In 2023, the reported global installed capacity of FPVwas 2.55 GWp and practical potential electricity generationfrom FPV might be able to produce up to 9434 TWh year−1with 30% array coverage on >100,000 reservoirs.

The ponds used in this study havealmost no watershed and are not connected to a stream orriver, thus limiting inputs of organic matter and nutrients fromoutside the ecosystem

We suggest three options that may reduce the effect of FPV onGHG emissions and dissolved oxygen availability.

Reducing the environmental impacts of FPV on waterbodiesmay influence public and legal acceptance of large-scaleadoption of this emerging renewable energy technology.

Adaptive strategies could be employed to minimize thenegative biogeochemical impacts of FPV deployment.

these changes in the context ofsustainability trade-offs associated with renewable energyproduction.

Experimental evidence sug-gests shading similar to that expected from FPV may lead toincreased phytoplankton biomass and reduced macrophytebiomass,50 though this remains to be tested

Using ourmeasured emissions per kWh, we can estimate that at present,FPV-derived GHG emissions from waterbodies are 6.7 GgCO2-eq year−1 (assuming ∼1000 kWh kWp−1). At modeledpractical potential generation of 9434 TWh year−1, FPV-derived waterbody GHG emissions may increase to 24.6 TgCO2-eq year−1.

we estimate a 26.8% increase in greenhouse gasemissions following FPV installation using a carbon dioxide-equivalent basis.

Sustainability trade-offs of FPV in aquatic ecosystems aredriven by a range of interactive factors, and the goal of net-zeroemissions is affected by biogeochemical processes on land andin water.

Shifts in primaryproducer abundance and dominance following FPV installationmight influence GHG cycling in several ways, including byaltering rates of photosynthesis and CO2 uptake,51,52 loading oforganic matter to the sediment,29 and mixing and stratificationdynamics.

Changes in sediment and watercolumn respiration also will be reflected in water column GHGdynamics (e.g., increased concentrations of CO2 and CH4following panel installation) and air−water GHG ex-change.

The sum of GHG effectsassociated with FPV can be represented by air−water GHGexchange that integrates GHG dynamics taking place withinthe waterbody

GHG emissions associated with water-use change duringand after FPV installation require different considerations andaccounting than for terrestrial PV

following FPV deployment, ponds with FPV becamecolder than ponds without and tended to have more uniformtemperatures throughout the water column (Figure S1).

Experimental Ponds facility to estimate an annual pondemission enrichment of 151.3 g of CO2-eq m−2 year−1 forponds with FPV.

We can combine the average difference in GHG emissions inponds with and without FPV determined here with apreviously published annual GHG budget for the Cornell

we estimate a water-usechange carbon emission from FPV of 2.61 g of CO2-eq kWh−1.

FPV emitted26.8 ± 20.2% more GHGs than ponds without FPV in terms ofCO2-eq pond−1 day−1 (Figure 6A).

Rates of bubble accumulation were similarbetween pond types (p = 0.955; Figure S4A), so any changesin CH4 ebullition associated with FPV installation must havebeen driven by differences in bubble CH4 concentration�indeed, the CH4 concentration in bubble trap headspace inponds with FPV (60.0 ± 4.70% CH4) was nearly twice as highas in ponds without FPV (34.4 ± 4.00% CH4; p < 0.001;Figure S4B).

Combin-ing measured dissolved gas concentrations and k600 values toestimate diffusive CO2 and CH4 flux, we found that, onaverage, whole-pond diffusive CO2 emissions were 23.6 ±7.50% lower and diffusive CH4 emissions were 17.5 ± 25.1%lower following FPV deployment (Figure 6A and Table S4).

Using a BACI approach, we demonstrate that FPV deploymentwith 70% coverage led to increased pond GHG emissionswithin days of deployment, and this effect lasted for weeks tomonths. Increased emissions were driven by greater CH4ebullition which offset reduced diffusive CO2 and CH4emissions in FPV-covered ponds.

Ebullitive CH4 emissions were onaverage nearly twice as high in ponds with FPV (0.21 ± 0.04mmol CH4 m−2 h−1) compared to ponds without FPV (0.11 ±0.02 mmol CH4 m−2 h−1) following FPV installation (p =0.031; Figure 5).

Gas transfer velocities (i.e., k600values) in the FPV-covered center of ponds were 4 times lowerfor CO2 (1.27 ± 0.18 cm h−1) and 3 times lower for CH4 (1.42± 0.59 cm h−1) than open pond centers in ponds without FPV(5.42 ± 2.23 and 4.25 ± 1.22 cm h−1 for CO2 and CH4respectively; Table S3), though these differences were notstatistically significant (p = 0.157 for k600CO2 and p = 0.107 fork600CH4), most likely due to the relatively small sample size.

In both treatments, CH4 dynamics followed seasonalpatterns, with the highest concentrations occurring duringwarm summer months

Ebullitive CH4 fluxesfollowed typical seasonal patterns in ponds both with andwithout FPV

wind speed was determinedby correcting wind speed data from the Ithaca-Tompkinsweather station (NOAA Station WBAN-94761), which islocated ∼2 km from the experimental ponds, using a previouslyestablished correction factor.

We sampled 16 ponds at theCornell Experimental Ponds Facility in Ithaca, NY, USA, insummer 2022 to identify six ponds that were most similarbased on the plant community, temperature, dissolved oxygen,pH, conductivity, dissolved nutrients, and dissolved GHGconcentration

We deployed FPV arrays on constructed ponds at the CornellExperimental Pond Facility in New York, USA in summer2023 (Figure 1).

We made several assumptions as part ofthese calculations: that k600 values for each treatment and forthe pond edge and center were constant throughout thesampling period, that pond edge and center dissolved gasconcentrations were the same for each treatment on eachsampling event, and that pond edge and center watertemperatures were the same for each treatment on eachsampling event.

Weconsidered samples collected from ponds before June 15, 2023,as “before” and samples collected after July 14, 2023, as “after”installation for these models. Data collected from June 15 toJuly 14 was excluded from statistical comparison as FPVconstruction and deployment for Pond 123 and 124 was takingplace during this time

we employed abefore-after-control-impact (BACI) approach to test the short-term response of pond greenhouse gas dynamics to theinstallation of floating solar arrays

We did not consider nitrous oxide dynamics inthis study as it is unimportant in the greenhouse gas budget(<0.001% of the annual CO2-equivalent emissions budget) ofponds at the Cornell Experimental Pond Facility.

wecalculated whole-pond diffusive flux, assuming edge area forboth control and treatment ponds was 270 m2, the pond centersurface area for control ponds was 630 m2, pond center surfacearea for treatment ponds was 270 m2 (this subtracts the totalarea of FPV array that is in physical contact with the watersurface), and that fluxes were constant over a 24 h period.

We compared GHG dynamicsbetween ponds with and without FPV using a mixed modelapproach in R Statistical Software following a BACIapproach.

measuring linear rates ofCO2 and CH4 accumulation (or depletion) in a floatingchamber (18.93 L; 0.071 m2 cross-sectional area) connected toa cavity-ringdown spectroscope (Los Gatos, Inc.) for 5 minand collecting surface water and air samples for analysis of CO2and CH4 concentrations from the same location immediatelyafter the 5 min incubation period as described previously

Diffusive exchange of dissolved gases between ponds and theatmosphere (mmol m−2 h−1) can be calculated from dissolvedgas concentrations as35k C Cdiffusive flux ( )x water air=where Cwater and Cair indicate the gas concentration (μmol L−1)in the water and atmosphere, respectively

We calculatedebullitive flux asVebullitive flux CH bubble volumefunnel area time4m= [ ] ×× ×where [CH4] is the concentration of CH4 in the trap (μL L−1)and Vm is the molar volume of gas at standard conditions (22.4L mol−1).

We deployed passive bubbletrap samplers from May to October 2023 to measure rates ofebullitive CH4 flux.

Wecalculated dissolved gas concentrations using constantsdetermined by Weiss32 and Wiesenburg and Guinasso.

using a gas chromatograph equipped with a flameionization detector and autosampler (Shimadzu GC 2014).

We sampled for dissolved GHGconcentrations in pond surface water on two occasions in2022, and 14 occasions in 2023 using a headspace equilibrationapproach.

We characterized the temperature and dissolved oxygenconcentrations of the water column in each pond using athermistor and an optical dissolved oxygen sensor attached to aManta +35 or a Manta +20 instrument (Eureka Water Probes,Austin, TX).

Floating solar arrays (Ciel etTerre International, France) were deployed on three ponds:the FPV array on pond 124 was constructed from June 15−29,2023, pond 123 from June 29 to July 14, 2023, and pond 125from September 18−28, 2023.

Using these measure-ments, we calculated diffusive CO2 and CH4 emissions andcompared total GHG emissions between ponds with andwithout FPV.

We measured water column temperature,dissolved oxygen saturation, and dissolved CO2 and CH4concentrations in surface and bottom waters, quantified ratesof CH4 ebullition, and determined treatment-specific air−watergas exchange rates (i.e., k600 values)

We deployed FPV arrays on constructed ponds at the CornellExperimental Pond Facility in New York, USA in summer2023 (Figure 1). Arrays were designed to maximize powerproduction potential and thus also potential impacts (70%panel coverage)

Knowing whether FPV leads to greater GHGemissions from waterscapes is key to accurate determination ofthe carbon footprint and savings of this burgeoning energyproduction system

Here, we report results from the first two years of anecosystem-scale experiment used to test the effect of FPVdeployment on GHG dynamics and atmospheric GHGexchange in pond

Accurate quantification ofGHG emissions associated with FPV deployment is warrantedto understand the sustainability trade-offs of this emergingrenewable energy technology.

Here, we usean ecosystem-scale experiment to assess how GHG dynamics in ponds respond toinstallation of operationally representative FPV

CH4 ebullition from small waterbodies is also controlled byfactors such as temperature, dissolved oxygen, and organicmatter availability that are likely affected by FPV installa-tion.

Production and consumption of CO2 and CH4 in ponds,lakes, and reservoirs are dependent on dissolved oxygen,temperature, and the balance between primary production andrespiration

Energy production technologies require land and can alterlandscape GHG emissions,16−20 which may be particularlyimportant when considering the carbon cost of renewableenergy production from technologies touted as low carbon.

FPVdeployment may alter greenhouse gas (GHG) production and emissions fromwaterbodies by changing physical, chemical, and biological processes, which canhave implications for the carbon cost of energy production with FPV.

Demir and Taşkın (2013) conducted the LCA of a con-ceptual wind farm at a designated area in Turkey with highwind potential.

the results of this study were compared withsimilar studies specific to Turkey and findings of the reviewstudies.

the manufacturing location is changed to the Aegean regionof Turkey, and these parts are transported to construction siteby trucks covering a distance of 600 km.

a country-specific database, a national strategy with the fol-lowing steps should be realized:a) Compile and appraise all the research activities per-formed on the subject up to now;b) Prioritize the areas that are not covered but is of impor-tance for the country;c) Assign collaborative researches to fill the data gaps.

It is recommended to perform similar site-specific stud-ies and collect data from actual sites that in turn will help inestablishing a valuable country-specific database.

Scenario analysis showed that recycling ratio assump-tions significantly affect four impact categories (AP, TETP,MAETP and GWP, namely). Therefore it is important tocover different recycling ratio scenario results in decision-making processes for the future energy projections.

. In order to establish the mentionedcountry-specific database, a national strategy should belaunched.

The GWP results of the base scenario of this study is 5.24g CO 2 eq/kWh.

Realdata based on monthly energy generation collected from awind farm for a year indicates capacity factors ranging from21 to 64% with an average value of 40%.

The results obtained by changing the recycle ratioof metals at EoL are given in Fig. 5.

In this part of the study, two scenarios involving the trans-portation of the main units during the construction phase andthe metal recycling ratios at end-of-life (EoL) are analysed.

Caduff et al. 2012 states that environmental impact pergenerated energy decreases as the turbine gets bigger.

Capacity factor is an important variablewhich defines the total energy production of the wind farmand hence affects the environmental impacts directly.

Another importantresult of the mentioned review is that impacts due to trans-portation have minor contributions on the total burdens(Arvesen and Hertwich 2012)

According to this review, for onshore wind farms,production of turbine components cause most of the emis-sions, which is in line with the results of this study as givenin Fig. 3 (Arvesen and Hertwich 2012)

Arvesen and Hertwich (2012) conducted an extensiveliterature review on LCA of energy generation from windpower by investigating 44 cases.

perspective without denoting the actual part of the wind tur-bine.

The following findings are obtained on factors effectingthe manufacturing and installation phase from an overall

The operation and maintenance phase has mostly insignif-icant effect on impacts.

As can be clearly seen from Fig. 3, apart from ODP, theend-of-life phase has a lowering effect on environmentalimpacts.

The main uncertainty in thisLCA is the considered amount of recycling in the futureafter decommissioning the wind farm, and the impact of thisuncertainty on the results is handled by performing scenarioanalysis for various recycling ratios.

Electricity consumption during the manufacturing andinstallation stage is strictly measured by the service providerto determine the cost. Similarly the exact amount of dieselconsumption is obtained from the facility records.

The contribution of various phases of life cycle to environ-mental impact categories are shown in Fig. 3.

From another point of view the following evaluations arederived for the manufacturing and installation phase. Use ofnon-renewable energy sources, in other words, use of coal,natural gas and crude oil are the main contributors of ADPfossil. The main reasons for AP are nitrogen oxide and sul-phur dioxide emissions to atmosphere. Emission of nitrogenoxides to atmosphere, on the other hand, is mainly responsiblefor EP. Trichlorofluoromethane and dichlorotetrafluoroethane

Razdan and Garrett(2015) found similar environmental credits for impacts as92% of the steel, aluminium and copper originating from thewind farm was recycled, and the rest was sent to a landfillafter dismantling.

In another study dealingwith the whole life cycle stages of a wind farm, foundationwas not dismantled, all of the composite rotor wastes weresent to incineration; glass content was directed towards alandfill; and 20% of the rest was recycled (Xu et al. 2018).

A cra-dle-to-grave LCA study performed on a 50-MW onshorewind plant with a 20-year lifetime showed similar negativeimpacts for decommissioning phase (Garret and Ronde,2013)

The wind farm is an onshore facility located in the Marmararegion near Istanbul.

Since metals such as steel are expensive and thereare factories processing recycled steel, the authors chose touse this baseline which also yields a sustainable outcome.

The LCA study is performed as given in ISO 14040/14044standards (ISO 2006a, b). Therefore, goal and scope defini-tion, inventory analysis, impact assessment and interpreta-tion are conducted in an iterative way.

Characterization factors in CML 2001 methodologyare adopted to convert the flows into impact categories(Guinée et al. 2002)

In this sense, this study is the first one thatmodels the data obtained directly from an actual Turkishwind farm.

As of the end of 2019, Turkey has 198wind power plants with a total installed capacity of 8056MW in operation (TWEA 2020).

According to the data presented by theTurkish Wind Energy Association, currently 7.42% of thetotal Turkish electricity generation is originating from windfarms (TWEA 2020).

The 2015–2019 strategic plan prepared by theTurkish Ministry of Energy and Natural Resources statesthat financial incentives will be taken to encourage renew-able energy investments in Turkey (MoENR 2017).

Along withobtaining environmental performances of energy technolo-gies, LCA studies aid lowering the unwanted environmentalimpacts (Strantzali and Aravossis 2016), examining environ-mental trade-offs (Modahl et al. 2012) and evaluating decar-bonization potentials (Ramirez et al. 2020).

It is a known fact that Turkey is not among the countriesthat adopt life cycle thinking, and there are only a few stud-ies contributing to the establishment of a country-specificLCA database.

As Arvesen and Hertwich (2012) advice,it is important to conduct LCA research on wind farms inregions other than Europe.

The objective of this study is to apprise the envi-ronmental impacts of a full-scale wind farm via LCA meth-odology in a cradle to grave scope.

The study by Jianget al. (2018) examines the environmental impacts of gearboxvia LCA.

. LCA is used to examine the environ-mental impacts of a wind farm with 76 turbines of 1.5 MWin another study (Ozoemena et al. 2018)

Although there are literature involving theenvironmental impacts of wind farms (Garrett and Rønde2013; Rashedi et al. 2013; Uddin and Kumar 2014; Var-gas et al. 2015) through LCA methodology as well as com-prehensive reviews of LCA of wind energy (Arvesen andHertwich 2012; Davidsson et al. 2012), it is a well-knownfact that obtaining reliable results depends on the usage ofsite-specific data.

Application of LCA methodology on various processes/products/services is known to create fruitful outcomes thatwill guide the decision-makers, manufacturers, researchersin developing sound strategies to lower the unfavour-able environmental impacts of such activities.

The facility in question is an onshore wind farm located in Turkey with a total installed capacity of 47.5 MWconsisting of 2.5 MW Nordex wind turbines.

Such an effort will makeit possible to analyse and compare different energy mixesin an electricity grid and their effect on the decarboniza-tion objectives of a country.

The aim of this study is to investigate the environmental impacts of a full-scale wind farm using life cycle assessmentmethodology.

Therefore, it is beneficial to employ holistic methodologiessuch as life cycle assessment (LCA) to investigate the pos-sible trade-offs between different impact categories.

Respect entails an understanding of the socioec-ological context of research as it relates to people and place.

There may be other considerations thatare context-specific to a particular culture, such as resourcestewardship institutions or responsibilities that have beendeveloped through years of experience and practice (Turnerand Berkes 2006; Reid et al. 2020)

. Ideally, scientists are invited to collaborate by Indigenouspeople to work on issues important to them, which requires ashift in thinking by scientists to not always take the lead onresearch development.

Cultural sensitivity requires that researchers employ respect,reciprocity, confidentiality, and more (Adams et al. 2014;Ramos 2018)

A key principle to consider isthat research shows the greatest prospects when accompaniedby strong and enduring local engagement in the process.

We therefore adviseresearchers to earn trust and foster healthy working relation-ships with Indigenous peoples to determine research prioritiesand agreements long before data collection begins (Lake et al.2017)

Research design should then unfold in acollaborative and transparent manner, with input from IKholders (Adams et al. 2014

At the onsetof collaborative studies, scientists should first develop researchagreements with Indigenous peoples in whatever form islocally appropriate, a step independent of any institutionalethics approvals

scientists must recog-nize that Indigenous peoples have rights to self-determination,which extends to research partnerships and the creation anddissemination of new knowledge.

There is often an assumption –one we wish to avoid perpetuating here – that IK must be sub-sumed within Western scientific frameworks of knowledge,which can force Indigenous peoples to express themselves inways potentially contradictory to their own value and belief sys-tems (Nadasdy 1999). This practice can distort the accuracy andapplicability of IK, and is harmful to Indigenous ways of being.

Collaborative research with Indigenous partners requiresrecognition that science and scientists have in the past and con-tinue at present to (1) impose harm on Indigenous peoples; (2)discount IK; and (3) inappropriately reproduce, apply, or other-wise use information derived from IK (Pierotti 2012; Berkes2018)

Those seeking collaborations should be acutely aware thatclear tensions exist between IK and Western science epistemolo-gies.

For example, in a meta-analysis of climatic changesobserved by subsistence-oriented peoples from 2230 localitiesin 137 countries around the world, Savo et al. (2016

Manyterritories in which cultural and knowledge transmission isongoing also tend to be remote and biodiverse, which posi-tion these title holders (that is, legal owners of land in thecontext of Indigenous laws) as natural biodiversity specialists(Figure 5; Garnett et al. 2018

This knowledge was in part derivedfrom how the area’s Haíɫzaqv people related to wolves; people ofthe territory also differ, depending on whether lineages originatefrom mainland or island areas.

Relational understanding was showcased in an example fromcoastal British Columbia, where IK holders shared knowledge oftwo wolf (Canis lupus) forms, locally referred to as “timberwolves” of the mainland and “coastal wolves” of the immediatelyadjacent offshore islands

with thegoal of transcending the incorporation (and often, assimilation)of IK into Western science through the adoption of an ethic andframework of knowledge coexistence and complementarity.

Yet these time-testedapproaches can also be complemented with modern tools andtechniques, including those of science that augment Indigenousways of knowing.

leadingthe authors to conclude that conservation efforts would beenhanced by hiring local people rather than opting forexpensive telemetry equipment.

Owing in part to these relationships, Indigenous peoplesare ideal partners for research about the natural world.

. Such insight into hypothesis formation was made possiblebecause relationships among people, organisms, and the environ-ment in this area (and elsewhere) comprise a central axis aroundwhich IK is conceived, generated, and transmitted.

Understanding these differences and commonalitiescan aid in collaborative research with Indigenous peoples.

McBride et al. (2017) usedParticipatory Geographic Information Systems that drew uponand analyzed IK observations from Indigenous peoples acrossthe US related to fuel load, forest type, and burn severity.

trackers could provideauxiliary natural history data whereas radio tracking waslimited solely to data on movement.

Attum et al. (2008) demon-strated that estimates of Egyptian tortoise (Testudo klein-manni) home ranges in North Sinai, Egypt, derived fromradio telemetry were in agreement with estimates byIndigenous people, who tracked tortoises on foot,

In the example mentioned above,Riedlinger and Berkes (2001) also described how Inuit observa-tions and hypotheses of climate change in northern Canadacould account for multiple interacting variables and ecologicalcomplexity, such as climate variability and sea-ice break up.

Similarly, Bonta et al. (2017) testedhypotheses about how fire-foraging raptors in tropicalsavannas in Australia could deliberately spread wildfires bycarrying burning sticks to unburned areas to flush outpotential prey species.

For instance,Riedlinger and Berkes (2001) detailed contexts in whichInuit developed hypotheses based on their own observa-tions, such as the prediction that increased winterkill ofcommon eiders (Somateria mollissima) would follow irregu-lar sea-ice conditions.

The conclusions drawn from IK have interdisciplinary rele-vance as well.

Knowledge holders acrossdistinct cultures and environments accumulate information innumerous ways, including harvesting, observation, animalhusbandry, and experimentation, all supplemented by teach-ings from oral histories and cultural practices (Turner et al.2000; Berkes and Berkes 2009)

Research at the IK–science interface can benefit from thediversity inherent in IK approaches

Suchrecognition of system complexity (including synergistic and con-founding variables) is characteristic of IK, with the holistic viewsof ecosystems stemming in part from “relational” understandingsamong ecosystem components, including humans (Cajete 1995;Turner et al. 2000; Atleo 2011

considered by science, a reality supported by the fact thatIndigenous peoples themselves regularly form and testhypotheses (Cajete 1995; Atleo 2011).

Hypotheses constructed within the borders of scientificknowledge may be limited in complex or little-studied systems, aconstraint IK can address.

Indigenousways of knowing can shape and detail predictions not

Insights from IK can be relevant at many stages of theresearch process, including but not limited to project con-ceptualization and hypothesis development.

IK is often closely rooted in human survival and relation-ships between people and nature, and may furthermoretightly couple knowledge accumulation with cultural respon-sibility (Reid et al. 2020)

IK and science can share common properties andoffer complementary conceptual underpinnings

Anexample of how IK can provide information about healthand body condition comes from East Africa. In Kenya andSouth Sudan,

Eckert et al. (2018), forinstance, quantified size changes in yelloweye rockfish(Sebastes ruberrimus) based on historical accounts from theHaíɫzaqv, Kitasoo/Xai’xais, Nuxalk, and Wuikinuxv peoplesof western Canada.

In the meridianAmazon of Brazil, dos Santos and Antonini (2008), in docu-menting Enawene-Nawe knowledge of stingless bees, foundthat IK holders could discriminate among 48 different spe-cies and specify the ecological niche of each species.

Lee et al. (2018) coupled historical observations from theHaíɫzaqv First Nation of British Columbia with zooarchaeo-logical and scientific data to estimate northern abalone(Haliotis kamtschatkana) abundance on the Pacific coast ofCanada from the Holocene to the present.

Polfus et al. (2014) developed habitatmodels for woodland caribou (Rangifer tarandus caribou)based on IK from the Taku River Tlingit First Nation ofnorthern British Columbia, and showed a high degree ofsimilarity between resource selection functions (RSF) thatestimated habitat use derived from IK and collared caribou.

in HaíɫzaqvTerritory (coastal British Columbia), explic-itly guided by the Gvi’ilas (customary law) ofthe Haíɫzaqv people. The approach combinedHaíɫzaqv cultural values with their knowl-edge of bears, salmon, and people in animportant large watershed.

IK has also been proposed as a counterto the “shifting baseline syndrome” in conser-vation,

IK cannotbe separated from the value systems thatunderpin decision- making processes inapplied ecology (Artelle et al. 2018)

Such biocultural approaches enhance long-terminvestment in conservation and management programs bypreserving the linkages between Indigenous peoples and theecosystems on which their cultures and societies depend.

Biocultural approaches to applied research and managementfurther extend this progression by addressing biological andcultural diversity simultaneously (Stephenson et al. 2014;Gavin et al. 2015; DeRoy et al. 2019)

The assertion of Indigenous rights to man-agement and conservation of resources doesnot exclude the application of science, and infact complementary approaches will likely beprevalent.

scientists should transition from considering Indigenouspeoples solely as participants in research to leaders inapplied resource management projects supportive of resur-gent self-governance and sovereignty (Thompson et al. 2020).

Long-termobservations by Indigenous peoples amountsto monitoring of species and ecosystems,which carries abundant potential for rapidand sensitive detection of contemporary eco-logical changes (Berkes et al. 2007; Serviceet al. 2014; Thompson et al. 2019)

Catley (2006) found agreement in diseaseidentification and diagnostic criteria between Indigenouspastoralists and veterinarians in their independentapproaches in monitoring livestock health. TranslatingIndigenous terms into a format recognizable by veterinari-ans, and vice-versa, enhanced livestock surveillance systemsby providing culturally relevant disease diagnostic criteriafor use in rural areas.

Polfuset al. (2016) described how the Sahtú Dene and Métis peo-ples of northern Canada distinguished among geneticallydifferent populations of boreal, mountain, and barren-ground caribou based on unique behaviors, habitat prefer-ences, and morphology, with subsequent genetic analysesproviding evidence of distinct caribou subpopulation struc-ture that aligned with Dene classifications.

distribution of non-invasive hair snares from which datawere subsequently used in a DNA-based capture–recaptureanalysis.

Place- basedknowledge of bear ecology guided theresearch design by informing the spatial

Drawing on millennia-old accumulation of knowledge andits contemporary recognition by others, IK has informed,enhanced, and complemented the study of ecology, evolu-tion, and related fields (Figure 2)

Housty et al. (2014) developed andapplied a monitoring program for grizzlybears (Ursus arctos horribilis) in HaíɫzaqvTerritory (coastal British Columbia), explic-itly guided by the Gvi’ilas (customary law) ofthe Haíɫzaqv people.

However, the perceptions and preferences ofIndigenous peoples considering collaborations withresearchers should supersede any counsel we offer here.

We do not imply of course that knowl-edges must be integrated, or that IK must be published in thescientific literature to be recognized.

While often used on its own or in parallel to science, IK is alsoincreasingly interwoven with data collected via the scientificmethod, and vice versa (that is, scientific methods are incorpo-rated into contemporary processes underlying IK generation).

IK has been recognizedin the scholarly literature as having enriched understandingof a range of individual-level processes, including behavior(eg Bonta et al. 2017) and habitat selection (eg Polfus et al.2014)

IK has also contributed to the literature on population- toecosystem-level processes.

IK can also address processes at the community and ecosys-tem levels, including interspecific interactions (eg Wehi 2009)and ecosystem function (eg Savo et al. 2016)

IK has also contributed to understanding related to evolu-tion in many systems.

Understanding of physiology can also emerge from long-term observations, including harvesting and preparingplants and animals for food, medicine, shelter, clothes, andmore.

respecting self- determination of Indigenous peoples is a necessary conditionto support mutually beneficial research processes and outcomes.

. IK is often augmented with contemporary obser-vations and experiences that refine accumulated knowledge andallow for flexibility and adaptability in the context of environ-mental and social change.

IK is distinct from science, localknowledge, and citizen science in that it includes not only directobservation and interaction with plants, animals, and ecosystems,but also a broad spectrum of cultural and spiritual knowledgesand values that underpin human–environment relationships(Berkes 2018)

IK in itsbroad scope also includes “Traditional Ecological Knowledge”(TEK) and “Indigenous Ecological Knowledge” (IEK) whenknowledge relates to ecology.

IK is generally thought ofas a body of place-based knowledges accumulated and transmit-ted across generations within specific cultural contexts.

Application ofthese broad and deep knowledges in a scientific context hasled to many contributions to the literature in ecology,evolution, and related fields

we outline the ethical duty required by scientists when work-ing with IK holders.

Thevaried contributions of IK stem from long periods of observation, interaction, and experimentation with species, ecosystems, andecosystem processes.

Despite its millennia-long and continued application by Indigenous peoples to environ-mental management, non- Indigenous “Western” scientific research and management have only recently considered IK.

Indigenous Knowledge (IK) is the collective term to represent the many place-based knowledges accumulated across generationswithin myriad specific cultural contexts.

It’s also timely for New York state, where floating solar could be considered as an alternative to terrestrial solar and is the source of debate and exploration.

The idea here is to nip that in the bud and re-envision the way we approach this energy transition.

three ponds at the Cornell Experimental Pond Facility

The data is particularly important because much of the floating solar development in the U.S. is currently happening on small lakes and ponds

“If you look at the history of energy transitions – from wood to fossil fuels, for example – everything was based on energy production, and the environment wasn’t taken into consideration

“It’s all about trade-offs,” Grodsky said. “But we need to be aware of what’s happening to be able to adapt – maybe siting differently, or designing the panels differently, or changing the percentage of cover.”

“There have been a flurry of papers about floating solar, but it’s mostly modeling and projections,” said Steven Grodsky

The study offers some bright sides for floating solar: When comparing floating solar to terrestrial solar in total emissions cost, from site development to maintenance and disposal

While floating solar – the emerging practice of putting solar panels on bodies of water – is promising in its efficiency and its potential to spare agricultural and conservation lands, a new experiment finds environmental trade-offs.

This is the first manipulative study to produce empirical results.

Grodsky and collaborators covered three ponds at the Cornell Experimental Pond Facility with solar panels, at 70% coverage, and found that, almost immediately, methane and carbon dioxide emissions

Housty et al. (2014) developed andapplied a monitoring program for grizzlybears (Ursus arctos horribilis) in HaíɫzaqvTerritory (coastal British Columbia), explic-itly guided by the Gvi’ilas (customary law) ofthe Haíɫzaqv people. The approach combinedHaíɫzaqv cultural values with their knowl-edge of bears, salmon, and people in animportant large watershed.

Understanding of physiology can also emerge from long-term observations, including harvesting and preparingplants and animals for food, medicine, shelter, clothes, andmore.

IK has also contributed to understanding related to evolu-tion in many systems.

IK can also address processes at the community and ecosys-tem levels, including interspecific interactions (eg Wehi 2009)and ecosystem function (eg Savo et al. 2016)

IK has also contributed to the literature on population- toecosystem-level processes.

IK has been recognizedin the scholarly literature as having enriched understandingof a range of individual-level processes, including behavior(eg Bonta et al. 2017) and habitat selection (eg Polfus et al.2014)

Drawing on millennia-old accumulation of knowledge andits contemporary recognition by others, IK has informed,enhanced, and complemented the study of ecology, evolu-tion, and related fields

IK is generally thought ofas a body of place-based knowledges accumulated and transmit-ted across generations within specific cultural contexts.

However, the perceptions and preferences ofIndigenous peoples considering collaborations withresearchers should supersede any counsel we offer here.

We do not imply of course that knowl-edges must be integrated, or that IK must be published in thescientific literature to be recognized.

respecting self- determination of Indigenous peoples is a necessary conditionto support mutually beneficial research processes and outcomes.

we outline the ethical duty required by scientists when work-ing with IK holders.