_{0}^{1} {beta _{1} } (a)S(t,a){mkern 1mu} da – gamma _{1} I_{1} (t) \ frac{{{text{d}}R(t)}}{{{text{d}}t}} & = gamma _{1} I_{2} (t) + gamma _{1} I_{2} (t), \ end{aligned}$$
    (4)
    The total infected population is (I(t)=I_1(t)+I_2(t)). Figure 4 shows a simulation of this system. Before the onset of the second variant, i.e. for (t< 1000), we observe a peak, followed by a small shoulder and a downward tilted plateau. The second variant corresponds to a higher transmission coefficient: namely, we take here (beta _2(a) equiv frac{3}{2} beta _1(a)). When it appears at time (t=1000), initially there is no effect, because the initial number of infectious with variant 2 is very small. Then, there is an exponential growth caused by this second variant gaining strength. The secondary peak is then higher than the first one. A very small shoulder precedes another stabilisation on a downward plateau.Figure 4 also shows the dynamics of fractions of infected with each one of the variants. Note that the infectious with variant 1 very rapidly all but disappear at the onset of the second exponential growth phase. One might have expected that the historical strain would be gradually replaced by the new strain, merely tilting further downward the plateau. But that does not happen. Thus, it is remarkable that the historical strain gets nearly wiped out at the very beginning of the second exponential growth.Figure 4Multiple epidemic rebounds due to a variant virus: susceptible individuals are divided into 50 discrete groups in the case where a new variant appears at Day (t=1000). The transmission rate (beta _2) is taken as (beta _2(a) = 1.5 , beta _1(a)), (d=0.0002), (gamma _1=0.1) and (gamma _2= 0.05). The fraction of infected individuals in the population is represented in the left graph in logarithmic scale. The total infected population is represented in linear scale in the right graph (black curve), variant 1 in red and variant 2 in green.Full size imageApplication to the Thau lagoon measurementsModel (1) describes the dynamics of the fraction of infectious in the population, that is (t mapsto I(t)/N). Therefore, we need to derive this fraction from the wastewater measurements. To this end, we use an “effective proportionality coefficient” between the two quantities. This coefficient itself is derived from the measurements (compare Section “SARS-CoV-2 concentration measurement from wastewater with digital PCR” in the “Methods” part below). Calibration of model (1) also requires fitting the values of (gamma), the profiles (a mapsto beta (a)) and the initial distribution of susceptible individuals in terms of a.We carried this procedure and the resulting fitted curve is displayed in Fig. 5. Note that the outcome correctly captures the shoulder and plateau patterns.Figure 5Calibrated model on Sète area: blue dots are measures of SARS-CoV-2 genome units and black curve represents the total infected individuals as an output of the model discretized into (n_g=20) groups in a. Initial distribution of susceptible individuals and (beta) function are taken as described in supplementary information. Parameters d and (gamma) are taken as follows: (d=2.5 times 10^{-4}) (day^{-1}), and (gamma =0.1) (day^{-1}).Full size imageThe underlying dynamics of the rate of susceptible individuals is given in Fig. 6 below for (n_g=20) groups. The lower curve illustrates the competition phenomenon between diffusion and sink term due to new infections, depending on the level of risk a of each state.Figure 6Calibrated model on Sète WWTP: density of susceptible individuals of each group for (n_g=20). The densities of susceptible of each group is represented in colour curves as functions of time. The curves are ordered from top to bottom according to increasing a. The resulting average total susceptible population is represented in black. Susceptible individuals of highest a trait, which are represented in the bottom light blue curve exhibit a non monotonic behaviour.Full size image More

  • in

    Author Correction: Resource–diversity relationships in bacterial communities reflect the network structure of microbial metabolism

    AffiliationsPhysics of Living Systems Group, Department of Physics, Massachusetts Institute of Technology, Cambridge, MA, USAMartina Dal Bello, Hyunseok Lee, Akshit Goyal & Jeff GoreAuthorsMartina Dal BelloHyunseok LeeAkshit GoyalJeff GoreCorresponding authorsCorrespondence to
    Martina Dal Bello or Jeff Gore. More

  • in

    Secondary predation constrains DNA-based diet reconstruction in two threatened shark species

    1.Diaz, S. et al. Pervasive human-driven decline of life on earth points to the need for transformative change. Science 366, eaax3100 (2020).Article 
    CAS 

    Google Scholar 
    2.Jones, K. R. et al. Area requirements to safeguard Earth’s marine species. One Earth 2, 188–196 (2020).Article 

    Google Scholar 
    3.Dulvy, N. K. et al. Extinction risk and conservation of the world’s sharks and rays. Elife 3, e00590 (2014).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    4.IUCN. International Union for Conservation of Nature Annual Report 2018. (Gland, Switzerland, 2018).5.Walker, T. I., Hudson, R. J. & Gason, A. S. Catch evaluation of target, by-product and by-catch species taken by gillnets and longlines in the shark fishery of south-eastern Australia. J. Northwest Atlantic Fishery Sci. 35, 505–530 (2005).Article 

    Google Scholar 
    6.Braccini, M., Van Rijn, J. & Frick, L. High post-capture survival for sharks, rays and chimaeras discarded in the main shark fishery of Australia?. PLoS ONE 7(1–9), e32547 (2012).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    7.Sumpton, W. D., Taylor, S. M., Gribble, N. A., McPherson, G. & Ham, T. Gear selectivity of large-mesh nets and drumlines used to catch sharks in the Queensland shark control program. Afr. J. Mar. Sci. 33, 37–43 (2011).Article 

    Google Scholar 
    8.Broadhurst, M. K. & Cullis, B. R. Mitigating the discard mortality of non-target, threatened elasmobranchs in bather-protection gillnets. Fisheries Res. 222, 105435 (2020).Article 

    Google Scholar 
    9.Stevens, J. D. & Wayte, S. E. Case study: The bycatch of pelagic sharks in Australia’s tuna longline fisheries. In Sharks of the Open Ocean; Biology, Fisheries and Conservation (eds Camhi, M. D. et al.) 260–267 (Blackwell Publishing, 2009).
    Google Scholar 
    10.Roff, G. et al. The ecological role of sharks on coral reefs. Trends Ecol. Evol. 31(5), 395–407 (2016).PubMed 
    Article 

    Google Scholar 
    11.Roff, G., Brown, C. J., Priest, M. A. & Mumby, P. J. Decline of coastal apex shark populations over the past half century. Commun. Biol. 1, 223 (2018).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    12.Raoult, V., Broadhurst, M. K., Peddemors, V. M., Williamson, J. E. & Gaston, T. F. Resource use of great hammerhead sharks (Sphyrna mokarran) off eastern Australia. J. Fish Biol. 95, 1430–1440 (2019).PubMed 
    Article 

    Google Scholar 
    13.Raoult, V. et al. Predicting geographic ranges of marine animal populations using stable isotopes: A case study of great hammerhead sharks in eastern Australia. Front. Mar. Sci. 7, 594636 (2020).Article 

    Google Scholar 
    14.Chapman, D. D. & Gruber, S. H. A further observation of the prey-handling behavior of the great hammerhead shark, Sphyrna mokarran: Predation upon the spotted eagle ray, Aetobatus narinari. Bull. Mar. Sci. 70, 947–952 (2002).
    Google Scholar 
    15.Cliff, G. Sharks caught in the protective gill nets off KwaZulu-Natal, South Africa. 8. The great hammerhead shark Sphyrna mokarran (Rüppell). S. Afr. J. Mar. Sci. 15, 105–114 (1995).Article 

    Google Scholar 
    16.Strong, W. R., Snelson, F. F. & Gruber, S. H. Hammerhead shark predation on stingrays: An observation of prey handling on Sphyrna mokarran. Copeia 3, 836–840 (1990).Article 

    Google Scholar 
    17.Mourier, J., Planes, S. & Buray, N. Trophic interactions at the top of the coral reef food chain. Coral Reefs 32, 285–285 (2013).ADS 
    Article 

    Google Scholar 
    18.Roemer, R. P., Gallagher, A. J. & Hammerschlag, N. Shallow water tidal flat use and associated specialized foraging behavior of the great hammerhead shark (Sphyrna mokarran). Mar. Freshw. Behav. Physiol. 49, 235–249 (2016).Article 

    Google Scholar 
    19.Gallagher, A. J. & Klimley, A. P. The biology and conservation status of the large hammerhead shark complex: The great, scalloped and smooth hammerheads. Rev. Fish Biol. Fisheries 28, 777–794 (2018).Article 

    Google Scholar 
    20.Barry, K. P., Condrey, R. E., Driggers, W. B. & Jones, C. M. Feeding ecology and growth of neonate and juvenile blacktip sharks Carcharhinus limbatus in the Timbalier-Terrebone Bay complex, LA, U.S.A. J. Fish Biol. 73, 650–662 (2008).Article 

    Google Scholar 
    21.Tavares, R. Occurrence, diet and growth of juvenile blacktip sharks, Carcharhinus limbatus, from Los Roques Archipelago National Park, Venezuela. Carib. J. Sci. 44, 291–302 (2008).Article 

    Google Scholar 
    22.Plumlee, J. D. & Wells, R. J. D. Feeding ecology of three coastal shark species in the northwest Gulf of Mexico. Mar. Ecol. Prog. Ser. 550, 163–174 (2016).ADS 
    CAS 
    Article 

    Google Scholar 
    23.Young, J. W. et al. The trophodynamics of marine top predators: Current knowledge, recent advances and challenges. Deep Sea Res. Part II 113, 170–187 (2015).Article 

    Google Scholar 
    24.Leigh, S. C., Papastamatiou, Y. & German, D. P. The nutritional physiology of sharks. Rev. Fish Biol. Fisheries 27, 561–585 (2017).Article 

    Google Scholar 
    25.Amundsen, P.-A. & Sánchez-Hernández, J. Feeding studies take guts—critical review and recommendations of methods for stomach contents analysis in fish. J. Fish Biol. 95, 1364–1373 (2019).PubMed 
    Article 

    Google Scholar 
    26.Alberdi, A. et al. Promises and pitfalls of using high-throughput sequencing for diet analysis. Mol. Ecol. Resour. 19, 327–348 (2019).PubMed 
    Article 

    Google Scholar 
    27.Nielsen, J. M., Clare, E. L., Hayden, B., Brett, M. T. & Kratina, P. Diet tracing in ecology: Method comparison and selection. Methods Ecol. Evol. 9, 278–291 (2018).Article 

    Google Scholar 
    28.Pompanon, F. et al. Who is eating what: diet assessment using next generation sequencing. Mol. Ecol. 21, 1931–1950 (2012).CAS 
    PubMed 
    Article 

    Google Scholar 
    29.Deagle, B. E. et al. Counting with DNA in metabarcoding studies: How should we convert sequence reads to dietary data?. Mol. Ecol. 28, 391–406 (2019).PubMed 
    Article 

    Google Scholar 
    30.Taberlet, P., Bonin, A., Zinger, L. & Coissac, E. Environmental DNA for Biodiversity Research and Monitoring (Oxford University Press, 2018).
    Google Scholar 
    31.Barbato, M., Kovacs, T., Coleman, M., Broadhurst, M. & de Bruyn, M. Metabarcoding of stomach-content analyses: Comparing tissue and ethanol preservative-derived DNA. Ecol. Evol. 9(5), 2678–2687 (2019).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    32.Berry, O. et al. Comparison of morphological and DNA metabarcoding analyses of diets in exploited marine fishes. Mar. Ecol. Prog. Ser. 540, 167–181 (2015).ADS 
    CAS 
    Article 

    Google Scholar 
    33.Bessey, C. et al. DNA metabarcoding assays reveal a diverse prey assemblage for Mobula rays in the Bohol Sea, Philippines. Ecol. Evol. 9(5), 2459–2474 (2019).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    34.Clarke, L. J., Trebilco, R., Walters, A., Polanowski, A. M. & Deagle, B. E. DNA-based diet analysis of mesopelagic fish from the southern Kerguelen Axis. Deep Sea Res. Part II Top. Stud. Oceanogr. 174, 104494 (2020).CAS 

    Google Scholar 
    35.Sousa, L. L. et al. DNA barcoding identifies a cosmopolitan diet in the ocean sunfish. Sci. Rep. 6, 28762 (2016).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    36.Takahashi, M. et al. Partitioning of diet between species and life history stages of sympatric and cryptic snappers (Lutjanidae) based on DNA metabarcoding. Sci. Rep. 10(1), 1–13 (2020).Article 
    CAS 

    Google Scholar 
    37.Yoon, T.-H. et al. Metabarcoding analysis of the stomach contents of the Antarctic Toothfish (Dissostichus mawsoni) collected in the Antarctic Ocean. PeerJ 5, e3977 (2017).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    38.Clare, E. L. Molecular detection of trophic interactions: emerging trends, distinct advantages, significant considerations and conservation applications. Evol. Appl. 7, 1144–1157 (2014).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    39.Varennes, Y.-D., Boyer, S. & Wratten, S. D. Un-nesting DNA Russian dolls: The potential for constructing food webs using residual DNA in empty aphid mummies. Mol. Ecol. 23, 3925–3933 (2014).CAS 
    PubMed 
    Article 

    Google Scholar 
    40.Miya, M. et al. MiFish, a set of universal PCR primers for metabarcoding environmental DNA from fishes: detection of more than 230 subtropical marine species. R. Soc. Open Sci. 2(7), 150088 (2015).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    41.Berry, T. E. et al. DNA metabarcoding for diet analysis and biodiversity: A case study using the endangered Australian sea lion (Neophoca cinerea). Ecol. Evol. 7(14), 5435–5453 (2017).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    42.Zhan, A. et al. High sensitivity of 454 pyrosequencing for detection of rare species in aquatic communities. Methods Ecol. Evol. 4, 558–565 (2013).Article 

    Google Scholar 
    43.Edgar, R. C. Search and clustering orders of magnitude faster than BLAST. Bioinformatics 26(19), 2460–2461 (2010).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    44.Frøslev, T. G. et al. Algorithm for post-clustering curation of DNA amplicon data yields reliable biodiversity estimates. Nat. Commun. 8(1), 1–11 (2017).Article 
    CAS 

    Google Scholar 
    45.Mousavi-Derazmahalleh, M., Stott, A., Lines, R., Peverley, G., Nester, G., Simpson, T., Zawierta, M., De La Pierre, M., Bunce, M., & Christophersen, C. eDNAFlow, an automated, reproducible and scalable workflow for analysis of environmental DNA (eDNA) sequences exploiting Nextflow and Singularity. Mol. Ecol. Resour. 21, 1697–1704 (2020).Article 
    CAS 

    Google Scholar 
    46.Venables, W. N. & Ripley, B. D. Modern Applied Statistics with S 4th edn. (Springer, 2002).MATH 
    Book 

    Google Scholar 
    47.R Core Team. R: A language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria. URL https://www.R-project.org/ (2017).48.Oksanen, J., et al. vegan: Community Ecology Package. R package version 2.5-7. https://CRAN.R-project.org/package=vegan (2020).49.Compagno, L. J. V. Sharks of the Order Carcharhiniformes (Princeton University Press, 1988).
    Google Scholar 
    50.Johnsen, P. B. & Teeter, J. H. Behavioral responses of the bonnethead shark (Sphyrna tiburo) to controlled olfactory stimulation. Mar. Behav. Phys. 11, 283–291 (1985).Article 

    Google Scholar 
    51.Nakaya, K. Hydrodynamic function of the head in the hammerhead sharks (Elasmobranchii: Sphyrinidae). Copeia 2, 330–336 (1995).Article 

    Google Scholar 
    52.Leray, M., Agudelo, N., Mills, S. C. & Meyer, C. P. Effectiveness of annealing blocking primers versus restriction enzymes for characterization of generalist diets: unexpected prey revealed in the gut contents of two coral reef fish species. PLoS ONE 8(4), e58076 (2013).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    53.Leray, M., Meyer, C. P. & Mills, S. C. Metabarcoding dietary analysis of coral dwelling predatory fish demonstrates the minor contribution of coral mutualists to their highly partitioned, generalist diet. PeerJ 3, e1047 (2015).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    54.Van Zinnicq Bergmann, M. P. M. et al. Elucidating shark diets with DNA metabarcoding from cloacal swabs. Mol. Ecol. Resour. 21, 1056–1067 (2021).PubMed 
    Article 
    CAS 

    Google Scholar  More

  • in

    Microbial community of soda Lake Van as obtained from direct and enriched water, sediment and fish samples

    1.Nyakeri, E. M., Mwirichia, R. & Boga, H. Isolation and characterization of enzyme-producing bacteria from Lake Magadi, an extreme soda lake in Kenya. J. Microbiol. Exp. 6(2), 57–68 (2018).
    Google Scholar 
    2.Grant, W. D. Alkaline environments and biodiversity. In Extremophiles (eds Gerday, E. C. & Glansdorff, N.) (UNESCO, Eolss Publishers, 2006).
    Google Scholar 
    3.Jones, B. E. & Grant, W. D. Microbial diversity and ecology of alkaline environments. In Adaptation to Exotic Environments (ed. Seckbach, J.) 177–190 (Kluwer Academic Publishers, 2000).
    Google Scholar 
    4.Antony, C. P. et al. Microbiology of Lonar Lake and other soda lakes. J. Int. Soc. Microb. Ecol. 7(3), 468–476 (2013).
    Google Scholar 
    5.Boros, E. & Kolpakova, M. A review of the defining chemical properties of soda lakes and pans: An assessment on a large geographic scale of Eurasian inland saline surface waters. PLoS ONE 13(8), e0202205 (2018).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    6.Grant, W. D. & Jones, B. E. Bacteria, archaea and viruses of soda lakes. In Soda lakes of East Africa (ed. Schagerl, M.) 97–148 (Springer p, 2016).
    Google Scholar 
    7.Lanzén, A. et al. Surprising prokaryotic and eukaryotic diversity, community structure and biogeography of Ethiopian soda lakes. PLoS ONE 8(8), e72577 (2013).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    8.Asao, M., Pinkart, H. C. & Madigan, M. T. Diversity of extremophilic purple phototrophic bacteria in Soap Lake, a Central Washington (USA) Soda Lake. Environ. Microbiol. 13(8), 2146–2157 (2011).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    9.Kulp, T. R. et al. Dissimilatory arsenate and sulfate reduction in sediments of two hypersaline, arsenic-rich soda lakes: Mono and Searles Lakes, California. Appl. Environ. Microbiol. 72(10), 6514–6526 (2006).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    10.Sorokin, D. Y. & Kuenen, J. G. Chemolithotrophic haloalkaliphiles from soda lakes. FEMS Microbiol. Ecol. 52(3), 287–295 (2005).CAS 
    PubMed 
    Article 

    Google Scholar 
    11.Groth, I. et al. Bogoriella caseilytica gen. nov., sp. Nov., a new alkaliphilic actinomycete from a soda lake in Africa. Int. J. Syst. Evol. Microbiol. 47(3), 788–794 (1997).CAS 

    Google Scholar 
    12.Glombitza, C. et al. Sulfate reduction controlled by organic matter availability in deep sediment cores from the saline, alkaline Lake Van (Eastern Anatolia, Turkey). Front. Microbiol. 4, 1–11 (2013).Article 

    Google Scholar 
    13.Bilgili, A. et al. Van Gölü’nden avlanan inci kefali örneklerinde arsenik düzeyleri. Turk. J. Vet. Anim. Sci. 23(2), 367–371 (1999).MathSciNet 

    Google Scholar 
    14.Kremer, B., Kaźmierczak, J. & Kempe, S. Authigenic replacement of cyanobacterially precipitated calcium carbonate by aluminium-silicates in giant microbialites of Lake Van (Turkey). Sedimentology 66(1), 285–304 (2019).CAS 
    Article 

    Google Scholar 
    15.Reimer, A., Landmann, G. & Kempe, S. Lake Van, Eastern Anatolia, hydrochemistry and history. Aquat. Geochem. 15(1–2), 195–222 (2009).CAS 
    Article 

    Google Scholar 
    16.Tomonaga, Y. et al. Porewater salinity reveals past lake-level changes in Lake Van, the Earth’s largest soda lake. Sci. Rep. 7(1), 1–10 (2017).CAS 
    Article 

    Google Scholar 
    17.Pecoraino, G., Dlessandro, W. & Inguaggiato, S. The other side of the coin: Geochemistry of alkaline lakes in volcanic areas. In Volcanic Lakes (eds Rouwet, D. et al.) 219–237 (Springer, 2015).Chapter 

    Google Scholar 
    18.Kaden, H. et al. Impact of lake level change on deep-water renewal and oxic conditions in deep saline Lake Van. Turkey. Water Resour. Res. https://doi.org/10.1029/2009WR008555 (2010).ADS 
    Article 

    Google Scholar 
    19.Landmann, G. & Kempe, S. Annual deposition signal versus lake dynamics: Microprobe analysis of Lake Van (Turkey) sediments reveals missing varves in the period 11.2–10.2 ka BP. Facies 51(1–4), 135–145 (2005).Article 

    Google Scholar 
    20.Degens, E. T. et al. A geological study of Lake Van, eastern Turkey. Geol. Rundsch. 73(2), 701–734 (1984).ADS 
    CAS 
    Article 

    Google Scholar 
    21.Duckworth, A. W. et al. Phylogenetic diversity of soda lake alkaliphiles. FEMS Microbiol. Ecol. 19(3), 181–191 (1996).CAS 
    Article 

    Google Scholar 
    22.Sorokin, D. Y. et al. Microbial diversity and biogeochemical cycling in soda lakes. Extremophiles 18(5), 791–809 (2014).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    23.Zargar, K. et al. Identification of a novel oxidase gene, arxA, in the haloalkaliphilic, arsenite-oxidizing bacterium Alkalilimnicola echrlichii strain MLHE-1. J. Bacteriol. 192, 3755–3762 (2010).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    24.Zargar, K. et al. ArxA, a new clade of arsenite oxidase within the DMSO reductase family of molybdenum oxidoreductases. Environ. Microbiol. 14(7), 1635–1645 (2012).CAS 
    PubMed 
    Article 

    Google Scholar 
    25.Zorz, J. K. et al. A shared core microbiome in soda lakes separated by large distances. Nat. Commun. 10(1), 1–10 (2019).CAS 
    Article 

    Google Scholar 
    26.Matyugina, E. & Belkova, N. Distribution and diversity of microbial communities in meromictic soda Lake Doroninskoe (Transbaikalia, Russia) during winter. Chin. J. Oceanol. Limn. 33(6), 1378 (2015).ADS 
    CAS 
    Article 

    Google Scholar 
    27.Liu, D. et al. Use of PCR primers derived from a putative transcriptional regulator gene for species-specific determination of Listeria monocytogenes. Int. J. Food Microbiol. 91, 297–304 (2004).CAS 
    PubMed 
    Article 

    Google Scholar 
    28.Camacho, C. et al. BLAST+: Architecture and applications. BMC Bioinform. 10, 421 (2009).Article 
    CAS 

    Google Scholar 
    29.Ionescu, D. et al. Microbial and chemical characterization of underwater fresh water springs in the Dead Sea. PLoS ONE 7, e38319 (2012).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    30.Klindworth, A. et al. Evaluation of general 16S ribosomal RNA gene PCR primers for classical and next-generation sequencing-based diversity studies. Nucleic Acids Res. 41, e1 (2013).CAS 
    PubMed 
    Article 

    Google Scholar 
    31.Ondov, B. et al. Interactive metagenomic visualization in a web browser. BMC Bioinform. 12, 385 (2011).Article 

    Google Scholar 
    32.Pruesse, E. et al. SINA: Accurate high throughput multiple sequence alignment of ribosomal RNA genes. Bioinformatics 28(14), 1823–1829 (2012).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    33.Quast, C. et al. The silva ribosomal RNA gene database project: Improved data processing and webbased tools. Nucleic Acids Res. 41, D590–D596 (2013).CAS 
    PubMed 
    Article 

    Google Scholar 
    34.Rognes, T. et al. Vsearch: A versatile open source tool for metagenomics. Peer J. 4, e2584 (2016).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    35.Hammer, Ø., Harper, D. A. & Ryan, P. D. Past: Paleontological statistics software package for education and data analysis. Palaeontol. Electron. 4(1), 1–9 (2001).
    Google Scholar 
    36.Duckworth, A. W. et al. Halomonas magadii sp. Nov., a new member of the genus Halomonas, isolated from a soda lake of the East African Rift Valley. Extremophiles 4(1), 53–60 (2000).MathSciNet 
    CAS 
    PubMed 
    PubMed Central 

    Google Scholar 
    37.Xin, H. et al. Natronobacterium nitratireducens sp. nov., a aloalkaliphilic archaeon isolated from a soda lake in China. Int. J. Syst. Evol. Microbiol. 51(5), 1825–1829 (2001).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    38.Joshi, A. et al. Nitrincola tapanii sp. nov., a novel alkaliphilic bacterium from An Indian Soda Lake. Int. J. Syst. Evol. Microbiol. 70(2), 1106–1111 (2020).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    39.Menes, R. J. et al. Bacillus natronophilus sp. nov., an alkaliphilic bacterium isolated from a soda lake. Int. J. Syst. Evol. Microbiol. 70(1), 562–568 (2020).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    40.Vavourakis, C. D. et al. A metagenomics roadmap to the uncultured genome diversity in hypersaline soda lake sediments. Microbiome. 6(1), 1–18 (2018).Article 

    Google Scholar 
    41.Yigit, A. et al. Determination of water quality by ion characterization of Van Lake Water. Iğdır Univ. J. Inst. Sci. Tech. 7(4), 169–179. https://doi.org/10.21597/jist.2017.210 (2017).Article 

    Google Scholar 
    42.Bilgili, A. et al. The natural quality of Van Lake and the levels of some heavy metals in grey mullet (Chalcalburus tariehi, Pallas 1811) samples taken from this lake. Ankara Üniv Vet Fak Dergisi 42, 445–450 (1995).
    Google Scholar 
    43.Demir Yetis, A. & Ozguven, A. Investigation of heavy metal pollution in surface waters of the Van Lake Edremit coast. Uludağ Univ. J. Fac. Eng. 25(2), 831–847. https://doi.org/10.17482/uumfd.752460 (2020).Article 

    Google Scholar 
    44.Ersoy Omeroglu, E. & Karaboz, I. Characterization and arsenic-tolerance potential of Halomonas sp. from Van Lake, Turkey. VI Congress of Macedonian Microbiologists With International Participation, 30 May–6 June, Abstract Book, pp. 200–201 (2018).45.Ersoy Omeroglu, E. Evaluation of arsenic pollution and the effect of arsenic on Branchybacterium paraconglomeratum in Van Lake. 1st World Conference On Sustaninable Life Sciences WOCOLS 2019, 30 June–7 July, Abstract Book, p. 17 (2019).46.Reimer, A. Hydrochemie und Geochemie der Sedimente und Porenwa¨sser des hochalkalinen Van Sees in der Osttu¨rkei. Dissertation, Facult Geosci Univ Hamburg, 136 pp, unpublished, (1995).47.Kempe, S. et al. Largest known microbialites discovered in Lake Van, Turkey. Nature 349, 605–608 (1991).ADS 
    Article 

    Google Scholar 
    48.Kazmierczak, J. & Kempe, S. Modern terrestrial analogues for the carbonate globules in Martian meteorite ALH84001. Naturwissenschaften 90, 167–172 (2003).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    49.Lopez-Garcia, P. et al. Bacterial diversity and carbonate precipitation in the microbialites of the highly alkaline Lake Van, Turkey. Extremophiles 9, 263–274 (2005).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    50.Poyraz, N. & Mutlu, M. B. Characterization of microbial populations of Lake Van by 16S metagenomics study. ESTUJST-A. 9(1), 80–88 (2020).
    Google Scholar 
    51.Poyraz, N. & Mutlu, B. M. Alkaliphilic bacterial diversity of Lake Van/Turkey. Biological Biodivers. Conserv. 10(1), 92–103 (2017).
    Google Scholar 
    52.Sen, F. et al. Endemic fish species of Van Lake basin. YYU J. Agr. Sci. 28, 63–70 (2018).
    Google Scholar 
    53.Danulat, E. & Kempe, S. Nitrogenous waste excretion at extremely alkaline pH: The story of Chalcalburnus tarichi (Cyprinidae), endemic to Lake Van, Eastern Turkey. Fish Physiol. Biochem. 9, 377–386 (1992).CAS 
    PubMed 
    Article 

    Google Scholar 
    54.Bostanci, D. & Polat, N. Age and growth of Alburnus tarichi (Güldenstädt, 1814): An endemic fish species of Lake Van (Turkey). J. Appl. Ichthyol. 27, 1346–1349 (2011).Article 

    Google Scholar 
    55.Burger, J. et al. Armenian Gull (Larus armenicus). Handbook of the Birds of the World Alive, Lynx Edicions, Barcelona (2015).56.Oremland, R. S. et al. Methanogenesis in Big Soda Lake, Nevada: An alkaline, moderately hypersaline desert lake. Appl. Environ. Microbiol. 43, 462–468 (1982).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    57.Iversen, N. et al. Big Soda Lake (Nevada): 3: Pelagic methanogenesis and anaerobic methane oxidation. Limnol. Oceanogr. 32, 804–814 (1987).ADS 
    CAS 
    Article 

    Google Scholar 
    58.Oremland, R. S. et al. The microbial arsenic cycle in Mono Lake, California. FEMS Microb. Ecol. 48, 15–27 (2004).CAS 
    Article 

    Google Scholar 
    59.Sorokin, D. Y. et al. Microbial thiocyanate utilization under highly alkaline conditions. Appl. Environ. Microbiol. 67, 528–538 (2001).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    60.Sorokin, D. Y. et al. Thioalkalimicrobium aerophilum gen. nov., sp. nov. and Thioalkalimicrobium sibiricum sp. nov., and Thioalkalivibrio versutus gen. nov., sp. nov., Thioalkalivibrio nitratis sp. nov. and Thioalkalivibrio denitrificans sp. nov., novel obligately alkaliphilic and obligately chemolithoautotrophic sulfur-oxidizing bacteria from soda lakes. Int. J. Syst. Evol. Microbiol. 51, 565–580 (2001).CAS 
    PubMed 
    Article 

    Google Scholar 
    61.Sorokin, D. Y. et al. Thioalkalivibrio thiocyanooxidans sp. nov. and Thioalkalivibrio paradoxus sp. nov., novel alkaliphilic, obligately autotrophic, sulfur-oxidizing bacteria from the soda lakes able to grow with thiocyanate. Int. J. Syst. Evol. Microbiol. 52, 657–664 (2002).CAS 
    PubMed 
    Article 

    Google Scholar 
    62.Gorlenko, V. M. et al. Ectothiorhodospira variabilis sp. nov., an alkaliphilic and halophilic purple sulfur bacterium from soda lakes. Int. J. Syst. Evol. Microbiol. 69, 558–564 (2009).
    Google Scholar 
    63.Mwirichia, R. et al. Bacterial diversity in the haloalkaline Lake Elmenteita, Kenya. Curr. Microbiol. 62, 209–221 (2011).CAS 
    PubMed 
    Article 

    Google Scholar 
    64.Mesbah, N. M. et al. Novel and unexpected prokaryotic diversity in water and sediments of the alkaline, hypersaline lakes of the Wadi an Natrun, Egypt. Microbial Ecol. 54, 598–616 (2007).CAS 
    Article 

    Google Scholar 
    65.Flandroy, L. et al. The impact of human activities and lifestyles on the interlinked microbiota and health of humans and of ecosystems. Sci. Total Environ. 627, 1018–1038 (2018).ADS 
    CAS 
    PubMed 
    Article 

    Google Scholar 
    66.Deshmukh, K. B. et al. Bacterial diversity of Lonar soda lake of India. Indian J. Microbiol. 51, 107–111 (2011).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    67.Zhao, D. et al. Abundant taxa and favorable pathways in the microbiome of soda-saline lakes in Inner Mongolia. Front. Microbiol. 11, 1740 (2020).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    68.Lavrentyeva, E. V. et al. Prokaryotic diversity in the biotopes of the Gudzhirganskoe saline lake (Barguzin Valley, Russia). Mikrobiologiya 89, 359–368 (2020).CAS 

    Google Scholar 
    69.Glaring, M. A. et al. Microbial diversity in a permanently cold and alkaline environment in Greenland. PLoS ONE 10, e0124863 (2015).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    70.Tavormina, P. L. et al. Methyloprofundus sedimenti gen. nov., sp. nov., an obligate methanotroph from ocean sediment belonging to the ‘deep sea-1’clade of marine methanotrophs. Int. J. Syst. Evol. Microbiol. 65(1), 251–259 (2015).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    71.Sorokin, D. Y. et al. Dethiobacter alkaliphilus gen. nov. sp. nov., and Desulfurivibrio alkaliphilus gen. nov. sp. nov.: Two novel representatives of reductive sulfur cycle from soda lakes. Extremophiles 12, 431–439 (2008).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    72.Holmes, D. E. et al. Potential role of a novel psychrotolerant member of the family Geobacteraceae, Geopsychrobacter electrodiphilus gen. nov., sp. nov., in electricity production by a marine sediment fuel cell. Appl. Environ. Microbiol. 70, 6023–6030 (2005).ADS 
    Article 
    CAS 

    Google Scholar 
    73.Pikuta, E. V. et al. Proteocatella sphenisci gen. nov., sp. nov., a psychrotolerant, spore-forming anaerobe isolated from penguin guano. Int. J. Syst. Evol. Microbiol. 59, 2302–2307 (2009).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    74.Stams, A. J. M. & Hansen, T. A. Fermentation of glutamate and other compounds by Acidaminobacter hydrogenoformans gen. nov. sp. nov., an obligate anaerobe isolated from black mud: Studies with pure cultures and mixed cultures with sulfate-reducing and methanogenic bacteria. Arch. Microbiol. 137, 329–337 (1984).CAS 
    Article 

    Google Scholar 
    75.Finegold, S. M. et al. Anaerofustis stercorihominis gen. nov., sp. nov., from human feces. Anaerobe 10, 41–45 (2004).CAS 
    PubMed 
    Article 

    Google Scholar 
    76.Matthies, C. et al. Anaerovorax odorimutans gen. nov., sp. nov., a putrescine-fermenting, strictly anaerobic bacterium. Int. J. Syst. Evol. Microbiol. 50, 1591–1594 (2000).CAS 
    PubMed 
    Article 

    Google Scholar 
    77.Higashiguchi, D. T. et al. Pilibacter termitis gen. nov., sp. nov., a lactic acid bacterium from the hindgut of the Formosan subterranean termite (Coptotermes formosanus). Int. J. Syst. Evol. Microbiol. 56, 15–20 (2006).CAS 
    PubMed 
    Article 

    Google Scholar 
    78.Labrenz, M. et al. Roseibaca ekhonensis gen. nov., sp. nov., an alkalitolerant and aerobic bacteriochlorophyll a-producing alphaproteobacterium from hypersaline Ekho Lake. Int. J. Syst. Evol. Microbiol. 59, 1935–1940 (2009).CAS 
    PubMed 
    Article 

    Google Scholar 
    79.Sorokin, D. Y. et al. Nitriliruptor alkaliphilus gen. nov., sp. nov., a deep-lineage haloalkaliphilic actinobacterium from soda lakes capable of growth on aliphatic nitriles, and proposal of Nitriliruptoraceae fam. Nov. and Nitriliruptorales ord. nov. Int. J. Syst. Evol. Microbiol. 59, 248–253 (2009).CAS 
    PubMed 
    Article 

    Google Scholar 
    80.Shahinpei, A. et al. Salinispirillum marinum gen. nov., sp. nov., a haloalkaliphilic bacterium in the family “Saccharospirillaceae”. Int. J. Syst. Evol. Microbiol. 64, 3610–3615 (2014).PubMed 
    Article 
    CAS 
    PubMed Central 

    Google Scholar 
    81.Munson, M. A. et al. Buchnera gen. nov. and Buchnera aphidicola sp. nov., a taxon consisting of the mycetocyte-associated, primary endosymbionts of aphids. Int. J. Syst. Bacteriol. 41, 566–568 (1991).Article 

    Google Scholar  More

  • in

    Current contrasting population trends among North American hummingbirds

    1.United Nations Environment Programme. Making Peace With Nature (Tech. Rep, United Nations Environment Programme, 2021).2.Newbold, T. et al. Global effects of land use on local terrestrial biodiversity. Nature 520, 45–50. https://doi.org/10.1038/nature14324 (2015).ADS 
    CAS 
    Article 
    PubMed 

    Google Scholar 
    3.Urban, M. C. Accelerating extinction risk from climate change. Science. (80-. ) 348, 571–573. https://doi.org/10.1126/science.aaa4984 (2015).ADS 
    CAS 
    Article 

    Google Scholar 
    4.Rosenberg, K. V. et al. Decline of the North American avifauna. Science. (80-. ) 366, 120–124. https://doi.org/10.1126/science.aaw1313 (2019).ADS 
    CAS 
    Article 

    Google Scholar 
    5.Jetz, W., Wilcove, D. S. & Dobson, A. P. Projected impacts of climate and land-use change on the global diversity of birds. PLoS Biol. 5, 1211–1219. https://doi.org/10.1371/journal.pbio.0050157 (2007).CAS 
    Article 

    Google Scholar 
    6.Abrahamczyk, S. & Renner, S. S. The temporal build-up of hummingbird/plant mutualisms in North America and temperate South America. BMC Evol. Biol.https://doi.org/10.1186/s12862-015-0388-z (2015).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    7.Grant, V. & Grant, K. A. A Hummingbird-Pollinated Species of Boraginaceae in the Arizona Flora. Proc. Natl. Acad. Sci. 66, 917–919. https://doi.org/10.1073/pnas.66.3.917 (1970).ADS 
    CAS 
    Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    8.Ratto, F. et al. Global importance of vertebrate pollinators for plant reproductive success: A meta-analysis. Front. Ecol. Environ. 16, 82–90. https://doi.org/10.1002/fee.1763 (2018).Article 

    Google Scholar 
    9.McGuire, J. A. et al. Molecular phylogenetics and the diversification of hummingbirds. Curr. Biol. 24, 910–916. https://doi.org/10.1016/j.cub.2014.03.016 (2014).CAS 
    Article 
    PubMed 

    Google Scholar 
    10.Sauer, J. R., Link, W. A., Fallon, J. E., Pardieck, K. L. & Ziolkowski, D. J. The North American breeding bird survey 1966–2011: Summary analysis and species accounts. N. Am. Fauna 79, 1–32. https://doi.org/10.3996/nafa.79.0001 (2013).Article 

    Google Scholar 
    11.Bairlein, F. Migratory birds under threat. Science (80-. ). 354, 547–548. https://doi.org/10.1126/science.aah6647 (2016).ADS 
    CAS 
    Article 

    Google Scholar 
    12.Battey, C. J. Ecological release of the Anna’s Hummingbird during a Northern range expansion. Am. Nat. 194, 306–315. https://doi.org/10.1086/704249 (2019).CAS 
    Article 
    PubMed 

    Google Scholar 
    13.Clark, C. J. EBird records show substantial growth of the Allen’s Hummingbird (Selasphorus sasin sedentarius) population in urban Southern California. Condor 119, 122–130. https://doi.org/10.1650/CONDOR-16-153.1 (2017).Article 

    Google Scholar 
    14.Sleeter, B. M. et al. Land-cover change in the conterminous United States from 1973 to 2000. Glob. Environ. Change 23, 733–748. https://doi.org/10.1016/j.gloenvcha.2013.03.006 (2013).Article 

    Google Scholar 
    15.Gallant, A. L., Loveland, T. R., Sohl, T. L. & Napton, D. E. Using an ecoregion framework to analyze land-cover and land-use dynamics. Environ. Manag.https://doi.org/10.1007/s00267-003-0145-3 (2004).Article 

    Google Scholar 
    16.Williamson, S. L. A Field Guide to Hummingbirds of North America (Peterson Field Guide Series) (Houghton Mifflin Company, 2002).
    Google Scholar 
    17.Panjabi, A. O. et al. Avian Conservation Assessment Database Handbook Version 2021. Tech. Rep. (Partners in Flight Technical Series, Bird Conservancy of the Rockies, 2021).
    Google Scholar 
    18.Gillespie, C., Contreras-Martinez, S., Bishop, C. & Alexander, J. Rufous Hummingbird: State of the Science and Conservation : simplebooklet.com. Tech. Rep., (Western Hummingbird Partnership, 2020).19.International Union for Conservation of Nature. IUCN Red List Categories and Criteria: Version 3.1. Tech. Rep. (IUCN Species Survival Commission, 2001).
    Google Scholar 
    20.Lehikoinen, A. Climate change, phenology and species detectability in a monitoring scheme. Popul. Ecol. 55, 315–323. https://doi.org/10.1007/s10144-012-0359-9 (2013).Article 

    Google Scholar 
    21.Massimino, D., Harris, S. J. & Gillings, S. Phenological mismatch between breeding birds and their surveyors and implications for estimating population trends. J. Ornithol. 162, 143–154. https://doi.org/10.1007/s10336-020-01821-5 (2021).Article 

    Google Scholar 
    22.McGrath, L. J., van Riper III, C. & Fontaine, J. J. Flower power: Tree flowering phenology as a settlement cue for migrating birds. J. Anim. Ecol. 78, 22–30. https://doi.org/10.1111/j.1365-2656.2008.01464.x (2009).Article 
    PubMed 

    Google Scholar 
    23.Jones, T. & Cresswell, W. The phenology mismatch hypothesis: Are declines of migrant birds linked to uneven global climate change?. J. Anim. Ecol. 79, 98–108. https://doi.org/10.1111/j.1365-2656.2009.01610.x (2010).Article 
    PubMed 

    Google Scholar 
    24.Courter, J. R. Changes in spring arrival dates of rufous hummingbirds (Selasphorus rufus) In Western North America in the past century. Wilson J. Ornithol. 129, 535–544. https://doi.org/10.1676/16-133.1 (2017).Article 

    Google Scholar 
    25.Rooney, T. Deer impacts on forest ecosystems: A North American perspective. Forestry 74, 201–208. https://doi.org/10.1093/forestry/74.3.201 (2001).Article 

    Google Scholar 
    26.Côté, S. D., Rooney, T. P., Tremblay, J.-P., Dussault, C. & Waller, D. M. Ecological impacts of deer overabundance. Annu. Rev. Ecol. Evol. Syst. 35, 113–147. https://doi.org/10.2307/annurev.ecolsys.35.021103.30000006 (2004).Article 

    Google Scholar 
    27.Decalesta, D. S. Effect of white-tailed deer on songbirds within managed forests in Pennsylvania. J. Wildl. Manag. 58, 711–718 (1994).Article 

    Google Scholar 
    28.English, S. G. et al. Neonicotinoid pesticides exert metabolic effects on avian pollinators. Sci. Rep. 11, 2914. https://doi.org/10.1038/s41598-021-82470-3 (2021).ADS 
    CAS 
    Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    29.Bishop, C. A. et al. Determination of neonicotinoids and butenolide residues in avian and insect pollinators and their ambient environment in Western Canada (2017, 2018). Sci. Total Environ. 737, 139386. https://doi.org/10.1016/j.scitotenv.2020.139386 (2020).ADS 
    CAS 
    Article 
    PubMed 

    Google Scholar 
    30.Graves, E. E. et al. Analysis of insecticide exposure in California hummingbirds using liquid chromatography-mass spectrometry. Environ. Sci. Pollut. Res. 26, 15458–15466. https://doi.org/10.1007/s11356-019-04903-x (2019).CAS 
    Article 

    Google Scholar 
    31.Hill, G. E., Sargent, R. R. & Sargent, M. B. Recent change in the winter distribution of Rufous Hummingbirds. Auk 115, 240–245. https://doi.org/10.2307/4089135 (1998).Article 

    Google Scholar 
    32.Smith, A. C. & Edwards, B. P. M. North American Breeding Bird Survey status and trend estimates to inform a wide range of conservation needs, using a flexible Bayesian hierarchical generalized additive model. Condor 123, 1–16. https://doi.org/10.1093/ornithapp/duaa065 (2021).Article 

    Google Scholar 
    33.Wilson, S. et al. Prioritize diversity or declining species? Trade-offs and synergies in spatial planning for the conservation of migratory birds in the face of land cover change. Biol. Conserv. 239, 108285. https://doi.org/10.1016/j.biocon.2019.108285 (2019).Article 

    Google Scholar 
    34.Toledo-Aceves, T., Meave, J. A., González-Espinosa, M. & Ramírez-Marcial, N. Tropical montane cloud forests: Current threats and opportunities for their conservation and sustainable management in Mexico. J. Environ. Manag. 92, 974–981. https://doi.org/10.1016/j.jenvman.2010.11.007 (2011).Article 

    Google Scholar 
    35.Hansen, M. C. et al. High-resolution global maps of 21st-century forest cover change. Science (80-. ). 342, 850–853. https://doi.org/10.1126/SCIENCE.1244693 (2013).ADS 
    CAS 
    Article 

    Google Scholar 
    36.Westerling, A. L. Increasing western US forest wildfire activity: Sensitivity to changes in the timing of spring. Philos. Trans. R. Soc. B Biol. Sci.https://doi.org/10.1098/RSTB.2015.0178 (2016).Article 

    Google Scholar 
    37.Neeraja, U. V., Rajendrakumar, S., Saneesh, C. S., Dyda, V. & Knight, T. M. Fire alters diversity, composition, and structure of dry tropical forests in the Eastern Ghats. Ecol. Evol. 11, 6593–6603. https://doi.org/10.1002/ECE3.7514 (2021).CAS 
    Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    38.Courter, J. R., Johnson, R. J., Bridges, W. C. & Hubbard, K. G. Assessing migration of Ruby-throated Hummingbirds (Archilochus colubris) at broad spatial and temporal scales at broad spatial and temporal scales. Auk 130, 107–117. https://doi.org/10.1525/auk.2012.12058 (2013).Article 

    Google Scholar 
    39.Greig, E. I., Wood, E. M. & Bonter, D. N. Winter range expansion of a hummingbird is associated with urbanization and supplementary feeding. Proc. R. Soc. B Biol. Sci.https://doi.org/10.1098/rspb.2017.0256 (2017).Article 

    Google Scholar 
    40.Jepson, W. L. & Hickman, J. C. The Jepson manual: Higher plants of California (University of California Press, 1993).
    Google Scholar 
    41.Scarfe, A. & Finlay, J. C. Rapid second nesting by Anna’s Hummingbird near its Northern breeding limit. West. Birds 32, 131–133 (2001).
    Google Scholar 
    42.Bibby, C. J., Burgess, N. D. & Hill, D. A. Bird Census Techniques (Academic Press, 1992).
    Google Scholar 
    43.Thogmartin, W. E. et al. A review of the population estimation approach of the North American landbird conservation plan. Auk 123, 892–904. https://doi.org/10.1093/auk/123.3.892 (2006).Article 

    Google Scholar 
    44.Carter, M. F., Hunter, W. C., Pashley, D. N. & Rosenberg, K. V. Setting conservation priorities for landbirds in the United States: The partners in flight approach. Auk 117, 541–548. https://doi.org/10.1093/auk/117.2.541 (2000).Article 

    Google Scholar 
    45.Sauer, J. R. & Link, W. A. Analysis of the North American breeding bird survey using hierarchical models. Auk 128, 87–98. https://doi.org/10.1525/auk.2010.09220 (2011).Article 

    Google Scholar 
    46.Sauer, J. R., Niven, D. K., Pardieck, K. L., Ziolkowski, D. J. & Link, W. A. Expanding the North American Breeding Bird Survey analysis to include additional species and regions. J. Fish Wildl. Manag. 8, 154–172. https://doi.org/10.3996/102015-JFWM-109 (2017).Article 

    Google Scholar 
    47.Stanton, J. C., Blancher, P., Rosenberg, K. V., Panjabi, A. O. & Thogmartin, W. E. Estimating uncertainty of North American landbird population sizes. Avian Conserv. Ecol.https://doi.org/10.5751/ACE-01331-140104 (2019).Article 

    Google Scholar 
    48.Schuster, R. et al. Optimizing the conservation of migratory species over their full annual cycle. Nat. Commun.https://doi.org/10.1038/s41467-019-09723-8 (2019).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    49.Johnston, A. et al. Abundance models improve spatial and temporal prioritization of conservation resources. Ecol. Appl. 25, 1749–1756. https://doi.org/10.1890/14-1826.1 (2015).Article 
    PubMed 

    Google Scholar 
    50.Robbins, C., Bystrak, D. & Geissler, P. The Breeding Bird Survey: Its First Fifteen Years, 1965–1979. Tech. Rep. (U.S. Fish and Wildlife Service, 1986).51.R Core Team. R: A language and environment for statistical computing (Version 4.0.3) [Computer software] (2020).52.Smith, A. C., Hudson, M.-A., Aponte, V. & Francis, C. North American Breeding Bird Survey—Canadian Trends Website. Data-version 2017 (2019).53.Edwards, B. P. M. & Smith, A. C. bbsBayes: An R package for hierarchical Bayesian analysis of North American breeding bird survey data. J. Open Res. Softw.https://doi.org/10.5334/JORS.329 (2021).Article 

    Google Scholar 
    54.North American Bird Conservation Initiative. Bird Conservation Region Descriptions. Tech. Rep. (U. S. Fish and Wildlife Service, 2000).
    Google Scholar  More

  • in

    Red Panda feces from Eastern Himalaya as a modern analogue for palaeodietary and palaeoecological analyses

    1.Pradhan, S., Saha, G. K. & Khan, J. A. Food habits of the red panda, Ailurus fulgens, in the Singalila National Park, Darjeeling, India. J. Bombay Nat. Hist. Soc. 98, 224–230 (2001).
    Google Scholar 
    2.Bista, D. et al. Distribution and habitat use of red panda in the Chitwan–Annapurna Landscape of Nepal. PLoS ONE 12, e0178797 (2017).PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    3.Martin, P. S. The discovery of America. Science 179, 969–974 (1973).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    4.Miller, G. H. et al. Pleistocene extinction of Genyornis newtoni: human impact on Australian megafauna. Science 283, 205–208 (1999).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    5.Grayson, D. K. & Meltzer, D. J. A requiem for North America overkill. J. Archaeol. Sci. 30, 585–593 (2003).Article 

    Google Scholar 
    6.van der Kaars, S. et al. Humans rather than climate the primary cause of Pleistocene megafaunal extinction in Australia. Nat. Commun. https://doi.org/10.1038/ncomms14142 (2017).Article 
    PubMed 
    PubMed Central 

    Google Scholar 
    7.Louys, J. & Roberts, P. Environmental drivers of megafaunal and hominin extinction in Southeast Asia. Nature 586, 402–406 (2020).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    8.Ripple, W. J. et al. Tertiary fossil fungi from Kiandra, New South Wales. Proc. Linn. Soc. NSW. 97, 141–149 (1975).
    Google Scholar 
    9.Schipper, J. et al. The status of the world’s land and marine mammals: diversity, threat, and knowledge. Science 322, 225–230 (2008).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    10.Brook, S. M. et al. Lessons learned from the loss of a flagship: the extinction of the Javan rhinoceros Rhinoceros sondaicus annamiticus from Vietnam. Biol. Conserv. 174, 21–29 (2014).Article 

    Google Scholar 
    11.Prasad, V., Stromberg, C. A. E., Alimohammadian, H. & Sahni, A. Dinosaur coprolites and the early evolution of grasses and grazers. Science 310, 1177–1180 (2005).ADS 
    CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    12.Shillito, L. M., Blong, J. C., Green, E. J. & VanAsperen, E. N. The what, how and why of archaeological human coprolite analysis. Earth Sci. Rev. 207, 103196 (2020).CAS 
    Article 

    Google Scholar 
    13.van Geel, B. et al. The ecological implications of a Yakutian mammoth’s last meal. Quat. Res. 69, 361–376 (2008).Article 
    CAS 

    Google Scholar 
    14.Rawlence, N. J., Wood, J. R., Bocherens, H. & Rogers, K. M. Dietary interpretations for extinct megafauna using coprolites, intestinal contents and stable isotopes: Complimentary or contradictory?. Quat. Sci. Rev. 142, 173–178 (2016).ADS 
    Article 

    Google Scholar 
    15.Carrion, J. S. Pleistocene landscape in central Iberia inferred from pollen analysis of hyena coprolite. J. Quat. Sci. 22(2), 191–202 (2007).Article 

    Google Scholar 
    16.Wood, J. R. et al. Coprolite deposits reveal the diet and ecology of the extinct New Zealand megaherbivore moa (Aves, Dinornithiformes). Quat. Sci. Rev. 27, 2593–2602 (2008).ADS 
    Article 

    Google Scholar 
    17.Gravendeel, B. et al. Multiproxy study of the last meal of a mid-Holocene Oyogos Yar horse, Sakha Republic, Russia. The Holocene 24(10), 1288–1296 (2014).ADS 
    Article 

    Google Scholar 
    18.Akeret, O., Haas, J. N., Leuzinger, U. & Jacomet, S. Plant macrofossils and pollen in goat/sheep faeces from the Neolithic lake-shore settlement Arbon Bleiche 3, Switzerland. The Holocene 9(2), 175–182 (1999).ADS 
    Article 

    Google Scholar 
    19.Birks, H. H. et al. Evidence for the diet and habitat of two late Pleistocene mastodons from the Midwest, USA. Quat. Res. 79, 1–21 (2018).ADS 

    Google Scholar 
    20.van der Waal, C. et al. Large herbivores may alter vegetation structure of semi-arid savannas through soil nutrient mediation. Oecologia 165, 1095–1107 (2011).ADS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    21.Velazquez, N. J. & Burry, L. S. Palynological analysis of Lama guanicoe modern feces and its importance for the study of coprolites from Patagonia, Argentina. Rev. Palaeob. Palynol. 184, 14–23 (2012).Article 

    Google Scholar 
    22.Basumatary, S. K., McDonald, H. G. & Gogoi, R. Pollen and non-pollen palynomorph preservation in the dung of the Greater one –horned rhino (Rhinoceros unicornis), and its implication to palaeoecology and palaeodietary analysis: a case study from India. Rev. Palaeo. Palynol. 244, 153–162 (2017).Article 

    Google Scholar 
    23.Basumatary, S. K., Singh, H., McDonald, H. G., Tripathi, S. & Pokharia, A. K. Modern botanical analogue of endangered Yak (Bos mutus) dung from India: Plausible linkage with living and extinct megaherbivores. PLoS ONE 14(3), e0202723 (2019).24.Roberts, M. S. & Gittleman, J. L. Ailurus fulgens. Mammalian species. Am. Soc. Mammal. 222, 1–8 (1984).
    Google Scholar 
    25.Johnson, K. G., Schaller, G. B. & Hu, J. C. Comparative behavior of red and giant pandas in the Wolong Reserve, China. J. Mammal. 69, 552–564 (1988).Article 

    Google Scholar 
    26.Yonzon, P. B. & Hunter, M. L. Ecological study of the red panda in Nepal-Himalaya. red panda Biology 1, 7 (1989).
    Google Scholar 
    27.Wei, F. W., Wang, W., Zhou, A., Hu, J. & Wei, Y. Preliminary study on food selection and feeding strategy of red pandas. Acta Theriol. Sin. 15, 259–266 (1995).
    Google Scholar 
    28.Zhang, Z. J., Hu, J. C., Yang, J. D., Li, M. & Wei, F. W. Food habits and space-use of red panda, Ailurus fulgens in the Fengtongzhai Nature Reserve, China: Food effects and behavioural response. Acta Theriol. 54, 225–234 (2009).Article 

    Google Scholar 
    29.Dorji, S., Vernes, K. & Rajaratnam, R. Habitat correlates of the red panda in the temperate forests of Bhutan. PLoS ONE 6, e26483 (2011).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    30.Panthi, S., Aryal, A., Raubenheimer, D., Lord, J. & Adhikari, B. Summer diet and distribution of the Red Panda (Ailurus fulgens fulgens) in Dhorpatan Hunting Reserve, Nepal. Zool. Stud. 51(5), 701–709 (2012).
    Google Scholar 
    31.Sharma, H. P., Swenson, J. E. & Belant, J. L. Seasonal food habits of the red panda (Ailurus fulgens) in Rara National Park, Nepal. Hystrix 25(1), 47–50 (2014).
    Google Scholar 
    32.Panthi, S., Coogan, S. C. P., Aryal, A. & Raubenheimer, D. Diet and nutrient balance of red panda in Nepal. Sci. Nat. 102, 54 (2015).Article 
    CAS 

    Google Scholar 
    33.Thapa, A. & Basnet, K. Seasonal diet of wild red panda (Ailurus fulgens) in Langtang national park, Nepal Himalaya. Inter. J. Conser. Sci. 6(2), 261–270 (2015).CAS 

    Google Scholar 
    34.Thapa, A. et al. The endangered red panda in Himalayas: potential distribution and ecological habitat associates. Glob. Ecol. Conser. 21, e00890 (2020).35.Hu, Y. et al. Genomic evidence for two phylogenetic species and long-term population bottlenecks in red pandas. Sci. Adv. 6, eaax5751 (2020).36.IUCN. IUCN red list of threatened species. Version 2018.1. [Online] Available: www.iucnredlist.org (August 14, 2018).37.Salesa, M. J., Peigne, S., Antón, M. & Morales, J. Evolution of the Family Ailuridae: Origins and Old- World Fossil Record. In Red Panda: Biology and Conservation of the First Panda (ed. Glatston, A. R.) 27–41 (Elsevier, 2011).Chapter 

    Google Scholar 
    38.Thapa, A. et al. Predicting the potential distribution of the endangered red panda across its entire range using MaxEnt modeling. Ecol. Evol. 8, 10542–10554 (2018).PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    39.Chaudhury, A. An overview of the status and conservation of the red panda (Ailurus fulgens) in India, with reference to its global status. Oryx 35(3), 250–259 (2001).Article 

    Google Scholar 
    40.Eizirik, E. et al. Pattern and timing of diversification of the mammalian order carnivora inferred from multiple nuclear gene sequences. Mol. Phylogenet. Evol. 56(1), 49–63 (2015).Article 
    CAS 

    Google Scholar 
    41.Hu, Y. et al. Comparative genomics reveals convergent evolution between bamboo-eating giant and red pandas. Proc. Natl. Acad. Sci. 114(5), 1081–1086 (2017).CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    42.Jha, A. K. Release and reintroduction of captive-bred red pandas into Singalila National Park, Darjeeling, India. In Red panda: biology and conservation of the first panda (ed. Glatson, A. R.) 435–446 (Academic Press, 2011).Chapter 

    Google Scholar 
    43.Wikramanayake, E., E. Terrestrial Ecoregions of the Indo-Pacific: A Conservation Assessment. Washington, D.C.: Island Press. ISBN 1-55963-923-7 (2002).44.Janzen, D. H. Why bamboos wait so long to flower. Ann. Rev. Eco. Syst. 7, 347–391 (1976).Article 

    Google Scholar 
    45.van Geel, B. et al. Giant deer (Megaloceros giganteus) diet from Mid-Weichselian deposits under the present North Sea inferred from molar-embedded botanical remains. J. Quat. Sci. 33, 924–933 (2018).Article 

    Google Scholar 
    46.Basumatary, S. K. & McDonald, H. G. Coprophilous fungi from dung of the greater one-horned Rhino in Kaziranga National Park, India and its implication to palaeoherbivory and palaeoecology. Quat. Res. 88, 14–22 (2017).Article 

    Google Scholar 
    47.Swati, T. et al. Multiproxy studies on dung of endangered sangai (Rucervus eldii eldii) and Hog deer (Axis porcinus) from Manipur, India: Implication for paleoherbivory and paleoecology. Rev. Palaeob. Palyn. 263, 85–103 (2019).Article 

    Google Scholar 
    48.Goh, T. K., Ho, W. H., Hyde, K. D., Whitton, S. R. & Umali, T. E. New records and species of Canalisporium (Hyphomycetes), with a revision of the genus. Canadian J. Bot. 76, 142–152 (1998).
    Google Scholar 
    49.Heudre, D., Wetzel, C. E., Moreau, L. & Ector, L. Sellaphora davoutiana sp. Nov.: a new freshwater diatom species (Sellaphoraceae, Bacillariophyta) in lakes of Northeastern France. Phytotaxa 346(3), 269–279 (2018).Article 

    Google Scholar 
    50.Biswas, O. et al. Can grass phytoliths and indices be relied on during vegetation and climate interpretations in the eastern Himalayas? Studies from Darjeeling and Arunachal Pradesh, India. Quat. Sci. Rev. 134, 114–132 (2016).ADS 
    Article 

    Google Scholar 
    51.Biswas, O. et al. A comprehensive calibrated phytolith based climatic index from the Himalaya and its application in palaeotemperature reconstruction. Sci. Total Environ. 750, 142 (2021).Article 
    CAS 

    Google Scholar 
    52.Chaudhuri, A. B. Common grasses and sedges of Kurseong, Kalimpong and Darjeeling forest divisions, West Bengal. Indian For. 86(6), 336–348 (1960).
    Google Scholar 
    53.Hajra, P. K. & Verma, D. M. Flora of Sikkim, Vol. II. Botanical Survey of India, (1996).54.Neto, M. A. M. & Guerra, M. P. A new method for determination of the photosynthetic pathway in grasses. Photosyn. Res. 142, 51–56 (2019).CAS 
    Article 

    Google Scholar 
    55.Frank, K., Bruckner, A., Hilpert, A., Heethoft, M. & Bluthgen, N. Nutrient quality of vertebrate dung as a diet for dung beetles. Sci. Rep. 17, 12141 (2017).ADS 
    Article 
    CAS 

    Google Scholar 
    56.Tieszen, L. L. Natural variations in the carbon isotope values of plants: implications for archaeology, ecology, and palaeoecology. J. Archaeol. Sci. 78, 227–248 (1991).Article 

    Google Scholar 
    57.Heaton, T. Spatial, species, and yemporal variations in the 13C/12C ratios of C3 plants: Implications for palaeodiet studies. J. Archaeol. Sci. 26, 637–649 (1999).Article 

    Google Scholar 
    58.Arens, N. C., Jahren, A. H. & Amundson, R. Can C3 plants faithfully record the carbon isotopic composition of atmospheric carbon dioxide?. Paleobiology 26(1), 137–164 (2000).Article 

    Google Scholar 
    59.Cerling, T. E., Harris, J. M. & Leakey, M. G. Browsing and grazing in modern and fossil proboscideans. Oecologia 120, 364–374 (1999).ADS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar 
    60.Mac Fadden, B. J., Cerling, T. E., Harries, J. M. & Prado, J. L. Ancient latitudinal gradients of C3/C4 grasses interpreted from stable isotopes of New World Pleistocene horse (Equus) teeth. Global Ecol. Biog. 8, 137–149 (1999).
    Google Scholar 
    61.Burney, D. A., Robinson, G. S. & Burney, L. P. Sporormiella and the late Holocene extinctions in Madagascar. Proc. Natl Acad. Sci. U.S.A. 100(19), 10800–10805 (2003).ADS 
    CAS 
    PubMed 
    PubMed Central 
    Article 

    Google Scholar 
    62.Davis, O. K. & Shafer, D. S. Sporormiella fungal spores, a palynological means of detecting herbivore density. Palaeog. Palaeoclim. Palaeo. 237, 40–50 (2006).ADS 
    Article 

    Google Scholar 
    63.Raper, D. & Bush, M. A test of Sporormiella representation as a predictor of megaherbivore presence and abundance. Quat. Res. 71, 490–496 (2009).Article 

    Google Scholar 
    64.Perrotti, A. G. & Van Asperen, E. N. 2019: Dung fungi as a proxy for megaherbivores: opportunities and limitations for archaeological applications. Veget. Hist. Archaeobot. 28, 93–104 (2019).Article 

    Google Scholar 
    65.Ingold, C. T. Ballistics in certain ascomycetes. New Phytol. 60, 143–149 (1961).Article 

    Google Scholar 
    66.Trail, F. Fungal cannons: explosive spore discharge in the Ascomycota. FEMS Microbio. Letters 276, 12–18 (2007).CAS 
    Article 

    Google Scholar 
    67.Yafetto, L. The fastest flights in nature: high-speed spore discharge mechanisms among fungi. PLoS ONE 3, e3237 (2008).ADS 
    PubMed 
    PubMed Central 
    Article 
    CAS 

    Google Scholar 
    68.Erdtman, G. An introduction to Pollen Analysis (Waltham, 1953).
    Google Scholar 
    69.Gupta, H.P. & Sharma, C. Pollen flora of North-west Himalaya. Indian Association of Palynostratigraphers, Lucknow, India, (1986).70.Van Geel, B. Environmental reconstruction of a Roman Period settlement site in Uitgeest (The Netherlands), with special reference to coprophilous fungi. J. Archaeo. Sci. 30, 873–883 (2003).Article 

    Google Scholar 
    71.Van Asperen, E. N., Kirby, J. R. & Hunt, C. O. The effect of preparation methods on dung fungal spores: Implications for recognition of megafaunal populations. Rev. Palaeobot. Palynol. 229, 1–8 (2016).Article 

    Google Scholar 
    72.Neumann, K. International code for phytolith nomenclature ICPN 2.0. Ann. Bot. 124, 189–199 (2019).Article 

    Google Scholar 
    73.Hill, M. O. & Gauch, H. G. Detrended correspondence analysis, an improved ordination technique. Vegetatio 42(1), 47–58 (1980).Article 

    Google Scholar 
    74.Ter Braak, C. J. F. Canonical correspondence analysis: a new eigenvector technique for multivariate direct gradient analysis. Ecology 67, 1167–1179 (1986).Article 

    Google Scholar 
    75.Ter Braak, C. J. F. Canoco-a FORTRAN program for canonical community ordination by (partial) (detrended) (canonical) correspondence analysis, principal components analysis and redundancy analysis (version 2.1).Technical Rep. LWA-88-02. GLW, Wageningen, 95 pp. (1988).76.Ter Braak, C. J. F. & Smilauer, P. CANOCO 4.5. Biometris. Wageningen University and Research Center, Wageningen, 500 pp. (2002).77.Agnihotri, R. et al. Radiocarbon measurements using new automated graphite preparation laboratory coupled with stable isotope mass-spectrometry at Birbal Sahni Institute of Palaeosciences, Lucknow (India). J. Environ. Radioact. 213, 106156 (2020).CAS 
    PubMed 
    Article 
    PubMed Central 

    Google Scholar  More

  • in

    Identifying and characterizing pesticide use on 9,000 fields of organic agriculture

    We first identify the location of organic crop fields in Kern County and then estimate whether status as organic versus conventional fields determines pesticide use (Fig. 5).Fig. 5: Methodology overview.Figure outlines the main method steps from identifying organic fields to creating the analysis data to performing the statistical analyses. All images shown are simplified, visual representations of the datasets. CDFA refers to the California Department of Food and Agriculture, while APN is the Assessor’s Parcel Number and TRS is the Township-Range-Section. Identifying organic fields combines the created CDFA organic APN, CDFA organic TRS, and organic pesticides data layers together to create the final organic versus conventional fields layer used in the analysis data section. All analysis data layers are then inputted into the various statistical analyses.Full size imageIdentifying organic fieldsWe identified organic fields using a combination of California Department of Food and Agriculture (CDFA) records and Kern County Agricultural Commissioner’s Office spatial data (“fields shapefiles”) and pesticide use records. No single source was complete, and as such, we evaluated several different approaches to identifying organic fields.California Department of Food and Agriculture (CDFA) recordsData on the location of organic fields, per the California State Organic Program, for 2013–2019 was obtained by request from the California Department of Food and Agriculture (CDFA). The CDFA, through the State Organic Program, requires annual registration of certified organic producers who have an expected gross sale of over $5000. We were specifically interested in the pesticide aspects of organic production, which is governed in our study region by the USDA’s National List of Allowed and Prohibited Substances. The National List of Allowed and Prohibited Substances delineates which synthetic substances can be used and which natural substances cannot be used for pest control in US organic production. Besides substances specifically (dis)allowed on the National List, allowed substances include non-synthetic biological, botanical, and mineral inputs. Field location data were in the form of either Assessor’s Parcel Number (APN) or PLS System Township-Range-Section (TRS) values, though data were reported without systematic formatting. We harmonized the CDFA APN values to merge with the Kern County Assessor’s parcel shapefile (2017), which we then spatially joined with the Kern fields shapefiles. We followed a similar process with PLSS TRS values, which were then merged with the Kern County PLS Section shapefile, and joined to Kern field shapefiles. We refer to our final organic designation as “CDFA Organic”. Details of the data cleaning process are described in the Ancillary Data Processing Methods section below.Using pesticide use reports to refine organic field identificationAfter spot-checking pesticide use on CDFA Organic fields, it became clear we had not entirely eliminated conventional fields. This was likely due to variation in polygon geometries between PLSS Sections, Kern County Assessor parcels, and Kern agricultural fields data. To further refine our classification, we used field-level pesticide use, again from the Kern County Agricultural Commissioner’s Office. As thousands of pesticide products (active ingredients + adjuvants) are in use in Kern County, we took an iterative approach to eliminate fields using conventional pesticides. We first limited the universe of pesticides to those applied to fields that were CDFA Organic. We then identified the 50 most commonly used pesticide products by a number of applications, and manually classified each as organic or conventional. Having identified these products as described below, we matched them back in, eliminating fields that used conventional products and identifying as “PUR Organic” those that used only organic products. We repeated this process, hand identifying the most commonly used products and eliminating fields using conventional products until we had isolated fields using only organic products.To classify a product as organic or conventional, we first searched for each product’s U.S. EPA-registered product label, using the exact product name and EPA product registration number. If there was any indication on the label that the product was certified as organic by the Organic Materials Review Institute (OMRI), or said “for use in organic production” or “organic”, then the pesticide was identified as organic (n = 132). If there was no organic indication on the product label, we searched the OMRI certification database for products with identical names and manufacturers, and identified products as organic if such certifications existed (n = 39). If all ingredients were defined (i.e., no inert or undefined ingredients) and were known organic active ingredients, then the pesticide was identified as organic (n = 1) (Supplementary Data 1). We failed to find EPA-registered labels for three products and confirmed on the California Department of Pesticide Regulation website that they are either inactive or out of production (EPA registration numbers: 52467-50008-AA-5905, 36208-50020-AA, 2935-48-AA-120). Each of the three was rarely used (n  0) to be the same as the mechanisms determining the amount sprayed when some pesticides are used (pesticides when pesticides  > 0). Double-hurdle models64 are an alternative to the Tobit model that allows for the separation of these two decisions.The mechanisms underlying the two decisions (to spray, how much to spray if spraying) can differ such that different covariates can describe each process, and the same covariates are allowed to influence the two processes in different ways (i.e., sign and magnitude can differ). The first, binary decision is usually modeled with a probit model.$${{{{{rm{P}}}}}}left(y=0|{{{{{bf{x}}}}}}right)=1-Phi left({{{{{bf{x}}}}}}gammaright)$$
    (1)
    Then, the second decision is modeled as a linear model with pesticide use following a lognormal distribution, conditional on positive pesticide use64$$log (y)|{{{{{bf{x}}}}}},y , > , 0 sim {{{{{rm{Normal}}}}}}({{{{{bf{x}}}}}}{{{{{mathbf{upbeta }}}}}},{sigma }^{2})$$
    (2)
    where Φ is the standard normal cdf, x is a vector of explanatory variables including organic status, y is pesticide use, and ({{{{{mathbf{upbeta }}}}}}) is a vector of coefficients. We use a lognormal hurdle model rather than a truncated normal hurdle model since pesticide use is highly non-normal, and Q-Q plots suggested substantial model improvement using a lognormal rather than normal distribution. In contrast to the panel data models described in the Ancillary Statistical Methods below, our estimation equation used natural log-transformed variables for pesticides (and field and farm size) rather than inverse hyperbolic sine (IHS) transformation since only positive observations are included in the second hurdle model. Following insights derived from our panel data models (Supplementary Notes), we build on the basic hurdle model concept using the farm-by-crop family interaction as a random intercept in both the first and second hurdle. We chose the farm-by-crop family interaction rather than a crossed random effect due to computational feasibility with thousands of permits and hundreds of crops, due to similarity of results to the within estimator model (i.e., fixed effects in causal inference terminology; Supplementary Notes, Supplementary Table 2), and due to AIC/BIC (Supplementary Table 3). Further, we find evidence of heteroskedasticity from both visual inspection and Levine’s test, which adds additional complications to computing crossed random effects. Thus, we proceed with the farm-by-crop family interaction in a random intercept model with cluster robust standard errors clustered at the same grouping. In doing so, observations, where the taxonomic family of the crop was unclear, were dropped. Of the 7367 fields that were dropped due to missing crop families, 6684 were uncultivated agriculture.Our data are effectively repeated cross-sections rather than a true panel since fields are defined by the farm-site-year combination and thus generally change year-to-year or when crops rotate. We model it as such. This implies we do not require observations to have no spray in all time periods, as would be the case in a double hurdle panel model. Linking field IDs over time through spatial processing is complicated by crop rotations of different size areas. Since farmers may farm multiple fields under different management systems, as we illustrate here, and have different contractual obligations at a sub-farm level, requiring farms to never use pesticides on all fields is not reflective of on-the-ground decisions.We repeated the lognormal hurdle models individually for carrots, grapes, oranges, potatoes, and onions, which were the only widely-grown crops with more than 100 organic fields. This allowed for a different slope and intercept by crop type.We conduct several robustness checks. First, we do not have data on crop yields. However, to assess the potential implications of a yield gap on our results, we modify our per hectare rates following Ponisio et al.15 as a robustness check. We group commodities into cereals, roots and tubers, oilseeds, legumes/pulses, fruits, and vegetables and assign them the Ponisio et al.15 yield gap estimates for that group. Crops that did not fall into any of the above groups (e.g., cannabis) were provided the all-crop average from Ponisio et al.15. Second, we analyze how conventional and organic differ with respect to soil quality using a within estimator approach to account for crop-specific differences in soil quality. Third, binary toxicity metrics, while valuable given the number of chemicals and endpoints of interest here, nevertheless fail to distinguish gradations of toxicity for chemicals above (or below) the regulatory threshold. As mentioned above, the data needed to calculate many aggregate indices (e.g., Pesticide Load57 and Environmental Impact Quotient58) are not readily available for all of the chemicals in our study. For completeness, we attempted to calculate the Pesticide Toxicity Index for one well-studied endpoint, fish. We supplemented data provided in Nowell et al.41 with data from Standartox42. However, only about 70% of the chemicals used in our study matched, and pesticide products used on organic fields were more likely to lack toxicity information for one or more chemicals. We briefly discuss the highly preliminary investigation, given the non-random missing toxicity data.All spatial analyses were performed in R Statistical Software v 3.5.3 and all statistical analyses were performed Stata 16 MP. For all tests, statistical significance was based on two-tailed tests with (alpha =0.05.)Ancillary data processing methodsCleaning parcel dataTo spatially locate organic fields, we needed to match the Assessor’s parcel numbers (APNs) provided in the CDFA tabular data to APNs in the Kern County Parcel shapefile (from 2017). Over 90% of the APN entries in the CDFA data were in the format [xxx-xxx-xx], though multiple APNs were often provided in the same cell separated by line breaks, semi-colons, commas, and/or spaces. We made initial edits separating values into individual cells in Microsoft Excel since formatting was highly inconsistent. Observations whose APNs were not in the [xxx-xxx-xx] were modified so that their format matched. In the R environment, dashes were inserted after the third, sixth, and eighth characters (1234567895 became 123-456-78-95) for APNs that did not already contain them. Occasionally, APN numbers were provided with dashes, but with segments of incorrect length (e.g., 12-34-567). In these instances, APN segments were either trimmed from the right or padded with a zero on the left so they matched the [xxx-xxx-xx] format. This approach yielded the greatest number of matches and was checked for accuracy as described below. Additional segments (from APNs with more than two dashes and eight numeric characters) were dropped. A handful of APNs with fewer than eight numeric characters and no dashes were dropped entirely.The edited CDFA APNs were then joined with the Kern County Assessor’s parcel shapefile, creating the “CDFA organic shapefile”. In total, 1637 of 1829 individual CDFA records joined successfully. To evaluate the accuracy of joins between CDFA tabular data, Kern County parcel, and Kern County agricultural spatial data, we spot-checked ownership information using “Company” (CDFA) and “PERMITTEE” (Kern County agricultural data) values.To then identify the crop fields within the organic parcels, we performed a spatial join between the CDFA organic shapefile and the Kern County fields shapefiles. Prior to performing the join, the CDFA parcels’ dimensions were reduced with a 50-m buffer to eliminate spatial joins between CDFA parcels and crop fields that were only touching the parcel margins. Of five different buffer widths evaluated, 50 m reduced the number of false positives and negatives, as determined by comparing the “Company” and “PERMITTEE” values. We refer to the fields that match as “APN Organic”.Cleaning PLSS Township-Range-Section valuesEach year several producers reported Township, Section, and Range (TRS) values, consistent with the PLS System (PLSS), rather than APN values. We used these TRS values to identify PLSS Sections that contained organic fields.We separated any cell containing multiple TRS values and removed any prefixes such as “S”, “Section”, “Sec.”, “T”, and “R” that would prevent joining to Kern County PLSS spatial data in Excel. In the R environment, we padded the left side of the “S” value with a 0 if it was a single digit, then concatenated the three columns into a “TRS” column. We joined TRS from the CDFA tabular data to PLSS spatial data, which identified 563 Sections as containing organic fields, from 2013 to 2019, out of a total of 664 unique TRS codes in the CDFA dataset. We then performed a spatial join between PLSS Sections that contain organic fields and Kern County fields shapefiles, to identify all agriculture fields that overlap with those Sections. Additional processing using the Pesticide Use Reports is described above.Ancillary statistical methodsWe began with a pooled ordinary least squares (OLS) model that, as the name suggests, pools observations over farms, years, and crop types. However, there may be attributes of crops or farms that may be systematically different between organic and conventional, and this systematic difference could bias our pooled OLS results. To address this, we first considered propensity score approaches but were unable to find a sufficient balance of our covariate distribution between organic and conventional fields. As an alternative, we limited our sample to fields with overlapping farmers and crop types. In other words, we focused on the subset of fields that are grown by farmers producing both organic and conventional fields and to crops that are produced both conventionally and organically. However, this shrunk our dataset by two-thirds.To leverage more of our data, we next considered panel data models as a means to address unobserved variables. We consider both within-estimator models (also known as “fixed effects” in causal inference terminology, but different from the biostatistical use of the term) and random effects models (with random intercepts), seeking to capture characteristics of the crop, grower, and year. The advantage of a within-estimator approach is that the omitted variables are removed (through differencing) and thus, they can be correlated with covariates without biasing the estimation. In other words, pesticide use and all covariates are differenced from their crop-specific mean (or crop family, farmer, etc. specific mean, depending on the model). In doing so, the propensity for certain crops (crop family, farmer) to be grown organic or to be fast or slow adopters of new technologies is removed. The disadvantage is that characteristics shared by all fields of a crop (e.g., value) are lost in the differencing, and more importantly, that the differencing is not easily translated to nonlinear models that we employ later in the analysis. Random effects are more easily translated to nonlinear models. The disadvantage of random effects is the strong assumption that the unobserved variables are uncorrelated with the covariates18,65, which is required for random effects coefficient estimates to be unbiased. Here, we see the difference in coefficient estimates between the within-estimator and random effects models are quite small (Supplementary Table 2).Random effects particularly crossed random effects with thousands of permits and hundreds of crops, introduce computational challenges due to large, sparse matrices. Further, we find evidence of heteroskedasticity from both visual inspection and Levine’s test, which adds additional complications to computing crossed random effects. We proceed using the farm-by-crop family interaction in a random intercept model with cluster robust standard errors clustered at the same grouping based on AIC/BIC (Supplementary Table 3), computational feasibility, and similarity to the within-estimator results (Supplementary Table 2). Observations, where the taxonomic family of the crop was unclear, were dropped in any models including family in either the random effects or the cluster robust standard errors. Of the 7367 fields that were dropped due to missing crop families, 6684 were uncultivated agriculture.In the panel data models, we used IHS transformations to accommodate highly non-normal pesticide (and field and farm size) data. IHS is very similar to natural log transformation66 but is defined at zero, which is important given a sizable fraction of our observations have zero pesticide use. As with log–log transformations, IHS–IHS transformation can be interpreted as elasticities. We pre-multiply pesticide use by 100 to improve estimation66, though this does not affect interpretation. As described above, we leverage insights on model specification from the panel data models, but rely on the double hurdle models to parse apart the decision to spray from the decision of how much to spray.Reporting summaryFurther information on research design is available in the Nature Research Reporting Summary linked to this article. More

  • in

    Localised labyrinthine patterns in ecosystems

    The absence of the first principles for biological systems in general, and in particular for vegetation populations where phenomena are interconnected makes their mathematical modelling complex. The theory of vegetation pattern formation rests on the self-organisation hypothesis and symmetry-breaking instability that provoke the fragmentation of the uniform cover. The symmetry-breaking instability takes place even if the environment is isotropic31,33,35. This instability may be an advection-induced transition that requires the pre-existence of the environment anisotropy due to the topography of the landscape34,39,40. Generally speaking, this transition requires at least two feedback mechanisms having a short-range activation and a long-range inhibition. In this respect, we consider three different vegetation models that are experimentally relevant systems: (i) the generic interaction redistribution model describing vegetation pattern formation which incorporates explicitly the facilitation, competition and seed dispersion nonlocal interactions (ii) the local nonvariational partial differential model described by a nonvariational Swift–Hohenberg type of model equation, and (iii) the reaction–diffusion system that incorporate explicetely water transport.The interaction-redistribution approachThe integrodifferential modelThis approach consists of considering a well-known logistic equation with nonlocal plant-to-plant interactions. Three types of interactions are considered: the facilitative (M_{f}(mathbf {r},t)), the competitive (M_{c}(mathbf {r},t)), and the seed dispersion (M_{d}(mathbf {r},t)) nonlocal interactions. To simplify further the mathematical modelling, we consider that the seed dispersion obeys a diffusive process (M_{d}(mathbf {r},t)approx nabla ^{2}b(mathbf {r},t)), with D the diffusion coefficient, b the biomass density, and (nabla ^{2}=partial ^2/partial x^2+partial ^2/partial y^2) is the Laplace operator acting in the (x,y) plane. The interaction-redistribution reads$$begin{aligned} M_{i}=expleft{ frac{xi _{i}}{N_{i}}int b(mathbf {r}+mathbf {r}’,t)phi _i(r,t)dmathbf {r}’right} , { text{ with } } phi _i(r,t)= exp(-r/L_{i}) end{aligned}$$
    (1)
    where (i=f,c). (xi _i) represents the strength of the interaction, (N_i) is a normalisation constant. We assume that their Kernels (phi _i(r,t)) are exponential functions with (L_i) the range of their interactions. The facilitative interaction (M_{f}(mathbf {r},t)) favouring vegetation development. They involve the accumulation of nutrients in the neighbourhood of plants, the reciprocal sheltering of neighbouring plants against climatic harshness which improves the water budget in the soil. The range of the facilitative interaction (L_f) operates on the crown size. The competitive interaction operates over a length (L_c) and involves the below-ground structures, i.e., the rhizosphere. In nutrient-poor or/and in water-limited territories, lateral spreading may extend beyond the radius of the crown. This extension of roots relative to their crown size is necessary for the survival and the development of the plant in order to extract enough nutrients and/or water from the soil. When incorporating these nonlocal interactions in the paradigmatic logistic equation, the spatiotemporal evolution of the normalised biomass density (b(mathbf {r}, t)) in isotropic environmental conditions reads14$$begin{aligned} partial _{t} b(mathbf {r},t)=b(mathbf {r},t)[1-b(mathbf {r},t)]M_{f}(mathbf {r},t)- mu b(mathbf {r},t)M_{c}(mathbf {r},t)+Dnabla ^{2}b(mathbf {r},t). end{aligned}$$
    (2)
    The normalisation is performed with respect to the total amount of biomass supported by the system. The first two terms in the logistic equation with nonlocal interaction Eq. (2) describe the biomass gains and losses, respectively. The third term models seed dispersion. The aridity parameter (mu) accounts for the biomass loss and gain ratio, which depends on water availability and nutrients soil distribution, topography, etc. The homogeneous cover solutions of Eq. (2) are: (b_{o}=0) which corresponds to the state totally devoid of vegetation, and the homogeneous cover solutions satisfy the equation$$begin{aligned} mu =(1-b)exp (Delta b), end{aligned}$$
    (3)
    with (Delta =xi _{f}-xi _{c}) measures the community cooperativity if (Delta >0) or anti-cooperativity when (Delta 0). The solution (u_{-}) is always unstable even in the presence of small spatial fluctuations. The linear stability analysis of vegetated cover ((u_{+})) with respect to small spatial fluctuations, yields the dispersion relation$$begin{aligned} sigma (k)=u_{+}(kappa -2u_{+})-(nu -gamma u_{+})k^{2}-alpha u_{+}k^{4}. end{aligned}$$
    (8)
    Imposing (partial sigma /partial k|_{k_{c}}=0) and (sigma (k_{c})=0), the critical mode can be determined$$begin{aligned} k_{c}=sqrt{frac{gamma -nu /u_{c}}{2alpha }}, end{aligned}$$
    (9)
    where (u_{c}) satisfies (4alpha u_{c}^2(2u_{c}-kappa )=(2gamma u_{c}-nu )^2). The corresponding aridity parameter (eta _{c}) can be calculated from Eq. (7).The reaction–diffusion approachThe second approach explicitly adds the water transport by below ground diffusion. The coupling between the water dynamics and the plant biomass involves positive feedbacks that tend to enhance water availability. Negative feedbacks allow for an increase in water consumption caused by vegetation growth, which inhibits further biomass growth.The modelling considers the coupled evolution of biomass density (b(mathbf {r},t)) and groundwater density (w(mathbf {r},t)). In its dimensionless form, this model reads33$$begin{aligned} frac{partial b}{partial t}= & {} frac{gamma w}{1+omega w}b-b^{2}-theta b+nabla ^{2}b, end{aligned}$$
    (10)
    $$begin{aligned} frac{partial w}{partial t}= & {} p-(1-rho b)w-w^{2}b+delta nabla ^{2}(w-beta b). end{aligned}$$
    (11)
    The first term in the first equation describes plant growth at a constant rate ((gamma /omega)) that grows linearly with w for dry soil. The quadratic nonlinearity (-b^{2}) accounts for saturation imposed by poor nutrients soil. The term proportional to (theta) accounts for mortality, grazing or herbivores. The mechanisms of dispersion are modelled by a simple diffusion process. The groundwater evolves due to a precipitation input p. The term ((1-rho b)w) in the second equation accounts for the evaporation and drainage, that decreases with the presence of vegetation. The term (w^{2}b) models the water uptake by the plants due to the transpiration process. The groundwater movement follows the Darcy’s law in unsaturated conditions; that is, the water flux is proportional to the gradient of the water matric potential41. The matric potential is equal to w, under the assumption that the hydraulic diffusivity is constant41. To model the suction of water by the roots, a correction to the matric potential is included; (-beta b), where (beta) is the strength of the suction. More